EPA Clean Water Act 303(c) Determinations On Oregon’s New and Revised Aquatic Life Toxic Criteria Submitted on July 8, 2004, and as Amended by Oregon’s April 23, 2007 and July 21, 2011 Submissions


U.S. ENVIRONMENTAL PROTECTION AGENCY - REGION 10

EPA Clean Water Act
303(c) Determinations

On Oregon's New and Revised
Aquatic Life Toxic Criteria Submitted on
July 8, 2004, and as Amended by Oregon's
April 23, 2007 and July 21, 2011 Submissions

January 30, 2013

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TABLE OF CONTENTS

Contents

I. INTRODUCTION	3

A.	Clean Water Act Requirements for Water Quality Standards	3

B.	History	3

C.	Summary of Actions on Specific Aquatic Life Criteria	5

II. OREGON'S FISH AND AQUATIC LIFE DESIGNATED USE AND APPLICABLE
TOXICS AQUATIC LIFE CRITERIA	7

A.	Fish and Aquatic Life Designated Use	7

B.	Oregon's Narrative and Numeric Aquatic Life Criteria for Toxic Substances	7

III. EPA'S ACTION ON THE INTRODUCTORY LANGUAGE, THE NEW AND REVISED
AQUATIC LIFE CRITERIA AND THE FOOTNOTES IN TABLE 33A	9

A.	Table 33A in Oregon's Water Quality Standards	9

B.	EPA's CWA Determinations on Table 33A	15

1.	EPA's Action on Introductory Language to Table 33A	15

2.	Approval Action for New or Revised Aquatic Life Criteria in Table 33 A (BHC-gamma
(Lindane), Dieldrin, Endrin, Pentachlorophenol)	16

3.	Disapproval Action for Changes to Aquatic Life Criteria Moved From Table 20 to Table
33A (Aldrin, BHC-gamma (Lindane), Chlordane, DDT 4,4, Dieldrin, Endosulfan, Endrin, and
Heptachlor)	17

4.	Disapproval Action for New Criteria in Table 33 A (Endosulfan alpha, Endosulfan beta, and
Heptachlor epoxide)	20

5.	EPA's Action on Footnotes in Table 33A	21

6.	EPA's Action on Non-substantive Formatting Changes in Table 33A	29

IV. EPA'S ACTION ON THE INTRODUCTORY LANGUAGE, NEW AND REVISED
AQUATIC LIFE CRITERIA, AND FOOTNOTES IN TABLE 33B	31

A.	Table 33B in Oregon's Water Quality Standards	31

B.	EPA's CWA Determinations on Table 33B	34

1.	EPA's Action on the Introductory Language to Table 33B	34

2.	Aquatic Life Criteria Deleted from Table 33B (Freshwater and Saltwater Arsenic Criteria,
Saltwater Chromium VI Criteria)	35

3.	Approval Action for New or Revised Aquatic Life Criteria in Table 33B	37

4.	Disapproval Action for New or Revised Aquatic Life Criteria in Table 33B	40

5.	EPA's Action on the New Footnotes In Table 33B	51

6.	Non-substantive Formatting Changes in Table 33B	58

1

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V. EPA'S ACTION ON REVISIONS TO TABLE 20	59

A.	Introductory Language to Table 20	59

B.	EPA's Action on the Addition of Freshwater Hardness-based Equations for Table 20	61

C.	EPA's Action on Non-substantive Editorial or Formatting Changes in Table 20	63

D.	Guidance Values Moved from Table 20 to Table 33C	64

ENCLOSURE 1

Aquatic Life Criteria Submitted by Oregon in July 2004 As Amended by the
April 2007 and July 2011 Water Quality Standards Submissions

ENCLOSURE 2
ENCLOSURE 3

Supplemental Technical Support Document

Responses to Supplemental Comments Submitted by Pacific Environmental
Advocacy Center to U.S. EPA Region 10 Concerning Oregon's New and
Revised Aquatic Life Criteria

ENCLOSURE 4

Aquatic Life Criteria In Effect for Clean Water Act Purposes

2

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I. INTRODUCTION

This document provides the basis for EPA's decisions under the federal water quality standards
regulations at 40 CFR 131.11 and section 303(c) of the Clean Water Act (CWA) to approve or
disapprove the new or revised aquatic life water quality criteria that Oregon submitted to EPA on July 8,
2004 as revised by Oregon's April 23, 2007 and July 21, 2011 submissions.

A.	Clean Water Act Requirements for Water Quality Standards

Under Section 303(c) of the CWA and federal implementing regulations at 40 CFR § 13 1.4, states have
the primary responsibility for reviewing, establishing, and revising WQS, which consist of the
designated uses of a waterbody, or waterbody segment, the water quality criteria necessary to protect
those designated uses, and an antidegradation policy. This statutory framework allows states to work
with local communities to adopt appropriate designated uses (as required in 40 CFR § 131.10 (a)) and to
adopt criteria to protect those designated uses (as required in 40 CFR § 131.11 (a)).

Section 303(c)(2)(B) requires states to adopt water quality criteria for toxic pollutants listed pursuant to
Section 307(a)(1) for which EPA has published criteria under 304(a) where the discharge or presence of
these toxics could reasonably be expected to interfere with the designated uses adopted by the state. In
adopting such criteria, states must establish numeric values based on one of the following: (1) 304(a)
guidance; (2) 304(a) guidance modified to reflect site-specific conditions; or, (3) other scientifically
defensible methods (40 CFR § 131.11 (b)). In addition, states can establish narrative criteria where
numeric criteria cannot be determined or to supplement numeric criteria.

States are required to review applicable WQS, and as appropriate, modify and adopt these standards (40
CFR § 13 1.20). The state must follow its own legal procedures for adopting such standards (40 CFR §
131.5) and submit certification by the state's attorney general or other appropriate legal authority within
the state that the WQS were duly adopted pursuant to state law (40 CFR § 131.6(e)). Section 303(c) of
the CWA also requires states to submit new or revised WQS to EPA for review.

EPA is required to review these changes to ensure revisions in designated water uses are consistent
with the CWA and that new or revised criteria protect the designated water uses. Furthermore, the
federal water quality standards regulations at 40 CFR § 131.21 state, in part, that when EPA
disapproves a state's water quality standards, EPA shall specify changes that are needed to ensure
compliance with the requirements of Section 303(c) of the CWA and federal water quality standards
regulations.

B.	History

In 1999, the Oregon Department of Environmental Quality (ODEQ) initiated a Water Quality Standards
Review (triennial review) to update Oregon's criteria for toxic pollutants, which were based on the
Quality Criteria for Water 1986 (U.S. Environmental Protection Agency, Office of Water, Washington,
D.C. EPA 440/5-86-001) and that were contained in OAR 340-041-0033 and Table 20 of Oregon's
water quality standards. This review was completed in 2003. During this review, ODEQ made
significant revisions to their aquatic life criteria1. The Oregon Environmental Quality Commission
(EQC) adopted these new and revised water quality standards on May 20, 2004. In accordance with

1 A number of the actions described here also addressed changes to human health criteria. Those human health criteria were
the subject of different EPA actions, and are not addressed further in this document.

3

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Section 303(c) of the CWA the ODEQ submitted these revisions to the EPA for review and approval on July
8, 2004. The ODEQ's 2004 revisions to the water quality standards included the following:

1. Revisions to the water quality standards provision at OAR 340-041-0033(1), (2), and (3) that
provide narrative language explaining the human health and aquatic life criteria tables.

2. Revisions to Table 20 (revised the introductory language to the table).

3. Addition of new tables 33A and 33B.

The ODEQ envisioned that once the EPA approved its new Tables 33A and 33B, Table 20 would
become obsolete because Tables 33 A and 33B would contain either the same, revised, or new criteria for
all of the parameters in Table 20. However, if the EPA does not approve a given new or revised
criterion then the corresponding criterion in Table 20 would remain in effect.

On February 22, 2007, the EQC adopted a number of rule revisions to correct errors and clarify language in
Division 41 of the water quality standards rules as revised in 2004. This rulemaking corrected a number of
typographical errors contained in Tables 33A and 33B, revised temperature narrative criteria for natural
lakes, ocean and bays, cool water (including the Klamath River) and the Borax Lake Chub. During this
rulemaking the revised freshwater and saltwater acute and chronic criteria for arsenic and the revised
saltwater acute and chronic criteria for chromium VI, which were part of the 2004 aquatic life criteria
revisions, were inadvertently removed from Table 33B. Oregon submitted these revisions to the EPA for
review and approval on April 23, 2007. EPA did not act on any provisions related to aquatic life toxic
criteria (including changes to Tables 20, 33A or 33B) except for a note to Table 33A and a note to Table 33B
that showed which criteria Oregon believes may be used by the state in NPDES permits2 (see February 28,
2011 letter from Michael A. Bussell, EPA to Neil Mullane, ODEQ).

On June 1, 2010 EPA completed its review of Oregon's new and revised human health (but not aquatic
life) water quality criteria for toxics and revisions to the narrative toxic provisions submitted to EPA on
July 8, 2004. In that action, EPA approved the revisions to the narrative toxic provisions at OAR 340-
041-0033(1) and (2). EPA determined that OAR 340-041-0033(3) was not a water quality standard and,
therefore, did not act on that provision under Section 303(c) of the CWA (see June 1, 2010 letter from
Michael A. Bussell, EPA to Neil Mullane, ODEQ, and Technical Support Document, for Action on the
State of Oregon's New and Revised Human Health Water Quality Criteria for Toxics and Revisions to
Narrative Toxics Provisions Submitted on July 8, 2004).

On June 15, 2011, the EQC revised the narrative language explaining the aquatic life criteria tables at
OAR 340-041-0033. Additionally, the hardness based acute and chronic equations were added in a table
below Table 20. The ODEQ submitted these revisions to the EPA for review and approval on July 21,

20113.

2 The 2007 adoption by ODEQ added the following notes to Tables 33 A and 33B. Table 33 A added the following: "Note:
The Environmental Quality Commission adopted the following criteria on May 20, 2004 to become effective February 15,
2005. However, EPA has not yet (as of June 2006) approved the criteria. Thus, Table 33A criteria may be used in NPDES
permits, but not for the section 303(d) list of impaired waters." Table 33B added the following: "Note: The Environmental
Quality Commission adopted the following criteria on May 20, 2004 to become effective on EPA approval. EPA has not yet
(as of June 2006) approved these criteria. The Table 33B criteria may not be used until they are approved by EPA."

3 Among other things this submittal changed the numbering of the narrative provisions as follows:

OAR 340-041-0033(1) became OAR 340-041-0033(2)

OAR 340-041-0033(2) became OAR 340-041-0033(3)

OAR 340-041-0033(3) became OAR 340-041-0033(5)

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On October 17, 2011, EPA approved minor revisions to the narrative water quality standards provision at
OAR 340-041-0033 (see Technical Support Document for Action on the State of Oregon's New and
Revised Human Health Water Quality Criteria for Toxics and Associated Implementation Provisions
Submitted July 12 and 21, 2011).

Today's action addresses Oregon's new and revised aquatic life water quality criteria for toxic pollutants
contained in Tables 20, 33 A, 33B that were submitted to EPA July 8, 2004, as revised by Oregon on
April 23, 2007 and July 21, 20ll4

C. Summary of Actions on Specific Aquatic Life Criteria

The table below provides a summary of the actions that EPA is taking on freshwater and saltwater
aquatic life criteria. This table does not address EPA's actions on new/revised introductory language,
new footnotes, or any editorial/formatting changes.

Red:	disapprove

Black:	APPROVE

Blue:	delei egon originally adopted these criteria into their water quality standards in

2004, but in 2007 Oregon inadvertently deleted these criteria from their WQS; EPA is not
taking an action on these criteria).

4

The ODEQ proposed revisions to OAR 340-041 on June 2, 2003. The public comment period extended from June 2, 2003,
through August 29, 2003. Revisions were adopted by the Oregon Environmental Quality Commission (Commission) on May
20, 2004, and filed with Oregon Secretary of State on May 28, 2004. ODEQ submitted these revisions to EPA for review and
approval on July 8, 2004 along with a letter dated July 8, 2004, from Larry Knudsen, Assistant Attorney General, certifying
that the revisions were adopted in accordance with Oregon State law. In 2005, ODEQ again proposed revisions to OAR 340-
041. The public comment period extended from October 17, 2005 through February 6, 2006. These revisions were adopted
by the Commission on February 22, 2007, and filed with Oregon Secretary of State on March 14 and 15, 2007. ODEQ
submitted these revisions to EPA for review and approval on April 23, 2007. Oregon's submittal included a letter dated April
10, 2007, from Larry Knudsen, certifying that the revisions were adopted in accordance with Oregon State law. On December
15, 2010 ODEQ proposed revisions to OAR 340-041. The public comment period extended from December 21, 2010 through
March 21, 2010. Revisions were adopted by the Commission on June 16, 2011, and filed with Oregon Secretary of State on
July 13, 2011. DEQ submitted these revisions to EPA for review and approval on July 21, 2011. Oregon's submittal
included a letter dated July 20, 2011, from Larry Knudsen, certifying that the revisions were adopted in accordance with
Oregon State law.

5

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COMPOUND

FRESHWATER

SALTWATER

Acute
(CMC)

Chronic
(CCC)

Acute
(CMC)

Chronic
(CCC)

Aldrin

disapprove

—

disapprove

—

Aluminum

disapprove

disapprove

—

—

Ammonia

disapprove

disapprove





Arsenic

deleted

deleted

deleted

deleted

BHC gamma- (Lindane)

approve

disapprove

disapprove

—

Cadmium

disapprove

approve

approve

approve

Chlordane

disapprove

disapprove

disapprove

disapprove

Chromium (III)

approve

approve

—

—

Chromium (VI)

approve

approve

deleted

deleted

Copper

disapprove

disapprove

approve

approve

DDT 4,4'-

disapprove

disapprove

disapprove

disapprove

Dieldrin

approve

approve

disapprove

disapprove

Endosulfan

disapprove

disapprove

disapprove

disapprove

Endosulfan alpha-

disapprove

disapprove

disapprove

disapprove

Endosulfan beta-

disapprove

disapprove

disapprove

disapprove

Endrin

approve

approve

disapprove

disapprove

Heptachlor

disapprove

disapprove

disapprove

disapprove

Heptachlor Epoxide

disapprove

disapprove

disapprove

disapprove

Lead

approve

approve

approve

approve

Nickel

approve

approve

approve

approve

Pentachlorophenol

approve

approve

—

approve

Selenium

disapprove

disapprove

approve

approve

Silver

approve

approve

approve

—

Tributyltin (TBT)

approve

approve

approve

approve

Zinc

approve

approve

approve

approve

Note: "—" means a new or revised criterion was not adopted by Oregon.

6

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II. OREGON'S FISH AND AQUATIC LIFE DESIGNATED USE AND
APPLICABLE TOXICS AQUATIC LIFE CRITERIA

A.	Fish and Aquatic Life Designated Use

Oregon's water quality standards regulations contain several provisions that address the designated uses
in Oregon Administrative Rules (OAR) sections 340-041-0101 through 340-041-0340. The terminology
Oregon uses to identify the State's aquatic life use is "Fish & Aquatic Life." Oregon has designated the
fish and aquatic life use for all waters of the State. Oregon has divided its waters into 21 basins; each
basin has a specific table listing the applicable designated use (e.g., fish and aquatic life, irrigation, and
boating).

EPA evaluated the protectiveness of Oregon's water quality criteria for the fish and aquatic life
designated use.

B.	Oregon's Narrative and Numeric Aquatic Life Criteria for Toxic Substances

This action addresses the new and revised criteria listed in the freshwater and saltwater columns of
Tables 33A and 33B, the introductory language to tables 20, 33A, and 33B, and the footnotes associated
with each table.

Since Oregon applies its numeric toxics criteria to the fish and aquatic life designated use, which
includes all of the aquatic communities present in Oregon's waters, EPA evaluated Oregon's numeric
toxics criteria with respect to all available acceptable toxicity tests for aquatic organisms that compose
aquatic communities in Oregon.

The remainder of this document is organized as follows:

Part III of this document provides Oregon's new and revised criteria (and associated footnotes) in
Table 33A and provides EPA's review and action.

Part IV of this document provides Oregon's new and revised criteria (and associated footnotes) in Table
33B and provides EPA's review and action.

Part V of this document provides Oregon's revisions to the introductory language for Table 20 and
other minor editorial changes to the table and EPA's review and action on these revisions.

Enclosure 1 to this document provides Tables 20, 33 A, and 33B submitted by Oregon in it July 2004
water quality standards submittal, as amended by its submissions in April 2007 and July 2011 (Aquatic
Life Criteria Submitted by Oregon in July 2004 As Amended by the April 2007 and July 2011 Water
Quality Standards Submissions)

Enclosure 2 to this document provides the Supplemental Technical Support Document (STSD), which
provides additional scientific and technical information supporting EPA's decision on those proposed
criteria that are consistent with EPA's CWA § 304(a) recommended criteria and that EPA is approving.

Enclosure 3 to this document provides responses to supplemental comments submitted by Pacific
Environmental Advocacy Center, on behalf of the Northwest Environmental Advocates, to U.S. EPA

7

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Region 10 concerning Oregon's 2004 new and revised aquatic life criteria (.Responses to Supplemental
Comments Submitted by Pacific Environmental Advocacy Center to U.S. EPA Region 10 Concerning
Oregon's New and Revised Aquatic Life Criteria).

Enclosure 4 to this document provides a summary of the aquatic life criteria in effect for CWA
purposes in Tables 20, 33 A, and 33B as a result of this action (,Aquatic Life Criteria In Effect for Clean
Water Act Purposes).

8

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III. EPA'S ACTION ON THE INTRODUCTORY LANGUAGE, THE NEW
AND REVISED AQUATIC LIFE CRITERIA AND THE FOOTNOTES IN
TABLE 33A

A. Table 33A in Oregon's Water Quality Standards

The following presents the introductory language to Table 33A, criteria contained in Table 33A, and
new footnotes to Table 33A. Table 33A contains (1) criteria that Oregon adopted and EPA approved
prior to the 2004 water quality standards rulemaking (i.e., these criteria were already part of Oregon's
water quality standards, and were simply moved from Table 20 to this new table), (2) new or revised
criteria, and (3) new footnotes.5 All new language from the 2004 and 2011 revisions, including new and
revised criteria, are underlined; strikeout text indicates the language that was removed during Oregon's
2011 water quality standards adoption.

Table 33A

Note: The Environmental Quality Commission adopted the following criteria on May 20, 2004 to become effective February
15, 2005. However, EPA has not yet (as of June 2006) approved the criteria. Thus, Table 33 A criteria may be used in NPDES
permits, but not for the section 303(d) list of impaired waters.6

AQUATIC LIFE WATER QUALITY CRITERIA SUMMARYa

The concentration for each compound listed in Table 33A is a criterion not to be exceeded in waters of the state in order to
protect aquatic life and human health. All values are expressed as micrograms per liter (u/L) except where noted. Compounds
are listed in alphabetical order with the corresponding EPA number (from National Recommended Water Quality
Criteria:2002. EPA 8220R-02-047). the Chemical Abstract Service (CAS) number, aquatic life freshwater acute and chronic
criteria, aquatic life saltwater acute and chronic criteria, and human health water & organism and organism only criteria, and
Drinking Water Maximum Contaminant Level (MCL). The acute criteria refer to the average concentration for one (1) hour
and the chronic criteria refer to the average concentration for 96 hours (4-davs). and that these criteria should not be exceeded
more than once every three (3) years.

EPA No.

Compound

CAS
Number

Freshwater

Saltwater

Acute
(CMC)

Effective
Date

Chronic
fCCC)

Effective
Date

Acute
(CMC)

Effective
Date

Chronic
fCCC)

Effective
Date

Acenaohthene

83329

Acenaohthvlene

208968

Acrolein

107028

Acrvlonitrile

107131

102

Aldrin

309002

3 O

1.3 O

1 N

Alkalinity

20,000
P

2 N

Aluminum (t>H 6.5 - 9.0)

7429905

3 N

Ammonia

7664417

5 In Oregon's 2004 water quality standards adoption, all of the footnotes pertaining to Table 33A and Table 33B were at the
end of Table 33B. In Oregon's 2011 water quality standards adoption, all of the footnotes located at the end of Table 33B
were inserted after Table 33A. Additionally, the footnotes associated with human health criteria were then struck out
(presumably to make it clear that these footnotes were being deleted because all of the human health criteria had been moved
to a separate Table).

6 This note to Table 33 A was approved by EPA in its February 18, 2011 action.

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EPA No.

Compound





CAS
Number



Freshwater

Saltwater

Acute
(CMC)

Effective
Date

Chronic
fCCC)

Effective
Date

Acute
(CMC)

Effective
Date

Chronic
fCCC)

Effective
Date

58

Anthracene





120127

















1

Antimonv





7440360

















2

Arsenic





7440382





































































15

Asbestos





1332214

















6 N

Barium





7440393

















19

Benzene





71432

















59

Benzidine





92875

















60

Benzof a)Anthracene





56553

















61

Benzof a)Pvrene





50328

















62

Benzo(b)Fluoranthene





205992

















63

Benzof e.h.i)Pervlene





191242

















64

Benzo(k)Fluoranthene





207089

















3

Bervllium





7440417











































103

BHC atoha-





319846

















104

BHC beta-





319857

















106

BHC delta-





319868

















105

BHC eamma- (Lindane)





58899

0.95



0.08

X

0.16 O







7 N

Boron





7440428

















20

Bromoform





75252

















69

BromoDhenvl Phenvl Ether
4-























70

Butvlbenzvl Phthalate





85687

















4

Cadmium





7440439

















21

Carbon Tetrachloride





56235

















107

Chlordane





57749

2.4 O

X

0.0043
O

X

0.09 O

X

0.004
O

X

8 N

Chloride





16887006

860000



230000































































9 N

Chlorine





7782505

19

X

11

X

13

X

7.5

X



























22

Chlorobenzene





108907

















23

Chlorodibromomethane





124481

















24

Chloroethane





75003

















65

ChloroethoxvMethane
Bis2-





111911

















66

ChloroethvlEther Bis2-





111444

















25

Chloroethvlvinvl Ether 2-





110758

















26

Chloroform





67663

















67

Chloroi sooroDvlEther
Bis2-





108601

















15 N

ChloromethvlEther. Bis





542881

















71

Chloronaohthalene 2-





91587

















45

Chloroohenol 2-





95578











































ION

Chloroohenoxv Herbicide
(2.4.5.-TP)





93721

















11N

Chloroohenoxv Herbicide
(2.4-D)





94757

















72

Chloroohenvl Phenvl Ether
4-





7005723

















12 N

Chloroovrifos





2921882

0.083

X

0.041

X

0.011

X

0.0056

X





















































5a

Chromium fill)























5b

Chromium (VI)





18540299

















73

Chrvsene





218019

















6

CoDDer





7440508

















10

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EPA No.

Compound





CAS
Number



Freshwater

Saltwater

Acute
(CMC)

Effective
Date

Chronic
fCCC)

Effective
Date

Acute
(CMC)

Effective
Date

Chronic
fCCC)

Effective
Date

14

Cvanide





57125

22 S

X

5.2 S

X

1 S

X

1 S

X

108

DDT 4.4'-





50293

1.1 O.T

X

0.001
O.T

X

0.13
O.T

X

0.001
O.T

X

109

DDE 4.4'-





72559

















110

DDD 4.4'-





72548

















14 N

Demeton





8065483





0.1

X





0.1

X

74

Dibenzof a.h)Anthracene





53703





































































75

Dichlorobenzene 1.2-





95501

















76

Dichlorobenzene 1.3-





541731

















77

Dichlorobenzene 1.4-





106467

















78

Dichlorobenzidine 3.3'-





91941

















27

Dichlorobromomethane





75274

















28

Dichloroethane 1.1-





75343

















29

Dichloroethane 1.2-





107062

















30

Dichloroethvlene 1.1-





75354











































46

Dichloroohenol 2.4-





120832

















31

Dichlorot>rot>ane 1.2-





78875

















32

Dichlorot>rot>ene 1.3-





542756

















111

Dieldrin





60571

0.24







0.71 O

X

0.0019

o

X

79

DiethvlPhthalate





84662

















47

Dimethvlohenol 2.4-





105679

















80

DimethvlPhthalate





131113

















81

Di-n-Butvl Phthalate





84742

















49

Dinitroohenol 2.4-





51285

















27 N

Dinitrot>henols





25550587

















82

Dinitrotoluene 2.4-





121142

















83

Dinitrotoluene 2.6-





606202































































































84

Di-n-Octvl Phthalate





117840

















16

Dioxin (2.3.7.8-TCDD)





1746016











































85

Diohenvlhvdrazine 1.2-





122667

















68

EthvlhexvlPhthalate Bis2-





117817



















Endosulfan







0.22 LP

X

0.056
LE

X

0.034
LE

X

0.0087
LE

X

112

Endosulfan aloha-





959988

0.22 O



0.056 O



0.034 O



0.0087
O



113

Endosulfan beta-





33213659

0.22 O



0.056 O



0.034 O



0.0087
O



114

Endosulfan Sulfate





1031078

















115

Endrin





72208

0.086







0.037 O



0.0023
O



116

Endrin Aldehvde





7421934

















33

Ethvlbenzene





100414

















86

Fluoranthene





206440

















87

Fluorene





86737

















17 N

Guthion





86500





0.01

X





0.01

X





















































117

Heotachlor





76448

0.52 O

X

0.0038

o

X

0.053 O

X

0.0036

o

X

118

Heotachlor Epoxide





1024573

0.52 O



0.0038

o



0.053 O



0.0036

o





























M

Hexachlorobenzene





118741

















11

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EPA No.

Compound





CAS
Number



Freshwater

Saltwater

Acute
(CMC)

Effective
Date

Chronic
fCCC)

Effective
Date

Acute
(CMC)

Effective
Date

Chronic
fCCC)

Effective
Date

89

Hexachlorobutadiene





87683

















91

Hexachloroethane





67721

























































































































19 N

Hexachlorocvclo-hexane-
Technical





319868

















90

Hexachlorocvclooentadien

e





77474

















92

Ideno 1.2.3 -f cd)Pvrene





193395

















20 N

Iron





7439896





1,000

X









93

Isoohorone





78591

















7

Lead





7439921

















21 N

Malathion





121755





0.1

X





0.1

X

22 N

Maneanese





7439965

















8a

Mercurv





7439976

2.4

X

0.012

X

2.1

X

0.025

X

23 N

Methoxvchlor





72435





0.03

X





0.03

X

34

Methvl Bromide





74839

















35

Methvl Chloride





74873

















48

Methvl-4.6-Dinitrot>henol
2-





534521

















52

Methvl-4-ChloroDhenol 3-





59507

















36

Methvlene Chloride





75092

















8b

Methvlmercurv





22967926

















24 N

Mirex





2385855





0.001

X





0.001

X



























94

Naphthalene





91203

















9

Nickel





7440020

















25 N

Nitrates





14797558

















95

Nitrobenzene





98953











































50

Nitroohenol 2-





88755

















51

Nitroohenol 4-





100027

















26 N

Nitrosamines





35576911

















28 N

Nitrosodibutvlamine.N





924163

















29 N

Nitrosodiethvlamine.N





55185

















96

N-Nitrosodimethvlamine





62759

















98

N-Nitrosodiohenvlamine





86306

















30 N

NitrosoDvrrolidine.N





930552

















97

N-Nitrosodi-n-
ProDvlamine





621647

















32 N

Oxveen. Dissolved





7782447

















33 N

Parathion





56382

0.065

X

0.013

X









119

Polvchlorinated Biohenvls
PCBs:





1336363

2 U

X

0.014 U

X

10 U

X

0.03 U

X



























34 N

Pentachlorobenzene





608935

















53

Pentachloroohenol





87865

M







13



7.9



99

Phenanthrene





85018

















54

Phenol





108952

















36 N

Phosphorus Elemental





7723140













0.1























































100

Pvrene





129000

















10

Selenium





7782492

















11

Silver





7440224

















40 N

Sulfide-Hvdroeen Sulfide





7783064





2

X





2

X



























43 N

Tetrachlorobenzene. 1.2.4.5





95943

















37

Tetrachloroethane 1.1.2.2-





79345

















12

-------
EPA No.

Compound





CAS
Number



Freshwater

Saltwater

Acute
(CMC)

Effective
Date

Chronic
fCCC)

Effective
Date

Acute
(CMC)

Effective
Date

Chronic
fCCC)

Effective
Date



























38

T etrachloroethvlene





127184











































12

Thallium





7440280

















39

Toluene





108883

















120

Toxaohene





8001352

0.73

X

0.0002

X

0.21

X

0.0002

X

40

Trans-Dichloroethvlene
1.2-





156605

















44 N

Tributvltin (TBT)





688733

















101

Trichlorobenzene 1.2.4-





120821











































41

Trichloroethane 1.1.1-





71556

















42

Trichloroethane 1.1.2-





79005

















43

Trichloroethvlene





79016

















45 N

TrichloroDhenol 2.4.5





95954

















55

TrichloroDhenol 2.4.6-





88062

















44

Vinvl Chloride





75014

















13

Zinc





7440666

















Footnotes for Table 33A and 33B:	

A Values in Table 20 are applicable to all basins.

B Human Health criteria values were calculated using a fish consumption rate of 17.5 grams per day (0.6 ounces/dav)
unless otherwise noted.

C Ammonia criteria for freshwater may depend on pH. temperature, and the presence of salmonids or other fish with
ammonia-sensitive early life stages. Values for freshwater criteria (of total ammonia nitrogen in mg N/L1 can be
calculated using the formulae specified in 1999 Update of Ambient Water Quality Criteria for Ammonia (EPA-822-R-
99-014: http://www.epa.gov/ost/standards/ammonia/99update.pdf):

Freshwater Acute:

salmonids present... .CMC = 0.275 + 39.0

1+ 1()7.204-pH 1+ 1()pH-7.204

salmonids not present... CMC= 0.411 + 58.4

1+ 1()7.204-pH 1+ 1()pH-7.204

Freshwater Chronic:

fish early life stages present:

CCC= 0.0577 + 2.487 * MIN (2.85.1.45*100028''(25'T)')

^q7.688-pH	j^QpH-7.688

fish early life stages not present:

CCC = 0.577 + 2.487 * 1.45*10ao28''(25'MAX(T-7))

^q7.688-pH	j^QpH-7.688

Note: these chronic criteria formulae would be applied to calculate the 30-day average concentration limit; in addition,
the highest 4-day average within the 30-day period should not exceed 2.5 times the CCC.

D Ammonia criteria for saltwater may depend on pH and temperature. Values for saltwater criteria (total ammonia) can
be calculated from the tables specified in Ambient Water Quality Criteria for Ammonia (Saltwater)—1989 (EPA 440/5-
88-004: http://www.epa.gov/ost/pc/ambientwac/ammoniasaltl989.pdf).

E Freshwater and saltwater criteria for metals are expressed in terms of "dissolved" concentrations in the water column,
except where otherwise noted (e.g. aluminum).

F The freshwater criterion for this metal is expressed as a function of hardness (ing/L) in the water column. Criteria
values for hardness may be calculated from the following formulae (CMC refers to Acute Criteria: CCC refers to
Chronic Criteria):

13

-------
CMC= (c\p(nu * 11 nfhardness) I + b_%))*CF
CCC= (c\p(iiv * 11 n( ha rdncss) I + b,0)*CF

where CF is the conversion factor used for converting a metal criterion expressed as the total recoverable fraction in the
water column to a criterion expressed as the dissolved fraction in the water column.

( homiciil



l>v

ill,

1).

Cadmium

l.Ulbb

-3.924

U.74U9

-4.719

Chromium III

0.8190

3.7256

0.8190

0.6848

Copper

0.9422

-1.700

0.8545

-1.702

Lead

1.273

-1.460

1.273

-4.705

Nickel

0.8460

2.255

0.8460

0.0584

Silver

1.72

-6.59





Zinc

0.8473

0.884

0.8473

0.884

Conversion factors (CF) for dissolved metals (the values for total recoverable metals criteria were multiplied by
the appropriate conversion factors shown below to calculate the dissolved metals criteria):

( hcmic;il

TivshwiUor

Siilmiiior

Anile

Chronic

Acnlc

Chronic

\rsenic

1.000

1.000

1.000

1.000

Cadmium

1.136672-[(ln
hardnessVO.041838)1

1.101672-[(ln
hardnessVO.041838)1

0.994

0.994

Chromium III

0.316

0.860

--

--

Chromium VI

0.982

0.962

0.993

0.993

Copper

0.960

0.960

0.83

0.83

Lead

1.46203-[(ln
hardnessVO. 145712)1

1.46203-[(ln
hardnessVO. 145712)1

0.951

0.951

Nickel

0.998

0.997

0.990

0.990

Selenium

0.996

0.922

0.998

0.998

Silver

0.85

0.85

0.85

--

Zinc

0.978

0.986

0.946

0.946

G Human Health criterion is the same as originally published in the 1976 EPA Red Book (Quality Criteria for Water.
EPA 110/9 76 0231 which predates the 1980 methodology and did not use a fish ingestion BCF approach.

H This value is based on a Drinking Water regulation.

I This value is based on criterion published in Ambient Water Quality Criteria for Endosulfan (EPA 440/5-80-046) and
should be applied as the sum of alpha and beta endosulfan.

J No BCF was available: therefore, this value is based on that published in the 1986 EPA Gold Beefe-

K Human Health criterion is for "dissolved concentration based on the 1976 EPA Red Book conclusion that adverse
effects from exposure at this level are aesthetic rather than toxic.

L This value is expressed as the fish tissue concentration of methvlmercurv.

M Freshwater aquatic life values for pentachlorophenol are expressed as a function of pH. and are calculated as follows:
CMC=(exp(1.005(pH)-4.869): CCC=exp(1.005(pH)-5.134).

N This number was assigned to the list of non-prioritv pollutants in National Recommended Water Quality Criteria: 2002
(EPA-822-R-02-047).

O This criterion is based on EPA recommendations issued in 1980 that were derived using guidelines that differed from
EPA's 1985 Guidelines for minimum data requirements and derivation procedures. For example, a "CMC" derived
using the 1980 Guidelines was derived to be used as an instantaneous maximum. If assessment is to be done using an
averaging period, the values given should be divided by 2 to obtain a value that is more comparable to a CMC derived
using the 1985 Guidelines.

P Criterion shown is the minimum (i.e. CCC in water should not be below this value in order to protect aquatic life).

O Criterion is applied as total arsenic (i.e. arsenic (IIP + arsenic (V)).

R Arsenic criterion refers to the inorganic form only.	

14

-------
s

This criterion is expressed as us free cvanide (CN)/L.

This criterion applies to DDT and its metabolites (i.e. the total concentration of DDT and its metabolites

should not exceed this value).

This criterion applies to total PCBs (e.e. the sum of all consener or all isomer or homolos or Arochlor analyses).

The CMC-1 /I (T1 /CMC 1)+(f2/CIVIC2) 1 where fl and f2 are the fractions of total selenium that are treated as selenite

and selenate. respectively, and CMC1 and CMC2 are 185.9 iig/L and 12.82 iig/L. respectively.

The acute and chronic criteria for aluminum are 750 iig/L and 87 lis/L. respectively. These values for aluminum are

expressed in terms of "total recoverable" concentration of metal in the water column. The criterion applies at pH<6.6
and hardness<12 me/L (as CaCCM.

The effective date for the criterion in the column immediately to the left is 1991.

No criterion

EPA's CWA Determinations on Table 33A

1. EPA's Action on Introductory Language to Table 33A

This section of the document addresses the introductory language to Table 33A. The introductory
language states:

The concentration for each compound listed in Table 33A is a criterion not to be exceeded in
waters of the state in order to protect aquatic life and human health. All values are expressed as
micrograms per liter (^/L) except where noted. Compounds are listed in alphabetical order with
the corresponding EPA number (from National Recommended Water Quality Criteria:2002.
EPA 8220R-02-047). the Chemical Abstract Service (CAS) number, aquatic life freshwater acute
and chronic criteria, aquatic life saltwater acute and chronic criteria, human health water &
organisms and organisms only, and Drinking Water Maximum Contaminant Level (MGk). The
acute criteria refer to the average concentration for one (1) hour and the chronic criteria refer to
the average concentration for 96 hours (4-davs). and that these criteria should not be exceeded
more than once every three (3) years.

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § Part 131,
EPA approves the introductory language for Table 33A.

EPA Rationale

The introductory language to the table provides the frequency and duration for each aquatic life
criterion (i.e., acute criterion is expressed as a one hour average not to be exceeded more than once
every three years, and the chronic criterion is expressed as a four day average not to be exceeded
more than once every three years), requires waters of the State not to exceed the criterion, describes
the units used for each chemical, and describes the organization of the table. Additionally, references
to human health criteria were deleted from the introductory language because in Oregon's 2011
adoption of the human health criteria, Table 40 was created and provides all of the human health
criteria.

The federal regulation at 40 CFR § 131.11(b) states that in establishing criteria, states should set
numerical values based on EPA's 304(a) recommendations (potentially modified to reflect site-
specific conditions) or other scientifically defensible methods. EPA's 304(a) recommendations
generally consist of a magnitude (level of pollutant that is allowable, usually expressed as a

-------
concentration), duration (the period of time over which the instream concentration is averaged for
comparison with criteria concentrations), and frequency (how often a particular criterion can be
exceeded). The introductory language specifies a reasonable duration and frequency to be used for
the magnitudes listed in the table that follows; therefore, EPA is approving this language. EPA's
specific determinations on the adequacy of the magnitude for each new or revised criterion to protect
Oregon's fish and aquatic life designated use, given the specified duration and frequency, are
provided below.

EPA approves the language stating "The concentration for each compound listed in Table 33A is a
criterion not to be exceeded in water of the state in order to protect aquatic life." This language
describes the intent of the criteria to protect aquatic life uses in Oregon in waters of the state. As
stated above, EPA's action on each individual criterion in Table 33A is provided below.

Additionally, EPA acknowledges the editorial changes made by removing references to human health
criteria in the introductory language. EPA approves these changes as non-substantive editorial
changes.

2. Approval Action for New or Revised Aquatic Life Criteria in Table 33A
(BHC-gamma (Lindane), Dieldrin, Endrin, Pentachlorophenol)

This section of the document addresses new and revised aquatic life criteria adopted by Oregon that
EPA is approving. As explained in the introductory language to Table 33A, acute criteria are
expressed as a one-hour average not to be exceeded more than once every three years. The chronic
criteria are expressed as a four-day average concentration not to be exceeded more than once every
three years. Specifically, this section provides EPA's action on the following criteria:

BHC-gamma (Lindane): freshwater acute: 0.95 |ig/L

Dieldrin: freshwater acute: 0.24 |ig/L

Endrin: freshwater acute: 0.086 |ig/L

Pentachlorophenol: saltwater chronic: 7.9 |ig/L

The freshwater acute criterion for pentachlorophenol is a pH dependent equation and is found in
Footnote M of Table 33 A. The acute criterion is:

Pentachlorophenol: freshwater acute: exp(l ,005(pH) - 4.869) expressed in |ig/L

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131, EPA
approves the magnitude (including the formula for pentachlorophenol found in Footnote M of Table
33A), frequency, and duration of the aquatic life toxic criteria referenced above.

-------
EPA Rationale

EPA evaluated each of the criteria referenced above to determine whether they will protect Oregon's
fish and aquatic life designated use. A detailed description of the methodology for evaluating criteria
is contained in the STSD in Enclosure 2 (see Section 1.0 Methodology for Criterion Evaluation). The
data and evaluation used to determine if each of the above criteria protects Oregon's fish and aquatic
life designated use is also contained in the STSD in Enclosure 2 (see Section 2.0).

3. Disapproval Action for Changes to Aquatic Life Criteria Moved From Table
20 to Table 33A (Aldrin, BHC-gamma (Lindane), Chlordane, DDT 4,4, Dieldrin,
Endosulfan, Endrin, and Heptachlor)

This section addresses the following aquatic life criteria:

Aldrin:

freshwater acute:
saltwater acute:

3 |ig/L
1.3 |ig/L

BHC-gamma (Lindane):

freshwater chronic:
saltwater acute:

0.08 |ig/L
0.16 |ig/L

Chlordane:

freshwater acute:
freshwater chronic:
saltwater acute:
saltwater chronic:

2.4 |ig/L
0.0043 |ig/L
0.09 |ig/L
0.004 |ig/L

DDT 4,4:

freshwater acute:
freshwater chronic:
saltwater acute:
saltwater chronic:

1.1 Hg/L
0.001 |ig/L
0.13 |ig/L
0.001 |ig/L

Dieldrin:

saltwater acute:
saltwater chronic:

0.71 |ig/L
0.0019 |ig/L

Endosulfan:

freshwater acute:
freshwater chronic:
saltwater acute:
saltwater chronic:

0.22 |ig/L
0.056 |ig/L
0.34 |ig/L
0.0087 |ig/L

Endrin:

saltwater acute:
saltwater chronic:

0.037 |ig/L
0.0023 |ig/L

Heptachlor:

freshwater acute:
freshwater chronic:
saltwater acute:
saltwater chronic:

0.52 |ig/L
0.0038 |ig/L
0.053 |ig/L
0.0036 |ig/L

17

-------
There are several changes that affect these criteria. First, the magnitudes for these criteria were
moved from Table 20 to Table 33A. Second, the duration and frequency associated with these
magnitudes were changed. These changes are reflected in two places: altered introductory language
to Table 20, and new introductory language in the new Table 33A. The revised introductory
language to Table 20, and the new introductory language to Table 33A, both provide that acute
criteria in the respective tables are expressed as a one-hour average concentration not to be exceeded
more than once every three years, and chronic criteria in the tables are expressed as a four-day
average concentration not be exceeded more than once every three years. This is a change from the
prior introductory language in Table 20, which stated that "... Specific descriptions of each compound
and an explanation of values are included in Quality Criteria for Water (1986)...." EPA's Quality
Criteria for Water (1986) provides that the acute criteria were maximum values not to be exceeded
(at any frequency), and the chronic criteria were 24-hour averages not to be exceeded (at any
frequency). Oregon's new introductory language had the effect of changing the duration and
frequency of the criteria.

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131, EPA
disapproves the frequency and duration changes referenced above. Thus, for the pesticide criteria
listed above, EPA disapproves the deletion of the appropriate duration and frequency introductory
language from Table 20, and disapproves the addition of the magnitudes to Table 33 A. EPA's
related disapproval of the introductory language to Table 20 is described in Part V.A. of this
document, and EPA's approval of the introductory language to Table 33 A (which no longer applies
to the pesticide criteria listed in this Section) is described in Part III.B. 1.

EPA Rationale

EPA has reviewed the magnitude, duration, and frequency for the above referenced chemicals. Prior to
Oregon's 2004 water quality standards adoption, Oregon's water quality standards contained criteria
for the chemicals referenced above; the magnitude, duration, and frequency for the criteria, prior to
the 2004 revisions, were consistent with EPA's 304(a) recommendations.

In Oregon's 2004 adoption, Oregon retained the magnitude for each of the above referenced
chemicals but, as a result of the new introductory language, Oregon effectively revised the frequency
and duration for each criterion. Oregon's 2004 adoption made the following changes:

1) Oregon's new introductory language had the effect of changing the duration and frequency for the
acute criteria from a maximum value not to be exceeded, to a one-hour average not to be exceeded
more than once every three years; and

2) Oregon's new introductory language had the effect of changing the duration and frequency for the
chronic criteria from a 24-hour average, to a four-day average not be exceeded more than once every
three years.

While the EPA's 304(a) acute criteria recommendations contemplate the potential use of a one-hour
averaging period for the above chemicals, in that case they would also provide for the criterion value
to be halved (e.g., the 304(a) acute criterion for aldrin is a "not to be exceeded value" of 3.0 |ig/L; if a
one-hour averaging period is used the recommended acute criterion would be 1.5 |ig/L).

-------
Though EPA approved the magnitudes for these chemicals at the durations and frequencies provided
in Oregon's WQS prior to 2004, with the new durations and frequencies, the unchanged (i.e. not
halved) magnitudes for these criteria may no longer be protective. Oregon did not provide supporting
documentation that would demonstrate that the designated aquatic life uses in Oregon are ensured
protection from discharges of the above referenced chemicals at the specified magnitude, duration,
and frequency. Therefore, EPA is disapproving the change in the durations and frequencies of these
criteria by disapproving the new introductory language in Table 20 and the transfer of these
magnitudes to Table 33A.

Remedies to Address EPA's Disapproval

Oregon must revise the frequency and duration to be consistent with EPA's 304(a) recommendations
for the above referenced chemicals to protect aquatic life. Oregon may do this using one of the
following methods:

• Move the magnitudes for each chemical to Table 33A as proposed, and modify the

introductory language to Table 33 A to provide that the acute magnitude is expressed as a
maximum value not to be exceeded and the chronic criterion is expressed as a 24-hour
maximum for the chemicals listed above.

•	Modify Table 33A in an alternate way that is consistent with EPA's 304(a) recommendations.

•	Leave the magnitudes in Table 20, and fix the introductory language to provide that the acute
magnitude is expressed as a maximum value not to be exceeded and the chronic criterion is
expressed as a 24-hour maximum for the chemicals listed above. Do not include the
magnitudes in Table 33A.

•	Development of Oregon-specific numeric criteria using a sound scientific methodology.

Freshwater and Saltwater Aquatic Life Criteria Currently in Effect in Oregon

As explained above, EPA is disapproving the addition of the magnitudes in Table 33 A for these
chemicals because of the new duration and frequency specified in Table 33 A. This leaves the same
magnitude in effect in Table 20, where these magnitudes are subject to the former duration and
frequency that were approved and appropriate for these magnitudes. The acute criteria are expressed
as a maximum value not to be exceeded and the chronic criterion is a 24-hour maximum, the numeric
values are listed below:

Aldrin:

freshwater acute:
saltwater acute :

3 |ig/L
1.3 |ig/L

Lindane:

freshwater chronic:
saltwater acute:

0.08 |ig/L
0.16 |ig/L

Chlordane:	freshwater acute:	2.4 |ig/L

freshwater chronic: 0.0043 |ig/L

saltwater acute:	0.09 |ig/L

saltwater chronic;	0.004 |ig/L

19

-------
DDT 4,4:

Dieldrin:

freshwater acute:
freshwater chronic:
saltwater acute:
saltwater chronic:
saltwater acute:
saltwater chronic:

1.1 Hg/L
0.001 |ig/L
0.13 |ig/L
0.001 |ig/L
0.71 |ig/L
0.0019 |ig/L

Endrin:

Heptachlor:

saltwater acute:
saltwater chronic:

freshwater acute:
freshwater chronic:
saltwater acute:
saltwater chronic:

0.037 |ig/L
0.0023 |ig/L

0.52 |ig/L
0.0038 |ig/L
0.053 |ig/L
0.0036 |ig/L

Endosulfan:

freshwater acute:
freshwater chronic:
saltwater acute:
saltwater chronic:

0.22 |ig/L
0.056 |ig/L
0.34 |ig/L
0.0087 |ig/L

4. Disapproval Action for New Criteria in Table 33A (Endosulfan alpha,
Endosulfan beta, and Heptachlor epoxide)

This section of the document addresses new criteria for chemicals that Oregon has adopted and EPA
is disapproving. As a result of the introductory language to Table 33A, acute criteria are expressed as
a one-hour average not to be exceeded more than once every three years, and the chronic criteria are
expressed as a four-day average concentration not to be exceeded more than once every three years.
Specifically, this section provides EPA's action on the following aquatic life criteria:

Endosulfan-alpha:

Endosulfan-beta:

freshwater acute:
freshwater chronic:
saltwater acute:
saltwater chronic;

freshwater acute;
freshwater chronic:
saltwater acute:
saltwater chronic:

0.22 |ig/L
0.056 |ig/L
0.34 |ig/L
0.0087 |ig/L

0.22 |ig/L
0.056 |ig/L
0.34 |ig/L
0.0087 |ig/L

Heptachlor Epoxide:	freshwater acute:	0.52 |ig/L

freshwater chronic:	0.0038 |ig/L

saltwater acute;	0.053 |ig/L

saltwater chronic:	0.0036 |ig/L

20

-------
EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131, EPA
disapproves all of the above referenced criteria. Specifically, the one-hour averaging periods
associated with the acute aquatic life criteria described above and the four-day averaging period
associated with the chronic aquatic life criteria are not appropriate averaging periods for these
magnitudes.

EPA Rationale

EPA's 304(a) recommendations express the acute criterion as a maximum value not to be exceeded,
and the chronic criterion is expressed as a 24-hour average. However, as a result of Oregon's
introductory language to Table 33 A the acute criteria are expressed as a one-hour average not to be
exceeded more than once every three years, and the chronic criteria are expressed as a four-day
average concentration not to be exceeded more than once every three years.

The acute criterion may be used with a one-hour averaging period for the above chemicals, however,
the criterion value must be halved (e.g., the 304(a) acute criterion for endosulfan alpha is a "not to be
exceeded value" of 0.22 |ig/L; if a one-hour averaging period is used the acute criterion must be 0.11
Hg/L).

Oregon did not provide supporting documentation that would demonstrate that the designated aquatic
life uses in Oregon are ensured protection from discharges of the above referenced chemicals at the
specified magnitude, duration, and frequency. Therefore, EPA is disapproving the above referenced
magnitudes.

Remedies to Address EPA's Disapproval

Oregon must adopt frequency and durations to be consistent with EPA's 304(a) recommendations for
the above referenced chemicals to protect aquatic life. Oregon may do this using one of the
following methods:

• Retain the magnitude for each chemical, and modify the introductory language to Table 33A to
make it clear that the acute criterion is a magnitude not to be exceeded and the chronic criterion
is a 24-hour maximum.

• Modify the table in an alternate way that is consistent with EPA's 304(a) recommendations.

• Develop Oregon-specific numeric criteria using a sound scientific methodology.

Freshwater and Saltwater Aquatic Life Criteria Currently in Effect in Oregon

Until EPA approves or promulgates revisions to numeric freshwater and saltwater acute and chronic
aquatic life criteria for endosulfan alpha, endosulfan beta, and heptachlor epoxide, the narrative
criterion (OAR 340-042-0033(2)) is applicable to the designated aquatic life uses in Oregon for CWA
purposes.

5. EPA's Action on Footnotes in Table 33A

This section of the document addresses the footnotes in Table 33A. In 2004 the footnotes for Tables
33A and 33B were all located after Table 33B. In 2011, Oregon added Footnotes A through Y after

-------
Table 33 A, but subsequently eliminated Footnotes B, G, H, J - L, and R because a number of criteria
moved to a different table. Each footnote adopted by Oregon is denoted in italics.

Footnote A

A Values in Table 20 are applicable to all basins.

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131, EPA is
disapproving this footnote because it directs the reader to the incorrect table. Oregon has explained
to EPA that this is an error and Oregon intends to correct the footnote to read "Values in Table 33 A
are applicable to all basins" (see October 3, 2012 letter from Greg Aldrich, ODEQ to Daniel Opalski,
EPA).

Remedy to Disapproval Language

Change the text in the footnote to "Values in Table 33A are applicable to all basins."

Narrative Language Currently in Effect in Oregon

OAR 340-041-0033(3) has been approved by EPA and is in effect for CWA purposes; it states:
"Levels of toxic substances in waters of the state may not exceed the applicable aquatic life criteria
listed in Tables 20, 33A, and 33B...." This language correctly requires the aquatic life criteria in
Table 33A to be applied to all waters of the state.

Footnote C

C Ammonia criteria for freshwater may depend on pH, temperature, and the presence or absence of
salmonids or other fish with ammonia-sensitive early life stages. Values for freshwater criteria
(of total ammonia nitrogen in mgN/L) can be calculated using the formulae specified in 1999
Update of Ambient Water Quality Criteria for Ammonia (EPA-822-R-99-014;
htty://www. eya. sov/ost/standards/ammonia/99uydate. ydf):

Freshwater Acute:

salmonids present.... CMC = 0.275 + 39.0

jq7.204~pH jqpH-7.204

salmonids not present... CMC= 0.411 + 58.4

jq7.204~pH jqpH-7.204

Freshwater Chronic:
fish early life stages present:

CCC = 0.0577 + 2.487 *MIN (2.85,1.45*1oOX)28*(25-T))

jjq7.688-PH jgpH-7.688

fish early life stages not present:

CCC = 0.577 + 2.487 * 1.45*j q0-028^25^^

jjq7.688-PH jjqpH-7.688

Note: these chronic criteria formulae would be applied to calculate the 30-day average concentration
limit; in addition, the highest 4-day average within the 30-day period should not exceed 2.5 times the
CCC.

-------
EPA Action

This footnote is not applicable to any criteria in Table 33A because there is no citation to this
footnote anywhere in Table 33A. Additionally, Footnote C to Table 33B sets forth the same criteria
for ammonia that are described above, and Footnote C is cited in Table 33B. Therefore, EPA's
decision regarding these criteria is set forth below in Parts IV.B.4.b (Freshwater Acute and Chronic
Ammonia Aquatic Life Criteria), and IV.B.5 (EPA's Action on the New Footnotes in Table 33B),
Footnote C.

EPA recommends the State delete this footnote from Table 33A since there is no citation to the
footnote in Table 33A.

Footnote D

I) Ammonia criteria for saltwater may depend on pH and temperature. Values for saltwater
criteria total ammonia) can be calculatedfrom the tables specified in Ambient Water Quality
Criteria for Ammonia (Saltwater)—1989 (EPA 440/5-88-004;
httv://www.eva.20v/ost/vc/ambientwQc/ammoniasalt1989.pdf.

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131, EPA is
approving Footnote D as a non-substantive formatting change. Prior to the 2004 water quality
standards adoption, the saltwater ammonia criteria were contained in Table 20 and referenced the
same criterion document. Oregon retained the same saltwater ammonia criteria and moved them to
Table 33 A. Footnote D directs the reader to the same EPA document which contains the unchanged
saltwater ammonia criteria.

Please note that the internet address has changed since this table was created and should be updated.
The current address is: http://water.epa.gov/scitech/swguidance/standards/criteria/current/index.cfm.

Footnotes E and F

E Freshwater and saltwater criteria for metals are expressed in terms of "dissolved"
concentrations in the water column, except where otherwise noted (e.g. aluminum).

F The freshwater criterion for this metal is expressed as a function of hardness (mg/L) in the water
column. Criteria values for hardness may be calculatedfrom the following formulae (CMC
refers to Acute Criteria; CCC refers to Chronic Criteria):

CMC = (exp(mA* [ln(hardness)] + bj))*CF
CCC = (exp(mc* [ln(hardness)] + bc))*CF

where CF is the conversion factor usedfor converting a metal criterion expressed as the total
water column.

23

-------
( licmictil

///,



m,

b,

Cadmium

1.0166

-3.924

0.7409

-4.719

Chromium III

0.8190

3.7256

0.8190

0.6848

Copper

0.9422

-1.700

0.8545

-1.702

Lead

1.273

-1.460

1.273

-4.705

Nickel

0.8460

2.255

0.8460

0.0584

Silver

1.72

-6.59





Zinc

0.8473

0.884

0.8473

0.884

Conversion factors (CF) for dissolved metals (the values for total recoverable metals criteria
were multiplied by the appropriate conversion factors shown below to calculate the dissolved
metals criteria):

( licmictil

l-'rcslnnifcr

SuIt water

Acute

( hionic

Acute

( hronic

.Irsenic

1.000

1.000

1.000

1.000

Cadmium

1.136672-[(ln
hardness)(0.041838)]

1.101672-[(ln
hardness) (0.041838)]

0.994

0.994

Chromium III

0.316

0.860

—

—

Chromium VI

0.982

0.962

0.993

0.993

Copper

0.960

0.960

0.83

0.83

Lead

1.46203-[(ln
hardness) (0.145712)]

1.46203-[(ln
hardness) (0.145712)]

0.951

0.951

Nickel

0.998

0.997

0.990

0.990

Selenium

0.996

0.922

0.998

0.998

Silver

0.85

0.85

0.85

—

Zinc

0.978

0.986

0.946

0.946

EPA Action

Footnotes E and F are not applicable to any criteria in Table 33A because there is no citation to these
footnotes anywhere in Table 33A. Additionally, Footnotes E and F to Table 33B set forth the same
criteria for metals that are described above, and citations to Footnotes E and F are contained in Table
33B. Therefore, EPA's decision regarding Footnotes E and F and the associated criteria is set forth
below in Part IV.B.5 (EPA's Action on the New Footnotes in Table 33B), Footnotes E and F.

EPA recommends the State delete these footnotes from Table 33A since there are no citations to them
in Table 33A.

Footnote I

I This value is based on criterion published in Ambient Water Quality Criteria for Endosulfan
(EPA 440/5-80-046) and should be applied as the sum of alpha and beta-endosulfan.

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131, EPA is
disapproving Footnote I. This footnote provides clarification regarding the basis for Oregon's
derivation of the endosulfan criteria. Footnote I also provides that the aquatic life criteria for
endosulfan should be applied as the sum of alpha- and beta-endosulfan. This footnote directly
affects how the endosulfan criteria are applied with respect to the forms of endosulfan, therefore,
EPA considers this footnote to be a WQS requiring action under CWA 303(c).

24

-------
EPA disapproves the addition of Footnote I to Table 33 A because EPA disapproved moving the
currently applicable endosulfan criteria from Table 20 to Table 33 A because it would result in a
duration and frequency that is inconsistent with EPA's 304(a) recommendations (see Part III.B.3),
therefore this footnote does not cite to any criteria in Table 33A.

Since this footnote is reasonable when applied to the correct criteria, no change in the substance of
the footnote would be necessary to address the disapproval as long as Oregon revises the underlying
criteria to which it applied, in a manner approvable by EPA.

Footnote M

M Freshwater aquatic life values for pentachlorophenol are expressed as a function ofpH, and are
calculated as follows: CMC = exp(1.005(pH)-4.869); CCC = exp(1.005(pH)-5.134).

EPA Action

Footnote M provides the pH-based formulas used to derive the acute criterion (CMC) and the
chronic criterion (CCC) for pentachlorophenol. The acute criterion for pentachlorophenol is
contained in Table 33A, and EPA's approval of the acute criterion is presented in Part III.B.2 above.

The chronic criterion (CCC) for pentachlorophenol is not contained in Table 33A; rather, it is
contained in Table 33B. EPA's approval of the chronic criterion is presented in Part IV.B.3(b)
below.

EPA recommends that Oregon remove the chronic criterion (CCC) value from the Footnote M for
Table 33A because the CCC for pentachlorophenol is contained in Table 33B.

Footnote N

N This number was assigned to the list of non-priority pollutants in "National Recommended
Water Quality Criteria: 2002 " (EPA-822-R-02-047).

EPA Action

EPA approves this footnote as a non-substantive editorial change. In 2002, EPA published a
compilation of national recommended 304(a) recommendations (National Recommended Water
Quality Criteria: 2002). One of the tables in EPA's compilation contained a numbered list of non-
priority pollutants. Oregon has simply copied the numbers associated with each non-priority
pollutant from EPA's 2002 list into their water quality standards. EPA acknowledges this minor
editorial change and approves the non-substantive editorial change.

Footnote O

0 This criterion is based on EPA recommendations issued in 1980 that were derived using
guidelines that differedfrom EPA's 1985 Guidelines for minimum data requirements and
derivation procedures. For example, a "CMC" derived using the 1980 Guidelines was derived to
be used as an instantaneous maximum. If assessment is to be done using an averaging period,
the values given should be divided by 2 to obtain a value that is more comparable to a CMC
derived using the 1985 Guidelines.

-------
EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131, EPA is
disapproving the addition of Footnote O.

EPA Rationale

Oregon's new Footnote O explains the origin of the criteria, and explains how the acute criterion
should be implemented if a one-hour averaging period is used. EPA is disapproving Footnote O
because it applies to aquatic life criteria that have been either disapproved due to inconsistency with
40 CFR 131.11(a) (see Part III.B.4) or the transfer of the criteria from Table 20 to Table 33 A has
been disapproved (see Part III.B.3). Therefore, this footnote is not applicable to any of the criteria in
Table 33A.

Footnote P

P Criterion shown is the minimum (i.e. CCC in water should not be below this value in order to
protect aquatic life).

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131, EPA is
approving the addition of Footnote P as applied to alkalinity only.

EPA Rationale

Oregon applied this footnote to freshwater and saltwater acute and chronic criterion for endosulfan
and to the chronic criterion for alkalinity.

Endosulfan

This footnote is incorrect as applied to endosulfan, as confirmed in a letter to EPA dated October
3, 2012 (letter from Greg Aldrich, ODEQ, to Daniel D. Opalski, EPA). Since EPA is
disapproving the transfer of the endosulfan criteria from Table 20 to Table 33A, as described in
Part III.B.3 above, the erroneous reference to this footnote in connection with the endosulfan
criteria is also disapproved.

Alkalinity

As applied to the alkalinity criteria the footnote is consistent with EPA's 304(a)
recommendations, therefore, EPA is approving this footnote for alkalinity and the reference to
footnote P contained in Table 33A for alkalinity.

Footnote O

Q Criterion is applied as total arsenic (i.e. arsenic (III) + arsenic (V)).

EPA Action

This footnote is not applicable to any criteria in Table 33A because there is no citation to this
footnote anywhere in Table 33A. Because this footnote does not apply to any criteria in Table 33A,

-------
it does not establish a legally binding requirement under State law nor does it describe a desired ambient
condition of a water body to support a particular designated use. Therefore, the footnote is not considered
a water quality standard subject to EPA review and approval under 303(c) of the CWA, and EPA is
taking no action to approve or disapprove the new footnote.

EPA recommends the State delete this footnote from Table 33A since there is no citation to the footnote
in Table 3 3 A.

Footnote S

S This criterion is expressed as ng free cyanide (CN)/L.

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131, EPA is
approving the addition of Footnote S.

EPA Rationale

Oregon has not changed the numeric criteria for cyanide (which were previously approved by EPA);
rather, the footnote clarifies the form of cyanide that should be measured. It is consistent with EPA's
304(a) recommendations for calculating the criterion, which states criteria are expressed as free cyanide
(see Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient Water, September
1996, EPA-820-8-96-001, pages F1-F3).

This footnote establishes a legally binding requirement under State law and helps describe a desired
ambient condition of a water body to support a particular designated use and is therefore considered a
WQS subject to EPA review and approval under 303(c) of the CWA. The description of the applicable
form of cyanide is a component of the overall description of the level of protection afforded by the
criterion. Since this footnote specifies the applicable form of the cyanide criterion Oregon adopted, EPA
approves this footnote as a WQS.

Footnote T

T This criterion applies to DDT and its metabolites (i.e. the total concentration of DDT and its metabolites
should not exceed this value).

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131, EPA is
disapproving the addition of Footnote T.

Oregon's new Footnote T for DDT explains that the criterion applies to DDT and its metabolites. It
directly affects how the DDT criteria are applied with respect to the forms of DDT, therefore, EPA
considers this footnote to be a WQS requiring action under CWA 303(c).

EPA disapproves the addition of Footnote T to Table 33 A because EPA disapproved transferring the
currently applicable DDT criteria from Table 20 to Table 33A. Therefore, this footnote does not
apply to criteria in Table 33A.

Since this footnote is reasonable when applied to the correct criteria, no change in the substance of
the footnote would be necessary to address the disapproval as long Oregon revises the underlying
criteria to which it applied, in a manner approvable by EPA.

-------
Footnote U

U This criterion applies to total PCBs (e.g. the sum of all congener or all isomer or homolog or
Arochlor analyses).

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131, EPA is
approving the addition of Footnote S.

Oregon's new Footnote U for PCBs explains that the criterion applies to total PCBs. EPA has reviewed
this footnote language and the 304(a) criteria recommendations, which state that the "criterion applies to
total PCBs, (e.g., the sum of all congener or all isomer or homolog or Aroclor analyses.)" Oregon's new
footnote language along with the aquatic life criterion values (which were previously approved) for
PCBs are consistent with EPA's recommended 304(a) national default values.

This footnote establishes a legally binding requirement under State law and helps describe a desired
ambient condition of a water body to support a particular designated use and is, therefore, considered a
WQS subject to EPA review and approval under 303(c) of the CWA. The description of the applicable
form of PCBs is a component of the overall description of the level of protection afforded by the
currently EPA approved criterion. Since this footnote specifies the applicable form of the PCB criterion
Oregon adopted, EPA approves this footnote as a WQS.

Footnote V

V The CMC=l/[(fl/CMCl)+(f2/CMC2)] where fl and f2 are the fractions of total selenium that
are treated as selenite and selenate, respectively, and CMC1 and CMC2 are 185.9 /jg/L and
12.82 ng/L, respectively.

EPA Action

This footnote is not applicable to any criteria in Table 33A because there is no citation to this
footnote anywhere in Table 33A. Additionally, Footnote V to Table 33B sets forth the same
criterion for acute selenium that is described above, and Footnote V is cited in Table 33B.
Therefore, EPA's decision regarding this criterion is set forth below in Part IV.B.4.e (Freshwater
Acute and Chronic Selenium Aquatic Life Criteria).

EPA recommends the State delete this footnote from Table 33A since there is no citations to the
footnote in Table 33A.

Footnote W

W The acute and chronic criteria for aluminum are 750 /jg/L and 87 ng/L, respectively. These
values for aluminum are expressed in terms of "total recoverable " concentration of metal in the
water column. The criterion applies atpH<6.6 and hardness<12 mg/L (as CaCOs).

EPA Action

This footnote is not applicable to any criteria in Table 33A because there is no citation to this
footnote anywhere in Table 33A. Additionally, Footnote W to Table 33B sets forth the same criteria
for aluminum that is described above, and Footnote W is cited in Table 33B. Therefore, EPA's
decision regarding this criterion is set forth below in Part IV.B.4.a (Freshwater Acute and Chronic
Aluminum Aquatic Life Criteria).

-------
EPA recommends the State delete the footnote from Table 33A since there is no citation to the foontnote
in Table 3 3 A.

Footnote X

X The effective date for the criterion in the column immediately to the left is 1991.

EPA Action

EPA is approving this footnote as a non substantive change that does not change the criteria or the
effective date of the criteria. The footnote simply acknowledges the criteria that became effective in
1991.

Footnote Y

Y No criterion.

EPA Action

This footnote is not applicable to any criteria in Table 33A because there is no citation to this
footnote anywhere in Table 33A. Because this footnote does not apply to any criteria in Table 33A,
it does not establish a legally binding requirement under State law nor does it describe a desired ambient
condition of a water body to support a particular designated use. Therefore the footnote is not considered
a water quality standard subject to EPA review and approval under 303(c) of the CWA, and EPA is
taking no action to approve or disapprove the new footnote.

EPA recommends the State delete the footnote from Table 33A since there is no citation to the foontnote
in Table 3 3 A.

6. EPA's Action on Non-substantive Formatting Changes in Table 33A

Oregon's revisions to its water quality standards resulted in formatting changes to its water quality
criteria table. The following numeric criteria in Table 33 A were previously contained in Table 20,
and previously approved by EPA. Oregon has not revised the criteria, they have simply moved the
criteria to a new Table.

Alkalinity (freshwater chronic)

Chloride (freshwater acute and chronic)

Chlorine (freshwater and saltwater acute and chronic)

Chloropyrifos (freshwater and saltwater acute and chronic)

Cyanide (freshwater and saltwater acute and chronic)

Demeton (freshwater acute, saltwater acute)

Guthion (freshwater chronic, saltwater chronic)

Iron (freshwater chronic)

Malathion (freshwater chronic, saltwater chronic)

Methoxychlor (freshwater chronic, saltwater chronic)

Mirex (freshwater chronic, marine chronic)

Parathion (freshwater acute and chronic)

Polychlorinated Biphenyls (freshwater and saltwater acute and chronic)

-------
Pentachlorophenol (saltwater acute and chronic)

Phosphorus-elemental (saltwater chronic)

Sulfide-Hydrogen Sulfide (freshwater and saltwater chronic)

Toxaphene (freshwater and saltwater acute and chronic)

Additionally, when Oregon adopted human health criteria in 2011, Oregon created a new Table 40
that contains all the human health criteria. Therefore, Oregon omitted from Table 33A not only the
human health criteria themselves, but also all references to human health criteria in the introductory
paragraph. Oregon also removed Footnotes B, G, H, J, K, L, and R (which all referred to the human
health criteria) at that time.

EPA Action

EPA acknowledges that the above referenced criteria, which were previously approved by EPA under
303(c) of the CWA, were moved from Table 20 to Table 33A; and acknowledges the editorial
changes made to the introductory language and the removal of the footnotes associated with human
health criteria. EPA approves these changes as non-substantive formatting changes.

30

-------
IV. EPA'S ACTION ON THE INTRODUCTORY LANGUAGE, NEW AND
REVISED AQUATIC LIFE CRITERIA, AND FOOTNOTES IN TABLE 33B

A. Table 33B in Oregon's Water Quality Standards

The following presents the introductory language to Table 33B, new/revised criteria contained in Table
33B, and new footnotes to Table 33B. All new language from the 2004 and 2011 revisions, including
new and revised criteria, is underlined; strikeout text indicates the language that was removed during
Oregon's 2007 water quality standards adoption (i.e., freshwater and saltwater acute and chronic arsenic
criteria, and the saltwater acute and chronic chromium VI criteria) or during the 2011 water quality
standards adoption (i.e., all other strikeout language).

Table 33B

Note: The Environmental Quality Commission adopted the following criteria on May 20, 2004 to become effective on EPA
approval. EPA has not yet (as of June 2006) approved the criteria. The Table 33B criteria may not be used until they are
approved by EPA7.

AQUATIC LIFE WATER QUALITY CRITERIA SUMMARYa

Compounds are listed in alphabetical order with the corresponding EPA number (from National Recommended Water
Quality Criteria:2002. EPA 8220R-02-047'). the Chemical Abstract Service (CAS) number, aquatic life freshwater acute and
chronic criteria, aquatic life saltwater acute and chronic criteria, and human health water & organism and organism only
criteria, and Drinking Water Maximum Contaminant Level (MCL). The acute criteria refer to the average concentration for
one (11 hour and the chronic criteria refer to the average concentration for 96 hours (4-davs). and that these criteria should not
be exceeded more than once every three (31 years.

EPA No.

Compound

CAS
Number

Freshwater

Saltwater

Acute
(CMC)

Effective

Chronic
(CCC)

Effective

Acute
(CMC)

Effective

Datp

Chronic
(CCC)

Effective
Date

2 N

Aluminum (t>H 6.5 - 9.0)

7429905

3 N

Ammonia

7664417

Arsenic

7440382

310 E.O

150 E.O

69 E. O

36E.O

Asbestos

1332214

Benzene

71432

Bervllium

7440417

105

BHC eamma- (Lindane)

58899

Cadmium

7440439

E.F

40 E

8.8 E

107

Chlordane

57749

CHLORINATED BENZENES

Chloroform

67663

ChloroisooroDvlEther Bis2-

108601

15 N

ChloromethvlEther. Bis

542881

Chromium fill)

E.F

Chromium (VI)

18540299

16 E

11 E

1100 E

50 £

CoDDer

7440508

E.F

4.8 E

3.1 E

108

DDT 4.4'-

50293

DIBUTYLPHTHALATE

7 EPA approved this note to Table 33B in its February 18, 2011 action.

-------
EPA No.

Compound





CAS
Number



Freshwater

Saltwater

Acute
(CMC)

Effective

Chronic
fCCC)

Effective

Acute
(CMC)

Effective

Datp

Chronic
fCCC)

Effective
Date



DICHLOROBENZENES

























DICHLOROBENZIDINE

























DICHLOROETHYLENES

























DICHLOROPROPENE























ill

Dieldrin





60571





0.056













DINITROTOLUENE

























DIPHENYLHYDRAZINE























115

Endrin





72208





0.036











86

Fluoranthene





206440



















HALOMETHANES























20 N

Iron





7439896

















7

Lead





7439921

E.F



E.F



210 E



8.1 E



22 N

Maneanese





7439965

















8a

Mercurv





7439976



















MONOCHLOROBENZENE























9

Nickel





7440020

E.F



E.F



74 E



8.2 E



53

Pentachloroohenol





87865





M











54

Phenol





108952



















POLYNUCLEAR AROMATIC
HYRDOCARBONS























10

Selenium





7782492

E.V



5 E



290 E



71 E



11

Silver





7440224

E.F.P



0.10 E



1.9 E.P







44 N

Tributvltin (TBT)





688733

0.46



0.063



0.37



0.01



41

Trichloroethane 1.1.1-





71556

















55

TrichloroDhenol 2.4.6-





88062

















13

Zinc





7440666

E.F



E.F



90 E



81 E



Footnotes for Table 33A and 33B	

A Values in Table 20 are applicable to all basins.

B Human Health criteria values were calculated using a fish consumption rate of 17.5 grams per day (0.6 ounces/dav>
unless otherwise noted, (was deleted in 20111

C Ammonia criteria for freshwater may depend on pH. temperature, and the presence of salmonids or other fish with
ammonia-sensitive early life stages. Values for freshwater criteria (of total ammonia nitrogen in mg N/L1 can be
calculated using the formulae specified in 1999 Update of Ambient Water Quality Criteria for Ammonia (EPA-822-R-
99-014: http://www.epa.gov/ost/standards/ammonia/99update.pdf):

Freshwater Acute:

salmonids present... .CMC = 0.275 + 39.0

1+ 1()7.204-pH 1+ 1()pH-7.204

salmonids not present... CMC= 0.411 + 58.4

1+ 1()7.204-pH 1+ 1()pH-7.204

Freshwater Chronic:

fish early life stages present:

CCC= 0.0577 + 2.487 * MIN (2.85.1.45*100028''(25'T)')

^q7.688-pH	j^QpH-7.688

fish early life stages not present:

CCC = 0.577 + 2.487 * 1.45*10ao28''(25'MAX(T-7))

^q7.688-pH	j^QpH-7.688

Note: these chronic criteria formulae would be applied to calculate the 30-day average concentration limit: in additioa
the highest 4-day average within the 30-day period should not exceed 2.5 times the CCC.

D Ammonia criteria for saltwater may depend on pH and temperature. Values for saltwater criteria (total ammonia) can
be calculated from the tables specified in Ambient Water Quality Criteria for Ammonia (Saltwater)—1989 (EPA 440/5-

32

-------
88-004: http://www.epa.gov/ost/pc/ambientwac/ammoniasaltl989.pdf).

E Freshwater and saltwater criteria for metals are expressed in terms of "dissolved" concentrations in the water column.

except where otherwise noted (e.g. aluminum).

F The freshwater criterion for this metal is expressed as a function of hardness (ing/L) in the water column. Criteria
values for hardness may be calculated from the following formulae (CMC refers to Acute Criteria: CCC refers to
Chronic Criteria):

CMC= (e\p(nu * 11 n(hardness) I + b_%))*CF
CCC= (exp(iiv * 11 n( ha rdness) I + b,0)*CF

where CF is the conversion factor used for converting a metal criterion expressed as the total recoverable fraction in the
water column to a criterion expressed as the dissolved fraction in the water column.

( homiciil

"1 \

l>v

ill,

l><

Cadmium

l.Ulbb

-3.924

U.74U9

-4.719

Chromium III

0.8190

3.7256

0.8190

0.6848

Copper

0.9422

-1.700

0.8545

-1.702

Lead

1.273

-1.460

1.273

-4.705

Nickel

0.8460

2.255

0.8460

0.0584

Silver

1.72

-6.59

Zinc

0.8473

0.884

0.8473

0.884

Conversion factors (CF) for dissolved metals (the values for total recoverable metals criteria were multiplied by the
appropriate conversion factors shown below to calculate the dissolved metals criteria):

( hcmic;il

TivshwiUor

Siilmiiior

Anile

Chronic

Acnlc

Chronic

Arsenic

1.000

Cadmium

1.136672-[(ln
hardnessKO.04183811

1.101672-[(ln
hardnessKO.04183811

0.994

Chromium III

0.316

0.860

Chromium VI

0.982

0.962

0.993

Copper

0.960

0.83

Lead

1.46203-[(ln
hardnessKO. 14571211

0.951

Nickel

0.998

0.997

0.990

Selenium

0.996

0.922

0.998

Silver

0.85

Zinc

0.978

0.986

0.946

G Human Health criterion is the same as originally published in the 1976 EPA Red Book (Quality Criteria for Water.
EPA 110/9 76 0231 which predates the 1980 methodology and did not use a fish ingestion BCF approach.

H This value is based on a Drinking Water regulation.

I This value is based on criterion published in Ambient Water Quality Criteria for Endosulfan (EPA 440/5-80-0461 and
should be applied as the sum of alpha and beta endosulfan.

J No BCF was available: therefore, this value is based on that published in the 1986 EPA Gold Beefe-

K Human Health criterion is for "dissolved concentration based on the 1976 EPA Red Book conclusion that adverse
effects from exposure at this level are aesthetic rather than toxic.

L This value is expressed as the fish tissue concentration of methvlmercurv.

M Freshwater aquatic life values for pentachlorophenol are expressed as a function of pH. and are calculated as follows:
CMC=(exp(1.005(pH1-4.8691: CCC=exp(1.005(pH1-5.1341.

N This number was assigned to the list of non-prioritv pollutants in National Recommended Water Quality Criteria: 2002
(EPA-822-R-02-0471.

O This criterion is based on EPA recommendations issued in 1980 that were derived using guidelines that differed from
EPA's 1985 Guidelines for minimum data requirements and derivation procedures. For example, a "CMC" derived
using the 1980 Guidelines was derived to be used as an instantaneous maximum. If assessment is to be done using an

-------
averaging period, the values given should be divided by 2 to obtain a value that is more comparable to a CMC derived
using the 1985 Guidelines.

P Criterion shown is the minimum (i.e. CCC in water should not be below this value in order to protect aquatic life).

Q—Criterion is applied as total arsenic (i.e. arsenic (III) + arsenic (V)).

R Arsenic criterion refers to the inorganic form only.

S This criterion is expressed as iig free cyanide (CNVL.

T This criterion applies to DDT and its metabolites (i.e. the total concentration of DDT and its metabolites
should not exceed this value).

U This criterion applies to total PCBs (e.g. the sum of all congener or all isomer or homolog or Arochlor analyses).

V The CMC=l/[(fl/CMCl)+(f2/CMC2)l where fl and f2 are the fractions of total selenium that are treated as selenite
and selenate. respectively, and CMC1 and CMC2 are 185.9 iig/L and 12.82 iig/L. respectively.

W The acute and chronic criteria for aluminum are 750 iig/L and 87 iig/L. respectively. These values for aluminum are
expressed in terms of "total recoverable" concentration of metal in the water column. The criterion applies at pH<6.6
and hardness<12 mg/L (as CaCOA

X The effective date for the criterion in the column immediately to the left is 1991.

Y No criterion.

B. EPA's CWA Determinations on Table 33B

1. EPA's Action on the Introductory Language to Table 33B

This section of the document addresses the introductory language to Table 33B. The introductory
language states:

The concentration for each compound listed in Table 33A is a criterion not to be exceeded in
waters of the state in order to protect aquatic life attd human health. All values are expressed as
micrograms per liter (ug/L) except where noted. Compounds are listed in alphabetical order with
the corresponding EPA number (from National Recommended Water Quality Criteria:2002.
EPA 8220R-02-047). the Chemical Abstract Service (CAS) number, aquatic life freshwater acute
and chronic criteria, aquatic life saltwater acute and chronic criteria, human health water &
organisms and organisms only, and Drinking Water Maximum Contaminant Level (MGD. The
acute criteria refer to the average concentration for one (1) hour and the chronic criteria refer to
the average concentration for 96 hours (4-davs). and that these criteria should not be exceeded
more than once every three (3) years.

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131, EPA
approves the introductory language for Table 33B.

EPA Rationale

The introductory language to the table provides the frequency and duration for each aquatic life
criterion (i.e., acute criterion is expressed as the one-hour average not to be exceeded more than once
every three years, and the chronic criterion is expressed as the four-day average not to be exceeded
more than once every three years), requires waters of the State not to exceed the criterion, describes
the units used for each chemical, and describes the organization of the table. Additionally, references
to human health criteria were deleted from the introductory language because in Oregon's 2011
adoption, Table 40 was created and contains all of the human health criteria.

-------
The federal regulation at 40 CFR 131.11(b) states that in establishing criteria, States should set
numerical values based on EPA's 304(a) recommendation (potentially modified to reflect site-
specific conditions) or other scientifically defensible methods. EPA's 304(a) recommendation
generally consist of a magnitude (level of pollutant that is allowable, usually expressed as a
concentration), duration (the period of time [averaging period] over which the instream concentration
is averaged for comparison with criteria concentrations), and frequency (how often a particular
criterion can be exceeded). The introductory language specifies a reasonable duration and frequency
to be used for the magnitudes listed in the table that follows; therefore, EPA is approving this
language. EPA's specific determinations on the adequacy of the magnitude for each new or revised
criterion to protect Oregon's fish and aquatic life designated use, given the specified duration and
frequency, is provided below.

An examination of Oregon's submission reveals that the reference to Table 33 A in the introductory
language to Table 33B is a non-substantive typographical error. EPA notes that there is sufficient
intrinsic evidence within the submission to establish that the language is an error (i.e., the language is
located within Table 33B and Table 33A already contains identical introductory language). Finally,
Oregon has confirmed that the reference to Table 33A in Table 33B is a mere typographical error (see
October 3, 2112 letter from Greg Aldrich, ODEQ to Daniel Opalski, EPA).

Additionally, EPA acknowledges the editorial changes made by removing references to human health
criteria in the introductory language. EPA approves this change as a non-substantive editorial
change.

2. Aquatic Life Criteria Deleted from Table 33B (Freshwater and Saltwater
Arsenic Criteria, Saltwater Chromium VI Criteria)

This section of the document addresses the freshwater and saltwater acute and chronic aquatic life
criteria for arsenic, and the saltwater acute and chronic criteria for chromium VI. EPA is including
this narrative in the record to document the events that occurred since 2004.

Oregon's July 2004 water quality standards submittal package to the EPA contained revised aquatic
life criteria for arsenic and chromium VI in Table 33B that superceded existing, less stringent criteria
located in Table 20 (which EPA had approved in 1999). On February 22, 2007, the EQC adopted a
number of rule revisions to correct errors and clarify language in Oregon's water quality standards;
Oregon submitted them to the EPA for review and approval on April 23, 2007. However, the 2007
revision of Table 33B inadvertently omitted the revised freshwater and saltwater acute and chronic
criteria for arsenic, and the revised saltwater acute and chronic criteria for chromium VI. Because the
2007 revision to Table 33B failed to carry forward the 2004 addition of these criteria to Table 33B, it had
the effect of eliminating the 2004 revision to these criteria prior to EPA taking any CWA § 303(c) action
on the revision. In an attempt to implement ESA § 7(a)(2) with respect to the July 2004 submission,
EPA subsequently consulted with the National Marine Fisheries Service and the U.S. Fish and
Wildlife Service ("Services") on the July 2004 revised criteria noted above. At the time that EPA

-------
initiated this consultation, EPA was unaware that the 2004 revised aquatic life criteria for arsenic and
chromium VI were no longer in existence under Oregon state law. In 2012, EPA became aware that
these criteria were no longer in existence, and thus could be neither approved nor disapproved.

The following presents the revised aquatic life criteria that Oregon added to Table 33B in July 2004 and
that Oregon subsequently deleted from Table 33B on February 22, 2007:

Arsenic, total (arsenic III + arsenic V). expressed as dissolved concentration

freshwater acute :	340 |ag/L

freshwater chronic :	150 |ag/L

saltwater acute :	69 |ug/L

saltwater chronic :	36 |ag/L

Chromium VI, expressed as dissolved concentration

saltwater acute :	1100 |_ig/L

saltwater chronic :	50 |ag/L

In 2004, Oregon also adopted conversion factors for the above criteria in Footnote F of Table 33B.
Conversion factors are used for converting a metal criterion expressed as a total recoverable fraction in
the water column to a criterion expressed as the dissolved fraction in the water column. The conversion
factors are still contained in Footnote F of Table 33B.

EPA Action

EPA is not taking action on the freshwater and saltwater acute and chronic arsenic criteria and the
saltwater acute and chronic chromium VI criteria adopted into Oregon's water quality standards
(Table 33B) in 2004 and subsequently removed from Oregon's water quality standards in 2007.
Oregon's 2007 rule revision removed the 2004 criteria from State law, and Oregon's 2007
submission to EPA superseded its 2004 submission to EPA. Therefore, the omitted criteria are no
longer pending before EPA for review.

Additionally, EPA is not taking action on the conversion factors for freshwater and saltwater acute
and chronic arsenic criteria or the conversion factors for saltwater acute and chronic chromium VI
criteria adopted in Oregon's water quality standards in Footnote F of Table 33B because the criteria
that these conversion factors applied to are no longer contained in Table 33B; therefore, they have no
effect.

Oregon's pre-2004 criteria for arsenic and chromium VI criteria remain in Table 20, and remain in
effect for CWA purposes. These criteria are:

Arsenic (III), expressed as total recoverable concentration

freshwater acute - 360 |ag/L
freshwater chronic - 190 |ag/L
saltwater acute - 69 |ag/L
saltwater chronic - 36 |ag/L

Chromium VI. expressed as total recoverable concentration

saltwater acute - 1100 |_ig/L
saltwater chronic - 50 |ag/L

36

-------
EPA notes that the arsenic and chromium VI criteria that Oregon adopted in 2004 and withdrew in
2007 are consistent with EPA's 304(a) recommendations. In addition, according to the National
Marine Fisheries Service and the U.S. Fish and Wildlife Service, EPA's approval of these criteria
will not cause jeopardy to any ESA-listed species and therefore, EPA recommends that Oregon re-
adopt these inadvertently omitted criteria. (See also Part IV.B.6, where EPA also recommends that
Oregon adopt Footnote Q, which is associated with the aquatic life arsenic criteria but was
inadvertently deleted from the footnote section of Table 33B).

3. Approval Action for New or Revised Aquatic Life Criteria in Table 33B

This section of the document contains EPA's specific determinations on the adequacy of the
magnitude for each new and revised criterion, identified below, to protect Oregon's fish and aquatic
life designated use, given the duration and frequency specified in the introductory language to Table
33B. Specifically, the acute criteria are expressed as one-hour averages that should not be exceeded
more than once in three years, and the chronic criteria are expressed as four-day averages that should
not be exceeded more than once in three years (see Part IV.B.l., above for EPA's approval action for
duration and frequency).

a) Approval Action for New or Revised Aquatic Life Metals Criteria

The hardness-based equations for each of the following freshwater aquatic life criteria are found in
Footnote F of Table 33B:

Cadmium:

Chromium III:

Lead:

Nickel:

Silver:

Zinc:

chronic only
acute and chronic
acute and chronic
acute and chronic
acute only
acute and chronic

The following freshwater numeric criteria are contained in Table 33B:

Chromium VI: acute and chronic
Silver:	chronic

Additionally, each of the above listed freshwater criteria (i.e., cadmium, chromium III, lead,
nickel silver, zinc, chromium VI, and silver) reference Footnote E of Table 33B which states that
the criteria are expressed in terms of dissolved concentrations in the water column.

The following saltwater numeric criteria are contained in Table 33B:

Cadmium:

acute and chronic

Copper:

acute and chronic

Lead:

acute and chronic

Nickel:

acute and chronic

Silver:

acute

Selenium:

acute and chronic

Zinc:

acute and chronic

37

-------
Additionally, each of the above listed saltwater criteria reference Footnote E of Table 33B,
which states that the criteria are expressed in terms of dissolved concentrations in the water
column.

Oregon adopted conversion factors (CF) for all of the criteria listed in table the below. The CFs
are found in Footnote F of Table 33B. A conversion factor (CF) is used for converting a metal
criterion expressed as the total recoverable fraction in the water column to a criterion expressed
as the dissolved fraction in the water column.

The following table provides a summary of the freshwater hardness-based equations (found in
Footnote F of Table 33B), the freshwater and saltwater numeric criteria (contained within Table
33B), and the conversion factors associated with each chemical (found in Footnote F):

Chemical

F reshwater/Saltwater
Acute/Chronic

Magnitude, dissolved

Conversion Factor (CF)

( ;i(l111 ill 111

freshwater dimmc

 |lii(liaaliiessi| -4 "I'^ii

1 1 <> 1 («-2-|(In hardiiessMi) ()41S"S11

sallwaler aaik

4o im 1.

o 'J'U

saltwater dimmc

S S mu 1.

0

Chromium III

freshwater aaik

(c\p(<> XI'Jo |lii(liai'diiessi| i ~25<>n ( 1'

() " I(.

freshwater dimmc

(e\p(HSI^o |lii(liai'diiessi| o (iS4Sii ( 1'

0 S(>o

Chromium VI

Iksliw ;ikr aaik

l(> IIu 1.

o ^

Iksliw ;ilcr d ironic

1 1 IIU 1.

o >J(i2

Copper

saltwater acute

4.8 (ig/L

0.83

saltwater chronic

3.1 ng/L

0.83

l.oiid

freshwater aaik

ie\p( 1 2"' |Iikhardnessi|-1 4<><)n ( 1'

1 4<>2<)"-|(In hardnessKO 145—1211

freshwater diroiiic

ie\pi 1 2"' |hi(hardiiessi|-4 "i)5n ( I'

1 4<>2<) '-|( In hardiiessiK) I45"I2)|

saltwater aaik

:io iitz 1.

o <)5 1

saltwater dii'ninc

S 1 Mi; 1.

o >J51

Nickel

freshwater acute

exp(0.8460 * [ln(hardness)] +2.255)) * CF

0.998

freshwater chronic

(exp(0.8460 * [ln(hardness)] +0.0584)) * CF

0.997

saltwater acute

74 (ig/L

0.990

saltwater chronic

8.2 ng/L

0.990

Sil\er

freshwater aaik

(e\pi 1 "2 |lii(hardiiessi| -<• 5l>>>:;= ( 1 "

() X5

Ik'shuakr diioiiic

II 0| ||u 1.

() S5

sallwalei' aaik

I.'J IIU 1.

o.S5

Selenium

sallwalei' aaik

2'«i iiu 1.

0 

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131,
EPA approves the magnitude and conversion factors for each of the criteria described above and
the reference to Footnote E, which expresses the criteria as the dissolved concentration in the
water column.

38

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EPA Rationale

EPA conducted an evaluation, in accordance with the methodology described in Section 1.0 of
the STSD (see Enclosure 2), of each of the criteria referenced above to determine whether the
criteria protect Oregon's fish and aquatic life designated use. Section 2.0 of the STSD presents
all of the relevant toxicological data that the EPA reviewed as well as an analysis and summary
of the data for each of the chemicals listed above. All of the relevant data show that the criteria
for the above referenced chemicals are protective of Oregon's fish and aquatic life use, therefore,
EPA approves these aquatic life criteria.

For the technical evaluation of a specific criterion, refer to Section 2.0 of the STSD (contained in
Enclosure 2).

b) Approval Action for Dieldrin, Endritt. Pentachloroyhenol. and Tributyltin Aquatic Life
Criteria

The following freshwater and saltwater criteria are contained in Table 33B:

Dieldrin:

Endrin:

Tributyltin:

(freshwater chronic) 0.056 |ig/L
(freshwater chronic) 0.036 |ig/L

(freshwater acute)
(freshwater chronic)
(saltwater acute)
(saltwater chronic)

0.46 |ig/L
0.063 |ig/L
0.37 |ig/L
0.01 |ig/L

The freshwater chronic criterion for pentachlorophenol is a pH-dependent equation and is found
in Footnote M of Table 33B. The chronic criterion is:

Pentachlorophenol: (freshwater chronic) CCC = exp(1.005(pH)-5.134)

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131,
EPA approves the magnitude (including the formula for Pentachlorophenol found in Footnote
M), frequency, and duration of the above referenced criteria.

Rationale

EPA conducted an evaluation, in accordance with the methodology described in Section 1 of the
STSD (see Enclosure 2), of each of the criteria referenced above to determine whether the
criteria protect Oregon's fish and aquatic life designated use. Section 2 of the STSD presents all
of the relevant toxicological data that the EPA reviewed as well as an analysis and summary of
the data for each of the chemicals listed above. All of the relevant data show that the criteria for
the above referenced chemicals are protective of Oregon's fish and aquatic life use, therefore
EPA approves these aquatic life criteria.

For the technical evaluation for a specific criterion refer to Section 2.0 of the STSD (contained in
Enclosure 2).

39

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4. Disapproval Action for New or Revised Aquatic Life Criteria in Table 33B

This section of the document addresses new or revised aquatic life criteria adopted by Oregon and
EPA's disapproval decisions.

a) Freshwater Acute and Chronic Aluminum Aquatic Life Criteria

Footnote W in Table 33B provides the magnitude for the freshwater acute and chronic aquatic life
criteria for aluminum, and specifies when the criteria are applicable. Specifically, Footnote W
states:

The acute and chronic criteria for aluminum are 750 |ig/L and 87 |ig/L, respectively.
These values for aluminum are expressed in terms of "total recoverable" concentration of
metal in the water column. The criterion applies at pH < 6.6 and hardness < 12 mg/L (as
CaC03).

The applicable duration and frequency are described in the introductory language to Table 33B
as a one-hour average that should not be exceeded more than once in three years for the acute
criterion, and a four-day average that should not be exceeded more than once in three years for
the chronic criterion (see Part IV.B. 1 for EPA's approval action for duration and frequency).

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131,
EPA disapproves the freshwater acute and chronic aquatic life aluminum criteria adopted in
Footnote W.

EPA Rationale

While Oregon adopted criteria that are numerically consistent with the magnitudes identified in
EPA's 304(a) recommendation (750 |ig/L and 87 |ig/L for acute and chronic criteria
respectively), Oregon also adopted additional language in Footnote W specifying that the
aluminum criteria apply to waters with pH values less than 6.6 and hardness values less than 12
mg/L (as CaCOs). This is inconsistent with EPA's 304(a) recommendation, which provides that
the same numeric concentrations apply specifically at pH values of 6.5 to 9.0 (see Ambient Water
Quality Criteria for Aluminum - 1988, EPA 440/5-86-008, August 1988). Different pH and
hardness values may affect the sensitivity of aquatic organisms to aluminum. Oregon did not
provide a sound scientific rationale in its supporting documentation to demonstrate that 750 |ig/L
(acute) and 87 |ig/L (chronic) are protective of designated aquatic life uses in Oregon at low pH
(i.e., less than 6.6) and low hardness values (i.e., less than 12 mg/L CaCOs). Therefore, the EPA
is disapproving the freshwater acute and chronic aquatic life criteria, which are contained in
Footnote W.

Remedies to Address EPA's Disapproval

There are several potential options Oregon could consider in establishing aluminum criteria that
are based on scientifically defensible methods and protect Oregon's designated aquatic life uses,
including:

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•	Replace the pH and hardness parameters of the aluminum criteria to match nationally
recommended 304(a) numeric criteria. Supply a sound scientific rationale for Oregon's view
that EPA's nationally recommended 304(a) numeric criteria for aluminum are protective of
Oregon's designated aquatic life uses, addressing the National Marine Fisheries Service's
("NMFS") concerns regarding the adoption of EPA's recommended 304(a) numeric criteria
for aluminum in Oregon (as expressed in NMFS's August 14, 2012 Biological Opinion).

•	Revise the aluminum criteria to protect Oregon's designated aquatic life uses. In developing
such criteria, address NMFS's Oregon-specific analysis of EPA's 304(a) recommended
criteria for aluminum (in the NMFS August 14, 2012 Biological Opinion). Supply a sound
scientific rationale to establish that Oregon's revised numeric criteria for aluminum are
protective of Oregon's designated aquatic life uses, addressing NMFS's concerns about
EPA's national recommended criteria to the extent such concerns are also relevant to the
protectiveness analysis for Oregon's revised criteria.

Unless Oregon informs EPA that it intends to bring the criteria into compliance as described
above, EPA will prepare and publish proposed regulations setting forth revised or new water
quality criteria for the protection of Oregon's aquatic life designated uses from exposure to
aluminum.

Freshwater Aquatic Life Criteria Currently in Effect in Oregon

Until EPA approves or promulgates revisions to numeric freshwater acute and chronic aquatic
life criteria for aluminum, the narrative criterion (OAR 340-042-0033(2)) applicable to the
designated aquatic life uses in Oregon is in effect for CWA purposes.

b) Freshwater Acute and Chronic Ammonia Aquatic Life Criteria

Oregon adopted the following freshwater acute and chronic aquatic life criteria for ammonia, in

Footnote C of Table 33B. Footnote C states the following:

Ammonia criteria for freshwater may depend on pH, temperature, and the presence of
salmonids or other fish with ammonia-sensitive early life stages. Values for freshwater
criteria (of total ammonia nitrogen in mgN/L) can be calculated using the formulae
specified in 1999 Update of Ambient Water Quality Criteria for Ammonia (EPA-822-R-
99-014; http://www. epa.gov/ost/standards/ammonia/99update.pdf):

Freshwater Acute:

salmonids present: CMC = 0.275 + 39.0

jq7.204~pH	jQpH-7.204

salmonids not present: CMC= 0.411	+ 58.4

jq7.204~pH	jqpH-7.204

Freshwater Chronic:

fish early life stages present:

CCC = 0.0577 + 2.487 *MIN (2.85,1.45*1oOX)28*(25-T))

jq7.688-PH	jgpH-7.688

41

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fish early life stages not present:

CCC = 0.577 + 2.487 * 1.45*j q0-028^25^^

jjq7.688-PH	jjQpH-7.688

Note: these chronic criteria formulae would be applied to calculate the 30-day average
concentration limit; in addition, the highest 4-day average within the 30-day period
should not exceed 2.5 times the CCC.

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131,
EPA disapproves the freshwater acute and chronic criteria for ammonia.

EPA Rationale

Oregon adopted the EPA's 1999 304(a) recommendations for freshwater acute and chronic
aquatic life criteria for ammonia. The 1999 recommendations were the most recent 304(a)
recommendation when Oregon revised their water quality criteria in 2004.

Since 1999, EPA has conducted several literature searches to locate results of laboratory toxicity
tests that quantify the adverse effects of ammonia on freshwater aquatic life, with particular attention
given to tests conducted with freshwater mussels because such data were not available for many of
these species at the time EPA published the 1999 304(a) recommendation for ammonia.

In 2009, EPA proposed a draft update to its 304(a) recommended criteria for ammonia. The
proposed acute and chronic criteria are more stringent than the 1999 304(a) recommended
criteria due to the new toxicity data for freshwater molluscs that are very sensitive to ammonia.

In developing recommendations under section 304(a) of the CWA, EPA bases its criteria on
approximately the 5th percentile genera for a given pollutant, which is often the four or five most

o

sensitive genera. Based on the toxicity data, the most sensitive genera used to develop the
proposed draft 2009 acute criterion are freshwater molluscs. This stands in contrast to the 1999
304(a) recommendation where, in the absence of the more recent mollusc data, the most sensitive
genera used to develop the acute criterion were fish, which appear to be less sensitive to
ammonia than freshwater mollusks.

Similarly, based on the available acquired chronic toxicity data, three of the four most sensitive
genera used to develop the draft 2009 chronic criterion were freshwater molluscs. This stands in
contrast to the 1999 304(a) recommendation, where only one of the four most sensitive genera
used to develop the chronic criterion was a mollusc. The most important difference between the
calculation of the 2009 draft chronic criteria and the 1999 304(a) recommendation is the more
recent data for molluscs, particularly freshwater mussels which appear to be more sensitive to
ammonia than fish (Draft 2009 Update Aquatic Life Ambient Water Quality Criteria for
Ammonia - Freshwater, December 2009).

8 As per the Guidelines, whenever there are 59 or greater GMAVs in the acute criteria dataset, the FAV is calculated using
the four GMAVs which have cumulative probabilities closest to 0.05. In the draft 2009 update of the acute water quality
criteria for ammonia, the four GMAVs with cumulative probabilities closest to 0.05 are sensitivity rank 2-5. If there are
fewer than 59 GMAVs, the four lowest GMAVs are used to calculate the FAV regardless of cumulative probabilities.

42

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Freshwater mussels are widely distributed throughout Oregon {Freshwater Mussels of the Pacific
Northwest, Ethan Nedeau, Allan K. Smith, Jen Stone, U.S. Fish and Wildlife Service). Given the
wide distribution of freshwater mussels in Oregon, and toxicity data showing that freshwater
mussels are particularly sensitive to ammonia, there is not a sound scientific rationale
demonstrating that Oregon's submitted ammonia criteria protect Oregon's designated aquatic life
uses, and the criteria are, therefore, inconsistent with CWA Section 303(c) and 40 CFR §131.11.

Remedies to Address EPA's Disapproval

To address this disapproval, Oregon must adopt ammonia criteria that are based on a sound
scientific rationale and protect Oregon's designated aquatic life uses. There are several means
by which Oregon may potentially accomplish this objective. They include:

•	Revise the adopted ammonia criteria to be consistent with the 2009 draft revised national
recommendations for ammonia criteria.

•	Revise the ammonia criteria to ensure protection of Oregon's designated aquatic life uses. Also
supply a sound scientific rationale to explain why the alternative ammonia criteria are protective
of Oregon's designated aquatic life uses, taking into account any data on freshwater mussels and
snails. Finally, to the extent that the adopted chronic aquatic life criterion for ammonia is less
stringent than that specified by the National Marine Fisheries Services ("NMFS") to avoid
jeopardy to listed species (i.e., less stringent than the value specified as a "Reasonable and
Prudent Alternative" in the NMFS's August 14, 2012 biological opinion), provide additional
sound scientific rationale to establish that the alternative chronic aquatic life criterion for
ammonia is protective of Oregon's designated aquatic life uses, given NMFS's opinion of the
effect of ammonia on Oregon's listed species.

Unless Oregon informs EPA that it intends to bring the criteria into compliance as described
above, EPA will prepare and publish proposed regulations setting forth revised or new water
quality criteria for the protection of Oregon's aquatic life designated uses from exposure to
ammonia.

Freshwater Acute and Chronic Ammonia Aquatic Life Criteria Currently in Effect in
Oregon

Until EPA approves or promulgates revisions to numeric freshwater acute and chronic aquatic
life criteria for ammonia, the previously approved numeric aquatic life criteria applicable to the
designated aquatic life uses in Oregon are in effect for CWA purposes. The criteria are as
follows:

Acute Criterion

The 1-hour average concentration of un-ionized ammonia (mg/L NH3) does not exceed more
often than once every three years on average, the numerical value given by:

0.52/FT/FPH/2 where:

FT= 100 03(20"TCAP); TCAP < T < 30 C
FT = 1 o°-03(20-T); 0 < T < TCAP

43

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FPH =1	8< pH < 9

FPH = 1 + 1Q74-ph 6.5 <8
1.25

TCAP = 20 C; Salmonids and other sensitive coldwater species present
TCAP = 25 C; Salmonids and other sensitive coldwater species absent

(An averaging period of one hour may not be appropriate if excursions of concentrations to
greater than 1.5 times the average occur during the hour; in such a case, a shorter averaging
period may be needed).

Chronic Criterion

The 4-day average concentration of un-ionized ammonia (mg/L NH3) does not exceed more
often than once every three years on average, the average* numerical value given by:

0.80/FT7FPH/RATIO

where FT and FPH are as above and:

RATIO =16	7.7 < pH < 9

RATIO = 24	6.5< pH < 7.7

TCAP = 15 C; Salmonids and other sensitive coldwater species present

TCAP = 20 C; Salmonids and other sensitive coldwater species absent

(*Because these formulas are nonlinear in pH and temperature, the criterion should be the

average of separate evaluation of the formulas reflective of the fluctuations of flow, pH and

temperature within the averaging period, it is not appropriate in general to simply apply the

formula to average pH, temperature and flow).

c) Freshwater Acute Cadmium Aquatic Life Criterion

The magnitude for the freshwater acute cadmium criterion to protect Oregon's fish and aquatic life
designated use is contained in Table 33B, which references Footnote F for the applicable equation
and parameters. The applicable duration and frequency are described in the introductory language
to Table 33B as a one hour average that should not be exceeded more than once in three years (see
Part IV.B. 1 above for EPA's approval action for duration and frequency).

Footnote E to Table 33B states that the criteria are expressed in terms of dissolved concentrations
in the water column. Footnote F also provides the conversion factors (CF) for converting a metal
criterion expressed as total recoverable fraction to a criterion expressed as dissolved fraction. The
freshwater acute criterion and associated conversion factor are provided below:

Chemical

Freshwater
Criteria

Magnitude, dissolved

Conversion Factor (CF)









Cadmium

Acute

(exp(1.016 - [In (hardness)] -3.924)) * CF

1.136672 - (In hardness)(0.041838)

44

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EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR Part 131,
EPA disapproves the freshwater acute criterion for cadmium (as described in Footnote F) and the
citation to Footnote E.

EPA Rationale

Oregon adopted EPA's 2001 304(a) recommendation for the freshwater acute aquatic life
criterion for cadmium. The CWA requires EPA to publish, and from time to time, revise
national criteria for water accurately reflecting the latest scientific knowledge. These criteria
provide EPA's recommendations to states as they establish their water quality standards as state
law. EPA recommends that where locally important or sensitive species occur, a more stringent
state or site-specific criterion may be appropriate.9

On August 14, 2012, EPA received the final biological opinion10 of the National Marine
Fisheries Service ("NMFS") regarding EPA's potential CWA approval of Oregon's revised
aquatic life criteria for cadmium. With respect to the freshwater acute cadmium aquatic life
criterion, NMFS stated that approving this particular criterion pursuant to CWA § 303(c) would
likely jeopardize the continued existence of threatened and endangered species residing in
Oregon.1 NMFS believes that approval of this particular criterion would likely jeopardize listed
species on the grounds that the criterion is "likely to reduce appreciably the likelihood of both
the survival and recovery of the listed species, and [is] likely to reduce appreciably the

12

conservation value of their critical habitats."

In light of the recent finalization of the biological opinion, the new information presented in the
biological opinion and similar information considered by other states, and the potential input into
each Agency's current evaluation processes by an ongoing National Academy of Sciences (NAS)
panel, EPA has not had sufficient opportunity to evaluate the validity of NMFS' conclusions
regarding potential jeopardy to listed species, nor to evaluate the need for (and potential
implementation of) alternatives. NMFS' concerns relevant to evaluating effects of cadmium on
listed species are at the frontier of scientific understanding, such that they are currently under
consideration by the above-noted NAS panel. EPA recognizes that to the extent NMFS's
concerns about the revised acute cadmium criterion are scientifically valid, they may influence
EPA's later conclusions about whether the revised criterion is: (1) based on sound scientific
rationale and (2) sufficient to protect the designated uses of Oregon waters.

The administrative record, in its current state of analysis, is not sufficient to provide a sound
scientific rationale for approval of this criterion. Because EPA has a legal obligation to act on

9	For example, in Idaho, a more stringent state specific adjustment to the national acute criterion was necessary to ensure the
protection of an important salmonid species residing in Idaho (Oncorhynchus clarkii). This same species reside throughout
Oregon, therefore this species may be at risk in Oregon.

10	Jeopardy and Adverse Modification of Critical Habitat Biological Opinion for the Environmental Protection Agency's
Proposed Approval of Certain Oregon Administrative Rules Related to Revised Water Quality Criteria for Toxic Pollutants,
National Marine Fisheries Service, Northwest Region, NMFS Consultation Number 2008/00148. ("Biological Opinion")

11	Biological Opinion at 547-8.

12	Biological Opinion at 548.

45

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13

the submission under CWA § 303(c) by January 31, 2013, and in light of the unresolved issues
noted above, EPA disapproves the acute cadmium criterion because it is not based on a sound
scientific rationale given the evolving nature of the data and science.

Remedy to Address Disapproval Action

To meet the requirements of the CWA, Oregon must develop a criterion with a sound scientific
rationale demonstrating that it is protective of the aquatic life designated use, given the data
regarding cadmium's scientifically demonstrated effects, and given the concerns raised in the
NMFS biological opinion. As described above, EPA has not completed its technical analysis of
the biological opinion such that it can recommend a specific numeric criterion protective of
Oregon aquatic life at this time. Additionally, new scientific data on the toxicity of cadmium is
now available and would need to be reviewed regarding their quality and relevance prior to being
considered in developing an updated recommendation for a specific numeric criterion protective
of Oregon aquatic life. EPA will collaborate with NMFS and Oregon to determine an
appropriate criterion by (1) considering the scientific bases of the NMFS opinion, (2) evaluating
the data used by the State of Idaho to develop its acute cadmium criterion, and (3) evaluating any
new data that may be available and meets appropriate quality assurance requirements.

Unless Oregon informs EPA that it intends to bring the criteria into compliance as described
above, EPA will prepare and publish proposed regulations setting forth a revised or new water
quality criterion for the protection of Oregon aquatic life from acute exposure to cadmium.

Freshwater Aquatic Life Criteria Currently in Effect in Oregon

Until EPA approves or promulgates revisions to numeric freshwater acute aquatic life criteria for
acute cadmium, the pre-2004 acute criterion for cadmium remains in effect for CWA purposes.
This criterion is expressed as total recoverable and is a one hour average that is not to be
exceeded more than once in three years. The equation is:

Acute criterion = exp(1.128[ln(hardness)] - 3.828)
d) Freshwater Acute and Chronic Cower Aquatic Life Criteria

The magnitude for the freshwater acute and chronic copper criteria to protect Oregon's fish and
aquatic life designated use are contained in Table 33B, which references Footnote F for the
applicable equation and parameters. The applicable duration and frequency are described in the
introductory language to Table 33B as a one-hour average that should not be exceeded more than
once in three years for the acute criterion, and a four-day average that should not be exceeded
more than once in three years for the chronic criterion (see Part IV.B. 1. above for EPA's approval
action for duration and frequency).

Footnote E to Table 33B states that the copper criteria are expressed in terms of dissolved
concentrations in the water column. Footnote F also provides the conversion factors (CF) for
converting a metal criterion expressed as total recoverable fraction to a criterion expressed as the
dissolved fraction.

13 Northwest Environmental Advocates v. United States Environmental Protection Agency. No. 6-cv-00479 (November 27,
2012) (consent decree providing that "EPA shall complete its final action approving and/or disapproving the aquatic life
criteria no later than January 31, 2013.")

46

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The freshwater criteria and associated conversion factors are provided below:

Chemical

Freshwater
Acute/Chronic

Magnitude, dissolved

Conversion Factor (CF)









Copper

acute

(exp(0.9422, [ln(hardness)] -1.700)) * CF

0.960

chronic

(exp(0.8545 - [ln(hardness)] -1.702)) * CF

0.960

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR Part 131,
EPA disapproves the freshwater acute and chronic criteria for copper (as described in Footnote
F) and the citations to Footnote E.

EPA Rationale

Oregon adopted EPA's 1995 304(a) recommendations for freshwater acute and chronic aquatic
life criteria for copper. The 1995 values were the most recent 304(a) recommendation at the
time Oregon adopted its copper criteria in 2004. The 1995 304(a) recommendation for
freshwater aquatic life criteria for copper were developed by relating the toxic effect
concentration of copper to water hardness. However, subsequent studies have shown that
hardness itself is not the most accurate determinant of copper toxicity. Rather than use hardness
as a surrogate, it is more accurate to directly consider the suite of separate water quality variables
(pH, alkalinity, and a number of specific ion concentrations such as calcium, sodium, etc.) that
often correlate with hardness in natural waters (and the lab water used in conducting the toxicity
tests that underlie the criteria).

There are many natural waters where hardness does not correlate well with other water quality
variables in regards to copper toxicity. Additionally, hardness may not correlate well with other
water quality variables in waterbodies influenced by discharges from treatment processes, storm
water runoff, agricultural runoff and other factors that create ambient water chemistry that may
be very different from a natural condition (or water chemistry used in conducting the toxicity
tests which underlie the hardness-dependent criteria). Thus the hardness-dependent copper
criterion is potentially under-protective or over-protective depending on the site-specific ambient
water chemistry.

In February 2007, EPA updated its national recommended aquatic life criteria for copper to
include new data that became available since the 1995 304(a) criteria were developed, and to
incorporate a more advanced modeling approach for developing water quality-dependent criteria
(Aquatic Life Ambient Freshwater Quality Criteria-Copper, 2007 Revision, EPA-822-R-07-001,
February 2007). This update incorporates the use of the biotic ligand model (the "BLM," a metal
bioavailability model) in the criteria derivation procedures. The BLM takes, as input, receiving
water body monitoring data. It enables the development of site-specific water quality criteria
using these inputs. The BLM requires ten input variables from the ambient water to calculate a
freshwater copper criterion: temperature, pH, dissolved organic carbon (DOC), calcium,
magnesium, sodium, potassium, sulfate, chloride, and alkalinity. Criteria that incorporate the
BLM can be tailored to the site-specific water chemistry of a water body and thus ensure the
protection of the aquatic life use, whereas the hardness-dependent criteria may or may not be

47

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protective of the aquatic life use, depending on the correlation in a particular water body between
the suite of water quality variables that affect copper toxicity, and the site-specific hardness.

EPA is disapproving the copper criteria for protection of aquatic life because it is inconsistent
with CWA Section 303(c) and 40 CFR § 131.11. Oregon relied on the EPA's 1995 304(a)
recommended criterion, which was superseded by the BLM in 2007. Given what is now known
about the improved accuracy of the BLM compared to the 1995 304(a) recommendation, and
given that Oregon's submission of revised copper criteria does not include a sound scientific
rationale to explain why the 1995 national recommended values will nevertheless suffice to
protect Oregon's designated aquatic life uses, EPA believes that the submitted acute and chronic
aquatic life criteria for copper lack a sound scientific rationale as required by 40 CFR §

131.11(a) and CWA Section 303(c).

Remedies to Address EPA's Disapproval

There are several potential options Oregon could consider in establishing copper criteria that are
based on scientifically defensible methods and protect Oregon's designated aquatic life uses,
including:

•	Replace the hardness-dependent copper criteria with the BLM contained in EPA's 2007
304(a) recommended criteria for copper, addressing NMFS Oregon specific analysis for
copper in the NMFS August 14, 2012 Biological Opinion. The BLM may be used on a
specific stream segment to calculate the applicable site-specific acute and chronic copper
criteria when the site-specific water chemistry needed to run the BLM is available. Site-
specific data must account for temporal and spatial variability to ensure that the derived
criteria are protective of designated uses.

Oregon-specific water quality data may be used in the BLM to develop state-wide default
acute and chronic criteria for copper (alternatively, the state may be divided into regions with
similar characteristics and default criteria may be developed for each region).

•	Revise the hardness-dependent copper criteria to protect Oregon's designated aquatic life
uses. In developing such criteria, give due consideration NMFS's Oregon-specific analysis
of EPA's pre-BLM 304(a) recommended criteria for copper (in the NMFS August 14, 2012
Biological Opinion). Supply a sound scientific rationale to establish that Oregon's revised
hardness-based copper criteria are protective of Oregon's designated aquatic life uses,
addressing NMFS's concerns about EPA's pre-BLM nationally recommended criteria to the
extent such concerns are also relevant to the protectiveness analysis for Oregon's revised
criteria.

•	Re-submit the pre-BLM hardness-dependent copper criteria with additional scientific basis
(including due consideration of the Oregon-specific analysis of the EPA's pre-BLM 304(a)
recommended criteria for copper included in the August 14, 2012 Biological Opinion of the
National Marine Fisheries Service), to establish that Oregon's pre-BLM hardness-dependent
criteria are protective of Oregon's designated aquatic life uses.

Unless Oregon informs EPA that it intends to bring the criteria into compliance as described
above, EPA will prepare and publish proposed regulations setting forth revised or new water

48

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quality criteria for the protection of Oregon's aquatic life designated uses from exposure to
copper.

Freshwater Copper Aquatic Life Criteria Currently in Effect in Oregon

Until Oregon adopts and EPA approves revisions to numeric freshwater acute and chronic
aquatic life criteria for copper, the previously approved numeric aquatic life criteria applicable to
the designated aquatic life uses in Oregon are in effect for CWA purposes. The acute criterion is
expressed as a 1-hour average not to be exceeded more than once in three years and the chronic
criterion is expressed as a 4-day average not to be exceeded more than once in three years; the
acute and chronic criterion are expressed as total recoverable, and the numeric values are:

CMC (acute criterion) = exp(0.9422[ln(hardness)]-1.464)

CCC (chronic criterion) = exp(0.8545[ln(hardness)]- 1.465)

Note: hardness is expressed as mg/L CaC03

e) Freshwater Acute and Chronic Selenium Aquatic Life Criteria

The magnitudes for the freshwater acute and chronic selenium criteria to protect Oregon's fish and
aquatic life designated use are contained in Table 33B, which provides a numeric concentration
for the chronic criterion, and references Footnote V for an equation and applicable parameters for
the acute criterion. The applicable duration and frequency are described in the introductory
language to Table 33B as a one-hour average that should not be exceeded more than once in three
years for the acute criterion, and a four-day average that should not be exceeded more than once in
three years for the chronic criterion (see Part IV.B.l above for EPA's approval action for duration
and frequency).

A citation to Footnote E provides that these criteria are expressed in terms of dissolved
concentrations in the water column. The criteria subject to EPA review are:

Selenium

Criterion, expressed as
dissolved

Comments

Acute (|ig/L)

1 /[(f 1 / CMC 1 )+(f2/CMC2)]

fl and f2 are the fractions of total selenium that are
treated as selenite and selenate, respectively, and CMC1
and CMC2 are 185.9 |ig/L and 12.82 |ig/L. respectively.

Chronic (|ig/L)

5

N/A

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131,
EPA disapproves the magnitudes for freshwater acute selenium criterion found in Footnote V
(and cited in table 33B), and the chronic selenium criterion found in Table 33B, and the citations
to Footnote E.

EPA Rationale

Oregon adopted criteria that are numerically consistent with the magnitudes identified in EPA's
304(a) recommendation. However, EPA's 304(a) recommended values are expressed as total

49

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recoverable concentrations in the water column, whereas the selenium criteria adopted by
Oregon are expressed as the dissolved concentrations in the water column. EPA has indicated
that it believes it is scientifically acceptable to use a conversion factor (CF) of 0.996 for the acute
criterion and a CF of 0.922 for the chronic criterion to convert the total recoverable value to a
dissolved value (see National Recommended Water Quality Criteria:2002, EPA-822-R-02-047,
Footnote T). Applying the CFs would result in the following criteria as dissolved:

Because Oregon expressed these criteria as dissolved without applying the appropriate
conversion factors (0.996 for acute and 0.992 for chronic), Oregon effectively has adopted acute
and chronic aquatic life selenium criteria that are slightly higher (less stringent) than EPA's
304(a) recommendations for these values. Oregon did not provide supporting documentation to
demonstrate that these less stringent values would nevertheless be protective of designated
aquatic life uses in Oregon. Therefore, the EPA is disapproving the revised freshwater acute and
chronic aquatic life criteria for selenium contained in Table 33B, including the reference to
Footnote E.

Remedies to Address EPA's Disapproval

To address this disapproval, Oregon must adopt selenium criteria that are based on a sound
scientific rationale and protect Oregon's designated aquatic life uses. There are several means
by which Oregon may potentially accomplish this objective. They include:

•	Revise the acute and chronic aquatic life criteria for selenium by incorporating the
application of the recommended conversion factors (0.996 for acute criteria, and 0.922 for
chronic criteria), consistent with EPA's approach for developing dissolved criteria. Also
incorporate the additional scientific data that have become available regarding selenium
toxicity since Oregon's 2004 submission to determine if additional revisions to the criteria
are needed to protect Oregon's designated aquatic life uses.

•	Otherwise, revise the acute and chronic aquatic life criteria for selenium by incorporating the
application of the recommended conversion factors (0.996 for acute criteria, and 0.922 for
chronic criteria), consistent with EPA's approach for developing dissolved criteria. Also
supply a sound scientific rationale why the additional scientific data that have become
available since Oregon's 2004 submission (respecting selenium toxicity) do not require
further revisions to these criteria to protect Oregon's designated aquatic life uses.

•	Resubmit the previously adopted acute and chronic selenium criteria with a sound scientific
rationale, to establish that the application of conversion factors (0.996 for acute criteria, and
0.922 for chronic criteria) are unnecessary to protect Oregon's designated aquatic life uses.
Also supply a sound scientific rationale why the additional scientific data that have become
available since Oregon's 2004 submission (regarding selenium toxicity) do not require
further revisions to the these criteria to protect Oregon's designated aquatic life uses.

•	Develop new acute and chronic aquatic life criteria for selenium to account for additional
scientific data that have become available regarding selenium toxicity since Oregon's 2004
submission.

Acute (|ig/L, dissolved):

1 /[(f 1 /CMC 1 )+(f2/CMC2)] |ig/L x 0.996

Chronic (|ig/L, dissolved):

5 |ig/L x 0.922 = 4.6 |ig/L

50

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Freshwater Aquatic Life Criteria Currently in Effect in Oregon

Until EPA approves or promulgates revisions to numeric freshwater acute and chronic aquatic
life criteria for selenium, the previously approved numeric aquatic life criteria applicable to the
designated aquatic life uses in Oregon are in effect for CWA purposes. The acute criterion is
expressed as a 1-hour average not to be exceeded more than once in three years and the chronic
criterion is expressed as a 4-day average not to be exceeded more than once in three years; the
acute and chronic criterion are expressed as total recoverable, and the numeric values are:

Acute criterion: 260 |ig/L

Chronic criterion: 35 |ig/L

5. EPA's Action on the New Footnotes In Table 33B

This section of the document addresses the footnotes in Table 33B. Oregon added Footnotes A
through X14 but subsequently eliminated Footnotes B, G, H, J, K, L, Q, and added Footnote Y.

Footnote A

A Values in Table 20 are applicable to all basins.

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131, EPA is
disapproving this footnote, which directs the reader to the incorrect table. Oregon has explained to
EPA that this is an error and Oregon intends to correct the footnote to read "Values in Table 33B are
applicable to all basins" (see October 3, 2012 letter from Greg Aldrich, ODEQ to Daniel Opalski,
EPA).

Remedy to Disapproval Language

Change the text in Footnote A to "Values in Table 33B are applicable to all basins."

Narrative Language Currently in Effect in Oregon

OAR 340-041-0033(3) has been approved by EPA and is in effect for CWA purposes; it states:
"Levels of toxic substances in waters of the state may not exceed the applicable aquatic life criteria
listed in Tables 20, 33A, and 33B...." This language correctly requires the aquatic life criteria in
Table 33B to be applied to all waters of the state.

Footnote C

C Ammonia criteria for freshwater may depend on pH, temperature, and the presence of salmonids
or other fish with ammonia-sensitive early life stages. Values for freshwater criteria (of total

14 In the 2004 water quality standards adoption all of the Footnotes for Table 33 A and Table 33B were contained at the end of
Table 33B. In the 2011 water quality standards adoption, Oregon removed all of the footnotes associated with human health
criteria because the human health criteria were removed from Table 33A and incorporated into a new Table 40. In the 2011
water quality standards adoption Oregon also included all of the footnotes at the end of Table 33 A, and retained all the
footnotes at the end of Table 33B except for the human health related footnotes, additionally in 2011 footnote Y was added to
Table 33B.

51

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ammonia nitrogen in mgN/L) can be calculated using the formulae specified in 1999 Update of
Ambient Water Quality Criteria for Ammonia (EPA-822-R-99-014;
http://www.epa.gov/ost/standards/ammonia/99update.pdf):

Freshwater Acute:

salmonids present.... CMC = 0.275 + 39.0

jq7.204~pH	jqpH-7.204

salmonids not present... CMC= 0.411	+ 58.4

jq7.204~pH	jQpH-7.204

Freshwater Chronic:
fish early life stages present:

CCC = 0.0577 + 2.487 *M1N (2.85,1.45*1oao28*(25'T))

jq7.688-PH	jjqpH-7.688

fish early life stages not present:

CCC = 0.577 + 2.487 * 1.45*j q0-028^25^^

jjq7.688-PH	jjgpH-7.688

Note: these chronic criteria formulae would be applied to calculate the 30-day average
concentration limit; in addition, the highest 4-day average within the 30-day period should not
exceed 2.5 times the CCC.

EPA Action

EPA is disapproving the criteria for freshwater ammonia, which includes a disapproval of Footnote
C. EPA's action on the freshwater ammonia criteria in Footnote C is discussed in Part IV.B.4(b)
(Freshwater Acute and Chronic Ammonia Aquatic Life Criteria)

Footnote D

I) Ammonia criteria for saltwater may depend on pH and temperature. Values for saltwater
criteria (total ammonia) can be calculatedfrom the tables specified in Ambient Water Quality
Criteria for Ammonia (Saltwater)—1989 (EPA 440/5-88-004;
http://www.epa. sov/ost/pc/ambientwqc/ammoniasalt1989.pdf.

EPA Action

This footnote is not applicable to any criteria in Table 33B because there is no citation to this
footnote anywhere in Table 33B. Additionally, Footnote D to Table 33A sets forth the same criteria
for ammonia that is described above, and Footnote D is cited in Table 33A. Therefore, EPA's
decision regarding this footnote is set forth above in Part III.B.5 (EPA's Action on Footnotes in
Table 33A).

EPA recommends the State delete this footnote from Table 33B since there is no citation to the
footnote in Table 33B.

Footnotes E

E Freshwater and saltwater criteria for metals are expressed in terms of "dissolved"
concentrations in the water column, except where otherwise noted (e.g. aluminum).

52

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EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131, EPA
approves expressing the metals criteria in terms of the "dissolved" concentrations in the water
column.

Rationale

EPA derives its national aquatic life criteria so that they protect water-column organisms from
exposure to pollutants that are present in the water column. The primary mechanism for water
column toxicity is adsorption at the gill surface which requires metals to be in the dissolved form.

The scientific evidence indicates that particulate-bound metals do not contribute toxicity when
suspended in the water column. Two expert workshops, one in Annapolis in 1993 (58 FR 32131,
June 8, 1993) and one in Pensacola in 1996 (Bergman, H.L. and E.J. Dorward-Kind (eds.),
Reassessment of Metal Criteria for Aquatic Life Protection. SETAC Press. Pensacola, FL. 1997)
were held to discuss this issue. Both workshops recommended that EPA express its aquatic life
criteria for metals in terms of dissolved metal. EPA agrees with the recommendations of the expert
workshops and with the supporting rationales. Therefore, EPA now expresses its aquatic life criteria
for metals in terms of dissolved metal instead of total recoverable metal because dissolved metal
more closely approximates bioavailable metal in the water column than does total recoverable
metal.15

Footnote F

F The freshwater criterion for this metal is expressed as a function of hardness (mg/L) in the water
column. Criteria values for hardness may be calculatedfrom the following formulae (CMC
refers to Acute Criteria; CCC refers to Chronic Criteria):

CMC = (exp(mA* [ln(hardness)] + bj))*CF
CCC = (exp(mc* [ln(hardness)] + bc))*CF

where CF is the conversion factor usedfor converting a metal criterion expressed as the total
recoverable fraction in the water column to a criterion expressed as the dissolvedfraction in the
water column.

( licmictil

in i



in,

b,

Cadmium

1.0166

-3.924

0.7409

-4.719

Chromium III

0.8190

3.7256

0.8190

0.6848

Copper

0.9422

-1.700

0.8545

-1.702

Lead

1.273

-1.460

1.273

-4.705

Nickel

0.8460

2.255

0.8460

0.0584

Silver

1.72

-6.59





Zinc

0.8473

0.884

0.8473

0.884

Conversion factors (CF) for dissolved metals (the values for total recoverable metals criteria
were multiplied by the appropriate conversion factors shown below to calculate the dissolved
metals criteria):

15 Water Quality Guidance for the Great Lakes System: Supplementary Information Document (SID), 1995, EPA 820-B-95-
001. http://www.epa.gov/region5/water/wqs5/pdf/supp_inf_doc.pdf

53

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( henikdI

Freshwater

Still water

Acute

(lironic

Acute

(lironic

. 1rsenic

1.000

1.000

1.000

1.000

Cadmium

1.136672-[(ln
hardness) (0.041838)]

1.101672-[(ln
hardness) (0.041838)]

0.994

0.994

Chromium III

0.316

0.860





Chromium VI

0.982

0.962

0.993

0.993

Copper

0.960

0.960

0.83

0.83

Lead

1.46203-[(ln
hardness) (0.145712)]

1.46203-[(ln
hardness) (0.145712)]

0.951

0.951

Nickel

0.998

0.997

0.990

0.990

Selenium

0.996

0.922

0.998

0.998

Silver

0.85

0.85

0.85

—

Zinc

0.978

0.986

0.946

0.946

EPA Action

EPA's action on each of the above can be found in this document in the following locations:

( hcmic;il

TivshwiUor

Siilmiiior

Anile

Chronic

Acnlc

(lironic

\rsenic

Part IV.B.2

Part IV.B.2

Part IV.B.2

Part IV.B.2

Cadmium

Part IV.B.4(c)

Part IV.B.3(a)

Part IV.B.3(a)

Part IV.B.3(a)

Chromium III

Part IV.B.3(a)

Part IV.B.3(a)

N/A

N/A

Chromium VI

Part IV.B.3(a)

Part IV.B.3(a)

Part IV.B.2

Part IV.B.2

Copper

Part IV.B.4(d)

Part IV.B.4(d)

Part IV.B.3(a)

Part IV.B.3(a)

Lead

Part IV.B.3(a)

Part IV.B.3(a)

Part IV.B.3(a)

Part IV.B.3(a)

Nickel

Part IV.B.3(a)

Part IV.B.3(a)

Part IV.B.3(a)

Part IV.B.3(a)

Selenium

Part IV.B4(e)

Part IV.B.4(e)

Part IV.B.3(a)

Part IV.B.3(a)

Silver

Part IV.B.3(a)

Part IV.B.3(a)

Part IV.B.3(a)

N/A

Zinc

Part IV.B.3(a)

Part IV.B.3(a)

Part IV.B.3(a)

Part IV.B.3(a)

Footnote I

I This value is base on criterion published in Ambient Water Quality Criteria for Endosulfan
(EPA 440/5-80-046) and should be applied as the sum of alpha and beta-endosulfan.

EPA Action

This footnote is not applicable to any criteria in Table 33B because there is no citation to this
footnote anywhere in Table 33B. Additionally, Footnote I to Table 33 A sets forth the same
information that is described above, and Footnote I is cited in Table 33A. Therefore, EPA's decision
regarding this footnote is set forth above in Part III.B.5 (EPA's Action on Footnotes in Table 33A),
Footnote I.

EPA recommends that Oregon remove this footnote from Table 33B since there are no citations to
the footnotes in Table 33B.

Footnote M

M Freshwater aquatic life values for pentachlorophenol are expressed as a function ofpH, and are
calculated as follows: CMC=exp(1.005(pH)-4.869); CCC=exp(1.005(pH)-5.134).

54

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EPA Action

The CMC for this criterion is set forth in Table 33A, therefore EPA's decision regarding the CMC is
set forth in Part III.B.2 above. The CCC is contained in Table 33B, EPA's decision on the CCC is
set forth in Part IV.B.3(b) above.

EPA recommends that Oregon remove the CMC value from Footnote M of Table 33B because the
CMC for pentachlorophenol is contained in Table 33 A.

Footnote N

N This number was assigned to the list of non-priority pollutants in National Recommended Water
Quality Criteria: 2002 (EPA-822-R-02-047).

EPA Action

Footnote O

This criterion is based on EPA recommendations issued in 1980 that were derived using guidelines
that differedfrom EPA's 1985 Guidelines for minimum data requirements and derivation
procedures. For example, a "CMC" derived using the 1980 Guidelines was derived to be used as an
instantaneous maximum. If assessment is to be done using an averaging period, the values given
should be divided by 2 to obtain a value that is more comparable to a CMC derived using the 1985
Guidelines.

EPA Action

This footnote is not applicable to any criteria in Table 33B because there is no citation to this
footnote anywhere in Table 33B. Additionally, Footnote O to Table 33A sets forth the same
language that is described above, and Footnote O is cited in Table 33A. Therefore, EPA's decision
regarding this footnote is set forth in Part III.B.5, Footnote O (EPA's Action on Footnotes in Table
33A).

EPA recommends that Oregon delete this footnote from Table 33B since there is no citation to the
footnote in Table 33B.

Footnote P

P Criterion shown is the minimum (i.e. CCC in water should not be below this value in order to
protect aquatic life).

-------
EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131, EPA is
disapproving the addition of footnote P in Table 33B.

EPA Rationale

Oregon applies Footnote P to the freshwater and saltwater acute criterion for silver. In a letter dated
October 3, 2012 from Greg Aldrich ODEQ to Daniel Opalski, EPA, Oregon acknowledged that
Footnote P is an error and should be removed.

Footnote P states that a water body should have an amount of silver in the water body that is no less
than the acute criterion value. In other words, a silver concentration in the water greater than the
acute criterion would meet this criterion. This use of the criterion is inconsistent with EPA's 304(a)
recommendation, which states that the acute criterion is the maximum amount of silver that may be
in a water body without causing adverse effects to aquatic life uses.

Since Oregon acknowledge that Footnote P is an error and should be removed, and because there is
no supporting documentation to show that using the silver criterion as described in Footnote P is
protective of aquatic life designated uses, EPA is disapproving this footnote.

Remedy to Address EPA Disapproval

This disapproval can be addressed by removing Footnote P from Table 33B.

Footnote R

R Arsenic criteria refer to the inorganic form only.

EPA Action

Footnote R was adopted in Oregon's 2004 water quality standards revision but was not applied to
any aquatic life criteria Table 33B (or Table 33 A); rather Footnote R was applied to the human
health criteria for arsenic contained in Table 33A. EPA disapproved footnote R as it applied to the
arsenic human health criteria in its June 1, 2010 action (see Technical Support Document for Action
on the State of Oregon's New and Revised Human Health Water Quality Criteria for Toxics and
Revisions to Narrative Toxics Provisions Submitted on July 8,2004, June 1, 2010).

In its 2011 water quality standard revision, Oregon moved the human health criteria and associated
footnote to Table 40. But it appears that the State inadvertently retained Footnote R in the footnotes
to Table 33B. At this time, EPA is not taking action on Footnote R as it is not a water quality
standard. There is no citation to Footnote R in Table 33B therefore the footnote does not establish a
legally binding requirement under State law nor does it describe a desired ambient condition of a water
body to support a particular designated use. Therefore the footnote is not considered a water quality
standard subject to EPA review and approval under 303(c) of the CWA, and EPA is taking no action to
approve or disapprove the footnote.

EPA recommends that Oregon delete Footnote R from Table 33B since there is no citation to the
footnote in Table 33B.

Footnotes S, T, U

S This criterion is expressed as ng free cyanide (CN)/L.

-------
T This criterion applies to DDT and its metabolites (i.e. the total concentration of DDT and its metabolites

should not exceed this value).

U This criterion applies to total PCBs (e.g. the sum of all congener or all isomer or homolog or
Arochlor analyses).

EPA Action

Footnotes S, T, and U are not applicable to any criteria in Table 33B because there is no citation to
these footnotes anywhere in Table 33B. Additionally, Footnotes S, T, and U to Table 33A set forth
the same information that is described above for these footnotes. Furthermore, Footnotes S, T, U are
cited in Table 33A. Therefore, EPA's decision regarding these footnotes is set forth in Part III.B.5
(EPA's Action on Footnotes in Table 33A).

EPA recommends the State delete these footnotes from Table 33B since there are no citations to
these footnotes in Table 33B.

Footnote V

EPA Action

EPA is disapproving the criteria for freshwater acute selenium, which includes a disapproval of Footnote
V. EPA's action on the freshwater acute selenium criterion in Footnote V is discussed in Part IV.B.4(e)
(Freshwater Acute and Chronic Selenium Criteria).

Footnote W

EPA Action

EPA is disapproving the criteria for freshwater aluminum, which includes a disapproval of Footnote W.
EPA's action on the freshwater aluminum criteria in Footnote W is discussed in Part IV.B.4(a)
(Freshwater Aluminum Acute and Chronic Aquatic Life Criteria).

Footnote X

X The effective date for the criterion in the column immediately to the left is 1991.

EPA Action

This footnote is not applicable to any criteria in Table 33B because there is no citation to this
footnote anywhere in Table 33B. Additionally, Footnote X to Table 33A sets forth the same
information that is described above, and Footnote X is cited in Table 33A. Therefore, EPA's decision
regarding this footnote is set forth in Part III.B.5 (EPA's Action on Footnotes in Table 33A), Footnote X.

EPA recommends Oregon delete this footnote from Table 33B since there is no citation to the footnote in
Table 33B.

-------
Footnote Y

Y No criterion.

EPA Action

This footnote is not applicable to any criteria in Table 33B because there is no citation to this
footnote anywhere in Table 33B. Because this footnote does not apply to any criteria in Table 33B,
it does not establish a legally binding requirement under State law nor does it describe a desired ambient
condition of a water body to support a particular designated use. Therefore the footnote is not considered
a water quality standard subject to EPA review and approval under 303(c) of the CWA, and EPA is
taking no action to approve or disapprove the new footnote.

EPA recommends Oregon delete this footnote from Table 33B since there is no citation to the footnote in
Table 33B.

6. Non-substantive Formatting Changes in Table 33B

Oregon adopted new human health criteria in 2011 and created a new Table 40 which contains all the
human health criteria. Therefore, Oregon removed all references to human health criteria in the
introductory paragraph to Table 33B, and removed Footnotes B, G, H, J, K, and L which all referred to
the human health criteria.16 Additionally, Oregon inadvertently removed footnote Q, which was
applicable to the aquatic life arsenic criteria that were inadvertently removed in the 2007 water quality
standards revision (see Part IV.B.2 for a more detailed explanation).

EPA Action

EPA acknowledges the editorial changes made to the introductory paragraph of Table 33B, and the
removal of the footnotes. EPA approves these changes as non-substantive formatting changes.

EPA has recommended that Oregon adopt the aquatic life arsenic criteria that were inadvertently deleted
in 2007. EPA also recommends that Oregon adopt the associated Footnote Q that affects how arsenic is
applied.

16 Oregon's 2004 water quality standards contained all footnotes applicable to Tables 33 A and 33B at the end of Table 33B.
Additionally, the introductory language to Table 33B contained references to human health criteria even though the table did
not contain any human health criteria.

-------
V. EPA'S ACTION ON REVISIONS TO TABLE 20

A. Introductory Language to Table 20

As stated previously, when Oregon submitted its 2004 revisions to the Oregon water quality standards it
envisioned that once the EPA approved the new Tables 33A and 33B, Table 20 would become obsolete
because Tables 33A and 33B would contain either the same, revised, or new criteria for all of the
parameters in Table 20. However, if EPA did not approve a new or revised criterion then the criterion in
Table 20 remain in effect.

As part of the 2004 adoption, Oregon revised the introductory language to Table 20. Further revisions
were made to the introductory language as part of its 2011 adoption by removing references to human
health criteria that were contained in the introductory language. All of the revisions to the introductory
language are provided below. Strikeout text indicates language that has been removed and underlined
language indicates language that is new.

The concentration for each compound listed in this chart is a criteria or guidance value* not to bo
exceeded in waters of the state for the protection of aquatic life and human health. Specific
descriptions of each compound and an explanation of values arc included in Quality Criteria for
Water (1986). Selecting values for regulatory purposes will depend on the most sensitive
beneficial use to bo protected, and what level of protection is necessary for aquatic life and
human health. The concentration for each compound listed in Table 20 is a criterion not to be
exceeded in waters of the state in order to protect aquatic life and human health. All values are
expressed as micrograms per liter (ug/L) except where noted. Compounds are listed in
alphabetical order with the corresponding designations as to whether EPA has identified it as a
priority pollutant and a carcinogen, aquatic life freshwater acute and chronic criteria, aquatic life
marine acute and chronic criteria, human health water & organism and fish consumption only
eriteria. and Drinking Water Maximum Contaminant Level (MCL). The acute criteria refer to
the average concentration for one (1) hour and the chronic criteria refer to the average
concentration for 96 hours (4 days), and that these criteria should not be exceeded more than
once every three (3) years.

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131, EPA is
disapproving the revisions to the introductory language to Table 20.

EPA Rationale

The new introductory language specifically identifies the duration and frequency of all acute criteria as
the average concentration for one hour that should not be exceeded more than once every three years,
and identifies the duration and frequency of chronic criteria as the average concentration for 4 days that
should not be exceeded more than once every three years. Prior to the 2004 water quality standard
revision, the introductory language to Table 20 stated: "... Specific descriptions of each compound and
an explanation of values are included in Quality Criteria for Water (1986)..." The Quality Criteria for
Water (1986) provided the frequency and duration periods for each of the chemicals in Table 20.

As discussed in Part III.B.3(Disapproval Action for Revised Aquatic Life Criteria in Table 33 A) of this
document, EPA is disapproving the revised criteria for Aldrin (freshwater acute criterion and saltwater
acute criteria), Lindane (freshwater chronic criterion, saltwater acute criterion), Chlordane (freshwater
acute and chronic criteria, and saltwater acute and chronic criteria), DDT 4,4 (freshwater acute and

-------
chronic criteria, and saltwater acute and chronic criteria), Dieldrin (saltwater acute and chronic criteria),
Endrin (saltwater acute and chronic criteria), Heptachlor (freshwater acute and chronic criteria and
saltwater acute and chronic criteria), and Endosulfan (freshwater acute and chronic criteria and saltwater
acute and chronic criteria). EPA is disapproving these specific criteria because the frequency and
duration periods were changed when these criteria were moved from Table 20 to Table 33A.

Specifically, the acute criteria were revised from a maximum value not to be exceeded to a one-hour
average not to be exceeded more than once every three years; and the chronic criteria were revised from
a 24-hour average to a four-day average not be exceeded more than once every three years. When EPA
disapproves a revised criterion the previously adopted numeric criteria for aquatic life protection are
effective for CWA purposes. In order to ensure that the previously adopted numeric criteria for these
specific criteria are effective, EPA is disapproving the new introductory language to Table 20 to ensure
that the frequency and duration period for the above referenced chemicals is retained (i.e., acute criterion
are expressed as a maximum value not be exceeded and the chronic criterion is expressed as a 24-hour
average).

Remedies of Address EPA's Disapproval

This disapproval may be addressed in the same manner as the remedies laid out in Part III.B.3
(Disapproval Action for Changes to Aquatic Life Criteria Moved From Table 20 to Table 33A)

Water Quality Standards Currently in Effect in Oregon

Until EPA approves or promulgates revisions to Oregon's introductory language to Table 20, the
previously approved language is in effect for CWA purposes. The applicable language is as follows:

The concentration for each compound listed in this chart is a criteria or guidance value* not to be
exceeded in waters of the state for the protection of aquatic life and human health. Specific
descriptions of each compound and an explanation of values are included in Quality Criteria for
Water (1986). Selecting values for regulatory purposes will depend on the most sensitive
beneficial use to be protected, and what level of protection is necessary for aquatic life and
human health.

Additionally, as stated in Oregon's water quality standards at OAR 340-041-0033(3)(a):

Each value in Table 33 A is effective on February 15, 2005, unless EPA has disapproved the
value before that date. If a value is subsequently disapproved, any corresponding value in Table
20 becomes effective immediately...

Since EPA disapproved the criteria for some parameters in Table 33A, the previously approved criteria
for these parameters in Table 20 are effective. The criteria in effect in Table 20 are listed below (see
also Part III.B.3 for freshwater and saltwater aquatic life criteria currently in effect in Oregon).

Aldrin:	(freshwater acute criterion and saltwater acute criteria)

Lindane:	(freshwater chronic criterion, saltwater acute criterion)

Chlordane:	(freshwater acute and chronic criteria, and saltwater acute and chronic criteria)

DDT 4,4:	(freshwater acute and chronic criteria, and saltwater acute and chronic criteria)

Dieldrin:	(saltwater acute and chronic criteria)

Endrin:	(saltwater acute and chronic criteria)

Heptachlor:	(freshwater acute and chronic criteria and saltwater acute and chronic criteria)

Endosulfan:	(freshwater acute and chronic criteria and saltwater acute and chronic criteria)

60

-------
B. EPA's Action on the Addition of Freshwater Hardness-based Equations for Table
20

In the June 15, 2011 EQC water quality standards adoption, the acute and chronic hardness-based
equations were added below Table 20. The underlined language indicates language that is new:

The freshwater criterion for this metal is expressed as a function of hardness (mg/L) in the water
column. Criteria values for hardness may be calculated from the following formulas (CMC
refers to Acute Criteria; CCC refers to Chronic Criteria):

CMC = (exp(mA^*rin(hardness)l + b_\J) * CF

CCC = (expfmr *rin(hardness)l + br V) * CF

Chemical

iha

—A

m£

lie

Cadmium

1.128

-3.828

0.7852

-3.49

Chromium III

0.819

3.688

0.819

1.561

CoDDer

0.9422

-1.464

0.8545

-1.465

Lead

1.273

-1.46

1.273

-4.705

Nickel

0.846

3.312

0.846

1.1645

Silver

1.72

-6.52

Zinc

0.8473

0.8604

0.8473

0.7614

EPA Action

In accordance with its Clean Water Act authority, 33 U.S.C § 1313(c)(3) and 40 CFR § 131, EPA
disapproves all of the new language identified above.

EPA Rationale

Prior to 2004, the introductory language to Table 20 referred the reader to EPA's Quality Criteria for
Water 1986 (EPA 440/5-86-001, hereafter referred to as the Gold Book) for a "descriptions of each
compound." The Gold Book contained the equations for each of the pollutants referenced above and
each criterion was expressed as the total recoverable metals concentration. None of the equations in the
Gold Book contained a conversion factor (CF), which is used to convert total recoverable metals criteria

to dissolved metals concentrations.

The State's 2011 revisions to the water quality standards inserted the equations found in the Gold Book
but added a CF to both the acute and chronic criteria equations. The value of each CF was not identified
in the revision. By adding the undefined CF, the State has revised the acute and chronic criterion
equations that were in Table 20.

1. Freshwater Acute Cadmium Criterion and Freshwater Acute and Chronic Copper Criteria: In

addition to the Table 20 revisions described above, the State adopted new criteria for acute cadmium and
acute and chronic copper criteria in Table 33B. The criteria adopted in Table 33B are more stringent
than the revised criteria in Table 20. EPA disapproved the revised acute cadmium criterion and the

17 The Gold Book contained EPA's 304(a) recommendations from 1986. EPA has since revised its 304(a) recommended
criteria several times to account for new information.

-------
acute and chronic copper criterion contained in Table 33B because they were not protective of

designated uses. EPA is relying on the same rationale for disapproving the less stringent revised acute
cadmium and acute and chronic copper criteria in Table 20. For a detailed description of EPA's
rationale see Part IV.B.4(c) and Part IV.B.4(d).

2. Freshwater Criteria for:

Cadmium:

Chromium III:

Lead:

Nickel:

Silver:

Zinc:

chronic only
acute and chronic
acute and chronic
acute and chronic
acute

acute and chronic

The State has revised the above referenced criteria in Table 20 by applying a CF to the equations for the
acute and chronic criteria, as described above. The State also adopted new criteria for the above
referenced criteria in Table 33B. The criteria adopted in Table 33B are more stringent than the revised
criteria in Table 20. EPA approved the revisions to the criteria in Table 33B (see Part VI.B.3(a) above).
As stated in OAR 3 40-041-003 3 (3 )(a):

Each value in Table 20 is effective until the corresponding value in Tables 33A or 33B becomes
effective... (B).... Each value in Table 33B is effective upon EPA approval.

EPA has approved the revised criteria in Table 33B for the above referenced criteria, therefore, the
revised criteria in Table 20 are no longer effective under State law. Nonetheless, EPA is disapproving
the revision of the added language to Table 20 (described above) because the State has not provided any
information on the value of the CF it is applying to each criterion , nor has it provided any information
to show that the revised criteria are protective of the state's aquatic life designated use.

Remedies to Address EPA's Disapproval

The specific remedies for freshwater acute cadmium are discussed in the remedy section of Part
IV.B.4(c). The specific remedies for acute and chronic copper are discussed in the remedy section of
Part IV.B.4(d).

No specific remedies are necessary for the remainder of the criteria because the effective criteria for the
criteria listed below are contained in Table 33B:

Cadmium:

Chromium III:

Lead:

Nickel:

Silver:

Zinc:

chronic only
acute and chronic
acute and chronic
acute and chronic
acute

acute and chronic

18 Though the State adopted values from EPA's 1986 CWA § 304(a) recommendations, as noted in the prior footnote, those
values have been revised several times since then because of new information that demonstrates that the 1986 recommended
values that Oregon adopted are not in fact protective.

-------
Freshwater Aquatic Life Criteria Currently in Effect in Oregon

Cadmium:	Acute: exp(1.128[ln(hardness)]-3.8280) (as total recoverable)

Copper:	Acute: exp(0.9422[ln(hardness)]-1.464) (as total recoverable)

Chronic: exp(0.8545[ln(hardness)]-1.465) (as total recoverable)

For the following parameters see Table 33B for the currently effective criteria in Oregon:

Cadmium:	chronic only

Chromium III:	acute and chronic

Lead:	acute and chronic

Nickel:	acute and chronic

Silver:	acute

Zinc:	acute and chronic

C. EPA's Action on Non-substantive Editorial or Formatting Changes in Table 20

The following non-substantive formatting changes were made to Table 20:

•	Removed column which identified a pollutant as either a carcinogen or non -carcinogen.

•	Removed the term "M.C.L. = Maximum Contaminant Level".

•	Removed the term: "** = human health criteria for carcinogens reported for three risk levels.
Value presented is the 10"6 risk level, which means the probability of one concern case per
million people at the stated concentration."

•	Removed the term: "f= fibers"

•	Removed the terms: |ig = micrograms; ng = nanograms; pg = pictograms, Y = Yes; N = No

•	Removed the term: "Water and Fish Ingestion: Values represent the maximum ambient water-
concentration for consumption of both contaminated water and fish or other aquatic organisms"

•	Removed the term: " Fish Ingestion: Values represent the maximum ambient water
concentration for consumption of fish or other aquatic organisms"

•	Removed the table which identified the Basins located within Oregon, and added Footnote 1
which states that "Values in Table 20 are applicable to all basins."

EPA Action

EPA acknowledges the above referenced editorial changes made to Table 20 and approves these changes
as non-substantive editorial changes.

The State has added the words "Aquatic Life" prior to the phrase "Water Quality Criteria Summary."
The heading to the table now reads "Aquatic Life Water Quality Summary.

The table that identified the basins within Oregon was removed, however, Footnote 1 was added and
states that all criteria in Table 20 are applicable to all basins, therefore, this is an editorial change only.

All other changes were associated with the human health criteria that were part of Table 20 prior to the
2011 water quality standards revision. In the 2011 water quality standards revision, all human health
criteria and the references associated with them were moved from Table 20 to a separate Table. Since

63

-------
human health criteria are no longer a part of Table20, it is reasonable to remove all references to human
health criteria.

D. Guidance Values Moved from Table 20 to Table 33C

In its 2004 water quality standards revisions, the State moved all of the aquatic life guidance values in
Table 2019 to a new Table 33C. EPA's review of this action is contained in EPA's Technical Support
Document for Action on the State of Oregon's New and Revised Human Health Water Quality Criteria
for Toxics and Revisions to Narrative Toxics Provisions Submitted on July 8, 2004 (June 1, 2010, pages
38 - 39). As stated in the June 2010 TSD ".. .the guidance values in Table 33C are not considered WQS
under the CWA. Instead, the guidance values are one of several sources that can be used to interpret the
narrative criterion at OAR 340-041-0033(1).20 The guidance values in Table 33C are not adopted as
criteria and, if used, the state would need to document why the number is appropriate for an individual
action... " Therefore, EPA is not making a determination on the adequacy of the values in Table 33C to
protect aquatic life.

19	In the table, the State distinguished these values from criteria using an asterisk that indicated "[i]nsufficient data to develop
criteria)."

20	OAR 340-041-0033(1) was re-numbered in the 2011 water quality standards revision and it is now identified as OAR 340-
041-0033(2).

64

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ENCLOSURE 1

Aquatic Life Criteria Submitted
by Oregon in July 2004 As Amended

by the April 2007 and July 2011
Water Quality Standards Submissions

-------
TABLE 20

AQUATIC LIFE WATER QUALITY CRITERIA SUMMARY1
(Applicable to all Basins)4

The concentration for each compound listed in this chart is a criteria or guidance value* not to be exceeded in waters of the state for
tho protection of aquatic life and human health. Specific descriptions of each compound and an explanation of values aro included in
Quality Criteria for Water (1986). Selecting values for regulatory purposes will depend on the most sensitive beneficial use to bo
protected, and what level of protection is necessary for aquatic life and human health. The concentration for each compound listed in
Table 20 is a criterion not to be exceeded in waters of the state in order to protect aquatic life and human health. All values are
expressed as micrograms per liter (^g/L) except where noted. Compounds are listed in alphabetical order with the corresponding
designations as to whether EPA has identified it as a priority pollutant and a carcinogen, aquatic life freshwater acute and chronic
criteria, aquatic life marine acute and chronic criteria, human health water & organism and fish consumption only criteria, and
Drinking Water Maximum Contaminant Level (MCL). The acute criteria refer to the average concentration for one (1) hour and the
chronic criteria refer to the average concentration for 96 hours (4 days), and that these criteria should not be exceeded more than once
every three (3) years.

Compound Name (or Class)

Priority
Pollutant

Carcinogen

Concentration in Micrograms Per Liter
for Protection of Aquatic Life





Fresh Acute
Criteria

Fresh Chronic
Criteria

Marine Acute
Criteria

Marine Chronic
Criteria

ACENAPTHENE

Y

N

*1,700







ACROLEIN

Y

N



m-





ACRYLONITRILE

Y

¥

*7,550

*2,600





ALDRIN

Y

¥

3



1.3



ALKALINITY

N

N



20,000





1

-------
Compound Name (or Class)

Priority
Pollutant

Carcinogen

Concentration in Micrograms Per Liter
for Protection of Aquatic Life





Fresh Acute
Criteria

Fresh Chronic
Criteria

Marine Acute
Criteria

Marine Chronic
Criteria

AMMONIA

N

N

CRITERIA ARE pH AND TEMPERATURE DEPENDENT—SEE DOCUMENT USEPA JANUARY 1985 (Fresh Water)
CRITERIA ARE pH AND TEMPERATURE DEPENDENT—SEE DOCUMENT USEPA APRIL 1989 (Marine Water)

ANTIMONY

Y

N

*9,000

*1,600





ARSENIC

Y

¥









ARSENIC (PENT)

Y

¥

±850

±4S

*2,319

±43

ARSENIC (TRI)

Y

¥

360

190

69

36

ASBESTOS

Y

¥









BARIUM

N

N









BENZENE

Y

¥

*5,300



*5,100

±700

BENZIDINE

Y

¥

*2,500







BERYLLIUM

Y

¥



±Sr3





BHC

Y

N

±400



±0r34



CADMIUM

Y

N

3.9+

1.1+

43

9.3

CARBON TETRACHLORIDE

Y

¥

*35,200



*50,000



CHLORDANE

Y

¥

2.4

0.0043

0.09

0.004

CHLORIDE

N

N

860 mg/L

230 mg/L





CHLORINATED BENZENES

Y

¥

±250

±50

±460



CHLORINATED
NAPHTHALENES

Y

N

*1,600



±7tS



CHLORINE

N

N

19

11

13

7.5

CHLOROALKYLETHERS

Y

N

*238,000







CHLOROETHYL ETHER (BIS-2)

Y

¥























CHLOROFORM

Y

¥

*28,900

*1,210





CHLOROISOPROPYL ETHER
(BIS-2)

Y

N









CHLOROMETHYL ETHER (BIS)

N

¥









CHLOROPHENOL 2

Y

N

*1,380

*2,000





CHLOROPHENOL 4

N

N





*29,700



2

-------
Compound Name (or Class)

Priority
Pollutant

Carcinogen

Concentration in Micrograms Per Liter
for Protection of Aquatic Life





Fresh Acute
Criteria

Fresh Chronic
Criteria

Marine Acute
Criteria

Marine Chronic
Criteria

CHLOROPHENOXY
HERBICIDES (2,4,5,-TP)

N

N









CHLOROPHENOXY
HERBICIDES (2,4-D)

N

N























CHLORP YRIF 0 S

N

N

0.083

0.041

0.011

0.0056

CHLORO-4 METHYL-3
PHENOL

N

N









CHROMIUM (HEX)

Y

N

16

11

1,100

50

CHROMIUM (TRI)

N

N

1,700.+

210.+

*10,300



COPPER

Y

N

18.+

12.+

2.9

2.9

CYANIDE

Y

N

22

5.2

1

1

DDT

Y

¥

1.1

0.001

0.13

0.001

(TDE) DDT METABOLITE

Y

¥

mm







(DDE) DDT METABOLITE

Y

¥

*1,050



±44-



DEMETON

Y

N



0.1



0.1















DIBUTYLPHTHALATE

Y

N









DICHLOROBENZENES

Y

N

*1,120



*1,970



DICHLOROBENZIDINE

Y

¥









DICHLOROETHANE 1,2

Y

¥

*118,000

*20,000

*113,000



DICHLOROETHYLENES

Y

¥

* 11,600



*221000



DICHLOROPHENOL 2,4

N

N

*2,020







DICHLOROPROPANE

Y

N

*23,000

*5,700

*10,300

*3,010

DICHLOROPROPENE

Y

N

*6,060

*211

&m



DIELDRIN

Y

¥

2.5

0.0019

0.71

0.0019

DIETHYLPHTHALATE

Y

N









DIMETHYL PHENOL 2,4

Y

N

*2,120







DIMETHYL PHTHALATE

Y

N









3

-------
Compound Name (or Class)

Priority
Pollutant

Carcinogen

Concentration in Micrograms Per Liter
for Protection of Aquatic Life





Fresh Acute
Criteria

Fresh Chronic
Criteria

Marine Acute
Criteria

Marine Chronic
Criteria

DINITROTOLUENE 2,4

N

¥









DINITROTOLUENE

Y

N









DINITROTOLUENE

N

¥



*330

*§90

*370

DINITRO-O-CRESOL 2,4

Y

N









DIOXIN (2,3,7,8-TCDD)

Y

¥

*0r04

*38pg/L





DIPHENYLHYDRAZINE

Y

N









DIPHENYLHYDRAZINE 1,2

Y

N

*370







DI-2-ETHYLHEXYL
PHTHALATE

Y

N









ENDOSULFAN

Y

N

0.22

0.056

0.034

0.0087

ENDRIN

Y

N

0.18

0.0023

0.037

0.0023

ETHYLBENZENE

Y

N

*32,000



*430



FLUORANTHENE

Y

N

*3,980



*40

*46

GUTHION

N

N



0.01



0.01

HALOETHERS

Y

N



*422





HALOMETHANES

Y

¥

*11,000



*12,000

*6,100

HEPTACHLOR

Y

¥

0.52

0.0038

0.053

0.0036

HEXACHLOROETHANE

N

¥

*980

*§40

*940



HEXACHLOROBENZENE

Y

N









HEXACHLOROBUT ADIENE

Y

¥



*9r3

*32-



HEXACHLOROCYCLOHEXAN
E (LINDANE)

Y

¥

2

0.08

0.16



HEXACHLOROCYCLOHEXAN
E-ALPHA

Y

¥









HEXACHLOROCYCLOHEXAN
E-BETA

Y

¥









HEXACHLOROCYCLOHEXAN
E-GAMA

Y

¥









4

-------
Compound Name (or Class)

Priority
Pollutant

Carcinogen

Concentration in Micrograms Per Liter
for Protection of Aquatic Life





Fresh Acute
Criteria

Fresh Chronic
Criteria

Marine Acute
Criteria

Marine Chronic
Criteria

HEXACHLOROCYCLOHEXAN
E-TECHNICAL

Y

¥









HEXACHLOROCYCLOPENTAD
IENE

Y

N

*1



*1



IRON

N

N



1,000





ISOPHORONE

Y

N

*117,000



*12,900



LEAD

Y

N

82.+

3.2+

140

5.6

MALATHION

N

N



0.1



0.1

MANGANESE

N

N









MERCURY

Y

N

2.4

0.012

2.1

0.025

METHOXYCHLOR

N

N



0.03



0.03

MIREX

N

N



0.001



0.001

MONOCHLOROBENZENE

Y

N









NAPHTHALENE

Y

N

*2,300



*2,350



NICKEL

Y

N

1,400.+

160+

75

8.3

NITRATES

N

N









NITROBENZENE

Y

N

*27,000



*6,680



NITROPHENOLS

Y

N



±450

*1,850



NITROSAMINES

Y

¥

*5,850



*3,300,000



NITROSODIBUTYL AMINE N

Y

¥









NITROSODIETHYLAMINE N

Y

¥









NITROSODIMETHYL AMINE N

Y

¥









NITROSODIPHENYL AMINE N

Y

¥









NITROSOPYRROLIDINE N

Y

¥









PARATHION

N

N

0.065

0.013





PCB's

Y

¥

2

0.014

10

0.03

PENT ACHLORINATED
ETHANES

N

N

*7,210

*1,100





PENTACHLOROBENZENE

N

N









5

-------


^ "S



•



Concentration in Micrograms Per Liter





'C &
.2 s
- s
Ph e

:
t

I



for Protection of Aquatic Life





t

i







0-

s
s

¦
i

Fresh Acute

Fresh Chronic

Marine Acute

Marine Chronic

Compound Name (or Class)



(J

p

Criteria

Criteria

Criteria

Criteria

PENTACHLOROPHENOL

Y

N

***20

***13

13

















PHENOL

Y

N

*10,200

*2,560

*5,800



PHOSPHORUS ELEMENTAL

N

N







0.1

PHTHALATE ESTERS

Y

N

*94©

*3-

*2 911

HA

POLYNUCLEAR AROMATIC















HYDROCARBONS

Y

¥







*300



SELENIUM

Y

N

260

35

410

54

SILVER

Y

N

4.1+

0.12

2.3



SULFIDE HYDROGEN















SULFIDE

N

N





2



2

TETRACHLORINATED















ETHANES

Y

N



*9,320







TETRACHLOROBENZENE















1,2,4,5

Y

N











TETRACHLOROETHANE















1,1,2,2

Y

¥





*2,100

*9,020



TETRACHLOROETHANES

Y

N

*9,320







TETRACHLOROETHYLENE

Y

¥

*5,280

*840

*10,200

*450

TETRACHLOROPHENOL















2,3,5,6

Y

N









*440

THALLIUM

Y

N

*1,100

*40

*2,130



TOLUENE

Y

N

*17,500



*6,300

*5,000

TOXAPHENE

Y

¥

0.73

0.0002

0.21

0.0002

TRICHLORINATED EtHANES

Y

¥

*18,000







TRICHLOROETHANE 1,1,1

Y

N





*31,2000



TRICHLOROETHANE 1,1,2

Y

¥



*9,100





TRICHLOROETHYLENE

Y

¥

*15,000

*21,900

*2,000



TRICHLOROPHENOL 2,4,5

N

N









6

-------
Compound Name (or Class)

Priority
Pollutant

Carcinogen

Concentration in Micrograms Per Liter
for Protection of Aquatic Life

Fresh Acute
Criteria

Fresh Chronic
Criteria

Marine Acute
Criteria

Marine Chronic
Criteria

TRICHLOROPHENOL 2,4,6

VINYL CHLORIDE

ZINC

120+

110+

MEANING OF SYMBOLS:

g = grams M.C.L =—Maximum Contaminant Level-

mg = milligrams + = Hardness Dependent Criteria (100 mg/L used).

The freshwater criterion for this metal is expressed as a function of hardness (mg/L) in the
water column. Criteria values for hardness may be calculated from the following formulae
(CMC refers to Acute Criteria; CCC refers to Chronic Criteria):
CMC = (exp(mA*rin(hardness)l +bA))*CF
CCC = (exp(mc*rin(hardnessYI + br.))*CF

(' 1 ic 1111
-------
ug = micrograms * = Insufficient data to develop criteria; value presented is the L.O.E.L - Lower Observed Effect

Level.

ng = nanograms ** =—Human health criteria for carcinogens reported for three risk levels. Value presented is the

10 6 risk level, which means the probability of one concern case per million people at the
stated concentration.

pg = picograms *** = pH Dependent Criteria (7.8 pH used).

f fibers

Y = Yes
N = No

1 = Values in Table 20 are applicable to all basins, as follows:

Basin

[J||1a
1\U1C

Basin

UiiIa
1VU1C

North Coast

310 011 205(p)

Umatilla

310 011 615(p)

Mid Coast

310 011 215 (p)

Walla Walla

310 011 685(p)

Umpqua

310 011 285(p)

Grande Ronde

310 011 725(p)

South Coast

310 011 325(p)

Powder

310 011 765(p)

Rogue

310 011 365(p)

Malheur River

310 011 805(p)

Willamette

310 011 115 (p)

Owyhee

310 011 815(p)

Sandy

310 011 185(p)

Malheur Lake

310 011 885(p)

Hood

310 011 525(p)

Goose & Summer Lakes

310 011 925(p)

Deschutes

310 011 565(p)

Klamath

310 011 965(p)

John Day

310 011 605(p)

Water and Fish Ingestion

Values represent the maximum ambient water concentration for consumption of both contaminated water and fish or other aquatic organisms.

Fish Ingestion

Values represent the maximum ambient water concentrations for consumption of fish or other aquatic organisms

-------
Table 33A

Note: The environmental Quality Commission adopted the following criteria on May 20, 2004 to become effective February 15, 2005.
However, EPA has not yet acted (as of June 2006) approved the criteria. Thus, Table 33 A criteria may be used in NPDES permits, but
not for the section 303(d) list of impaired waters.1

AQUATIC LIFE WATER QUALITY CRITERIA SUMMARY4

The concentration for each compound listed in Table 33 A is a criterion not to be exceeded in waters of the state in order to protect
aquatic life and human health. All values are expressed as micrograms per liter (u/L) except where noted. Compounds are listed in
alphabetical order with the corresponding EPA number (from National Recommended Water Quality Criteria:2002, EPA 8220R-02-
047), the Chemical Abstract Service (CAS) number, aquatic life freshwater acute and chronic criteria, aquatic life saltwater acute and
chronic criteria, and human health water & organism and organism only criteria, and Drinking Water Maximum Contaminant Level
(MCL). The acute criteria refer to the average concentration for one (1) hour and the chronic criteria refer to the average
concentration for 96 hours (4-davs), and that these criteria should not be exceeded more than once every three (3) years.

EPA No.

Compound

CAS
Number

Freshwater

Saltwater

Acute (CMC)

Effective

Chronic (CCC)

Effective

Acute (CMC)

Effective

Chronic

rcca

Effective

Acenanhthene

83329

Acenaohthvlene

208968

Acrolein

107028

Acrvlonitrile

107131

102

Aldrin

309002

3 O

1.3 O

Alkalinity

20,000_P

2 N

Aluminum (dH 6.5 - 9.0s)

7429905

1 This note was approved by EPA in its February 28, 2011 action.

-------
EPA No.

Compound

CAS
Number

Freshwater

Saltwater

Acute (CMC)

Effective

Chronic (CCC)

Effective

Acute (CMC)

Effective

Chronic

rcca

Effective

3 N

Ammonia

7664417

Anthracene

120127

Antimony

7440360

Arsenic

7440382

Asbestos

1332214

6 N

Barium

7440393

Benzene

71432

Benzidine

92875

Bcnzo(a)Anthraccne

56553

Benzo(a)Pvrcnc

50328

B c nzo(b) F1 uo ra lit lie nc

205992

Benzof a.h.i)Pcrvlcnc

191242

B e nzo(k)F1 uo ra nthe ne

207089

Beryllium

7440417

103

BHC ataha-

319846

104

BHCbeta-

319857

106

BHC delta-

319868

105

BHC aamma- (Lindane)

58899

0.95

0.08

0.16 0

7 N

Boron

7440428

Bromoform

75252

Bromoohenvl Phenyl Ether
4=

-------
EPA No.

Compound

CAS
Number

Freshwater

Saltwater

Acute (CMC)

Effective

Chronic (CCC)

Effective

Acute (CMC)

Effective

Chronic

rcca

Effective

Butvlbenzvl Phthalate

85687

Cadmium

7440439

Carbon Tetrachloride

56235

107

Chlordane

57749

2.4 O

0.0043 O

0.09 O

0.004 O

8 N

Chloride

16887006

860000

230000

9 N

Chlorine

7782505

7.5

Chlorobenzene

108907

Chlorodibromomethane

124481

Chloroethane

75003

ChloroethoxvMethane Bis2-

111911

ChloroethvlEther Bis2-

111444

Chloroethvlvinvl Ether 2-

110758

Chloroform

67663

ChloroisooroBvlEther Bis2-

108601

15 N

ChloromethvlEther. Bis

542881

Chloronaohthalene 2-

91587

Chloroohenol 2-

95578

ION

Chloroohenoxv Herbicide
(2.4.5.-TP)

93721

11 N

Chloroohenoxv Herbicide
(2A-D)

94757

Chloroohenvl Phenyl Ether
4=

7005723

12 N

ChloroDvrifos

2921882

0.083

0.041

0.011

0.0056

-------
o

-------
EPA No.

Compound

CAS
Number

Freshwater

Saltwater

Acute (CMC)

Effective

Chronic (CCC)

Effective

Acute (CMC)

Effective

Chronic

rcca

Effective

DiethvlPhthalate

84662

Dimethvlohenol 2.4-

105679

DimethvlPhthalate

131113

Di-n-Butvl Phthalate

84742

Dinitroohenol 2.4-

51285

27 N

Dinitroohenols

25550587

Dinitrotoluene 2.4-

121142

Dinitrotoluene 2.6-

606202

Di-n-Octvl Phthalate

117840

Dioxin (2.3.7.8-TCDD)

1746016

Diohenvlhvdrazine 1.2-

122667

EthvlhexvlPhthalate Bis2-

117817

Endosulfan

0.22 I.P

0.056 I.P

0.034 I.P

0.0087 I.P

112

Endosulfan aloha-

959988

0.22 O

0.056 O

0.034 O

0.0087 O

113

Endosulfan beta-

33213659

0.22 O

0.056 O

0.034 O

0.0087 O

114

Endosulfan Sulfate

1031078

115

Endrin

72208

0.086

0.037 O

0.0023 O

116

Endrin Aldehvde

7421934

Ethvlbenzene

100414

Fluoranthene

206440

Fluorene

86737

17 N

Guthion

86500

0.01

-------
EPA No.

Compound

CAS
Number

Freshwater

Saltwater

Acute (CMC)

Effective

Chronic (CCC)

Effective

Acute (CMC)

Effective

Chronic

rcca

Effective

117

Hcotachlor

76448

0.52 O

0.0038 O

0.053 O

0.0036 O

118

Hcotachlor Epoxide

1024573

0.52 O

0.0038 O

0.053 O

0.0036 O

Hexachlorobenzene

118741

Hexachlorobutadiene

87683

£1

Hexachloroethane

67721

19 N

Hexachlorocvclo-hexane-
Technical

319868

Hexachlorocvclooentadiene

77474

Ideno 1.2.3 -(cd)Pvrcne

193395

20 N

Iron

7439896

1,000

Isophorone

78591

Lead

7439921

21 N

Malathion

121755

0.1

22 N

Mansanese

7439965

Mercury

7439976

2.4

0.012

2.1

0.025

23 N

Methoxvchlor

72435

0.03

Methvl Bromide

74839

Methvl Chloride

74873

Methvl-4.6-Dinitror)henol
2z

534521

Methvl-4-Chloroohenol 3-

59507

-------
EPA No.

Compound

CAS
Number

Freshwater

Saltwater

Acute (CMC)

Effective

Chronic (CCC)

Effective

Acute (CMC)

Effective

Chronic

rcca

Effective

Methylene Chloride

75092

Methvlmercurv

22967926

24 N

Mirex

2385855

0.001

Naphthalene

91203

Nickel

7440020

25 N

Nitrates

14797558

Nitrobenzene

98953

Nitroohcnol 2-

88755

Nitroohenol 4-

100027

26 N

Nitrosamines

35576911

28 N

Nitrosodibutvlamine.N

924163

29 N

Nitrosodiethvlamine.N

55185

N-Nitrosodimethvlamine

62759

N-Nitrosodiohenvlamine

86306

30 N

NitrosoDvrrolidinc.N

930552

N-Nitro sodi -n-Proovlamine

621647

32 N

Oxvsen. Dissolved

7782447

33 N

Parathion

56382

0.065

0.013

119

Polvchlorinated Biohenvls
PCBs:

1336363

2 U

0.014 U

10 U

0.03 U

34 N

Pentachlorobenzene

608935

Pentachloroohenol

87865

Phenanthrene

85018

Phenol

108952

-------
EPA No.

Compound

CAS
Number

Freshwater

Saltwater

Acute (CMC)

Effective

Chronic (CCC)

Effective

Acute (CMC)

Effective

Chronic

rcca

Effective

36 N

Phosphorus Elemental

7723140

0.1

100

Pvrene

129000

Selenium

7782492

Silver

7440224

40 N

Sulfide-Hvdroeen Sulfide

7783064

43 N

Tetrachlorobenzene. 1.2.4.5

95943

Tetrachloroethane 1.1.2.2-

79345

T etrachloroethvlene

127184

Thallium

7440280

Toluene

108883

120

Toxaphene

8001352

0.73

0.0002

0.21

0.0002

Trans-Die hloroethvlene 1.2-

156605

44 N

Tributvltin (TEST)

688733

101

Trichlorobenzene 1.2.4-

120821

Trichloroethane 1.1.1-

71556

Trichloroethane 1.1.2-

79005

T ric hloroethvlene

79016

45 N

TrichloroDhenol 2.4.5

95954

TrichloroDhcnol 2.4.6-

88062

Vinvl Chloride

75014

Zinc

7440666

-------
Footnotes for Table 33A and 33B

A Values in Table 20 are applicable to all basins.

B Human Health criteria values were calculated using a fish consumption rate of 17.5 grams per day (0.6 ounces/day) unless otherwise noted.
C Ammonia criteria for freshwater may depend on pH. temperature, and the presence of salmonids or other fish with ammonia-sensitive early life stages.
Values for freshwater criteria (of total ammonia nitrogen in mg N/L1 can be calculated using the formulae specified in 1999 Update of Ambient Water
Quality Criteria for Ammonia (EPA-822-R-99-014: http://www.epa.gov/ost/standards/ammonia/99update.pdf):

Freshwater Acute:

salmonids present... .CMC = 0.275 + 39.0

1+ 1()7.204-pH 1+ 1()pH-7.204

salmonids not present... CMC= 0.411 + 58.4

1+ 1()7.204-pH 1+ 10pH-7.204

Freshwater Chronic:
fish early life stages present:

CCC= 0.0577 + 2.487 * MIN (2.85.1.45*100028''(25'T>)

^q7.688-pH j^QpH-7.688

fish early life stages not present:

CCC= 0.577 + 2.487 * 1.45*10ao28''(25'MAX(T-7))

^q7.688-pH j^QpH-7.688

Note: these chronic criteria formulae would be applied to calculate the 30-day average concentration limit; in addition, the highest 4-day average within
the 30-day period should not exceed 2.5 times the CCC.

D Ammonia criteria for saltwater may depend on pH and temperature. Values for saltwater criteria (total ammonia) can be calculated from the tables
specified in Ambient Water Quality Criteria for Ammonia (Saltwater)—1989 (EPA 440/5-88-004:
http://www.epa.gov/ost/pc/ambientwqc/ammoniasaltl989.pdf).

E Freshwater and saltwater criteria for metals are expressed in terms of "dissolved" concentrations in the water column, except where otherwise noted
(e.g. aluminum).

F The freshwater criterion for this metal is expressed as a function of hardness (mg/L) in the water column. Criteria values for hardness may be calculated
from the following formulae (CMC refers to Acute Criteria: CCC refers to Chronic Criteria):

CMC= (exp(nu * 11 n(hardness) I + b_%))*CF

-------
CCC= (c\p(ini:*lln(hardncss)l + bi:))*CF
where CF is the conversion factor used for converting a metal criterion expressed as the total recoverable fraction in the water column to a criterion
expressed as the dissolved fraction in the water column.

( hemie;il

iua

nii_

!>l

Cadmium

l.Ulbb

-3.y24

u.74uy

-4.71y

Chromium III

0.8190

3.7256

0.8190

0.6848

Copper

0.9422

-1.700

0.8545

-1.702

Lead

1.273

-1.460

1.273

-4.705

Nickel

0.8460

2.255

0.8460

0.0584

Silver

1.72

-6.59

Zinc

0.8473

0.884

0.8473

0.884

Conversion factors (CF) for dissolved metals (the values for total recoverable metals criteria were multiplied by the appropriate conversion factors shown
below to calculate the dissolved metals criteria):

( hemie;il

l-'reslm siler

S;ilm;Uer

Aeule

( lirunie

Aeule

( lirunie

Arsenic

1.000

Cadmium

1.136672-r(lnhardness)(0.041838)1

1.101672-Mn hardness)(0.04183 8)1

0.994

Chromium III

0.316

0.860

Chromium VI

0.982

0.962

0.993

Copper

0.960

0.83

Lead

1.46203-f (In hardness)(0.145712)1

0.951

Nickel

0.998

0.997

0.990

Selenium

0.996

0.922

0.998

Silver

0.85

Zinc

0.978

0.986

0.946

G Human Health criterion is the same as originally published in the 1976 EPA Red Book (Quality Criteria for Water. EPA 110/9 76 0231 which predates

the 1980 methodology and did not use a fish ingestion BCF approach.

H This value is based on a Drinking Water regulation.

I This value is based on criterion published in Ambient Water Quality Criteria for Endosulfan (EPA 440/5-80-046) and should be applied as the sum of

-------
alpha and beta endosulfan.

J No BCF was available: therefore, this value is based on that published in the 1986 EPA Gold Beekr

K Human Health criterion is for "dissolved concentration based on the 1976 EPA Red Book conclusion that adverse effects from exposure at this level are
aesthetic rather than toxic-

L This value is expressed as the fish tissue concentration of methvlmercurv.

M Freshwater aquatic life values for pentachlorophenol are expressed as a function of pH. and are calculated as follows: C'1VIC'=(c\d( 1.005(pH )-4.869):
CCC=exp(1.005(pHV5.134V

N This number was assigned to the list of non-prioritv pollutants in National Recommended Water Quality Criteria: 2002 (EPA-822-R-02-047').

O This criterion is based on EPA recommendations issued in 1980 that were derived using guidelines that differed from EPA's 1985 Guidelines for
minimum data requirements and derivation procedures. For example, a "CMC" derived using the 1980 Guidelines was derived to be used as an
instantaneous maximum. If assessment is to be done using an averaging period, the values given should be divided by 2 to obtain a value that is more
comparable to a CMC derived using the 1985 Guidelines.

P Criterion shown is the minimum (i.e. CCC in water should not be below this value in order to protect aquatic life).

O Criterion is applied as total arsenic (i.e. arsenic (IIP + arsenic (V)V

R Arsenic criterion refers to the inorganic form only.

S This criterion is expressed as ug free cyanide (CNVL.

T This criterion applies to DDT and its metabolites (i.e. the total concentration of DDT and its metabolites should not exceed this value).

U This criterion applies to total PCBs (e.g. the sum of all congener or all isomer or homolog or Arochlor analyses').

V The CMC=l/[(fl/CMClH(f2/CMC2')l where fl and f2 are the fractions of total selenium that are treated as selenite and selenate. respectively, and
CMC1 and CMC2 are 185.9 iig/L and 12.82 iig/L. respectively.

W The acute and chronic criteria for aluminum are 750 iig/L and 87 iig/L. respectively. These values for aluminum are expressed in terms of "total
recoverable" concentration of metal in the water column. The criterion applies at pH<6.6 and hardness<12 mg/L (as CaCQO.

X The effective date for the criterion in the column immediately to the left is 1991.

Y No criterion-

2 Footnote Y was added in Oregon's 2011 adoption.

-------
Table 33B

Note: The environmental Quality Commission adopted the following criteria on May 20, 2004 to become effective on EPA approval.

EPA has not yet (as of June 2006) approved the criteria. The Table 33B criteria may not be used until they are approved by EPA .

AQUATIC LIFE WATER QUALITY CRITERIA SUMMARY4

The concentration for each compound listed in Table 33 A is a criterion not to be exceeded in waters of the state in order to protect
aquatic life and human health. All values are expressed as micrograms per liter (u/L) except where noted. Compounds are listed in
alphabetical order with the corresponding EPA number (from National Recommended Water Quality Criteria:2002, EPA 8220R-02-
047), the Chemical Abstract Service (CAS) number, aquatic life freshwater acute and chronic criteria, aquatic life saltwater acute and
chronic criteria, and human health water & organism and organism only criteria, and Drinking Water Maximum Contaminant Level
(MCL). The acute criteria refer to the average concentration for one (1) hour and the chronic criteria refer to the average
concentration for 96 hours (4-davs), and that these criteria should not be exceeded more than once every three (3) years.

EPA No.

Compound

CAS
Number

Freshwater

Saltwater

Acute (CMC)

Effective

Chronic

rcca

Effective
Date

Acute (CMC)

Effective
Date

Chronic

rcca

Effective
Date

2 N

Aluminum (dH 6.5 - 9.0s)

7429905

3 N

Ammonia

7664417

Arsenic

7440382

310 E.O

150 E. O

69 E.O

36 E.O

Asbestos

1332214

3 This note was approved by EPA in its February 28, 2011 action.

-------
EPA No.

Compound

CAS
Number

Freshwater

Saltwater

Acute (CMC)

Effective

Chronic
(CCC)

Effective
Date

Acute (CMC)

Effective
Date

Chronic
(CCC)

Effective
Date

Benzene

71432

Beryllium

7440417

105

BHC eamma- (Lindane)

58899

Cadmium

7440439

E.F

40 E

8.8 E

107

Chlordane

57749

CHLORINATED BENZENES

Chloroform

67663

ChloroisooroDvl Ether Bis2-

108601

15 N

ChloromethvlEther. Bis

542881

Chromium (III)

E.F

Chromium (VI)

1854029
9

16 E

11 E

1100 E

Copper

7440508

E.F

4.8 E

3.1 E

108

DDT 4.4'-

50293

DIBUTYLPHTHALATE

DICHLOROBENZENES

DICHLOROBENZIDINE

-------
EPA No.

Compound

CAS
Number

Freshwater

Saltwater

Acute (CMC)

Effective

Chronic

rcca

Effective
Date

Acute (CMC)

Effective
Date

Chronic

rcca

Effective
Date

DICHLOROETHYLENES

DICHLOROPROPENE

Ill

Dieldrin

60571

0.056

DINITROTOLUENE

DIPHENYLHYDRAZINE

115

Endrin

72208

0.036

Fluoranthene

206440

HALOMETHANES

20 N

Iron

7439896

Lead

7439921

E.F

210 E

8.1 E

22 N

Mansanese

7439965

Mercury

7439976

MONOCHLOROBENZENE

Nickel

7440020

E.F

74 E

8.2 E

Pentachlorophenol

87865

Phenol

108952

-------
EPA No.

Compound

CAS
Number

Freshwater

Saltwater

Acute (CMC)

Effective

Chronic
(CCO

Effective
Date

Acute (CMC)

Effective
Date

Chronic
(CCO

Effective
Date

POLYNUCLEAR AROMATIC
HYRDOCARBONS

Selenium

7782492

E.V

5 E

290 E

71 E

Silver

7440224

E.F.P

0.10 E

1.9 E.P

44 N

Tributvltin (TBT)

688733

0.46

0.063

0.37

0.01

Trichloroethane 1.1.1-

71556

Trichlorophenol 2.4.6-

88062

Zinc

7440666

E.F

90 E

81 E

Footnotes for Table 33A and 33B

A Values in Table 20 are applicable to all basins.

B Human Health criteria values were calculated using a fish consumption rate of 17.5 grams per day (0.6 ounces/day) unless otherwise noted, (was deleted in
20111

C Ammonia criteria for freshwater may depend on pH. temperature, and the presence of salmonids or other fish with ammonia-sensitive early life stages. Values
for freshwater criteria (of total ammonia nitrogen in mg N/L1 can be calculated using the formulae specified in 1999 Update of Ambient Water Quality Criteria
for Ammonia (EPA-822-R-99-014: http://www.epa.gov/ost/standards/ammonia/99update.pdf):

Freshwater Acute:

salmonids present... .CMC = 0.275 + 39.0

1+ 1()7.204-pH 1+ 1()pH-7.204

salmonids not present... CMC= 0.411 + 58.4

1+ 1()7.204-pH 1+ 10pH-7.204

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Freshwater Chronic:

fish early life stages present:
CCC= 0.0577 + 2.487

jq7.688-pH j_|_ j^QpH-7.688

* MIN (2.85.1.45*100 028*(25"t)')

fish early life stages not present:
CCC= 0.577 + 2.487

^Q7.688-pH j_|_ j^QpH-7.688

* 1 45^ioao28W(25_MAX(T,7))

Note: these chronic criteria formulae would be applied to calculate the 30-day average concentration limit: in additioa the highest 4-day average within the 30-
day period should not exceed 2.5 times the CCC.

D Ammonia criteria for saltwater may depend on pH and temperature. Values for saltwater criteria (total ammonia) can be calculated from the tables specified in

Ambient Water Quality Criteria for Ammonia (Saltwater)—1989 (EPA 440/5-88-004: http://www.epa.gov/ost/pc/ambientwac/ammoniasaltl989.pdf).
E Freshwater and saltwater criteria for metals are expressed in terms of "dissolved" concentrations in the water column, except where otherwise noted (e.g.
aluminum).

F The freshwater criterion for this metal is expressed as a function of hardness (ing/L) in the water column. Criteria values for hardness may be calculated from
the following formulae (CMC refers to Acute Criteria: CCC refers to Chronic Criteria):

CMC= (ex p (nu * 11 n (ha rd ne s s) I + b^,))*CF
CCC= (c\d( nv*l ln( hardness) I + br))*CF

where CF is the conversion factor used for converting a metal criterion expressed as the total recoverable fraction in the water column to a criterion expressed
as the dissolved fraction in the water column.

ClK'ink'iil Ik nil h>

Cadmium

1.0166

-3.924

0.7409

-4.719

Chromium III

0.8190

3.7256

0.8190

0.6848

Copper

0.9422

-1.700

0.8545

-1.702

Lead

1.273

-1.460

1.273

-4.705

Nickel

0.8460

2.255

0.8460

0.0584

Silver

1.72

-6.59

Zinc

0.8473

0.884

0.8473

0.884

Conversion factors (CF) for dissolved metals (the values for total recoverable metals criteria were multiplied by the appropriate conversion factors shown
below to calculate the dissolved metals criteria):

ClK'ink'iil

li\'sh\\;ik'i

S;il(\\;ik'i

-------

Acnlc

Chronic

Anile

Chronic

Arsenic

1.000

Cadmium

1.136672-r(lnhardness)(0.041838)1

1.101672-r(lnhardness)(0.041838)1

0.994

Chromium III

0.316

0.860

Chromium VI

0.982

0.962

0.993

Copper

0.960

0.83

Lead

1.46203-IYln hardness)(0.145712)1

1.46203-r(ln hardness)(0.145712)1

0.951

Nickel

0.998

0.997

0.990

Selenium

0.996

0.922

0.998

Silver

0.85

Zinc

0.978

0.986

0.946

G Human Health criterion is the same as originally published in the 1976 EPA Red Book (Quality Criteria for Water. EPA 110/9 76 0231 which predates the
1980 methodology and did not use a fish ingestion BCF approach.

H This value is based on a Drinking Water regulation.

I This value is based on criterion published in Ambient Water Quality Criteria for Endosulfan (EPA 440/5-80-0461 and should be applied as the sum of alpha
and beta endosulfan.

J No BCF was available: therefore, this value is based on that published in the 1986 EPA Gold Beekr

K Human Health criterion is for "dissolved concentration based on the 1976 EPA Red Book conclusion that adverse effects from exposure at this level are
aesthetic rather than toxic-

L This value is expressed as the fish tissue concentration of methvlmercurv.

M Freshwater aquatic life values for pentachlorophenol are expressed as a function of pH. and are calculated as follows: C1VIC=(c\d( 1.005(pH )-4.869):
CCC=exp(1.005(pH)-5.134).

N This number was assigned to the list of non-prioritv pollutants in National Recommended Water Quality Criteria: 2002 (EPA-822-R-02-047).

O This criterion is based on EPA recommendations issued in 1980 that were derived using guidelines that differed from EPA's 1985 Guidelines for minimum
data requirements and derivation procedures. For example, a "CMC" derived using the 1980 Guidelines was derived to be used as an instantaneous maximum.
If assessment is to be done using an averaging period, the values given should be divided by 2 to obtain a value that is more comparable to a CMC derived
using the 1985 Guidelines.

P Criterion shown is the minimum (i.e. CCC in water should not be below this value in order to protect aquatic life").

Q—Criterion is applied as total arsenic (i.e. arsenic (III) + arsenic (V)).

R Arsenic criterion refers to the inorganic form only.

S This criterion is expressed as iig free cyanide (CNVL.

T This criterion applies to DDT and its metabolites (i.e. the total concentration of DDT and its metabolites should not exceed this value).

U This criterion applies to total PCBs (e.g. the sum of all congener or all isomer or homolog or Arochlor analyses').

V The CMC=l/r(fl/CMCl)+(f2/CMC2)l where fl and f2 are the fractions of total selenium that are treated as selenite and selenate. respectively, and CMC1 and
CMC2 are 185.9 iig/L and 12.82 iig/L. respectively.

W The acute and chronic criteria for aluminum are 750 iig/L and 87 iig/L. respectively. These values for aluminum are expressed in terms of "total recoverable"
concentration of metal in the water column. The criterion applies at pH<6.6 and hardness<12 mg/L (as CaCQ j.

-------
X The effective date for the criterion in the column immediately to the left is 1991.
Y. No criterion.

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ENCLOSURE2

Supplemental
Technical Support Document

for

EPA Clean Water Act
303(c) Determinations

On Oregon's New and Revised Aquatic Life

Criteria Submitted on
July 8, 2004, and as Amended by Oregon's
April 23, 2007 and July 21, 2011 Submissions

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TABLE OF CONTENTS

1.0 METHODOLOGY FOR CRITERIA EVALUATION 10

1.1 SOURCES OF TOXICITY TEST DATA USED IN EPA DETERMINATIONS 10

1.2 Evaluation of the protectiveness of Oregon's acute criterion concentration 12

1.3 Evaluation of the protectiveness of Oregon's chronic criterion concentration 15

1.4 Final determination method 17

2.0 CRITERIA EVALUATION 19

2.1 Freshwater 19

2.1.1 Ammonia 19

2.1.2 Cadmium 20

2.1.2.1 Evaluation of the Acute Freshwater Criterion Concentration for Cadmium 20

2.1.2.2 Evaluation of the Chronic Freshwater Criterion Concentration for Cadmium 20

2.1.2.3 References for Cadmium 25

2.1.3 Chromium III 30

2.1.3.1 Evaluation of the Acute Freshwater Criterion Concentration for Chromium III. 30

2.1.3.2 Evaluation of the Chronic Freshwater Criterion Concentration for Chromium III..... 31

2.1.3.3 References for Chromium III 34

Chromium VI 36

2.1.3.4 Evaluation of the Acute Freshwater Criterion Concentration for Chromium VI 36

2.1.3.5 Evaluation of the Chronic Freshwater Criterion Concentration for Chromium VI 38

2.1.3.6 References for Chromium VI 42

2.1.4 Copper 45

2.1.5 Dieldrin 46

2.1.5.1 Evaluation of the Acute Freshwater Criterion Concentration for Dieldrin 46

2.1.5.2 Evaluation of the Chronic Freshwater Criterion Concentration for Dieldrin 47

2.1.5.3 References for Dieldrin 48

2.1.7 Endrin 51

2.1.7.1 Evaluation of the Acute Freshwater Criterion Concentration for Endrin 51

2.1.7.2 Evaluation of the Chronic Freshwater Criterion Concentration for Endrin 53

2.1.7.3 References for Endrin 55

2.1.8 Lead 58

2.1.8.1 Evaluation of the Acute Freshwater Criterion Concentration for Lead. 58

2.1.8.2 Evaluation of the Chronic Freshwater Criterion Concentration for Lead. 59

2.1.8.3 References for Lead 60

2.1.9 Lindane (gamma-BHC) 63

2.1.9.1 Evaluation of the Acute Freshwater Criterion Concentration for Lindane 63

2.1.9.2 References for Lindane 64

2.1.10 Nickel 67

2.1.10.1 Evaluation of the Acute Freshwater Criterion Concentration for Nickel. 67

2.1.10.2 Evaluation of the Chronic Freshwater Criterion Concentration for Nickel. 69

2.1.10.3 References for Nickel 72

2.1.11 Pentachlorophenol 75

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2.1.11.1 Evaluation of the Acute Freshwater Criterion Concentration for Pentachlorophenol

2.1.11.2 Evaluation of the Chronic Freshwater Criterion Concentration for
Pentachlorophenol 77

2.1.11.3 References for Pentachlorophenol 81

2.1.12 SELENIUM (Selenate and SELENITE) 85

2.1.13 Silver 86

2.1.13.1 Evaluation of the Acute Freshwater Criterion Concentration for Silver 86

2.1.13.2 Evaluation of the Chronic Freshwater Criterion Concentration for Silver 89

2.1.13.3 References for Silver 91

2.1.14 T ributyltin 94

2.1.14.1 Evaluation of the Acute Freshwater Criterion Concentration for Tributyltin 94

2.1.14.2 Evaluation of the Chronic Freshwater Criterion Concentration for Tributyltin 95

2.1.14.3 References for Tributyltin 96

2.1.15 Zinc 98

2.1.15.1 Evaluation of the Acute Freshwater Criterion Concentration for Zinc 98

2.1.15.2 Evaluation of the Chronic Freshwater Criterion Concentration for Zinc 101

2.1.15.3 References for Zinc 105

2.2 Saltwater 110

2.2.1 Cadmium 110

2.2.1.1 Evaluation of the Acute Saltwater Criterion Concentration for Cadmium 110

2.2.1.2 Evaluation of the Chronic Saltwater Criterion Concentration for Cadmium 113

2.2.1.3 References for Cadmium 117

2.2.2 Copper 122

2.2.2.1 Evaluation of the Acute Saltwater Criterion Concentration for Copper 122

2.2.2.2 Evaluation of the Chronic Saltwater Criterion Concentration for Copper 125

2.2.2.3 References for Copper 129

2.2.3 Lead 134

2.2.3.1 Evaluation of the Acute Saltwater Criterion Concentration for Lead 134

2.2.3.2 Evaluation of the Chronic Saltwater Criterion Concentration for Lead 135

2.2.3.3 References for Lead 137

2.2.4 Nickel 139

2.2.4.1 Evaluation of the Acute Saltwater Criterion Concentration for Nickel 139

2.2.4.2 Evaluation of the Chronic Saltwater Criterion Concentration for Nickel 141

2.2.4.3 References for Nickel 143

2.2.5 Pentachlorophenol 145

2.2.5.1 Presentation of Acute Saltwater Data in Support of Chronic Pentachlorophenol 145

2.2.5.2 Evaluation of the Chronic Saltwater Criterion Concentration for Pentachlorophenol
146

2.2.5.3 References for Pentachlorophenol 148

2.2.6.1 Evaluation of the Acute Saltwater Criterion Concentration for Selenium 150

2.2.6.2. Evaluation of the Chronic Saltwater Criterion Concentration for Selenium 151

2.2.6.3 References for Selenium 153

2.2.7.1 Evaluation of the Acute Saltwater Criterion Concentration for Silver 155

-------
2.2.7.2 References for Silver 156

2.2.8 Tributyltin 158

2.2.8.1 Evaluation of the Acute Saltwater Criterion Concentration for Tributyltin 158

2.2.8.2 Evaluation of the Chronic Saltwater Criterion Concentration for Tributyltin 159

2.2.8.3 References for Tributyltin 161

2.2.9 Zinc 164

2.2.9.1 Evaluation of the Acute Saltwater Criterion Concentration for Zinc 164

2.2.9.2 Evaluation of the Chronic Saltwater Criterion Concentration for Zinc 167

2.2.9.3 References for Zinc 171

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TABLE OF TABLES

Table 2.1.2-1: Genus Mean Chronic Values (GMCVs) for Cadmium 21

Table 2.1.3-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Chromium III 30

Table 2.1.3-2: Genus Mean Chronic Values (GMCVs) for Chromium III 32

Tables 2.1.4-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Chromium VI 36

Table 2.1.4-2: Genus Mean Chronic Values (GMCVs) for Chromium VI 39

Table 2.1.6-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Dieldrin 46

Table 2.1.6-2: Genus Mean Chronic Values (GMCVs) for Dieldrin 48

Table 2.1.7-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Endrin 51

Table 2.1.7-2: Genus Mean Chronic Values (GMCVs) for Endrin 53

Table 2.1.8-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Lead 58

Table 2.1.8-2: Genus Mean Chronic Values (GMCVs) for Lead 59

Table 2.1.9-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Lindane 63

Table 2.1.10-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Nickel 67

Table 2.1.10-2: Genus Mean Chronic Values (GMCVs) for Nickel 70

Table 2.1.11-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Pentachlorophenol 75

Table 2.1.11-2: Genus Mean Chronic Values (GMCVs) for Pentachlorophenol 78

Table 2.1.13-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Silver 86

Table 2.1.13-2: Genus Mean Chronic Values (GMCVs) for Silver 90

Table 2.1.14-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Tributyltin 94

Table 2.1.14-2: Species Mean Chronic Values (SMCVs) for Tributyltin 95

Table 2.1.15-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Zinc 98

Table 2.1.15-2: Genus Mean Chronic Values (GMCVs) for Zinc 102

Table 2.2.1-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Cadmium 110

Table 2.2.1-2: Species Mean Chronic Values (SMCVs) for Cadmium 114

Table 2.2.2-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Copper 122

Table 2.2.2-2: Genus Mean Chronic Values (GMCVs) for Copper 126

Table 2.2.3-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Lead 134

Table 2.2.3-2: Genus Mean Chronic Values (SMCVs) for Lead 136

-------
Table 2.2.4-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Nickel 139

Table 2.2.4-2: Genus Mean Chronic Values (GMCVs) for Nickel 141

Table 2.2.5-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Pentachlorophenol 145

Table 2.2.5-2: Genus Mean Chronic Values (SMCVs) for Pentachlorophenol 147

Table 2.2.7-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Silver 155

Table 2.2.7-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Tributyltin 158

Table 2.2.7-2: Genus Mean Chronic Values (GMCVs) for Tributyltin 160

Table 2.2.8-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values (GMAVs)

for Zinc 164

Table 2.2.8-2: Genus Mean Chronic Values (GMCVs) for Zinc 168

-------
LIST OF APPENDICES

APPENDIX A: QA/QC PROCEDURES 174

APPENDIX B: PROCEDURES USED IN EPA'S BIOLOGICAL EVALUATION AND COMPARISON TO THIS ANALYSIS
REGARDING DATA ACCEPTABILITY 180

APPENDIX C CADMIUM (FRESHWATER) 208

APPENDIX D CHROMIUM III (FRESHWATER) 311

APPENDIX E CHROMIUM VI (FRESHWATER) 324

APPENDIX F DIELDRIN (FRESHWATER) 333

APPENDIX G ENDRIN (FRESHWATER) 346

APPENDIX H LEAD (FRESHWATER) 356

APPENDIX I LINDANE (FRESHWATER) 408

APPENDIX J NICKEL (FRESHWATER) 429

APPENDIX K PENTACHLOROPHENOL (FRESHWATER) 446

APPENDIX L SILVER (FRESHWATER) 474

APPENDIX M TRIBUTYLTIN (FRESHWATER) 487

APPENDIX N ZINC (FRESHWATER) 495

APPENDIX O CADMIUM (SALTWATER) 553

APPENDIX P COPPER (SALTWATER) 609

APPENDIX Q LEAD (SALTWATER) 653

APPENDIX R NICKEL (SALTWATER) 663

APPENDIX S PENTACHLOROPHENOL (SALTWATER) 666

APPENDIX T SILVER (SALTWATER) 678

APPENDIX U TRIBUTYLTIN (SALTWATER) 684

APPENDIX V ZINC (SALTWATER) 699

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Supplemental Technical Support Document for
EPA CWA 303(c) Determinations on
Oregon's Aquatic Life Criteria

This document provides additional scientific and technical information supporting EPA's
decision on those proposed criteria that are consistent with EPA's CWA § 304(a) recommended
criteria and that EPA is approving.

Consistent with EPA guidance on the development of aquatic life water quality criteria, Oregon
adopted acute (maximum concentration) and chronic (continuous concentration) criteria for
freshwater and saltwater. EPA's Guidelines for Deriving Numerical National Water Quality
Criteria for the Protection of Aquatic Life and Their Uses1 (hereafter 1985 Guidelines),
recommends that numeric aquatic life criteria be expressed as two numbers, so that the criteria
more accurately reflect toxicological and practical realities. The combination of a maximum
concentration and a continuous concentration protects aquatic organisms and their uses from
acute and chronic toxicity (1985 Guidelines p. 4). Because freshwater and saltwater have
different chemical compositions and because freshwater and saltwater (i.e., estuarine and true
marine) species rarely inhabit the same water simultaneously, the 1985 Guidelines also provide
for the derivation of separate criteria for these waters (p. 14).

In determining whether Oregon's new and revised chemical-specific criteria are protective of the
Fish and Aquatic Life designated use in Oregon waters, EPA identified the available toxicity
studies on the chemicals, reviewed the studies for data quality and relevance, and considered
these quality-assured and relevant data in its evaluation of whether the Oregon criteria would
protect fish and aquatic life in Oregon's waters. In making the determination as to whether the
Fish and Aquatic Life designated use was protected by Oregon's criteria, EPA evaluated whether
the criteria would cause mortality or adverse effects to enough members of a species such that
aquatic ecosystems in Oregon would no longer reflect balanced, integrated, and adaptive
communities of organisms having species composition and diversity of functional organization
comparable to that of the natural habitat of Oregon.

Section 1 of this document describes EPA's additional methods (beyond those provided in the
1985 Guidelines) for assessing whether these criteria are protective of the Fish and Aquatic Life
designated use, and includes a discussion of the sources of data and information EPA used in
conducting its evaluation. Section 2 of this document describes EPA's evaluation of Oregon's
acute and chronic criteria for each chemical and EPA's basis for concluding that the criterion is
protective of Oregon's designated use.

Appendix A of this document describes the test result quality review (QA/QC) requirements that
EPA used to review available toxicity studies for scientific data quality and relevance. Studies

1 Stephan, C.E., D.I. Mount, D.J. Hanson, J.H. Gentile, G.A. Chapman, and W.A. Brungs. 1985. Guidelines for
Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses. EPA
PB85-227049.

-------
that met the QA/QC requirements were deemed by EPA to be of sufficient scientific quality and
relevance and were used by EPA to evaluate whether Oregon's criteria values would protect the
Fish and Aquatic Life designated fish and aquatic life use.

Appendix B describes, in brief, the procedures that EPA used in its Endangered Species Act
(ESA) Biological Evaluation (BE) of Oregon's criteria and how those procedures relate to this
analysis. The BE was developed for the purpose of providing the U.S. Fish and Wildlife Service
and the National Marine Fisheries Services (hereafter referred to as the Services) with the
information that EPA understood the Services desired in order for the Services to complete their
review of EPA's action under section 7(a)(2) of the Endangered Species Act (ESA). This
information consists of a review of all available studies of the toxicity of these chemicals to
aquatic species, including data that were not included, after due consideration, in EPA's
determination of whether Oregon's criteria are protective of Oregon's Fish and Aquatic Life
designated use due to significant scientific concerns over the viability of the tests.

Also included are Appendices (C-V) for each chemical evaluated in this assessment that contain
studies not utilized in this determination complete with the codified reasons for QA/QC failure.

-------
1.0 Methodology for Criteria Evaluation

This section describes the steps EPA used in the effects determination (Section 2) to determine
whether the criteria under review would be expected to protect Oregon's Fish and Aquatic Life
designated uses. Consistent with the federal water quality standards regulations at 40 CFR
131.11, EPA incorporated this analysis into its CWA section 303(c) determination.

This methodology consists of the following key steps: (1) identification of available studies of
the acute and chronic toxicity to aquatic species for the revised chemicals (see table, Section 1),
(2) review of available toxicity studies for data quality and relevance (see Appendix A for
quality control methods) which occurs in two stages, as described below, (3) consideration of
toxicity test data of sufficient quality and relevance to determine potential effects to fish and
aquatic life in Oregon, and (4) determination of whether Oregon's criteria for each chemical is
expected to be protective of aquatic communities residing in Oregon and thus protective of
Oregon's Fish and Aquatic Life designated use.

Section 1.1 identifies sources of data EPA considered in making its CWA section 303(c)
determinations and references the QA/QC requirements that EPA used in determining which data
is considered to be of sufficient scientific quality and relevance for use in CWA determinations.
Sections 1.2 and 1.3 discuss how EPA evaluated the effects to species based on Oregon's acute
and chronic criteria, respectively, in light of the data and information contained in these sources.
Section 1.4 discusses how EPA determined, on the basis of its review, whether a particular
criterion would be protective of the aquatic communities in Oregon's waters and thereby support
protection of Oregon's Fish and Aquatic Life designated use. A graphical summary of the
process is provided in figure 1.

1.1 Sources of toxicity test data used in EPA determinations

EPA's evaluation of the relevant new or revised criteria was based on data referenced in the most
recent EPA criteria document for each chemical plus other data gathered during a literature
search update for each chemical.

When EPA develops nationally recommended criteria for the protection of aquatic life under
304(a) of the CWA, EPA conducts a comprehensive search of available scientific literature to
identify studies and data on the acute and chronic toxicity of a chemical to aquatic species.

These studies are identified in the 304(a) criteria documents available online . The ECOTOX
database, maintained by EPA, is the primary source of information regarding toxicity to aquatic
species. The ECOTOX process includes a QA/QC step, detailed in Appendix A and represented

2When EPA issues a CWA Section 304(a) national aquatic life criterion for a chemical, EPA publishes a criteria
document that presents the recommended criterion, the data upon which it is based, and an explanation of the
derivation of the criterion. The criteria recommendations are referred to as the 304(a) criteria or the national
recommended water quality criteria.

3 http ://water. epa. gov/scitech/swguidance/standards/criteria/current/index. cfm

-------
by the decision point 1 in Figure 1, that identifies tests deemed to be of potentially acceptable
quality. EPA then moves into a more specific evaluation of each study that passes the ECOTOX
screen (referred to as the Office of Water QA procedures, largely defined in the 1985 Guidelines
and various EPA and ASTM standards, identified as decision point 3 in Figure 1).

EPA also prepared a biological evaluation (BE) for the purpose of providing the US Fish and
Wildlife Service and National Marine Fishes Services (referred to together as 'the Services')
with information that the Services indicated to EPA was necessary in order for the Services to
complete their biological opinion (BO) under ESA section 7(a)(2) on EPA's action to approve
Oregon's water quality standards. When EPA develops a BE, EPA typically uses the data
referenced in the criteria document(s) and supplements these test data with data obtained from
updated literature searches. This practice of conducting an updated literature search is in
recognition of the fact that additional toxicity testing may have occurred between the time that
the latest national recommended criteria were issued and the time of EPA's action to approve or
disapprove a State's water quality standards. Not only did EPA conduct an updated literature
search for the purposes of the BE, EPA also, in deference to the Services, was broadly inclusive
with regard what information was identified in the BE. That is, EPA included some studies for
consideration in the BE that it would typically have excluded in criteria development because
they did not qualify as sufficiently scientifically robust in regards to study quality, in order to
accommodate the Services desire to have access to as much information as possible.

Because EPA's objective in developing the BE was to be responsive to the Services' desire to
have as much information as possible to consider as they developed their BO under the ESA, the
information in the BE differs in some respects from what EPA considered as it evaluated the
protectiveness of Oregon's criteria under the CWA (for a detailed explanation of these
differences, see Appendix B, section B.3).

For this CWA determination, EPA considered those data referenced in the criteria document
along with the new data referenced in the BE that met EPA test quality requirements described in
Appendix A. Some of the data referenced in the BE did not meet the QA/QC requirements and
were identified in their respective, chemical specific appendices following Section 2 of this
document along with a reason for rejection for purposes of full transparency. Specifically, in the
case of the acute and chronic toxicity studies used in the BE, EPA examined studies in greater
depth when either: (1) the study results indicated toxicity that was near or below the
recommended criteria value, or (2) the study included tests with a species associated with one
the four most sensitive GMAVs for the pollutant.4 EPA undertook this additional review of
these particular studies because studies near the criteria values are most influential in
determining in the adequacy of the criteria for protecting sensitive genera and species. Values
considered to be above the criterion are not of concern due to lack of sensitivity. For each study

4 Specifically, EPA double-checked its prior test quality evaluations for those studies yielding SMAVs less than 2
fold greater or SMCV values that were below the respective Oregon acute and chronic criterion values in addition to
any study providing an acute or chronic toxicity value for a species associated with one of the four most sensitive
genera used to calculate the corresponding criterion. The derivation of the SMAV and SMCV values is described in
Sections 1.2 and 1.3.

-------
that was potentially influential but did not pass the quality review, the study was not used in this
determination and the rationale for its exclusion is detailed in each criterion's respective
appendix. In addition, for each chemical, a list of all studies that were utilized in the
determination is provided in a reference table located in each chemical specific subsection of
Section 2.0.

Finally, for the purposes of this document, EPA did not consider it appropriate to make CWA
determinations based on estimates or projections of potential toxicity to particular species in
cases where no actual toxicity data are available for these species via use of models. This is
because these projections involve a high degree of uncertainty. Projections based on these types
of models have been shown in some cases to be 5 fold different from actual toxicity results when
toxicity testing is actually undertaken on the species5. Accordingly, EPA has not used the
model-based estimates or projections of potential toxicity of chemicals to aquatic species in its
determination of whether Oregon's criteria are protective of Oregon's Fish and Aquatic Life
designated use and considers the distribution of taxa represented by the minimum data
requirements and the use of the fifth percentile genus protection sufficient for the purpose of
offering protection to untested species and genera.

1.2 Evaluation of the protectiveness of Oregon's acute criterion
concentration

After EPA verified the quality of available toxicity test data and identified those acute toxicity
tests that were of sufficient quality and relevance, EPA analyzed the protectiveness of Oregon's
acute criteria using these data.

Acute toxicity tests in the published literature are typically laboratory studies that determine the
concentration of a chemical that causes 50% of the organisms in a given test to perish or be
severely affected, typically in 96 hour toxicity tests for vertebrates and 48 hour tests for
invertebrates such as Daphnid species. EPA often finds more than one scientifically sound and
relevant acute toxicity study on a particular chemical for a particular species. Frequently, the
reported toxicity value for a single species varies across studies in a given laboratory and across
laboratories. Because of this, EPA calculates Species Mean Acute Values (SMAVs) from the
acceptable toxicity tests for a given species that are found to be scientifically sound and relevant.
The SMAV is the geometric mean of the acute toxicity values for a species (the most sensitive
tested life stage of the species is always used if identified). The geometric mean of the
acceptable acute toxicity values for a species is considered to be the most representative of the
central tendency of those values.6 If only one acceptable toxicity study is available for a species,
then EPA uses that value to represent the SMAV in order to include as many species as possible
in the criteria development. These values are then combined into a genus level estimate of

5 Raimondo et al., Influence of Taxonomic Relatedness and Chemical Mode of Action in Acute Interspecies
Estimation Models for Aquatic Species, Environ. Sci. Techno/., 2010, 44 (19), pp 7711-7716

6 Geometric means are used to calculate central tendency values for acute values, chronic values, and acute-chronic
ratios because such data tend to be log normally distributed rather than normally distributed.

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organism effects termed the Genus Mean Acute Value (GMAV). The GMAV is the geometric
mean of the acute toxicity values for all available, acceptable species data in a genus and is
considered to be the most representative of the central tendency of those values for the genus.
These genus values are then loosely classified into taxanomic groups, per the 1985 Guidelines, in
order to represent a cross-section of the expected natural composition of aquatic water bodies.
Any criterion derived by this guidance will contain the requisite biodiversity in order to derive a
protective level sufficient to be deemed protective of aquatic life.

The evaluation used in this effort consisted of a tiered process. As per the 1985 Guidelines, data
at the genera level was evaluated first (GMAV, GMCV). A more focused evaluation was then
performed.

This more focused step in the process involves calculating an estimate of the concentration that
would result in little or no mortality or effect. This value is statistically indistinguishable from
control mortality or effect in the acceptable tests found in the literature. EPA develops this low
effect value for each chemical and species combination by dividing each SMAV by 2. EPA
derived the factor of 2 and this approach from an analysis of 219 acute toxicity tests on a range
of chemicals, as described in the Federal Register on May 18, 1978 (43 FR 21506-18).7 As
noted in the Federal Register notice:

"The figure of 0.44 is an 'adjustmentfactor' applied to LC50 data to determine
the concentration likely to be lethal to between 0 percent and 10percent. It is
based on 219 acute toxicity tests which showed that the mean concentration lethal
to 0-10 percent of the test population was 0.44 times the LC50. "

Thus, in EPA's scientific judgment, the magnitude of acute effects to a particular species at the
SMAV/2 would not be projected to significantly impact the population of the species, because it
is expected to be statistically indistinguishable from effects to control (unexposed) organisms.

These SMAV/2 values were compared to the Oregon criterion to ascertain concentrations
resulting in effects at the species level that are expected to be undistinguishable from control
effects, in order to assist with the determination of the protectiveness of Oregon's aquatic life
designated use. When the SMAV/2 for a particular species was greater than the chemical criteria
level adopted by Oregon, EPA determined that the chemical criteria adopted by Oregon would
not result in significant impacts if members of the species were exposed at the criterion. When
the SMAV/2 for a particular species that inhabits Oregon is less than the Oregon criteria for a
particular chemical, EPA determined that there may be potential for impacts to members of the
species.

7 The analysis consisted of calculating the geometric mean of the ratios of the highest concentration (HC) affecting
or causing lethality to 0 to 10% of organisms divided by the LC50 or EC50 for the same organisms in the same
toxicity test. The geometric mean of the 219 HC/LC50 (or HC/EC50) ratios was 0.44; that is, the mean
concentration that was lethal to 0 to 10% of the test population was 0.44 times the LC50 (or EC50). EPA used the
reciprocal of 0.44, which is 2.27, and best professional judgment was used to round 2.27 to 2. (In 2006, the same
data set was reanalyzed, and the geometric mean was corrected from 0.44 to 0.43).

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If the test species of concern does not reside in Oregon, EPA determined that these test results
were not relevant to the evaluation of criteria relative to protecting Oregon's waters and did not
include this test result in the final CWA determination. Where EPA confirmed that the species is
present in Oregon but there is no significant difference between the Oregon criterion and the
SMAV/2, EPA concluded that the acute criterion adopted by Oregon would not result in
significant impacts to exposed members of the species, and therefore, will not impact the species
in the aquatic ecosystem if exposed beyond the frequency and duration requirements. Where
there was a significant difference between the test result and the criterion, EPA examined the
details underlying the value to make a final determination for that species. It should be noted
that EPA's protection goal of "fishable" as presented in the CWA and codified by the Guidelines
for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms
and Their Uses, is to protect approximately the 5th percentile genera of the full distribution of
data, and by extension the 5th percentile of potential organisms in the aquatic ecosystem. Based
on this approach, it is not uncommon for a species to be sensitive at the criterion concentration.
This fact is why EPA recommends that the national 304(a) criterion be adjusted for
recreationally or commercially important species and pertains to this more in-depth review of the
available, scientifically sound information.

It is also important to note that water quality criteria provide recommendations for specific
concentrations (or magnitudes) that are protective, and importantly, provide additional protection
by limiting how long (duration) and how often (frequency) such concentrations should be limited
to in order to provide additional protection to aquatic organisms. EPA's acute criteria generally
recommend that the specific concentration identified as sufficiently protective of aquatic
ecosystems not be exceeded instantaneously or for more than one hour (duration) once every
three years (frequency). It is useful to consider that toxicity values upon which acute criteria
magnitudes are based are determined in multi-day tests (generally 2-4 days tests), not one-hour
tests. Thus, comparing the low-to-no-level acute effect magnitudes (SMAVs/2) from multi-day
tests to criteria magnitudes that may not be exceeded for more than 1 hour every three years
provides a substantial level of additional protection to aquatic organisms. This added protection
is not quantitatively evaluated in this effort, but should be considered and addressed in any
subsequent, species specific, determinations.

In cases where individual species may be affected, EPA noted such in the technical support for
each chemical in Section 2 of this document. The weight of evidence was then evaluated for
each criterion and a determination made as to the protection of Oregon's aquatic life designated
use.

Note: In this evaluation, the reporting of calculated values (SMAV, GMAV, SMCV, GMCV)
has been limited to a minimum of four significant figures for convenience with the exception of
very high values, which are reported as whole numbers. The results of such calculations in
aquatic life criteria documents are given to four significant figures to prevent roundoff error in
subsequent calculations, not to reflect the precision of the values.

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1.3 Evaluation of the protectiveness of Oregon's chronic criterion
concentration

After EPA evaluated available acute toxicity data, EPA identified those chronic toxicity tests that
were of sufficient data quality and relevance to analyze the protectiveness of Oregon's chronic
criteria using the test quality acceptability requirements identified in Appendix A.

In general, there are far fewer published chronic toxicity tests than published acute toxicity tests.
Chronic toxicity tests are typically run for 7 to 365 days during which time scientists evaluate the
adverse effects of the chemical on tested species. These effects may include, but are not limited
to, weight loss or growth effects, impacts on reproduction and development, mortality or any
effect quantitatively linked to those endpoints.

In order to fully evaluate potential effects to aquatic life due to exposure to the criterion
concentration, EPA developed the following approach, which is different and significantly more
detailed than outlined in the 1985 Guidelines, that examines the relative responses across all
genera and species relative to the state adopted chronic standard value. The intention of this
section is to examine all existing species sensitivity information, related to species which occur
in the state, in order to inform the final risk management decision relative to Oregon's aquatic
life designated use. EPA notes here, however, that much of this information is exracted from the
results of acute tests and extrapolated to chronic effects. This method is novel and is intended
only as a further screen by which to determine confidence in the existing criteria in regards to the
protection provided to Oregon's aquatic life designated use.

EPA's evaluation of Oregon's new or revised chronic standard concentrations was based either
on experimentally determined Species Mean Chronic Values (SMCVs) or on predicted Genus
Mean Chronic Values (GMCVs). EPA calculated a predicted GMCV for a genera and chemical
combination by dividing the GMAV by the Final Acute-Chronic Ratio (ACR) in order to derive
consistent measures of chronic sensitivity for all genera for which acute values were available.
An ACR is the quotient of an acceptable experimentally determined acute toxicity test value
divided by an acceptable experimentally determined chronic toxicity test value, when the acute
value and the chronic value are determined in the same dilution water using organisms from the
same source when available. Many of the ACRs come directly from the national recommended
water quality criteria documents. In cases where new data was available from the updated
literature search, this data was used to calculate a revised ACR.

EPA summarized experimentally determined SMCVs and ACRs from the data contained in the
studies which passed the test quality requirements. By definition, an experimentally determined
SMCV was derived by taking either the geometric mean between the No Observed Effects
Concentration (NOECs) and the Lowest Observable Effects Concentration (LOECs), which is
also termed the Maximum Acceptable Test Concentration (MATC), or a point estimate

-------
o

determined via regression analysis (e.g., an EC20) from a scientifically sound and relevant
chronic test.

EPA then compared the experimentally determined SMCVs or estimated GMCVs to the Oregon
chronic criterion. When the experimentally determined SMCV or estimated GMCV for a
particular species was greater than the chronic criteria concentration adopted by Oregon, EPA
determined that this chronic criteria concentration should be protective of exposed members of
the genera and therefore will not be expected to significantly impact local populations. When the
GMCV for a particular genus is less than the Oregon criteria for a particular chemical, EPA
further analyzed the data to determine whether the species that comprise the genus value reside
in Oregon and whether there is a significant difference between the criteria level adopted by
Oregon and the GMCV, considering the inherent uncertainties in the analyses. This information
was used to evaluate the protectiveness of Oregon's aquatic life designated use against chronic
effects.

If a test species of concern does not reside in Oregon, EPA determined that these test results
were not relevant to the evaluation of criteria relative to protecting Oregon's waters and did not
include this test result in the final CWA determination; however they are noted at the end of each
chemical specific section for full transparency. Where EPA found that the species did exist in
Oregon but there was no significant difference between the Oregon criterion and the GMCV,
EPA concluded that the chronic standard concentration adopted by Oregon would not be
expected to result in significant impacts in reproduction or growth and therefore would be
expected to neither impact local populations or the biological integrity of the ecological
communities in the waterbody where criteria are met.

As described in the acute section above, it is also essential to note that water quality criteria
provide recommendations for specific concentrations, and also, importantly, provide additional
protection by limiting how long (duration) and how often (frequency) such concentrations should
be limited to in order to provide additional protection to aquatic organisms. EPA's chronic
criteria generally recommend that the specific concentration identified as sufficiently protective
of chronic effects in aquatic ecosystems not be exceeded for more than four days (duration), once
every three years (frequency). Thus, comparing low level chronic effect magnitudes (GMCVs)
based on long-duration tests, (generally, weeks-to-months long tests) to criteria magnitudes that
may not be exceeded for more than 4 days every three years provides a substantial level of
additional protection to aquatic organisms. A more detailed response to the frequency and
duration components of criteria is included in the response to comments document.

A final determination regarding the protection of the aquatic life designated use by each criterion
is made based on the summation of the data or weight of evidence based on the relevant data as
provided in this document.

8 An EC20 is the statistically derived concentration that is expected to cause a 20% reduction in survival, growth, or
reproduction, depending on which endpoint is most sensitive to the chemical of concern. On the average, the EC20
from an acceptable chronic test is similar to the geometric mean of the NOEC and the LOEC (the MATC used here)
from the same chronic test.

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1.4 Final determination method

As discussed above in sections 1.1, 1.2, and 1.3, in making this determination, EPA
collected aquatic toxicity test results for the chemicals for which Oregon adopted new or
revised aquatic life criteria. EPA then reviewed the data using established test quality
requirements (Appendix A), and used the resulting scientifically acceptable data to
determine whether Oregon's criteria for each chemical would be sufficiently protective of
the diversity of aquatic organisms and the associated aquatic life designated use if
organisms were exposed at the criterion concentration acutely or chronically. When the
data for a genera or species was greater than the Oregon criterion for a particular
chemical, EPA determined that the species and genera would be protected by the
criterion.

When the SMAV/2 or estimated GMCV (SMCV, if available in the literature) for a
particular species was less than the Oregon criterion for a particular chemical, EPA
performed additional analyses to determine if the species resided in Oregon, and if so, if
the difference between the test results and the criterion were significant.

If the species resides in Oregon, EPA conducted analyses to determine if the difference
between the test results and the criterion was significant. If a species was found to be
sensitive, EPA noted the expected sensitivity in the technical evaluation for each
chemical (Section 2).

Under EPA's guidance, in order to protect aquatic life designated uses, the Agency has
derived a nationally relevant method designed to protect the majority of species in the
majority of environments. The selected level of protection is the 5th percentile of all
tested genera, which is designed to represent ecologically relevant populations in the
environment, based on the minimum eight taxa data requirements. In effect, this
approach is intended to protect 95% of genera from negative effects on survival, growth,
or reproduction, if exposed to criterion concentrations for no more than four days
chronically or one day acutely once every three years on average. Due to the use of a
calculated fifth percentile of a species sensitivity distribution for each determination, a
simple count of acceptable studies that are above and below the criterion value is
insufficient for final decision making.

Final approval or disapproval of Oregon's individual standards is based on the relevant
facts and weight of evidence for each criterion. Ecologically (including ESA listed
species), commercially, or recreationally important species, if sensitive, may require the
consideration of site or state specific adjustments to the nationally recommended 304(a)
criteria to account for that sensitivity as directed in the 1985 Guidlines. All science based
decisions are supported by the technical evaluation presented in Section 2.

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criteria concentrations if
exposed beyond frequency
and duration requirements

Figure 1. Flow diagram describing the decision framework within which EPA evaluated the available,
acceptable scientific data. The end determination was based on the sensitivity of genera identified by the
above process.

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2.0 Criteria Evaluation

2.1 Freshwater

2.1.1 AMMONIA

Please see the main decision document for information regarding the disapproval of this
criterion.

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2.1.2 CADMIUM

2.1.2.1 Evaluation of the Acute Freshwater Criterion Concentration for Cadmium

Please see the primary decision document for information regarding the disapproval of this
criterion.

2.1.2.2 Evaluation of the Chronic Freshwater Criterion Concentration for Cadmium

A. Presentation of Toxicological Data

Oregon adopted a freshwater chronic criterion concentration of 0.25 |ig/L for cadmium
expressed as the dissolved metal concentration at a total hardness of 100 mg/L CaCC>3 in the
water column. This concentration is the same as the freshwater CCC recommended for use
nationally by EPA for the protection of aquatic life9. EPA developed the recommended criterion
in accordance with the 1985 Guidelines pursuant to CWA section 304(a).

Table 3.1.2-1 presents a compilation of SMAVs and GMAVs calculated in support of EPA's on-
going review of available acute toxicity data, any experimentally determined SMCVs obtained
from the criteria document and EPA ECOTOX download used for the BE, and estimated
GMCVs based on the GMAV/FACR. The 2001 criteria document for cadmium did not report a
FACR. However, the acute-chronic ratios included in the document ranged from 0.9021 for the
chinook salmon to 433.8 for the flagfish (greater than a factor of ten), with eighteen other values
scattered throughout this range (see Tables 2e and 3c in the 2001 criteria document). Because
salmonids are among the most sensitive genera, EPA determined the ACR of 0.9021 is the most
appropriate ACR to protect sensitive species in general. However, in accordance with the
Guidelines, the FACR cannot be less than 2 due to testing considerations, so it is adjusted up to
2. Since no additional acceptable ACRs are available, EPA calculated the predicted GMCVs for
cadmium in Table 3.1.2-1 using an FACR of 2 and the following equation: Predicted GMCV =
GMAV/FACR.

EPA compared the GMCVs for each species to Oregon's cadmium chronic criterion to determine
whether the chronic criterion will protect the aquatic life designated use.

9 See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.

The data which serve as the basis for the current nationally-recommended criteria are from U.S. EPA. 2001. 2001

Update of Ambient Water Quality Criteria for Cadmium. EPA-822-R-01-001.

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Table 2.1.2-1: Genus Mean Chronic Values

GMCVs) for Cadmium

Genus

Species

Common name

Most
Representative
SMAV
(MS)"-)

GMAV

(Mg/L)

Acute References

(used in the calculation
of the SMAV)

SMCV
(Mg/L)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV

(Mg/L)

Chironomus

rtpartus

Midge

185025

Chironomus

tentans

Midge

22930

25,100

4.260

Chironomus

plumosus

Midge

15042

39962

98,99

19981
(4.260)

Oreochromis

aureus

Blue tilapia

>35.90

Oreochromis

niloticus

Nile tilapia

65456

Oreochromis

mossambica

Mozambique
tilapia

14675

30993

95,96

15497
(>35.90)

Cyprinus

carpio

Common carp

28454

71,93,94

14227

Dendrocoelum

lacteum

Turbellarian,
planarian

26865

13433

Rhithrogena

hageni

Mayfly

21488

23,91

10744

Gambusia

affinis

Western
mosquitofish

12412

6206

Rhyacodrilus

montanus

Oligochaete

11782

5891

Branchiura

sowerbyi

Oligochaete

11469

71,83

5734

Gasterosteus

aculeatus

Threespine
stickleback

10387

89,90

5194

Stylodrilus

heringianus

Oligochaete

10286

5143

Ictalurus

punctatus

Channel catfish

9654

4827

Lepomis

macrochirus

Bluegill

11513

13,88

26.40

Lepomis

cyanellus

Green sunfish

5662

8074

4037
(26.40)

Hexagenia

rigida

Mayfly

7428

3714

Spirosperma

nikolskyi

Oligochaete

8416

Spirosperma

ferox

Tubificid worm,
Oligochaete

6545

7422

3711

Cyprinella

lutrensis

Red shiner,
Rainbow dace

7328

3664

Varichaeta

pacifica

Earthworm

7107

3553

Perca

flavescens

Yellow perch

6763

3381

Catostomus

commersoni

White sucker

5989

11.86

2995
(11.86)

Quistadrilus

multisetosus

Oligochaete

5984

2992

Jordanella

floridae

Flagfish

5437

81,82

8.079

10,11

2719
(8.079)

Poecilia

reticulata

Guppy

4702

79,80

2351

Ephemerella

grandis

Mayfly

4350

2175

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Genus

Species

Common name

Most
Representative
SMAV
(MS)"-)

GMAV

(Mg/L)

Acute References

(used in the calculation
of the SMAV)

SMCV
(Mg/L)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV

(Mg/L)

Tubifex

tubifex

Tubificid worm

3950

20,74,75,76,77

1975

Crangonyx

pseudogracilis

Amphipod

3247

1623

Xenopus

laevis

African clawed
frog

2920

1460

Diaptomus

forbesi

Copepod

2879

1439

Procambarus

alleni

Crayfish

6410

Procambarus

clarkii

Red swamp
crayfish

2180

66,70

Procambarus

acutus

Crayfish

791.2

2228

1114

Carassius

auratus

Goldfish

1612

806.0

Limnodrilus

hoffmeisteri

Tubificid worm,
Oligochaete

1480

740.1

Orconectes

virilis

Crayfish

22649

Orconectes

immunis

Crayfish

21981

Orconectes

juvenilis

Crayfish

130.5

Orconectes

placidus

Crayfish

64.14

1429

714.4

Gammarus

pseudolimnaeus

Scud

150.3

1366

39,40

682.9

Ambystoma

gracile

Northwestern
salamander

995.7

497.9

Asellus

bicrenata

Isopod

901.7

450.8

Physa

acuta

Snail

2096

Physa

gyrina

Pouch snail

191.3

633.2

316.6

Coregonus

clupeaformis

Lake whitefish

619.8

309.9

Plumatella

emarginata

Bryozoan

496.0

248.0

Alona

affinis

Water flea

472.2

236.1

Lymnaea

stagnalis

Pond snail

452.9

226.4

Ptychocheilus

oregonensis

Northern
squawfish

4243

Ptychocheilus

lucius

Colorado
squawfish

43.04

427.3

213.7

Cyclops

varicans

Cyclopoid
copepod

426.4

213.2

Glossiphonia

complanata

Leech

367.7

183.9

Pectinatella

magnifica

Bryozoa

318.5

159.3

Lumbriculus

variegatus

Worm

249.5

124.7

Aplexa

hypnorum

Snail

198.4

13,56

7.323

99.19
(7.323)

Hydra

vulgaris

Hydra

177.2

53,54,55

Hydra

oligactis

Hydra

142.1

Hydra

viridissima

Hydra

37.30

97.92

53,54

48.96

Lirceus

alabamae

Aquatic sowbug

92.51

46.26

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Genus

Species

Common name

Most
Representative
SMAV
(MS)"-)

GMAV

(Mg/L)

Acute References

(used in the calculation
of the SMAV)

SMCV
(Mg/L)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV

(Mg/L)

Utterbackia

imbecillis

Mussel

85.75

29,42,51

42.88

Moina

macrocopa

Water flea

82.30

41.15

Gila

elegans

Bonytail

73.95

36.98

Ceriodaphnia

reticulata

Water flea

78.45

33,34

Ceriodaphnia

dubia

Water flea

66.78

72.38

25,31,42,45,
46,47,48,49

41.27

36.19
(41.27)

Xyrauchen

texanus

Razorback sucker

69.94

34.97

Lophopodella

carteri

Bryozoa

68.26

34.13

Villosa

vibex

Southern rainbow
mussel

67.18

33.59

Lasmigona

subviridis

Mussel

65.11

32.56

Actinonaias

pectorosa

Mussel

64.56

32.28

Lampsilis

straminea
claibornensis

Southern
fatmucket

91.05

Lampsilis

teres

Yellow sandshell

45.65

64.47

32.24

Aeolosoma

headleyi

Oligochaete

31.51

12,16

(31.51)

Simocephalus

serrulatus

Water flea

57.69

39,40,41

28.85

Daphnia

pulex

Water flea

90.51

31,33,34,35,
36,37,38

9.369

Daphnia

magna

Water flea

41.93

<0.5764

1,2,3

Daphnia

ambigua

Water flea

24.25

45.15

22.57
(2.324)

Pimephales

promelas

Fathead minnow

28.71

24.88

14.35
(24.88)

Micropterus

dolomieui

Smallmouth bass

12.34

(12.34)

Esox

lucius

Northern pike

12.29

(12.29)

Anodonta

couperiana

Mussel

22.92

11.46

Prosopium

williamsoni

Mountain
whitefish

15.21

7.607

Cottus

bairdi

Mottled sculpin

10.70

19,22,23

5.349

Oncorhynchus

kisutch

Coho salmon

11.88

6.479

Oncorhynchus

tshawytscha

Chinook salmon

8.222

9,10,20,21

3.968

Oncorhynchus

my kiss

Rainbow trout

4.397

7.545

2,4,9,10,11,12,13,14,
15,16,17,18,19

1.987

3.773
(3.710)

Morone

saxatilis

Striped bass

5.586

2.793

Salmo

salar

Atlantic salmon

12.03

Sal mo

trutta

Brown trout

5.445

4,5,6,7

7.602

2.723
(9.563)

Etheostoma

fonticola

Fountain darter

4.612

2.306

Salvelinus

namaycush

Lake trout

12.29

Salvelinus

confluentus

Bull trout

4.110

-------
Genus

Species

Common name

Most
Representative
SMAV
(MS)"-)

GMAV

(Mg/L)

Acute References

(used in the calculation
of the SMAV)

SMCV
(Mg/L)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV

(Mg/L)

Salvelinus

fontinalis

Brook trout

3.420

3.749

4.015

1.875
(7.025)

Hyalella

azteca

Amphipod

H. azteca is sensitive to chloride concentration. EPA has decided to not use data for this species until additional
tests are conducted. Chronic data for this species from Ingersoll and Kemble (Manuscript) is designated as

Unused - Failed QA QC.

Note 1: Species that are bold and italicized indicate those associated with the four most sensitive genera used to derive the FAV in the 2001 update of the ALC document. Underlined
species with an asterisk (*) indicate known or suspected Oregon non-resident species, and for this evaluation, only those non-resident species below the criterion or related to the four
most sensitive genera are identified as such.

-------
B. Evaluation of the Protectiveness of the Oregon Freshwater Chronic Criterion for
Cadmium

Following the review of the GMCV in Table 2.1.2-1, all tested genera and species have values
greater than Oregon's chronic criterion for cadmium. Therefore, EPA concluded that chronic
effects are not expected to occur at ambient concentrations equal to or lower than the criterion
and the aquatic life designated use is protected.

2.1.2.3 References for Cadmium

A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the chronic table, and are the source from which EPA obtained SMAVs
(for SMCV estimation) and experimentally-derived SMCVs.

Reference No.

Used Reference Citation

(associated with reference numbers and provided above in Table 2.1.2-1)

Acute References

Carroll, J.J., S.J. Ellis and W.S. Oliver. 1979. Influences of hardness constituents on the acute toxicity of cadmium
to brook trout (Salvelinus fontinalis). Bull. Environ. Contam. Toxicol. 22:575-581.

Stratus Consulting, Inc. 1999. Sensitivity of bull trout (Salvelinus confluentus) to cadmium and zinc in water
characteristic of the Coeur D'Alene River Basin: acute toxicity report. Final Report to U.S. EPA Region X. 55 pp.

Southwest Texas State University. 2000.Comparison of EPA Target Toxicity Aquatic Test Organisms to the
Fountain Darter. 7 Day Chronic Toxicity Test Using Cadmium Chloride. Performed 11/12/99 - 3/6/00 (5 parts).
Edwards Aquifer Res. and Data Center (EARDC), Southwest Texas State Univ., San Marcos, TX. Fed. Assist.
Agree. No. X-986345-01: 179 p. (Author Communication Used).

Stubblefield, W.A. 1990. An evaluation of the acute toxicity of cadmium chloride (CdCI2) to brown trout (Salmo
trutta), rainbow trout (Oncorhynchus mykiss), and mountain whitefish (Prosopium williamsoni): Fort Collins, CO
and Laramie, WY, ENSR Consulting and Engineering and University of Wyoming Red Buttes Environmental
Biology Laboratory.

Davies, P.H. and S.F. Brinkman. 1994c. Toxicology and chemical data on unregulated pollutants. Water Pollution
Studies, Federal Aid in Fish and Wildlife Restoration, Project #33: Fort Collins, CO, Colorado Division of Wildlife.

Brinkman, S.F. and D. Hansen. 2004a. Effect of hardness on cadmium toxicity to brown trout (Salmo trutta)
embryos, larvae, and fry. Water Pollution Studies. Federal Aid in Fish and Wildlife Restoration Project F-243-R11.
Colorado Division of Wildlife, Fort Collins, CO.

Brinkman, S.F. and D.L. Hansen. 2007. Toxicity of cadmium to early life stages of brown trout (Salmo trutta) at
multiple water hardnesses. Environ. Toxicol. Chem. 26(8): 1666-1671.

Palawski, D., J.B. Hunn and F.J. Dwyer. 1985. Sensitivity of young striped bass to organic and inorganic
contaminants in fresh and saline water. Trans. Am. Fish. Soc. 114: 748-753.

Chapman, G.A. 1975. Toxicity of copper, cadmium and zinc to Pacific Northwest salmonids. U.S. EPA, Corvallis,
Oregon.

Chapman, G.A. 1978. Toxicities of cadmium, copper, and zinc to four juvenile stages of chinook salmon and
steelhead. Trans. Am. Fish. Soc. 107: 841.

Cusimano, R.F., D.F. Brakke and G.A. Chapman. 1986. Effects of pH on the toxicities of cadmium, copper, and
zinc to steelhead trout (Salmo gairdneri). Can. J. Fish. Aquat. Sci. 43: 1497-1503.

Davies, P.H. 1976. Use of dialysis tubing in defining the toxic fractions of heavy metals in natural water. In: R.W.
Andrew, et al. (eds.), Toxicity to Biota of Metal Forms in Natural Water. International Joint Commission, Windsor,
Ontario, p. 110.

Phipps, G.L. and G.W. Holcombe. 1985. A method for aquatic multiple species toxicant testing: acute toxicity of
10 chemicals to 5 vertebrates and 2 invertebrates. Environ. Pollut. (Series A). 38: 141-157.

Davies, P.H., W.C. Gorman, C.A. Carlson and S.F. Brinkman. 1993. Effect of hardness on bioavailability and
toxicity of cadmium to rainbow trout. Chem. Spec. Bioavail. 5(2): 67-77.

Davies, P.H. and S.F. Brinkman. 1994b. Appendix II: Cadmium toxicity to rainbow trout: bioavailability and kinetics
in waters of high and low complexing capacities, in Davies, P.H., ed., Water Pollution Studies, Federal Aid in Fish
and Wildlife Restoration, Project #33: Fort Collins, CO, Colorado Division of Wildlife.

Hollis, L., J.C. McGeer, D.G. McDonald, and C.M. Wood. 2004a. Effects of long term sublethal Cd exposure in

-------
Reference No.

Used Reference Citation

(associated with reference numbers and provided above in Table 2.1.2-1)

rainbow trout during soft water: implications for biotic ligand modelling. Aquat. Toxicol. 51(1): 93-105.

Hollis, L., J.C. McGeer, D.G. McDonald, and C.M.Wood. 1999. Cadmium Accumulation, Gill Cd Binding,
Acclimation, and Physiological Effects During Long Term Sublethal Cd Exposure in Rainbow Trout. Aquat.Toxicol.
46(2): 101-119

Niyogi, S., P. Couture, G.G. Pyle, D.G. McDonald and C.M. Wood. 2004. Acute cadmium biotic ligand model
characteristics of laboratory-reared and wild yellow perch (Perca flavescens) relative to rainbow trout
(Oncorhynchus mykiss). Can. J. Fish. Aquat. Sci. 61(6): 942-953.

Besser, J.M., C.A. Mebane, D.R. Mount, C.D. Ivey, J.L. Kunz, I.E. Greer, T.W. May and C.G. Ingersoll. 2007.
Sensitivity of mottled xculpins (Cottus bairdi) and rainbow trout (Oncorhynchus mykiss) to acute and chronic
toxicity of cadmium, copper, and zinc. Environ.Toxicol.Chem. 26(8), 1657-1665

Chapman, G.A. 1982. Letter to C.E. Stephan. U.S. EPA, Corvallis, Oregon. December 6.

Finlayson, B.J. and K.M. Verrue. 1982. Toxicities of copper, zinc and cadmium mixtures to juvenile chinook
salmon. Trans. Am. Fish. Soc. 111: 645-650.

Besser, J.M., C.A. Mebane, C.D. Ivey, J.L. Kunz, E.I. Greer, T.W. May and C.G. Ingersoll. 2006. Relative
sensitivity of mottled sculpins (Cottus bairdi) and rainbow trout (Onchorhynchus mykiss) to toxicity of metals
associated with mining activities. Columbia, Mo., U.S. Geological Survey, Columbia Environmental Research
Laboratory, Administrative Report to U.S. Environmental Protection Agency, Project No. DW14939902-01-0. 37 p.

Brinkman, S. and N. Vieira. 2007. Water Pollution Studies. Federal Aid Project F-243-R14. Colorado Div. of
Wildlife, Ft. Collins, CO.

Nebeker, A.V., S.T. Onjukka, M.A. Cairns and D.F. Frawczyk. 1986b. Survival of Daphnia magna and Hyalella
azteca in cadmium-spiked water and sediment. Environ. Toxicol. Chem. 5(10): 933-938.

Suedel, B.C., J.H. Rodgers Jr. and E. Deaver. 1997. Experimental factors that may affect toxicity of cadmium to
freshwater organisms. Arch. Environ. Contam. Toxicol. 33(2): 188-193.

Jackson, B.P., P.J. Lasier, W.P. Miller and P.W. Winger. 2000. Effects of calcium, magnesium, and sodium on
alleviating cadmium toxicity to Hyalella azteca. Bull. Environ. Contam. Toxicol. 64: 279-286.

Collyard, S.A., G.T. Ankley, R.A. Hoke and T. Goldenstein. 1994. Influence of age on the relative sensitivity of
Hyalella azteca to diazinon, alkylphenol ethoxylates, copper, cadmium, and zinc. Arch. Environ. Contam. Toxicol.
26(1): 110-113.

McNulty, E.W., M.R. Ellersieck, E.I. Greer, C.G. Ingersoll, and C.F. Rabeni. 1999. Evaluation of Ability of
Reference Toxicity Tests to Identify Stress in Laboratory Populations of the Amphipod Hyalella azteca.
Envi ron .Toxicol. Chem. 18(3) :544-548

Keller, A. E. Unpublished. Personal communication to U.S. EPA.

Spehar, R.L. and J.T. Fiandt. 1986. Acute and chronic effects of water quality criteria-based metal mixtures on
three aquatic species. Environ. Toxicol. Chem. 5: 917-931.

Shaw, J.R., T.D. Dempsey, C.Y. Chen, J.W. Hamilton and C.L. Folt. 2006. Comparative toxicity of cadmium, zinc,
and mixtures of cadmium and zinc to daphnids. Environ. Toxicol. Chem. 25(1): 182-189.

Attar, E.N. and E.J. Maly. 1982. Acute toxicity of cadmium, zinc, and cadmium-zinc mixtures to Daphnia magna.
Arch. Environ. Contam. Toxicol. 11: 291.

Elnabarawy, M.T., A.N. Welter and R.R. Robideau. 1986. Relative sensitivity of three daphnid species to selected
organic and inorganic chemicals. Environ. Toxicol. Chem. 5: 393-398.

Hall, W.S., R.L. Paulson, L.W. Hall, Jr. and D.T. Burton. 1986. Acute toxicity of cadmium and sodium
pentachlorophenate to daphnids and fish. Bull. Environ. Contam. Toxicol. 37: 308-316.

Bertram, P.E. and B.A. Hart. 1979. Longevity and reproduction of Daphnia pulex (deGeer) exposed to cadmium-
contaminated food or water. Environ. Pollut. 19: 295.

Roux, D.J., P.L. Kempster, E. Truter and L. van der Merwe. 1993. Effect of cadmium and copper on survival and
reproduction of Daphnia pulex. Water SA. 19(4): 269-274.

Stackhouse, R.A. and W.H. Benson. 1988. The influence of humic acid on the toxicity and bioavailability of
selected trace metals. Aquat. Toxicol. 13: 99-108.

Niederlehner, B.R., A.L. BuikemaJr., C.A. Pittinger and J. Cairns Jr. 1984. Effects of cadmium on the population
growth of a benthic invertebrate Aelosoma headleyi (Oligochaeta). Environ. Toxicol. Chem. 2(3): 255-262.

Spehar, R.L. and A.R. Carlson. 1984a. Derivation of site-specific water quality criteria for cadmium and the St.
Louis River Basin, Duluth, Minnesota. PB84-153196. National Technical Information Service, Springfield, VA.

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Giesy, J.P., Jr., G.J. Leversee and D.R. Williams. 1977. Effects of naturally occurring aquatic organic fractions on
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Black, M.C. 2001. Water quality standards for North Carolina's endangered mussels. Final Report, Dept. Env.
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Pardue, W.J. and T.S. Wood. 1980. Baseline toxicity data for freshwater bryoza exposed to copper, cadmium,
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Buhl, K.J. 1997. Relative sensitivity of three endangered fishes, Colorado squawfish, bonytail, and razorback
sucker, to selected metal pollutants. Ecotoxicol. Environ. Safety. 37: 186-192.

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Bitton, G., K. Rhodes and B. Koopman. 1996. Ceriofast™: an acute toxicity test based on Ceriodaphnia dubia
feeding behavior. Environ. Toxicol. Chem. 15(2): 123-125.

Diamond, J.M., D.E. Koplish, J. McMahon III and R. Rost. 1997. Evaluation of the water-effect ratio procedure for
metals in a riverine system. Environ. Toxicol. Chem. 16(3): 509-520.

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responses to cadmium: an experimental study in effluent dominated stream mesocosms. Environ. Toxicol. Chem.
23(4): 1057-1064.

Jun, B.H., S.I. Lee, H.D. Ryu and Y.J. Kim. 2006. Temperature-based rapid toxicity test using Ceriodaphnia dubia.
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Hatakeyama, S. and M. Yasuno. 1981(b). Effects of cadmium on the periodicity of parturation and brood size of
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Keller, A.E. and S.G. Zam. 1991. The acute toxicity of selected metals to the freshwater mussel, Anodonta
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Bosnak, A. D. and E. L. Morgan. 1981. Acute toxicity of cadmium, zinc, and total residual chlorine to epigean and
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Karntanut, W. and D. Pascoe. 2002. The toxicity of copper, cadmium and zinc to four different Hydra (Cnidaria:
Hydrozoa). Chemosphere 47(10): 1059-1064.

Karntanut, W. and D. Pascoe. 2000. A Comparison of Methods for Measuring Acute Toxicity to Hydra vulgaris.
Chemosphere 41: 1543-1548.

Holcombe, G.W., G.L. Phipps and J.W. Marier. 1984. Methods for conducting snail (Aplexa hypnorum) embryo
through adult exposures: effects of cadmium and reduced pH levels. Arch. Environ. Contam. Toxicol. 13: 627.

Schubauer-Berigan, M.K., J.R. Dierkes, P.D. Monson and G.T. Ankley. 1993. pH-dependent toxicity of Cd, Cu, Ni,
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Brown, A.F. and D. Pascoe. 1988. Studies on the acute toxicity of pollutants to freshwater macroinvertebrates: V.
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Ghosh, T.K., J.P. Kotangale and K.P. Krishnamoorthi. 1990. Toxicity of selective metals to freshwater algae,
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Andros, J.D. and R.R. Garton. 1980. Acute lethality of copper, cadmium, and zinc to northern squawfish. Trans.
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Coeurdassier, M., A. De Vaufleury and P.M. Badot. 2004. Effects of cadmium on the survival of three life-stages
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McNicol, R.E. 1997. The influence of environmental factors on the preference-avoidance responses of lake
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Wier, C.F. and W.M. Walter. 1976. Toxicity of cadmium in the freshwater snail, Physa gyrina Say. J. Environ.
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northwestern salamander Ambystoma gracile. Arch. Environ. Contam. Toxicol. 29: 492-499.

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Mirenda, R.J. 1986. Toxicity and accumulation of cadmium in the crayfish, Orconectes virilis (Hagen). Arch.
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Reynoldson, T.B., P. Rodriguez and M.M Madrid. 1996. A comparison of reproduction, growth and acute toxicity
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Jude, D.J. 1973. Sublethal effects of ammonia and cadmium on growth of green sunfish. Ph.D. Thesis. Michigan
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Eaton, J.G. 1980. Memo to C.E. Stephan, U.S. EPA. August 5,1980. "Chronic Cadmium Toxicity to the Bluegill
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Pascoe, D. and P. Cram. 1977. The effect of parasitism on the toxicity of cadmium to the three-spined stickleback,
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Ham, L., R. Quinn and D. Pascoe. 1995. Effects of cadmium on the predator-prey interaction between the
Turbellarian Dendrocoelum lacteum (Muller, 1774) and the isopod crustacean Asellus aquaticus (L.). Arch.
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Gaikwad, S.A. 1989. Effects of mixture and three individual heavy metals on susceptibility of three freshwater
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100

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Borgmann, U., K.M. Ralph and W.P. Norwood. 1989. Toxicity test procedures for Hyaiella azteca, and chronic

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through adult exposures: effects of cadmium and reduced pH levels. Arch. Environ. Contam. Toxicol. 13: 627.

Carlson, A.R., J.A. Tucker, V.R. Mattson, G.L. Phipps and P.M. Cook. 1982. Cadmium and Endrin Toxicity to Fish
in Waters Containing Mineral Fibers. EPA-600/3-82-053. National Technical Information Service, Springfield, VA.

Spehar, R.L. 1974. Cadmium and Zinc Toxicity to Jordaneiia fioridae. EPA-600/3-76-096, U.S. EPA, Duluth, MN:
34 (1976) / M.S. Thesis, Univ. of Minnesota, Minneapolis, MN: 67 p.

Niederlehner, B. 1984. A comparison of techniques for estimating the hazard of chemicals in the aquatic
environment. M.S. thesis. Virginia Polytechnic Institute and State University.

Rombough, P.J. and E.T. Garside. 1982. Cadmium toxicity and accumulation in eggs and alevins of Atlantic
salmon Saimo saiar. Can. J. Zool. 60: 2006.

Pickering, Q.H. and M.H. Gast. 1972. Acute and chronic toxicity of cadmium to the fathead minnow (Pimephaies
promeias) J. Fish. Res. Board Can. 29: 1099.

Eaton, J.G. 1974. Chronic cadmium toxicity to the bluegill (Lepomis macrochirus Rafinesque). Trans. Am. Fish.
Soc. 4: 729.

Niederlehner, B.R., A.L. Buikema Jr., C.A. Pittinger and J. Cairns Jr. 1984. Effects of cadmium on the population
growth of a benthic invertebrate Aeoiosoma headieyi (Oligochaeta). Environ. Toxicol. Chem. 3(2): 255-262.

Papoutsoglou, S.E. and P.D. Abel. 1988. Sublethal toxicity and accumulation of cadmium in Tiiapia aurea. Bull.
Environ. Contam. Toxicol. 41: 404-411.

Jop, K.M., A.M. Askew and R.B. Foster. 1995. Development of a water-effect ratio for copper, cadmium, and lead
for the Great Works River in Maine using Ceriodaphnia dubia and Saiveiinus fontinaiis. Bull. Environ. Contam.
Toxicol. 54: 29-33.

B. Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated the studies and determined that the results were not reliable for use in this
determination, either because they were not pertinent to this determination or they failed the
QA/QC procedures listed in Appendix A. For specific study determinations, see Appendix
C.

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2.1.3 CHROMIUM III

2.1.3.1 Evaluation of the Acute Freshwater Criterion Concentration for Chromium III
A. Presentation of Toxicological Data

Oregon adopted a freshwater acute criterion concentration of 570 |ig/L for chromium III that is
expressed as a function of total hardness in the water column and in terms of the dissolved
concentration of the metal. This dissolved metal concentration reflects the criterion normalized
to a total hardness of 100 mg/L as CaCC>3 and is the same as the freshwater CMC recommended
for use nationally by EPA for the protection of aquatic life10. EPA developed the recommended
criterion in accordance with the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.1.3-1 provides available GMAVs based on available acute toxicity data for chromium III
to aquatic life from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Table 2.1.3-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values
(GMAVs) for Chromium III

Most

Representative
SMAV

GMAV

Acute References

(used in the calculation

Genus

Species

Common name

(Mg/L)

of the SMAV)

Crangonyx

pseudogracilis

Amphipod

162227

Hydropsyche

betteni

Caddisfly

39615

Caddisfly
(unidentified)

27874

Damselfly
(unidentified)

24027

Fundulus

diaphanus

Banded killifish

8713

Lepomis

gibbosus

Pumpkinseed

8764

Lepomis

macrochirus

Bluegill

8373

8566

Morone

saxatilis

Striped bass

9126

Morone

americana

White perch

7426

8232

Anguilla

rostrata

American eel

7169

Chironomus

sp.

Midge

6132

Amnicola

sp.

Spire snail

5692

Cyprinus

carpio

Common carp

5285

9,10

Nais

sp.

Worm

5185

Pimephales

promelas

Fathead minnow

4951

Carassius

auratus

Goldfish

4841

Oncorhynchus

mykiss

Rainbow trout

4191

Poecilia

reticulata*

Guppy

3932

Daphnia

magna

Cladoceran

4563

6,7

10 See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.

The data which serve as the basis for the current nationally-recommended criteria are from the 1995 Great Lakes
Initiative Updates to these criteria as cited in: U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents
for the Protection of Aquatic Life in Ambient Water. EPA-820-B-96-001.

-------

Most

Representative
SMAV

GMAV

Acute References

(used in the calculation

Genus

Species

Common name

(Mg/L)

(M9/L)

of the SMAV)

Daphnia

pulex

Cladoceran

1353

2485

Gammarus

sp.

Scud, Amphipod

1784

Eohmerella

subvaria*

Mayfly

1238

Note 1: Species that are bold and italicized indicate those associated with the four most sensitive genera used to derive the FAV in
the 1995 GLI update of the ALC document. Underlined species with an asterisk (*) indicate known or suspected Oregon non-
resident species, and for this evaluation, only those non-resident species below the criterion or related to the four most sensitive
genera used in the derivation of the 304(a) criteria are identified as such.

Note 2: The reporting of calculated values has been limited to a minimum of four significant figures for convenience and use in this
evaluation with the exception of very high values, which are reported as whole numbers - see text in section 2.2 of this evaluation for
an explanation of this decision, particularly for metals such as chromium III which are normalized to a water hardness of 100 mg/L
as CaC03 and expressed on a dissolved metal basis for a comparison with the acute criterion concentration.

B. Evaluation of the Protectiveness of the Oregon Freshwater Acute Criterion

Following review of GMAV and SMAV/2 values in Table 2.1.3-1, all tested genera and species
are protected by Oregon's acute criterion magnitude for chromium III. Therefore, EPA
concluded that acute effects are not expected to occur at ambient concentrations equal to or
lower than the criterion and the aquatic life designated use is protected.

2.1.3.2 Evaluation of the Chronic Freshwater Criterion Concentration for Chromium III
A. Presentation of Toxicological Data

Oregon adopted a freshwater chronic criterion concentration of 74 |ig/L for chromium III
expressed as the dissolved metal concentration at a total hardness of 100 mg/L CaC03 in the
water column. This concentration is the same as the freshwater chronic criterion concentration
recommended for use nationally by EPA for the protection of aquatic life11. EPA developed the
recommended criterion in accordance with the 1985 Guidelines pursuant to CWA section 304(a).

Table 3.1.3-2 presents a compilation of the experimentally determined GMCVs obtained from
the criteria document and EPA ECOTOX download used for the BE, and estimated GMCVs

based on the GMAV/ACR. The 1984 criteria document for chromium reported an FACR of
41.84, which includes the two lowest values of three experimentally determined ACRs
(expressed on a total recoverable metal basis) of 64.11, 27.30, and >356.4 for rainbow trout,
fathead minnow, and the acutely insensitive (at the time) cladoceran, Daphnia magna,
respectively. New acute toxicity data for D. magna used in this evaluation indicates that this
cladoceran is not as acutely insensitive as previously determined. Therefore, EPA determined
that the use of an ACR for D. magna is appropriate to protect sensitive species in general. The
three ACRs for rainbow trout, fathead minnow and D. magna, when expressed on dissolved
metal basis and normalized to a water hardness of 100 mg/L as CaC03, equate to 10.03, 23.56
and 67.76, respectively. (Note that this latter ACR of 67.76 for D. magna excludes one of the
three ACRs for D. magna determined at 206 mg/L as CaC03 which is a greater than value per

11 See footnote 12 above.

12 U.S. EPA. 1985. Ambient Water Quality Criteria Document for Chromium-1984. EPA-440/5-84-029.

-------
the 1985 Guidelines). Since no additional acceptable ACRs are available, EPA calculated the
predicted GMCVs for chromium III in Table 2.1.3-2 using an FACR of 25.20 and the following
equation: Predicted GMCV = GMAV/FACR.

EPA compared the GMCVs for each species to Oregon's chromium III chronic criterion
magnitude to determine whether the chronic criterion will protect these genera.

Table 2.1.3-2: Genus Mean Chronic Values (GMCVs) for Chromium III

Genus

Species

Common name

GMAV
(MS)"-)

SMCV

(Mg/L)

(experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(MS)"-)

Crangonyx

pseudogracilis

Amphipod

162227

6438

Hydropsyche

betteni

Caddisfly

39615

1572

Caddisfly
(unidentified)

27874

1106

Damselfly
(unidentified)

24027

953.5

Fundulus

diaphanus

Banded killifish

8713

345.8

Lepomis

gibbosus

Pumpkinseed

Lepomis

macrochirus

Bluegill

8566

339.9

Morone

saxatilis

Striped bass

Morone

americana

White perch

8232

326.7

Anguilla

rostrata

American eel

7169

284.5

Chironomus

sp.

Midge

6132

243.3

Amnicola

sp.

Spire snail

5692

225.9

Cyprinus

carpio

Common carp

5285

209.7

Nais

sp.

Worm

5185

205.7

Pimephales

promelas

Fathead
minnow

4951

493.6

196.5
(493.6)

Carassius

auratus

Goldfish

4841

192.1

Oncorhynchus

mykiss

Rainbow trout

4191

177.9

166.3
(177.9)

Poecilia

reticulata*

Guppy

3932

156.0

Daphnia

magna

Cladoceran

69.71

Daphnia

pulex

Cladoceran

2485

98.61
(69.71)

Gammarus

sp.

Scud,
Amphipod

1784

70.79

Eohmerella

subvaria*

Mayfly

1238

49.13

See same notes as above under Table 2.1.3-1.

B. Evaluation of the Protectiveness of the Oregon Freshwater Chronic Criterion

Following the review of the GMCVs in Table 2.1.3-2, 17 of 19 genera (including 19 of 22
species) had values greater than Oregon's chronic criterion for chromium III. Therefore, EPA
concluded that chronic effects are not expected to occur at ambient concentrations equal to or
lower than the criterion for these genera and all except a small proportion of genera are
protected.

The mayfly, Ephmerella subvaria, is not a resident species and is not considered further.

When compared to Oregon's chronic criterion for chromium III, estimated SMCV values for two
test species (an insect, and an amphipod) were lower than the chronic criterion concentration of

-------
74 |ig/L dissolved chromium III. Experimental test data for Daphnia magna was also lower than
the criterion. Of these species, only the planktonic crustaceans Daphnia magna andpulex and the
amphipod Gammarus sp. are expected to reside in Oregon waters. Therefore, EPA reviewed the
data from the studies that make up the most representative data for each of the these species.

The SMCV for D. pulex was estimated by applying the ACR of 25.20 described above to the
SMAV obtained from Stackhouse and Benson (1989). Since additional information or
confidence intervals were reported in the study, the SMCV for comparison with the CCC for
chromium III is 53.70 |ig/L. Because the Oregon chronic criterion for dissolved chromium III is
greater than SMCV for D. pulex, EPA concludes that the Oregon CCC for chromium III is not
protective of all individuals within this species.

The SMCV for D. magna was calculated as the geometric mean of the measured NOECs and
LOECs for growth rate reported for three tests performed at different water hardness levels by
Chapman et al. (1980) to obtain a hardness normalized dissolved SMCV of 69.71 |ig/L. It is
worth noting that the NOEC for the chronic test performed at a water hardness of 206 mg/L as
CaC03 was the control treatment, as the lowest test concentration significantly affected daphnid
growth over the exposure. Using the LOEC as the chronic value for this test, the resultant LOEC
at this hardness level (206 mg/L as CaCOs) is less than 20.94 |ig/L. This surrogate chronic value
was used along with the two other chronic values obtained from chronic tests conducted at water
hardness levels of 52 and 100 mg/L as CaC03, respectively, to obtain a geometric mean across
the three tests of 69.71 |ig/L (see text box A -D. magna). The geometric mean of the LOECs of
the three tests was 89.46 |ig/L, which is above the criterion. Because the geometric mean of the
LOEC values surrounding the SMCV for D. magna is greater than the Oregon chronic criterion
for chromium III, EPA concludes that the Oregon CCC for chromium III is protective of this
species.

The SMCV for Gammarus sp. was estimated by applying the ACR of 25.20 described above to
the SMAV from table 3.1.3-1. Since no additional information or confidence intervals were
reported in the study, the SMCV of 70.79 ug/L was directly compared with the CCC for
chromium III. Because the Oregon CCC for dissolved chromium III is greater than SMCV for
for Gammarus sp., EPA concludes that the Oregon CCC for chromium III is not protective of all
individuals within this species. As noted above, 17 of 19 genera had GMCVs greater than the
chronic criterion so that chronic effects are not expected to occur at concentrations equal to or
lower than the criterion concentration for these genera, and all except a small proportion of
genera are protected at ambient concentrations equal to or lower than the chronic criterion value
for chromium III. Thus the Oregon criterion concentration for chromium III is expected to
protect the aquatic life designated use.

Freshwater chromium III chronic criterion comparison

Text Box A - Basis for the meta analysis comparing the SMCV for the cladoceran (D. magna) to
the chronic criterion for chromium III (74 |ig/L dissolved metal concentration normalized to a
hardness of 100 mg/L as CaCOs).

-------
Daphnia magna

Reported Values:

Normalized Dissolved Chronic Values:

Hardness

NOEC

LOEC

NOEC

LOEC

CV CCC

66.11

69.05

136.6

97.13 74

100

129

291

193.7

110.9

250.3

166.6

206

20.94

SMCV

Geomean

106.0

82.60

89.46

69.71

2.1.3.3 References for Chromium III

A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the acute and chronic tables, and are the source from which EPA
obtained SMAVs (acute table) and experimentally-derived SMCVs (chronic table).

Reference No.

Used Reference Citation

(associated with reference numbers and provided above in Tables 2.1.3-1 and 2.1.3-2)

Acute References

Warnick, S. L. and H.L. Bell. 1969. The acute toxicity of some heavy metals to different species of aquatic
insects. J. Water Pollut. Control Fed. 41(2): 280-284.

Stackhouse, R.A. and W.H. Benson. 1989. The effect of humic acid on the toxicity and bioavailability of trivalent
chromium. Ecotoxicol. Environ. Saf. 17(1): 105-111.

Rehwoldt, R., L. Lasko, C. Shaw and E. Wirhowski. 1973. The acute toxicity of some heavy metal ions toward
benthic organisms. Bull. Environ. Contam. Toxicol. 10(5): 291-294.

Pickering, Q. H. and C. Henderson. 1964. The acute toxicity of some heavy metals to different species of
warmwater fishes. Proc. 19th Ind. Waste Conf., Purdue University, West Lafayette, IN: 578-591; Air Water Pollut.
Int. J. 10: 453-463 (1966) (Author Communication Used).

Stevens, D. G. and G.A. Chapman. 1984. Toxicity of trivalent chromium to early life stages of steelhead trout.
Environ. Toxicol. Chem. 3(1): 125-133.

Guilhermino, L., T.C. Diamantion, R. Ribeiro, F. Goncalves and A. Soares. 1997. Suitability of test media
containing EDTA for the evaluation of acute metal toxicity to Daphnia magna Straus. Ecotoxicol. Environ. Saf.
38(3): 292-295.

Chapman, G.A., S. Ota and F. Recht. 1980. Effects of water hardness on the toxicity of metals to Daphnia
maqna. Manuscript. U.S. EPA, Corvallis, OR.

Pickering, Q. H. 1980. Chronic toxicity of trivalent chromium to the fathead minnow (Pimephaies promeias) in
hard water. Manuscript, U.S. EPA, Cincinnati, OH.

Rehwoldt, R., L.W. Menapace, B. Nerrie and D. Allessandrello. 1972. The effect of increased temperature upon
the acute toxicity of some heavy metal ions. Bull. Environ. Contam. Toxicol. 8(2): 91-96.

Virk, S. and R.C. Sharma. 1995. Effect of nickel and chromium on various life stages of Cyprinus carpio Linn.
Indian J. Ecol. 22(2):77-81.

Martin, T.R. and D.M. Holdich. 1986. The acute lethal toxicity of heavy metals to peracarid crustaceans (with
particular reference to fresh-water asellids and gammarids). Wat. Res. 20(9): 1137-1147.

Chronic References

Chapman, G. A., S. Ota and F. Recht. 1980. Effects of water hardness on the toxicity of metals to Daphnia
maqna. Manuscript. U.S. EPA, Corvallis, OR.

Stevens, D. G. and G.A. Chapman. 1984. Toxicity of trivalent chromium to early life stages of steelhead trout.
Environ. Toxicol. Chem. 3(1):125-133.

Pickering, Q. H. 1980. Chronic toxicity of trivalent chromium to the fathead minnow (Pimephaies promeias) in
hard water. Manuscript, U.S. EPA, Cincinnati, OH.

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B. Studies That EPA Considered But Did Not Utilize In This Determination

1) For the studies that were not utilized, but the most representative SMAV/2 or
most representative SMCV fell below the criterion, or, if the studies were for a
species associated with one of the four most sensitive genera used to calculate the
FAV in the most recent national ambient water quality criteria dataset used to
derive the CMC13, EPA is providing a transparent rationale as to why they were
not utilized (see below).

2) For the studies that were not utilized because they were not found to be pertinent
to this determination (including failing the QA/QC procedures listed in Appendix
A) upon initial review of the download from ECOTOX, EPA is providing the
code that identifies why EPA determined that the results of the study were not
reliable.

13 U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient
Water. EPA-820-B-96-001.

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CHROMIUM VI

2.1.3.4 Evaluation of the Acute Freshwater Criterion Concentration for Chromium VI
A. Presentation of Toxicological Data

Oregon adopted a freshwater acute criterion with a magnitude of 16 |ig/L that is expressed in
terms of the dissolved concentration of the metal in the water column. This dissolved metal
concentration is the same as the freshwater CMC recommended for use nationally by EPA for
the protection of aquatic life14. EPA developed the recommended criterion in accordance with
the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.1.4-1 provides available SMAVs and GMAVs based on available acute toxicity data for
chromium VI to aquatic life from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Tables 2.1.4-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values
(GMAVs) for Chromium VI

Genus

Species

Common name

Most
Representative
SMAV
(ng/L)

GMAV
(ng/L)

Acute References

(used in the calculation of
the SMAV)

Agnetina

capitata

Stonefly

1836340

Cyprinus

carpio

common carp

176899

44,45

Orconectes

rusticus

Crayfish

172832

Thymallus

arcticus

Arctic grayling

166071

Enallagma

aspersum

Damselfly

137480

Lepomis

macrochirus

Bluegill

131281

Lepomis

cyanellus

Green sunfish

112637

121602

Carassius

auratus

Goldfish

117371

Clioperla

clio

Stonefly

101525

Oncorhynchus

tshawytscha

Chinook salmon

124152

Oncorhynchus

kisutch

Coho salmon

101381

Oncorhynchus

mykiss

Rainbow trout

67758

94832

Gila

elegans

Bonytail

90130

Ptychocheilus

lucius

Colorado sguawfish

88478

Luxilus

chrysocephalus

Striped shiner

84059

Pomoxis

annularis

White crappie

71293

Salvelinus

fontinalis

Brook trout

57938

Tanytarsus

dissimilis

Midge

56269

Notropis

stramineus

Sand shiner

73257

Notropis

buccatus

Silverjaw minnow

48707

Notropis

atherinoides

Emerald shiner

47529

55352

Notemigonus

crysoleucas

Golden shiner

54010

Campostoma

anomalum

Central stoneroller

50328

Xyrauchen

texanus

Razorback sucker

46477

Pimephales

notatus

Bluntnose minnow

53249

Pimephales

promelas

Fathead minnow

40394

46378

8,29,30,31,32,33

Poecilia

reticulata

Guppy

45681

34,35,36

Etheostoma

nigrum

Johnny darter

45172

14 See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.

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Genus

Species

Common name

Most
Representative
SMAV
(MS)"-)

GMAV
(MS)"-)

Acute References

(used in the calculation of
the SMAV)

Perca

flavescens

Yellow perch

35647

Gasterosteus

aculeatus

Threespine
stickleback

35528

26,27

Morone

saxatilis

Striped bass

34966

24,25

Physa

heterostropha

Snail

22596

22,23

Ictalurus

punctatus

Channel catfish

14534

Dugesia

tigrina

Planarian

12679

Chironomus

tentans

Midge

11588

Helisoma

trivolvis

Ramshorn snail

10802

Lumbriculus

variegatus

Oligochaete

10802

Asellus

intermedius

Aquatic sowbug

5205

Lymnaea

luteola

Pond snail

3810

Tubifex

tubifex

Tubificid worm

2946

13,14,15,16,17,18

Lophopodella

carteri

Bryozoan

1532

Pectinatella

magnifica

Bryozoan

1414

Plumatella

emarginata

Bryozoan

638.3

Hyalella

azteca

619.0

Crangonyx

pseudogracilis

Amphipod

572.5

Moina

macrocopa

Cladoceran

353.5

Gammarus

fasciatus

Scud

108.0

Gammarus

oseudolimnaeus*

Amphipod

65.89

84.37

Ceriodaphnia

dubia

Cladoceran

141.4

Ceriodaphnia

reticulata

Cladoceran

44.29

79.14

1,2

Caenorhabditis

elegans

Nematode

58.92

Daohnia

obtusa*

Cladoceran

116.3

6,7

Daphnia

pulex

Cladoceran

35.65

Daphnia

magna

Cladoceran

22.65

45.46

1,2

Simocephalus

serrulatus

Cladoceran

40.16

Simocephalus

vetulus

Cladoceran

31.72

35.69

B. Evaluation of the Protectiveness of the Oregon Freshwater Acute Criterion

Following review of GMAV values in Table 2.1.4-1, all tested genera are protected by Oregon's
acute criterion magnitude for chromium VI. Therefore, EPA concluded that acute effects to these
genera are not expected to occur at ambient concentrations equal to or lower than the criterion
and thus these species would be protected.

When compared to Oregon's acute criterion for chromium VI, SMAV/2 values for the two most
sensitive test species (both planktonic cladocerans) of the 56 species tested are near the acute
criterion concentration of 16 |ig/L dissolved chromium VI, therefore were low enough to warrant
further consideration. These two cladoceran species, Daphnia magna and Simocephalus vetulus,
are both expected to reside in Oregon waters. Therefore, EPA reviewed the data from the studies
that comprise the most representative SMAV for D. magna and S. vetulus and compared the
confidence intervals of the SMAV for these species to determine whether the values are
quantitatively less than the criterion value of 16 |ig/L.

-------
The SMAV for D. magna was 22.65 |ig/L with no 5 or 95 percent confidence intervals reported
for either test (Mount 1982; Mount and Norberg 1984).

The SMAV for S. vetulus was 31.72 |ig/L with no 5 or 95 percent confidence intervals reported
(Mount 1982).

Due to the lack of additional supporting information or confidence intervals for these species,
EPA opted to assume that the process by which the GMAV is compared to a level at which the
test is indifferentiabe from controls (eg, GMAV/2) may also apply to the SMAV.

Because the Oregon acute criterion for chromium VI is greater than the estimate of SMAV/2 for
D. magna, EPA concludes that the occurrence of ambient concentrations of chromium VI at or
above the Oregon CMC for could result in acute toxicity to some individuals of this species.
Because the Oregon acute criterion for chromium VI is equivalent to the estimate of SMAV/2 for
S. vetulus, EPA concludes that the Oregon CMC for chromium VI is protective of this species.
As noted above, the Oregon criterion is protective of all tested organisms at the genus level, and
thus would be expected to be protective of the aquatic life designated use.

2.1.3.5 Evaluation of the Chronic Freshwater Criterion Concentration for Chromium VI
A. Presentation of Toxicological Data

Oregon adopted a freshwater chronic criterion concentration of 11 |ig/L for chromium VI
similarly expressed as the dissolved metal concentration in the water column. This concentration
is the same as the freshwater CCC recommended for use nationally by EPA for the protection of
aquatic life developed in accordance with the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.1.4-2 presents a compilation of the GMAVs from Table 2.1.4-1, any experimentally
determined SMCVs obtained from the criteria document and EPA ECOTOX download used for
the BE, and estimated GMCVs based on the GMAV/ACR. The 1984 criteria document for
chromium reported an FACR of 2.917, which is the geometric mean value of four experimentally
determined ACRs of 1.130, 2.055, 5.920, and 5.267 for four cladocerans: Ceriodaphnia
reticulata, Simocephalus serrulatus, Daphniapulex, and S. vetulus, respectively. EPA
determined that these four ACRs from the acutely sensitive cladocerans were the most
appropriate ACRs to protect sensitive species in general. One other ACR of 6.957 for D. magna
was excluded because it represented a greater than ">" value, and three other ACRs of 18.55,
223.0, and 260.8, respectively, from insensitive fish species were also excluded. Thus, since no
additional acceptable ACRs are available, EPA calculated the predicted GMCVs for chromium
in Table 2.1.4-2 using an FACR of 2.917 and the following equation: Predicted GMCV =
GMAV/FACR.

EPA compared the GMCVs for each species to Oregon's chromium VI chronic criterion to
determine whether the chronic criterion is protective of the aquatic life designated use.

-------
Table 2.1.4-2: Genus Mean (

hronic Values (GMCVs) for Chromium VI

Genus

Species

Common name

GMAV
(Mg/L)

SMCV

(Mg/L)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(MS)"-)

Agnetina

capitata

Stonefly

1836340

629530

Cyprinus

carpio

common carp

176899

60644

Orconectes

rusticus

Crayfish

172832

59250

Thymallus

arcticus

Arctic grayling

166071

56932

Enallagma

aspersum

Damselfly

137480

47131

Lepomis

macrochirus

Bluegill

Lepomis

cyanellus

Green sunfish

121602

41687

Carassius

auratus

Goldfish

117371

40237

Clioperla

clio

Stonefly

101525

34805

Oncorhynchus

tshawytscha

Chinook salmon

Oncorhynchus

kisutch

Coho salmon

Oncorhynchus

mykiss

Rainbow trout

94832

133.9

32510
(133.9)

Gila

elegans

Bonytail

90130

30898

Ptychocheilus

lucius

Colorado
squawfish

88478

30332

Luxilus

chrysocephalus

Striped shiner

84059

28817

Pomoxis

annularis

White crappie

71293

24441

Salvelinus

fontinalis

Brook trout

57938

254.5

19862
(254.5)

Tanytarsus

dissimilis

Midge

56269

19290

Notropis

stramineus

Sand shiner

Notropis

buccatus

Silverjaw
minnow

Notropis

atherinoides

Emerald shiner

55352

18976

Notemigonus

crysoleucas

Golden shiner

54010

18516

Campostoma

anomalum

Central
stoneroller

50328

17253

Xyrauchen

texanus

Razorback
sucker

46477

15933

Pimephales

notatus

Bluntnose
minnow

Pimephales

promelas

Fathead minnow

46378

1864

4,5,6

15899
(1864)

Poecilia

reticulata

Guppy

45681

15660

Etheostoma

nigrum

Johnny darter

45172

15486

Perca

flavescens

Yellow perch

35647

12220

Gasterosteus

aculeatus

Threespine
stickleback

35528

12180

Morone

saxatilis

Striped bass

34966

11987

Physa

heterostropha

Snail

22596

7746

Ictalurus

punctatus

Channel catfish

14534

4982

Dugesia

tigrina

Planarian

12679

4347

Chironomus

tentans

Midge

11588

3972

Helisoma

trivolvis

Ramshorn snail

10802

3703

Lumbriculus

variegatus

Oligochaete

10802

3703

Asellus

intermedius

Aquatic sowbug

5205

1784

Lymnaea

luteola

Pond snail

3810

1306

Tubifex

tubifex

Tubificid worm

2946

1010

Lophopodella

carteri

Bryozoan

1532

525.2

Pectinatella

magnifica

Bryozoan

1414

484.8

Plumatella

emarginata

Bryozoan

638.3

218.8

Hyalella

azteca

619.0

212.2

Crangonyx

pseudogracilis

Amphipod

572.5

196.3

Moina

macrocopa

Cladoceran

353.5

121.2

Gammarus

fasciatus

Scud

-------
Genus

Species

Common name

GMAV
(MQ/L)

SMCV
(MQ/L)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(Mfl/L)

Gammarus

oseudolimnaeus*

Amphipod

84.37

28.92

Ceriodaphnia

dubia

Cladoceran

Ceriodaphnia

reticulata

Cladoceran

79.14

38.48

27.13
(38.48)

Caenorhabditis

elegans

Nematode

58.92

20.20

Daohnia

obtusa*

Cladoceran

Daphnia

pulex

Cladoceran

5.899

Daphnia

magna

Cladoceran

45.46

<4.810

1,2

15.58
(5.327)

Simocephalus

serrulatus

Cladoceran

19.14

Simocephalus

vetulus

Cladoceran

35.69

5.899

12.24
(10.63)

See same notes as above under Table 2.1.4-1.

B. Evaluation of the Protectiveness of the Oregon Freshwater Chronic Criterion

Following the review of the GMCV values in Table 2.1.4-2, all genera should be protected at or
below the criterion concentration because all GMCVs are greater than the criterion. The
majority of species had experimentally determined SMCVs greater than Oregon's chronic
criterion for chromium VI. Therefore, EPA concluded that chronic effects are not expected to
occur at concentrations lower than the criterion for these species and thus these species would be
protected.

When compared to Oregon's chronic criterion for chromium VI, SMCV values for three test
species (all planktonic cladocerans - D. magna, S. vetulus, and D. pulex) were lower than the
CCC of 11 |ig/L dissolved chromium VI. All of these species are expected to reside in Oregon
waters. Therefore, EPA reviewed the data from the studies that make up the SMCVs for this
species and compared the confidence intervals of these SMCVs to determine whether the SMCV
values were quantitatively different from the criterion value of 11 |ig/L.

The SMCV for D. magna was calculated as the geometric mean of the measured LOECs for
reproduction reported by Mount (1982) and Mount and Norberg (1984) to obtain the dissolved
SMCV of 4.810 |ig/L (text box A -D. magna chronic). For both tests, the NOEC was the
control treatment; therefore, the respective LOECs for the tests were used as estimated chronic
values to calculate the SMCV for the species. The geometric mean of the CVs for the two tests
(4.810 |ig/L) is lower than the CCC for chromium VI of 11 |ig/L.

The SMCV for S. vetulus was calculated as the geometric mean of the measured NOEC and
LOEC for reproduction reported by Mount (1982) to obtain a SMCV of 5.899 |ig/L (text box B -
D. magna chronic). The LOEC for this test of 7.700 |ig/L is below the CCC for chromium VI of
11 Hg/L.

The SMCV for D. pulex was calculated as the geometric mean of the measured NOEC and
LOEC for reproduction reported by Mount (1982) to obtain a SMCV of 5.899 |ig/L (text box C -

-------
D. pulex chronic). The LOEC for this test of 7.700 |ig/L is lower than the CCC for chromium VI
of 11 |ig/L.

Because the measured LOEC values for I), magna, S. vetulus, and D. pulex are lower than the
Oregon chronic criterion for dissolved chromium VI, EPA concludes that the sustained
occurrence (greater than four days exposure) of ambient concentrations at or above the Oregon
CCC for chromium VI could result in chronic effects to these three planktonic crustacean
species. As noted above, the Oregon criterion is protective of all tested organisms at the genus
level, and thus would be expected to be protective of the aquatic life designated use

Freshwater chromium VI chronic criterion comparison

Text Box A (chronic) - Basis for the meta analysis comparing the SMCV for the cladoceran (D.
pulex) to the chronic criterion for chromium VI (11 |ig/L dissolved metal concentration).

Dapnia magna

Reported Chronic Values

Dissolved Chronic Values

Hardness

NOEC

LOEC

NOEC

LOEC

CCC

45.0

2.500

0.000

2.410

45.0

10.00

0.000

9.620

SMCV

Geomean

5.000

0.000

4.810

Notes: Because NOEC

=0, CV reported as the LOEC.

Final SMCV reported was

the geometric mean of the LOEC of the two studies.

Text Box B (chronic) - Basis for the meta analysis comparing the SMCV for the cladoceran (S.
vetulus) to the chronic criterion for chromium VI (11 |ig/L dissolved metal concentration).

Simocephalus vetulus

Reported Chronic Values Dissolved Chronic Values

Hardness NOEC LOEC SMCV NOEC LOEC SMCV CCC

45.0 4.7 8 6.132 4.520 7.700 5.899 11

Text Box C (chronic) - Basis for the meta analysis comparing the SMCV for the cladoceran (D.
pulex) to the chronic criterion for chromium VI (11 |ig/L dissolved metal concentration).

Dapnia pulex

Reported Chronic Values

Dissolved Chronic Values

Hardness NOEC LOEC SMCV

NOEC LOEC SMCV

CCC

45.0 4.7 8 6.132

4.520 7.700 5.899

-------
2.1.3.6 References for Chromium VI

A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the acute and chronic tables, and are the source from which EPA
obtained SMAVs (acute table) and experimentally-derived SMCVs (chronic table).

Reference No.

Used Reference Citation

(associated with reference numbers and provided above inTables 2.1.4-1 and 2.1.4-2)

Acute References

Mount, D.I. 1982. Memorandum to Charles E. Stephan. U.S. EPA, Duluth, MN. June 7.

Mount, D.I. and T.J. Norberg. 1984. A seven-day life-cycle cladoceran toxicity test. Environ. Toxicol. Chem.
3: 425.

Williams, P.L. and D.B. Dusenbery. 1990. Aquatic toxicity testing using the nematode, Caenorhabditis
elegans. Environ. Toxicol. Chem. 9(10): 1285-1290.

Call, D.J., L.T. Brooke, N. Ahmad and J.E. Richter. 1983. Toxicity and metabolism studies with EPA priority
pollutants and related chemicals in freshwater organisms. PB83-263665. National Technical Information
Service, Springfield, VA.

Ewell, W.S., J.W. Gorsuch, R.O. Kringle, K.A. Robillard and R.C. Spiegel. 1986. Simultaneous evaluation of
the acute effects of chemicals on seven aquatic species. Environ. Toxicol. Chem. 5(9): 831-840.

Rossini, G.D.B. and A.E. Ronco. 1996. Acute toxicity bioassay using Daphnia obtusa as a test organism.
Environ. Toxicol. Water Qual. 11(3): 255-258.

Coniglio, L. and R. Baudo. 1989. Life-tables of Daphnia obtusa (Kurz) surviving exposure to toxic
concentrations of chromium. Hydrobiologia 188/189: 407-410.

Spehar, R.L. and J.T. Fiandt. 1986. Acute and chronic effects of water quality criteria-based metal mixtures
on three aquatic species. Environ. Toxicol. Chem. 5(10): 917-931.

Wong, C.K. 1992. Effects of chromium, copper, nickel, and zinc on survival and feeding of the cladoceran
Moina macrocopa. Bull. Environ. Contam. Toxicol. 49: 593-599.

Martin, T.R. and D.M. Holdich. 1986. The acute lethal toxicity of heavy metals to peracarid crustaceans (with
particular reference to fresh-water asellids and gammarids). Water Res. 20(9): 1137-1147.

Call, D.J., L.T. Brooke, N. Ahmad and D.D. Vaishnav. 1981. Aquatic Pollutant Hazard Assessments and
Development of a Hazard Prediction Technology by Quantitative Structure-activity Relationships. Second
Quarterly Report to EPA. Center for Lake Superior Environmental Studies, University of Wisconsin-Superior,
Superior, Wl: 74 p.

Pardue. W.J. and T.S. Wood. 1980. Baseline toxicity data for freshwater bryozoa exposed to copper,
cadmium, chromium, and zinc. J. Tenn. Acad. Sci. 55:27.

Khangarot, B.S. 1991. Toxicity of metals to a freshwater tubificid worm, Tubifex tubifex (Muller). Bull.
Environ. Contam. Toxicol. 46: 906-912.

Fargasova, A. 1994. Toxicity of metals on Daphnia magna and Tubifex tubifex. Ecotoxicol. Environ. Saf.
27(2): 210-213.

Fargasova, A. 1994. Comparative toxicity of five metals on various biological subjects. Bull. Environ.
Contam. Toxicol. 53(2): 317-324.

Fargasova, A. 1999. Ecotoxicology of metals related to freshwater benthos. Gen. Physio. Biophys. 18: 48-
53.

Rathore, R.S. and B.S. Khangarot. 2002. Effects of temperature on the sensitivity of sludge worm Tubifex
tubifex Muller to selected heavy metals. Ecotoxicol. Environ. Saf. 53(1):27-36.

Reynoldson, T.B., P. Rodriguez and M.M. Madrid. 1996. A comparison of reproduction, growth and acute
toxicity in two populations of Tubifex tubifex (Muller, 1774) from the North American Great Lakes and
Northern Spain. Hydrobiologia 334(1-3): 199-206.

Khangarot, B.S. and P.K. Ray. 1988. Sensitivity of freshwater pulmonate snails, Lymnaea iuteoia L., to
heavy metals. Bull. Environ. Contam. Toxicol. 41(2): 208-213.

Khangarot, B.S. and P.K. Ray. 1989. Sensitivity of midge larvae of Chironomus tentans Fabricius (Diptera
Chironomidae) to heavy metals. Bull. Environ. Contam. Toxicol. 42(3): 325-330.

Gendusa, T.C., T.L. Beitinger and J.H. Rodgers. 1993. Toxicity of hexavalent chromium from aqueous and
sediment dources to Pimephaies promeias and Ictaiurus punctatus. Bull. Environ. Contam. Toxicol. 50(1):
144-151.

Academy of Natural Sciences. 1960. The Sensitivity of Aquatic Life to Certain Chemicals Commonly Found
in Industrial Wastes. Philadelphia, PA.

Patrick, R., J. Cairns, Jr. and A. Scheier. 1968. The relative sensitivity of diatoms, snails, and fish to twenty
common constituents of industrial wastes. Prog. Fish-Cult. 30: 137-140.

-------
Reference No.

Used Reference Citation

(associated with reference numbers and provided above inTables 2.1.4-1 and 2.1.4-2)

Palawski, D., J.B. Hunn and F.J. Dwyer. 1985. Sensitivity of young striped bass to organic and inorganic
contaminants in fresh and saline waters. Trans. Am. Fish. Soc. 114: 748-753.

Hughes, J.S. 1973. Acute toxicity of thirty chemicals to striped bass (Morone saxatilis). Presented at the
Western Association of State Game and Fish Commissioners, Salt Lake city, Utah. July.

Van den Dikkenberg, R.P., H.H. Canton, L.A.M. Mathijssen-Spiekman and C.J. Roghair. 1989. The
Usefulness of Gasterosteus aculeatus - the Three-Spined Stickleback - as a Test Organism in Routine
Toxicity Testing. Rep. No. 718625003, Natl. Inst. Public Health E

Jop, K.M., T.F. Parkerton, J.H. Rodgers Jr., K.L. Dickson and P.B. Dorn. 1987. Comparative toxicity and
speciation of two hexavalent chromium salts in acute toxicity tests. Environ. Toxicol. Chem. 6(9): 697-703.

White, A.M. Manuscript. The Toxicity of Hexavalent Chromium (Cr+b) to Twenty-one Species of Aquatic
Animals Native to Ohio. John Carroll University, University Heights, OH.

Adelman, I.R. and L.L. Smith, Jr. 1976. Standard Test Fish Development. Part 1. Fathead Minnows
(.Pimephales promelas) and Goldfish (Carassius auratus) as Standard Fish in Bioassays and Their Reaction
to Potential Reference Toxicants. EPA-600/3-76-061a, Duluth, MN.

Broderius, S.J. and L.L. Smith, Jr. 1979. Lethal and sublethal effects of binary mixtures of cyanide and
hexavalent chromium, zinc, or ammonia to the fathead minnow (Pimephales promelas) and rainbow trout
(Salmo qairdneri). Jour. Fish. Res. Board Can.

Pickering, Q.H. 1980. Chronic toxicity of hexavalent chromium to the fathead minnow (Pimephales
promelas). Arch. Environ. Contam. Toxicol. 9: 405.

Ruesink, R.G. and L.L. Smith, Jr. 1975. The relationship of the 96-hour LC50 to the lethal threshold
concentration of hexavalent chromium, phenol and sodium pentachlorophenate for fathead minnows
(Pimephales promelas Rafinesque). Trans. Am. Fish. Soc. 3: 567.

Waheda, M.F. 1977. Effect of Size of Fathead Minnows (Pimephales promelas) and Green Sunfish
(.Lepomis cyanellus) on Hexavalent Chromium Toxicity. Thesis. Wright State University, Dayton, OH.

Khangarot, B.S. and P.K. Ray. 1990. Acute toxicity and toxic interaction of chromium and nickel to common
guppy Poecilia reticulata (Peters). Bull. Environ. Contam. Toxicol. 44(6): 832-839.

Oliveira-Filho, E.C. and F.J.R. Paumgartten. 1997. Comparative study on the acute toxicities of alpha, beta,
gamma, and delta isomers of hexachlorocyclohexane to freshwater fishes. Bull. Environ. Contam. Toxicol.
59(6): 984-988.

Pickering, Q.H. and C. Henderson. 1966. The acute toxicity of some heavy metals to different species of
warmwater fishes. Air Water Pollut. Int. J. 10: 453.

Buhl, K.J. 1997. Relative sensitivity of three endangered fishes, Colorado squawfish, bonytail, and razorback
sucker, to selected metal pollutants. Ecotoxico. Environ. Saf. 37: 186-92

Hartwell, S.I., J.H. Jin, D.S. Cherry and J. Cairns Jr. 1989. Toxicity versus avoidance response of golden
shiner, Notemigonus crysoleucas, to five metals. J. Fish Biol. 35(3): 447-456.

Benoit, D.A. 1976. Toxic effects of hexavalent chromium on brook trout (Salvelinus fontinalis) and rainbow
trout (Salmo gairdneri). Water Res. 10:497.

Buhl, K.J. and S.J. Hamilton. 1991. Relative sensitivity of early life stages of Arctic grayling, Coho salmon,
and rainbow trout to nine inorganics. Ecotoxicol. Environ. Saf. 22: 184-197.

Poulton, B.C., T.L. Beitingerand K.W. Stewart. 1989. The effect of hexavalent chromium on the critical
thermal maximum and body burden of Clioperla clio (Plecoptera: Perlodidae). Arch. Environ. Contam.
Toxicol. 18(4): 594-600.

Hamilton, S.J. and K.J. Buhl. 1990. Safety assessment of selected inorganic elements to fry of Chinook
salmon (Oncorhynchus tshawytscha). Ecotoxicol. Environ. Saf. 20(3): 307-324.

Cairns, J., Jr., K. W. Thompson and A. C. Hendricks. 1981. Effects of Fluctuating Sublethal Applications of
Heavy Metal Solutions upon the Gill Ventilatory Response of Bluegills (Lepomis macrochirus). National
Technical Information Service, Springfield, VA. PB81-150 997. 90 pp.

Al-Akel, A.S. 1996. Chromium toxicity and its impact on behavioural responses in freshwater carp, Cyprinus
carpio, from Saudi Arabia. Pakistan J. Zool. 28: 361-363.

Thatheyus, A.J. 1992. Behavioral alterations induced by nickel and chromium in common carp Cyprinus
carpio var communis (Linn). Environ. Ecol. 10(4): 911-913.

Chronic References

Trabalka, J.R. and C.W. Gehrs. 1977. An observation on the toxicity of hexavalent chromium to Daphnia
magna. Toxicol. Letters 1: 131.

Mount, D.I. 1982. Memorandum to Charles E. Stephan. U.S. EPA, Duluth, Minnesota. June 7.

Benoit, D.A. 1976. Toxic effects of hexavalent chromium on brook trout (Salvelinus fontinalis) and rainbow
trout (Salmo gairdneri). Water Res. 10: 497.

Barron, M.G. and I.R. Adelman. 1984. Nucleic acid, protein content, and growth of larval fish sublethally
exposed to various toxicants. Can. J. Fish. Aquat. Sci. 41(1): 141-150.

Spehar, R.L. and J.T. Fiandt. 1986. Acute and chronic effects of water quality criteria-based metal mixtures
on three aquatic species. Environ. Toxicol. Chem. 5(10): 917-931.

Pickering, Q.H. 1980. Chronic toxicity of hexavalent chromium to the fathead minnow (Pimephales
promelas). Arch. Environ. Contam. Toxicol. 9:405.

-------
B. Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this
determination, either because they were not pertinent to this determination or they failed the
QA/QC procedures listed in Appendix A.

1) For the studies that were not utilized, but the most representative GMAV/2 or
most representative SMCV fell below the criterion, or, if the studies were for a
species associated with one of the four most sensitive genera used to calculate the
FAV in the most recent national ambient water quality criteria dataset used to
derive the CMC, EPA is providing a transparent rationale as to why they were not
utilized (see below).

-------
2.1.4 COPPER

Please see the primary decision document regarding the disapproval of this criterion.

-------
2.1.5 DIELDRIN

2.1.5.1 Evaluation of the Acute Freshwater Criterion Concentration for Dieldrin
A. Presentation of Toxicological Data

Oregon adopted a freshwater acute criterion with a magnitude of 0.24 |ig/L for dieldrin. This
concentration is the same as the freshwater CMC recommended for use nationally by EPA for
the protection of aquatic life15. EPA developed the recommended criterion in accordance with
the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.1.6-1 provides available SMAVs based on available acute toxicity data for dieldrin to
aquatic life from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Table 2.1.6-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values
(GMAVs) for Dieldrin

Acute

Most

References

Representative
SMAV

GMAV

(used in the
calculation of the

Genus

Species

Common name

(MS)"-)

(Mg/L)

SMAV)

Orconectes

nais

Crayfish

740.0

Chironomus

tentans

Midge

560.0

Gammarus

fasciatus

Scud

620.0

Gammarus

lacustris

Scud

460.0

534.0

Simocephalus

serrulatus

Cladoceran

214.0

Bufo

woodhousei

Fowler's toad

150.0

Daphnia

pulex

Cladoceran

228.0

14,15

Daphnia

magna

Cladoceran

81.40

136.2

Pseudacris

triseriata

Western chorus frog

100.0

Gambusia

affinis

Western mosquitofish

31.00

Lumbriculus

variegatus

Oligochaete, worm

21.80

Palaemonetes

kadiakensis

Grass shrimp, freshwater prawn

20.00

Pimephales

promelas

Fathead minnow

17.70

1,3,9

Ischnura

verticalis

Damselfly

12.00

Ameiurus

melas

Black bullhead

10.00

Oreochromis

mossambica

Mozambique tilapia

10.00

Lepomis

macrochirus

Bluegill

11.50

1,3,4,9,11

Lepomis

cyanellus

Green sunfish

8.082

Lepomis

gibbosus

Pumpkinseed

6.700

8.539

Poecilia

reticulata*

Guppy

5.500

Asellus

brevicaudus*

Isopod

5.000

Carassius

auratus

Goldfish

4.906

1,3

Ictalurus

punctatus

Channel catfish

4.500

Oncorhynchus

kisutch

Coho salmon

10.80

Oncorhynchus

clarki

Cutthroat trout

6.197

1,7

Oncorhynchus

tshawytscha

Chinook salmon

6.100

Oncorhynchus

my kiss

Rainbow trout

0.6200

3.989

Micropterus

salmoides

Largemouth bass

3.500

C/aassen/'a

sabulosa*

Stonefly

0.5800

15 See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.

The data which serve as the basis for the current nationally-recommended criteria are from the 1995 Great Lakes Initiative Updates to these
criteria as cited in: U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient Water.
EPA-820-B-96-001.

-------

Acute

Most

References

Representative
SMAV

GMAV

(used in the
calculation of the

Genus

Species

Common name

(MS)"-)

(MQ/L)

SMAV)

Pteronarcella

badia

Stonefly

0.5000

Pteronarcys

californicus

Stonefly

0.5000

B. Evaluation of the Protectiveness of the Oregon Freshwater Acute Criterion

Following review of GMAV values in Table 2.1.6-1, all genera and species had values
significantly greater than Oregon's acute criterion concentration for dieldrin. Therefore, EPA
concluded that acute effects to these species and genera are not expected to occur at
concentrations equal to or lower than the acute criterion and thus the aquatic life designated use
would be protected.

2.1.5.2 Evaluation of the Chronic Freshwater Criterion Concentration for Dieldrin
A. Presentation of Toxicological Data

Oregon adopted a freshwater chronic criterion with a concentration of 0.056 |ig/L for dieldrin.
This concentration is the same as the freshwater CCC recommended for use nationally by EPA
for the protection of aquatic life. EPA developed the recommended criterion in accordance with
the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.1.6-2 presents a compilation of the GMAVs from Table 2.1.6-1, any experimentally
determined SMCVs obtained from the criteria document and EPA ECOTOX literature download
used for the BE, and estimated GMCVs based on the GMAV/ACR. The 1980 criteria document
for dieldrin16 reported an FACR of 8.530, which EPA calculated as the geometric mean of three
experimentally determined ACRs ranging from 6.2 for an acutely sensitive saltwater
invertebrate, the mysid (Americamysis bahia) to 11.0 for an acutely sensitive fish, rainbow trout
(Onchorhynchus mykiss). EPA determined the FACR of 8.530 with the ACRs from two
freshwater species (Poecilia reticulata, rainbow trout) and one saltwater species {Americamysis
bahia). Since no additional acceptable ACRs are available, EPA calculated the predicted
GMCVs for dieldrin in Table 2.1.6-2 using the FACR of 8.530 and the following equation:
Predicted GMCV = GMAV/FACR.

16 U.S. EPA. 1980. Ambient Water Quality Criteria Document for Aldrin/Dieldrin. EPA-440/5-80-019.

-------
EPA compared the GMCVs for the data set to Oregon's dieldrin chronic criterion to determine
whether the value will protect the designated use.

Table 2.1.6-2: Genus Mean Chronic Values

(GMCVs)

'or Dieldrin

Genus

Species

Common name

GMAV
(MS)"-)

SMCV
(MS)"-)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV

(Mg/L)

Orconectes

nais

Crayfish

740.0

86.75

Chironomus

tentans

Midge

560.0

65.65

Gammarus

lacustris

Scud

534.0

62.61

Simocephalus

serrulatus

Cladoceran

214.0

25.09

Bufo

woodhousei

Fowler's toad

150.0

17.58

Daphnia

pulex

Cladoceran

Daphnia

magna

Cladoceran

136.2

57.00

15.97
(57.00)

Pseudacris

triseriata

Western chorus frog

100.0

11.72

Gammarus

fasciatus

Scud

Gambusia

affinis

Western mosquitofish

31.00

3.634

Lumbriculus

variegatus

Oligochaete, worm

21.80

2.556

Palaemonetes

kadiakensis

Grass shrimp,
freshwater prawn

20.00

2.345

Pimephales

promelas

Fathead minnow

17.70

2.075

Ischnura

verticalis

Damselfly

12.00

1.407

Ameiurus

melas

Black bullhead

10.00

1.172

Oreochromis

mossambica

Mozambique tilapia

10.00

1.172

Lepomis

macrochirus

Bluegill

Lepomis

cyanellus

Green sunfish

Lepomis

gibbosus

Pumpkinseed

8.539

1.001

Poecilia

reticulata*

Guppy

5.500

0.4500

0.6448
(0.4500)

Asellus

brevicaudus*

Isopod

5.000

0.5862

Carassius

auratus

Goldfish

4.906

0.5751

Ictalurus

punctatus

Channel catfish

4.500

0.5275

Oncorhynchus

kisutch

Coho salmon

Oncorhynchus

clarki

Cutthroat trout

Oncorhynchus

tshawytscha

Chinook salmon

Oncorhynchus

my kiss

Rainbow trout

3.989

0.4000

2,3

0.4676
(0.4000)

Micropterus

salmoides

Largemouth bass

3.500

0.4103

Claassenia

sabulosa*

Stonefly

0.5800

0.0680

Pteronarcella

badia

Stonefly

0.5000

0.0586

Pteronarcys

californicus

Stonefly

0.5000

0.0586

See notes as above under Table 2.1.6-1.

B. Evaluation of the Protectiveness of the Oregon Freshwater Chronic Criterion

Following the review of the GMCV values in Table 2.1.6-2, all genera and species had values
greater than Oregon's chronic criterion for dieldrin. Therefore, EPA concluded that chronic
effects are not expected to occur at concentrations equal to or lower than the criterion acute and
thus the aquatic life designated use would be protected.

2.1.5.3 References for Dieldrin

-------
A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the acute and chronic tables, and are the sources from which EPA
obtained SMAVs (acute table) and experimentally-derived SMCVs (chronic table).

Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in tables 2.1.6-1 and 2.1.6-2)

Acute References

Mayer, F.L. and M.R. Ellersieck. 1986. Manual of Acute Toxicity: Interpretation and Data Base for 410
Chemicals and 66 Species of Fresh-water Animals. Resource Publ. No. 160, U.S. Dep. Interior, Fish Wildl.
Serv., Washington, DC: 505 p. (USGS Data File)

Shubat, P.J. and L.R. Curtis. 1986. Ration and toxicant preexposure influence on dieldrin accumulation by
rainbow trout (Saimo qairdneri). Environ. Toxicol. Chem. 5: 69-77.

Henderson, C., Q.H. Pickering and C.M. Tarzwell. 1959. Relative toxicity often chlorinated hydrocarbon
insecticides to four species offish. Trans. Am. Fish. Soc. 88(1): 23-32.

Sanders, H.O. 1972. Toxicity of Some Insecticides to Four Species of Malacostracan Crustaceans. Tech.
Pap. No. 66, Bur. Sports Fish. Wildl., Fish Wildl.Serv., U.S.D.I., Washington, D.C.: 19 p. (Publ in Part As
6797).

Anderson, P.D. and L.J. Weber. 1975. Toxic response as a quantitative function of body size. Toxicol.
Appl. Pharmacol. 33(3): 471-483.

Katz, M. 1961. Acute toxicity of some organic insecticides to three species of salmonids and to the
threespine stickleback. Trans. Am. Fish. Soc. 90(3): 264-268.

Swedburg, D. 1969. Chronic toxicity of insecticides to cold-water fish. Prog. Sport Fish Res., Div. Fish.
Res., Bureau Sport Fish Wildl. 88: 8-9.

Cairns, J., Jr. and A. Scheier. 1964. The effect upon the pumpkinseed sunfish Lepomis gibbosus (Linn.) of
chronic exposure to lethal and sublethal concentrations of dieldrin. Not. Nat. (Phila.) 370: 1-10.

Tarzwell, C.M. and C. Henderson. 1957. Toxicity of dieldrin to fish. Trans. Am. Fish. Soc. 86: 245-257.

Nunogawa, J.H., N.C. Burbank, Jr., R.H.F. Young and L.S. Lau. 1970. Relative Toxicities of Selected
Chemicals to Several Species of Tropical Fish. Water Resour. Res. Center, University of Hawaii, Honululu,
HI: 38 p. (U.S. NTIS PB-196312).

Macek, K.J., C. Hutchinson and O.B. Cope. 1969. The effects of temperature on the susceptibility of
bluegills and rainbow trout to selected pesticides. Bull. Environ. Contam. Toxicol. 4(3): 174-183 (Publ in Part
As 6797).

Brooke, L.T. 1993. Conducting Toxicity Tests with Freshwater Organisms Exposed to Dieldrin,
Fluoranthene and Phenanthrene. U.S. EPA Contract No. 68-C1-0034, Work Assignment No. 5, to R.L.
Spehar, U.S. EPA, Duluth, MN: 18 p.

Sanders, H.O. 1970. Pesticide toxicities to tadpoles of the Western chorus frog Pseudacris triseriata and
Fowler's toad Bufo woodhousii fowieri. Copeia 2: 246-251 (Author Communication Used) (Publ in Part As
6797).

Sanders, H.O. and O.B. Cope. 1966. Toxicities of several pesticides to two species of cladocerans. Trans.
Am. Fish. Soc. 95: 165.

Daniels, R.E. and J. D. Allan. 1981. Life table evaluation of chronic exposure to a pesticide. Can. J. Fish.
Aquat. Sci. 38: 485-494.

Sanders, H.O. 1969. Toxicity of pesticides to the crustacean, Gamnarus iacustris. Bur. Sport Fish. Wildl.
Tech. Pap. No. 25.

Hansen, C.R.J, and J.A. Kawatski. 1976. Application of 24-hour postexposure observation to acute toxicity
studies with invertebrates. J. Fish. Res. Board Can. 33(5): 1198-1201.

Chronic References

Adema, D.M.M. 1978. Daphnia magna as a test animal in acute and chronic toxicity tests. Hydrobiol. 59:
125.

Chadwick, G. and D.L. Shumway. 1969. Effects of dieldrin on the growth and development of steelhead
trout. In: J.W. Gillett (Ed.), The Biological Impact of Pesticides in the Environment, Environmental Health
Ser. No. 1, Oregon State Univ., Corvallis, OR: 90-96.

Roelofs, T.D. 1971. Effects of Dieldrin on the Intrinsic Rate of Increase of the Guppy, Poeciiia reticulata
Peters. Ph.D. Thesis, Oregon State Univ., Corvallis, OR: 88 p.

-------
B. Studies That EPA Considered But Did Not Utilize In This Determination

1) For the studies that were not utilized, but the most representative SMAV/2 or
most representative SMCV fell below the criterion, or, if the studies were for a
species associated with one of the four most sensitive genera used to calculate the
FAV in the most recent national ambient water quality criteria dataset used to
derive the CMC17, EPA is providing a transparent rationale as to why they were
not utilized (see below).

17 U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient
Water. EPA-820-B-96-001.

-------
2.1.7 ENDRIN

2.1.7.1 Evaluation of the Acute Freshwater Criterion Concentration for Endrin
A. Presentation of Toxicological Data

Oregon adopted a freshwater acute criterion concentration of 0.086 |ig/L for endrin. This
concentration is the same as the freshwater CMC recommended for use nationally by EPA for

the protection of aquatic life . EPA developed the recommended criterion in accordance with
the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.1.7-1 provides available SMAVs and GMAVs based on available acute toxicity data for
endrin to aquatic animals from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Table 2.1.7-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values

(GMAVs) for

Cndrin

Most

Acute References

Representative
SMAV

GMAV

(used in the
calculation of the

Genus

Species

Common name

(MS)"-)

SMAV)

Pseudacris

triseriata

Western chorus frog

180.0

1,17

Bufo

woodhousei

Fowler's toad

120.0

Hexaqenia

bilineata

Mayfly

62.99

1,8

Daphnia

pulex

Cladoceran

60.44

1,14,16

Daphnia

maqna

Cladoceran

49.78

54.85

1,2,14

Orconectes

immunis

Crayfish

89.00

Orconectes

nais

Crayfish

32.00

53.37

Lumbriculus

varieqatus

Oligochaete, worm

42.60

Simocephalus

serrulatus

Cladoceran

34.21

1,3

Ceriodaphnia

reticulata

Cladoceran

24.00

Tipula

sp.

Cranefly

12.00

Oreochromis

mossambica

Mozambique tilapia

5.600

Atherix

varieqata

Snipefly

4.600

Gammarus

fasciatus

Scud, Amphipod

3.100

Gammarus

lacustris

Scud, Amphipod

3.000

3.050

1,13

Rana

catesbeiana

Bullfrog

2.500

Clarias

batrachus

Walking catfish

2.470

Ishnura

verticalis

Damselfly

2.090

1,8

Cypridopsis

vidua

Ostracod, Seed shrimp

1.800

Tilapia

zillii

Tilapia

1.620

Poecilia

reticulata

Guppy

1.600

Asellus

brevicaudus

Aquatic sowbug

1.500

1,8

Palaemonetes

kadiakensis

Grass shrimp

1.265

1,8

Carassius

auratus

Goldfish

0.9500

Baetis

sp.

Mayfly

0.9000

Jordanella

floridae

Flagfish

0.8500

Tanytarsus

dissimilis

Midge

0.8400

Claassenia

sabulosa

Stonefly

0.7600

18 See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.

The data which serve as the basis for the current nationally-recommended criteria are from: U.S. EPA. 1996. 1995

Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient Water. EPA-820-B-96-

001.

-------

Most

Acute References

Representative
SMAV

GMAV

(used in the
calculation of the

Genus

Species

Common name

(MS)"-)

SMAV)

Gambusia

affinis

Western mosquitofish

0.6900

Pteronarcella

badia

Stonefly

0.5400

Pimephales

promelas

Fathead minnow

0.4899

2,7

Ameiurus

melas

Black bullhead

0.4500

Gasterosteus

aculeatus

Threespine stickleback

0.4400

Oncorhynchus

tshawytscha

Chinook salmon

1.200

Oncorhynchus

mykiss

Rainbow trout

0.3000

Oncorhynchus

kisutch

Coho salmon

0.2130

0.4249

1,6

Ictalurus

punctatus

Channel catfish

0.4200

Acroneuria

pacifica

Stonefly

0.3900

Brachycentrus

americanus

Caddisfly

0.3400

Cyprinus

carpio

Common carp

0.3200

Micropterus

salmoides

Largemouth bass

0.3100

Pteronarcys

californica

Stonefly

0.2500

Lepomis

macrochirus

Bluegill

0.2090

Perca

flavescens

Yellow perch

0.1500

Note 1: Species that are bold and italicized indicate those associated with the four most sensitive genera used to derive the FAV or
FCV in the 1995 GLI update of the ALC document. Underlined species with an asterisk (*) indicate known or suspected Oregon non-
resident species, and for this evaluation, only those non-resident species below the criterion or related to the four most sensitive
genera used in the derivation of the 304(a) criteria are identified as such.

B. Evaluation of the Protectiveness of the Oregon Freshwater Acute Criterion

Following review of SMAV and GMAV values in Table 2.1.7-1, all species and genera have
acute effects values greater than Oregon's acute criterion concentration for endrin. Therefore,
EPA concluded that acute effects to these species are not expected to occur at concentrations
equal to or lower than the criterion, and thus these genera and species and the aquatic life
designated use would be protected by the criterion.

When EPA examined the SMAV/2 and GMAV/2 values to consider low level toxicity effects
(levels nearly indistinguishable from controls), 43 of 44 species and 38 of 39 genera had
SMAV/2 and GMAV/2 values, respectively, greater than the acute criterion value, indicating that
all but a very small proportion of species would be expected to be fully protected at the ambient
concentrations equal to or lower than the acute criterion, thus these genera and species and the
aquatic life designated use would be fully protected by the criterion. For one species, the yellow
perch (Perca flavescens) the SMAV/2 was 0.075 |ig/L endrin, lower than the acute criterion of
0.086 |ig/L endrin. Thus, the occurrence of ambient concentrations at or above the criterion may
result in acute toxicity to some individuals of this species. This species is expected to reside in
Oregon waters..

The SMAV for Perca flavescens was 0.1500 |ig/L, with 5 and 95 percent confidence intervals of
0.1200 |ig/L and 0.1800 |ig/L, respectively (Mayer and Ellersieck 1986).

Freshwater endrin acute criterion comparison

-------
Text Box A - Basis for the meta analysis comparing the SMAV/2 for the yellow perch (P.
flavescens) to the acute criterion for endrin (0.086 |ig/L).

Perca flavescens

Reported Values

Reported Values/2

LC50 5% CI

95% CI

LC50/2

CMC

0.1500 0.1200

0.1800

0.0750

0.0860

(SMAV)

(SMAV/2)

2.1.7.2 Evaluation of the Chronic Freshwater Criterion Concentration for Endrin
A. Presentation of Toxicological Data

Oregon adopted a freshwater chronic criterion concentration of 0.036 |ig/L for endrin. This
concentration is the same as the freshwater CCC recommended for use nationally by EPA for the
protection of aquatic life19. EPA developed the recommended criterion in accordance with the
1985 Guidelines pursuant to CWA section 304(a).

Table 2.1.7-2 presents a compilation of the GMAVs from Table 2.1.7-1, any experimentally
determined SMCVs obtained from the criteria document and EPA ECOTOX download used for
the BE, and estimated GMCVs based on the GMAV/ACR. The 1996 criteria document for
endrin reported an ACR of 4.833, which EPA calculated as the geometric mean of three
experimentally determined ACRs of 1.9, 18, and 3.3. EPA determined the ACR of 3.3 with the
freshwater flagfish (Jordanella floridae) (Hermanutz 1978), while EPA determined the other two
ACRs with saltwater species. Since no additional acceptable ACRs are available, EPA calculated
the predicted GMCVs for endrin in Table 2.1.7-2 using an ACR of 4.833 and the following
equation: Predicted GMCV = GMAV/FACR.

EPA compared the GMCVs for each species to Oregon's endrin chronic criterion concentration
to determine whether the chronic criterion will protect the species.

Table 2.1.7-2: Genus Mean

Chronic Values

GMCVs) for Endrin

Genus

Species

Common name

GMAV
(MS)"-)

SMCV
(MS)"-)

(experimentally
derived)

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV

(Mg/L)

Pseudacris

triseriata

Western chorus
frog

180.0

37.24

Bufo

woodhousei

Fowler's toad

120.0

24.83

Hexaqenia

bilineata

Mayfly

62.99

13.03

Daphnia

pulex

Cladoceran

Daphnia

maqna

Cladoceran

54.85

11.35

Orconectes

immunis

Crayfish

19 U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient
Water. EPA-820-B-96-001.

-------

Chronic

SMCV

References

Genus

Species

Common name

GMAV
(MS)"-)

(MS)"-)

('experimentally
derived}

(used in the
calculation of
the SMCV)

Predicted
GMCV

(Mg/L)

Orconectes

nais

Crayfish

53.37

11.04

Lumbriculus

variegatus

Oligochaete, worm

42.60

8.814

Simocephalus

serrulatus

Cladoceran

34.21

7.078

Ceriodaphnia

reticulata

Cladoceran

24.00

4.966

Tipula

sp.

Cranefly

12.00

2.483

Oreochromis

mossambica

Mozambique tilapia

5.600

1.159

Atherix

varieqata

Snipefly

4.600

0.9518

Gammarus

fasciatus

Scud, Amphipod

Gammarus

lacustris

Scud, Amphipod

3.050

0.6310

Rana

catesbeiana

Bullfrog

2.500

0.5173

Clarias

batrachus

Walking catfish

2.470

0.5111

Ishnura

verticalis

Damselfly

2.090

0.4324

Cypridopsis

vidua

Ostracod, Seed
shrimp

1.800

0.3724

Tilapia

zillii

Tilapia

1.620

0.3352

Poecilia

reticulata

Guppy

1.600

0.3311

Asellus

brevicaudus

Aquatic sowbug

1.500

0.3104

Palaemonetes

kadiakensis

Grass shrimp

1.265

0.2617

Carassius

auratus

Goldfish

0.9500

0.1966

Baetis

sp.

Mayfly

0.9000

0.1862

Jordanella

floridae

Flagfish

0.8500

0.2600

0.1759
(0.2600)

Tanytarsus

dissimilis

Midge

0.8400

0.1738

Claassenia

sabulosa

Stonefly

0.7600

0.1573

Gambusia

affinis

Western
mosquitofish

0.6900

0.1428

Pteronarcella

badia

Stonefly

0.5400

0.1117

Pimephales

promelas

Fathead minnow

0.4899

0.1014

Ameiurus

melas

Black bullhead

0.4500

0.0931

Gasterosteus

aculeatus

Threespine
stickleback

0.4400

0.0910

Oncorhynchus

tshawytscha

Chinook salmon

Oncorhynchus

my kiss

Rainbow trout

Oncorhynchus

kisutch

Coho salmon

0.4249

0.0879

Ictalurus

punctatus

Channel catfish

0.4200

0.0869

Acroneuria

pacifica

Stonefly

0.3900

0.0807

Brachycentrus

americanus

Caddisfly

0.3400

0.0703

Cyprinus

carpio

Common carp

0.3200

0.0662

Micropterus

salmoides

Largemouth bass

0.3100

0.0641

Pteronarcys

californica

Stonefly

0.2500

0.0517

Lepomis

macrochirus

Bluegill

0.2090

0.0433

Perca

flavescens

Yellow perch

0.1500

0.0310

See same notes as above under Table 2.1.7-1.

B. Evaluation of the Protectiveness of the Oregon Freshwater Chronic Criterion

Following the review of the GMCV values in Table 2.1.7-2, 38 of 39 genera have GMCVs
greater than Oregon's chronic criterion for endrin. Therefore, EPA found that all but a very small
proportion of species would be expected to be protected at the ambient concentrations equal to or
lower than the chronic criterion, thus the aquatic life designated use would be protected by the
criterion.

-------
When compared to Oregon's CCC for endrin, using the SMCV value for one test species (the
yellow perch Perca flavescens) was lower than the chronic criterion concentration of 0.036 |ig/L
endrin. This species is expected to reside in Oregon waters. Therefore, EPA reviewed the data
from the studies that make up the most representative SMCVs for this species and compared the
confidence intervals of these SMCVs to determine whether the SMCV values were quantitatively
different from the criterion value of 0.036 |ig/L.

The SMCV for P. flavescens was estimated by applying the ACR of 4.833 described above to the
SMAV.

The Oregon chronic criterion for endrin of 0.036 |ig/L lies within the calculated confidence
bounds around the SMCV for P. flavescens, indicating that there is some uncertainly whether
there would actually be chronic effects at the chronic criterion value for this species.

An alternative analysis would be to use the freshwater fish ACR of 3.3 and apply it to the
freshwater yellow perch species under analysis, because an ACR for a freshwater species may be
most useul for evaluating effects to other freshwater fish species. Using this approiach, the
SMCV for perch would be calculated as 0.045 |ig/L endrin, which is greater than the acute
criterion.

Given these analyses, there is uncertainty whether there would be expected to be any chronic
effects to even one of the tested species, yellow perch, at ambient concentrations equal to or less
than the criterion.

Thus, given that at a minimum, 38 of 39 tested species have predicted chronic values greater than
the criterion, EPA concludes that the aquatic life designated use would be protected by the
chronic criterion.

Freshwater endrin chronic criterion comparison

Text Box B - Basis for the meta analysis comparing the SMCV for the yellow perch (P.
flavescens) to the chronic criterion for endrin (0.036 |ig/L).

Perca flavescens

Reported Acute Values

Chronic Values

LC50 5%CI 95%CI

ACR

(LC50 / ACR)

CCC

0.1500 0.1200 0.1800

4.833

0.0310

0.036

0.1500 0.1200 0.1800

3.3

0.045

SMCV

2.1.7.3 References for Endrin
A. Studies That EPA Utilized in this Determination

-------
EPA determined that these studies were acceptable to be utilized in this determination. The
studies listed below were used in the acute and chronic tables, and are the source from which
EPA obtained SMAVs (acute table) and experimentally-derived SMCVs (chronic table).

Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in tables 2.1.7-1 and 2.1.7-2)

Acute references

Mayer, F.L.J, and M.R. Ellersieck. 1986. Manual of Acute Toxicity: Interpretation and Data Base for 410
Chemicals and 66 Species of Freshwater Animals. Resour. Publ. No. 160, U.S. Dep. Interior, Fish Wildl. Serv.,
Washington, DC: 505 p. (USGS Data File).

Thurston, R.V., T.A. Gilfoil, E.L. Meyn, R.K. Zajdel, T.L. Aoki and G.D. Veith. 1985. Comparative toxicity often
organic chemicals to ten common aquatic species. Water Res. 19(9): 1145-1155.

Sanders, H.O. and O.B. Cope. 1968. The relative toxicities of several pesticides to naiads of three species of
stoneflies. Limnol. Oceanogr. 13: 112-117.

Anderson, R.L. and D.L. De Foe. 1980. Toxicity and bioaccumulation of endrin and methoxychlor in aquatic
invertebrates and fish. Environ. Pollut. Ser. A Ecol. Biol. 22(2):111 -121 (Author Communication Used).

Jensen, L.D. and A.R. Gaufin. 1964. Effects often organic insecticides on two species of stonefly naiads. Trans.
Am. Fish. Soc. 93(1): 27-34.

Katz, M. 1961. Acute toxicity of some organic insecticides to 3 species of salmonids and the threespine
stickleback. Trans. Am. Fish. Soc. 90: 264.

Brungs, W.A. and G.W. Bailey. 1966. Influence of suspended solids on the acute toxicity of endrin to fathead
minnows. Proc. Zlst Purdue Ind. Waste Conf., Part 1. 50: 4.

Sanders, H.O. 1972. Toxicity of Some Insecticides to Four Species of Malacostracan Crustaceans. U.S. Dep.
Inter. Bur. Sport Fish, and Wildl. Tech. Paper 66.

Hermanutz, R. 1978. Endrin and malathion toxicity to flagfish (Jordaneiia fioridae). Arch. Environ. Contam.
Toxicol. 7: 159.

Henderson, C., Q.H. Pickering and C.M. Tarzwell. 1959. Relative toxicity of ten chlorinated hydrocarbon
insecticides to four species offish. Trans. Am. Fish. Soc. 88: 23-32.

El Sebae, A.H., M.A. El Amayem, I. Sharaf and M. Massod. 1986. Factors Affecting Acute and Chronic Toxicity
of Chlorinated Pesticides and Their Biomagnification in Alexandria Region. In: Papers Presented at the
FAO/UNEP Meeting on the Toxicity and Bioaccumulation of Selected Substances in Marine Organisms, Rovinj,
Yugoslavia, 5-9 Nov., 1984, FAO Fish. Rep. No. 334 (Suppl.): 73-79.

Bhattacharya, S., S. Mukherjee and S. Bhattacharya. 1975. Toxic effects of endrin on hepatopancreas of the
teleostfish, Ciarias batrachus (Linn.). Indian J. Exp. Biol. 13(2):185-186.

Sanders, H.O. 1969. Toxicity of Pesticides to the Crustacean Gammarus iacustris. U.S. Dep. Inter. Bur. Sport
Fish. Wildl. Tech. Paper 25.

Elnabarawy, M.T., A.N. Welter and R.R. Robideau. 1986. Relative sensitivity of three daphnid species to
selected organic and inorganic chemicals. Environ. Toxicol. Chem. 5(4): 393-398.

Brooke, L. 1993. Acute and Chronic Toxicity of Several Pesticides to Five Species of Aquatic Organisms.
Report to R. Spehar, U.S. EPA, Duluth, MN.: 31 pp.

Priester, L.E., Jr. 1965. The Accumulation and Metabolism of DDT, Parathion, and Endrin by Aquatic Food-
Chain Organisms. Ph.D. Thesis, Clemson University, Clemson, SC: 74.

Sanders, H.O. 1970. Pesticide toxicities to tadpoles of the Western chorus frog Pseudacris triseriata and
Fowler's toad Bufo woodhousii fowieri. Copeia 2:246-251 (Author Communication Used) (Publ in Part As 6797).

Chronic references

Hermanutz, R. 1978. Endrin and malathion toxicity to flagfish (Jordaneiia fioridae). Arch. Environ. Contam.
Toxicol. 7: 159.

B. Studies That EPA Considered But Did Not Utilize In This Determination

-------
FAV in the most recent national ambient water quality criteria dataset used to

derive the CMC , EPA is providing a transparent rationale as to why they were
not utilized (see below).

20 U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient
Water. EPA-820-B-96-001.

-------
2.1.8 LEAD

2.1.8.1 Evaluation of the Acute Freshwater Criterion Concentration for Lead
A. Presentation of Toxicological Data

Oregon adopted a freshwater acute criterion concentration of 65 |ig/L for lead that is expressed
as a function of total hardness in the water column and in terms of the dissolved concentration of
the metal. This dissolved metal concentration reflects the criterion normalized to a total hardness
of 100 mg/L as CaCC>3 and is the same as the freshwater acute criterion concentration

recommended for use nationally by EPA for the protection of aquatic life . EPA developed the
recommended criterion in accordance with the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.1.8-1 provides available SMAVs and GMAVs based on available acute toxicity data for
lead to aquatic life from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Table 2.1.8-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values

(GMAVs) for Lead

Most

Acute References

Representative
SMAV

GMAV

(used in the
calculation of the

Genus

Species

Common name

(Mg/L)

SMAV)

Procambarus

clarkii

Red swamp crayfish

2752779

Tanytarsus

dissimilis

Midge

450938

Carassius

auratus

Goldfish

193259

Poecilia

reticulata

Guppy

126431

Amnicola

limosa

Snail

109029

Lepomis

macrochirus

Bluegill

99994

Chironomus

tentans

Midge

63440

Gila

elegans

Bonytail

>56000

Xyrauchen

texanus

Razorback sucker

>56000

Ptychocheilus

lucius

Colorado squawfish

>56000

Crangonyx

pseudogracilis

Amphipod

52759

Lethocerus

sp.

Water bug

48745

Salvelinus

fontinalis

Brook trout

9214

Oncorhynchus

kisutch

Coho salmon

25445

Oncorhynchus

my kiss

Rainbow trout

1455

6085

13,14,15,16

Pimephales

promelas

Fathead minnow

4737

Thymallus

arcticus

Arctic grayling

2009

Aplexa

hypnorum

Snail

1988

Lumbriculus

variegatus

Oligochaete, worm

1665

Micropterus

dolomieui

Smallmouth bass

1311

Daphnia

pulex

Cladoceran

519.8

Daphnia

magna

Cladoceran

391.8

451.3

6,7,8,9,10,11

Ceriodaphnia

reticulata

Cladoceran

487.4

Ceriodaphnia

dubia

Cladoceran

205.6

316.6

1,2,3

Gammarus

oseudolimnaeus*

Scud

272.6

4,5

21 See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.

The data which serve as the basis for the current nationally-recommended criteria are from: U.S. EPA. 1984. Ambient Water Quality Criteria for
Lead. EPA-440/5-84-027.

-------
this evaluation, only those non-resident species below the criterion or related to the four most sensitive genera used in the derivation
of the 304(a) criteria are identified as such.

Note 2: The reporting of calculated values has been limited to a minimum of four significant figures for convenience and use in this
evaluation with the exception of very high values, which are reported as whole numbers - see text in section 2.2 of this evaluation for
an explanation of this decision, particularly for metals such as lead which are normalized to a water hardness of 100 mg/L as CaC03
and expressed on a dissolved metal basis for a comparison with the acute criterion concentration.

B. Evaluation of the Protectiveness of the Oregon Freshwater Acute Criterion

Following review of GMAV and SMAV/2 values in Table 2.1.8-1, all tested genera and species
had values greater than Oregon's acute criterion concentration for lead. Therefore, EPA
concluded that acute effects to these species are not expected to occur at concentrations equal to
or lower than the criterion and thus these genera and species and the aquatic life designated use
will be protected.

2.1.8.2 Evaluation of the Chronic Freshwater Criterion Concentration for Lead
A. Presentation of Toxicological Data

Oregon adopted a freshwater chronic criterion concentration of 2.5 |ig/L for lead expressed as
the dissolved metal concentration at a total hardness of 100 mg/L CaC03 in the water column.
This concentration is the same as the freshwater chronic criterion concentration recommended

for use nationally by EPA for the protection of aquatic life . EPA developed the recommended
criterion in accordance with the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.1.8-2 presents a compilation of the GMAVs from Table 2.1.8-1, any experimentally
determined SMCVs obtained from the criteria document and EPA ECOTOX download used for
the BE, and estimated GMCVs based on the GMAV/ACR. The 1984 criteria document for lead23
reported an FACR of 24.39, which EPA calculated as the geometric mean of experimentally
determined ACRs for five freshwater species and one saltwater species ranging from 4.769 for
an acutely sensitive freshwater invertebrate, the cladoceran Ceriodaphnia dubia, to 61.97 for an
acutely sensitive fish, rainbow trout {Onchorhynchus mykiss). However, upon further review of
the data, EPA concludes that the ACRs for the six species increase as the SMAV increases, and
thus, as recommended by the Guidelines, calculated an FACR of 9.299 from the two most
acutely sensitive freshwater species, C. dubia and Daphnia magna. Since no additional
acceptable ACRs are available, EPA calculated the predicted GMCVs for lead in Table 2.1.8-2
using the FACR of 9.299 and the following equation: Predicted GMCV = GMAV/FACR.

EPA compared the GMCVs for each species to Oregon's lead chronic criterion to determine
whether the chronic criterion will protect the species.

Table 2.1.8-2: Genus Mean Chronic Values (GMCVs) for Lead

22 See footnote 23 above.

23 U.S. EPA. 1984. Ambient Water Quality Criteria Document for Lead. EPA-440/5-84-027.

-------
Genus

Species

Common name

GMAV
(Mg/L)

SMCV
(MS)"-)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(Mg/L)

Procambarus

clarkii

Red swamp
crayfish

2752779

296030

Tanytarsus

dissimilis

Midge

450938

48493

Carassius

auratus

Goldfish

193259

20783

Poecilia

reticulata

Guppy

126431

13596

Amnicola

limosa

Snail

109029

11725

Lepomis

macrochirus

Bluegill

99994

10753

Chironomus

tentans

Midge

63440

6822

Gila

elegans

Bonytail

>56000

>6022

Xyrauchen

texanus

Razorback sucker

>56000

>6022

Ptychocheilus

lucius

Colorado
squawfish

>56000

>6022

Crangonyx

pseudogracilis

Amphipod

52759

5674

Lethocerus

sp.

Water bug

48745

5242

Salvelinus

fontinalis

Brook trout

9214

185.3

990.8
(185.3)

Oncorhynchus

kisutch

Coho salmon

Oncorhynchus

my kiss

Rainbow trout

6085

152.1

5,6,7,8

654.3
(152.1)

Pimephales

promelas

Fathead minnow

4737

742.2

509.4
(742.2)

Thymallus

arcticus

Arctic grayling

2009

216.0

Aplexa

hypnorum

Snail

1988

213.8

Lumbriculus

variegatus

Oligochaete,
worm

1665

179.1

Micropterus

dolomieui

Smallmouth bass

1311

>186.4

140.9
(>186.4)

Daphnia

pulex

Cladoceran

Daphnia

magna

Cladoceran

451.3

49.66

48.53
(49.66)

Ceriodaphnia

reticulata

Cladoceran

Ceriodaphnia

dubia

Cladoceran

316.6

133.9

3,4

34.04
(133.9)

Gammarus

oseudolimnaeus*

Scud

272.6

29.31

Lymnaea

palustris

Marsh snail

13.24

(13.24)

See same notes as above under Table 2.1.8-1.

B. Evaluation of the Protectiveness of the Oregon Freshwater Chronic Criterion

Following the review of the values in Table 2.1.8-2, all tested genera and species had GMCVs
and SMCVs greater than Oregon's chronic criterion for lead. Therefore, EPA concluded that
chronic effects are not expected to occur at concentrations equal to or lower than the criterion
and thus these genera and species and the aquatic life designated use will be protected by the
lead chronic criterion.

2.1.8.3 References for Lead

A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed

-------
below were used in the acute and chronic tables, and are the source from which EPA
obtained SMAVs (acute table) and experimentally-derived SMCVs (chronic table).

Reference No.

Used Reference Citation

(associated with reference numbers and provided above in tables 2.1.8-1 and 2.1.8-2)

Acute References

Bitton, G., K. Rhodes and B. Koopman. 1996. CerioFAST: An acute toxicity test based on Ceriodaphnia dubia
feeding behavior. Environ. Toxicol. Chem. 15(2): 123-125.

Diamond, J.M., D.E. Koplish, J. McMahon III and R. Rost. 1997. Evaluation of the water-effect ratio procedure
for metals in riverine system. Environ. Toxicol. Chem. 16(3): 509-520.

Spehar, R.L. and J.T. Fiandt. 1986. Acute and chronic effects of water quality criteria-based metal mixtures on
three aquatic species. Environ. Toxicol. Chem. 5(10): 917-31.

Spehar, R.L., R.L. Anderson and J.T. Fiandt. 1978. Toxicity and bioaccumulation of cadmium and lead in
aquatic invertebrates. Environ. Pollut. 15: 195-208.

Chapman, G.A., S. Ota and F. Recht. 1980. Effects of water hardness on the toxicity of metals to Daphnia
magna. U.S. EPA, Corvallis, OR.

Elnabarawy, M.T., A.N. Welter and R.R. Robideau. 1986. Relative sensitivity of three daphnid species to
selected organic and inorganic chemicals. Environ. Toxicol. Chem. 5(4): 393-8.

LeBlanc, G. A. 1982. Laboratory investigation into the development of resistance of Daphnia magna (Straus) to
environmental pollutants. Environ. Pollut. Ser. A 27(4): 309-322.

McWilliam, R. A. and D. J. Baird. 2002. Postexposure feeding depression: A new toxicity endpoint for use in
laboratory studies with Daphnia magna. Environ. Toxicol. Chem. 21(6): 1198-1205.

Wilson, J. B. 1980. The effects of temperature on the acute toxicity of lead and cadmium to Daphnia magna
and three naturally-occurring species of Great Lakes crustacean. In: J. F. Klaverkamp, S. L. Leonhard and K. E.
Marshall (Eds.), Proc. 6th Annual Aquatic Toxicity Workshop, Nov. 6-7, 1979, Winnipeg, Manitoba, Can. Tech.
Rep. Fish. Aquat. Sci. No. 975: 73-80.

Ziegenfuss, P. S., W. J. Renaudette and W. J. Adams. 1986. Methodology for assessing the acute toxicity of
chemicals sorbed to sediments: Testing the equilibrium partitioning theory. In: T. M. Poston and R. Purdy
(Eds.), Aquatic Toxicology and Environmental Fate, 9th Volume, ASTM STP 921, Philadelphia, PA. 479-493.

Coughlan, D.J., S.P. Gloss and J. Kubota. 1986. Acute and sub-chronic toxicity of lead to the early life stages of
smallmouth bass (Micropterus doiomieui). Water Air Soil Pollut. 28(3-4): 265-75.

Davies, P.H., J.P. Goettl, Jr., J.R. Sinley and N.F. Smith. 1976. Acute and chronic toxicity of lead to rainbow
trout (Oncorhynchus mykiss) in hard and soft water. Water Res. 10: 199-206.

Goettl, J.P., et al. 1972. Laboratory water pollution studies. Colorado Fisheries Research Review.

Davies, P.H. and W.E. Everhart. 1973. Effects of chemical variations in aquatic environments: Lead toxicity to
rainbow trout and testing application factor concept. EPA-R3-73-011C. National Technical Information Service,
Springfield, VA.

Rogers, J. T., J. G. Richards and C. M. Wood. 2003. lonoregulatory disruption as the acute toxic mechanism for
lead in the rainbow trout (Oncorhynchus mykiss). Aquat. Toxicol. 64(2): 215-234.

Phipps, G.L., V.R. Mattson, and G.T. Ankley. 1995. Relative sensitivity of three freshwater benthic
macroinvertebrates to ten contaminants. Arch. Environ. Contam. Toxicol. 28(3): 281-286.

Call, D.J., L.T. Brooke, N. Ahmad and D.D. Vaishnav. 1981. Aquatic pollutant hazard assessments and
development of a hazard prediction technology by quantitative structure-activity relationships. First Quarterly
Report to EPA. Center for Lake Superior Environmental Studies University of Wisconsin-Superior, Superior, Wl.

Buhl, K.J. and S.J. Hamilton. 1990. Comparative toxicity of inorganic contaminants released by placer mining to
early life stages of salmonids. Ecotoxicol. Environ. Saf. 20(3): 325-342.

Holcombe, G.W., D.A. Benoit, E.N. Leonard and J.M. McKim. 1976. Long term effects of lead exposure on
three generations of brook trout (Saiveiinus fontinaiis). J. Fish. Res. Board Can. 33: 1731-1741.

Oladimeji A.A. and B.O. Offem. 1989. Toxicity of lead to Ciarias iazera, Oreochromis niioticus, Chironomus
tentans and Benacus species. Water Air Soil Pollut. 44(3-4): 191-201.

Martin, T.R. and D.M. Holdich. 1986. The acute lethal toxicity of heavy metals to peracarid crustaceans (with
particular reference to fresh-water asellids and gammarids). Water Res. 20(9): 1137-1147.

Buhl, K. J. 1997. Relative sensitivity of three endangered fishes, Colorado squawfish, bonytail, and razorback
sucker to selected metal pollutants. Ecotoxicol. Environ. Saf. 37: 182-192.

Pickering, Q.H. and C. Henderson. 1966. The acute toxicity of some heavy metals to different species of
warmwater fishes. Air Water Pollut. Int. J. 10: 453-463. (Author Communication Used).

Mackie, G.L. 1989. Tolerances of five benthic invertebrates to hydrogen ions and metals (cadmium, lead,
aluminum). Arch. Environ. Contam. Toxicol. 18(1-2): 215-223.

Naqvi, S.M and R.D. Howell. 1993. Toxicity of cadmium and lead to juvenile red swamp crayfish, Procambarus
ciarkii, and effects on fecundity of adults. Bull. Environ. Contam. Toxicol. 51(2): 303-308.

Chronic References

-------
Reference No.

Used Reference Citation

(associated with reference numbers and provided above in tables 2.1.8-1 and 2.1.8-2)

Borgmann, U., 0. Kramarand C. Loveridge. 1978. Rates of mortality, growth, and biomass production of
Lymnaea paiustris during chronic exposure to lead. J. Fish. Res. Board Can. 35: 1109-1115.

Chapman, G.A., S. Ota and F. Recht. 1980. Effects of water hardness on the toxicity of metals to Daphnia
magna. U.S. EPA, Corvallis, OR.

Jop, K.M., A.M. Askew and R.B. Foster. 1995. Development of a water-effect ratio for copper, cadmium, and
lead for the Great Works River in Maine using Ceriodaphnia dubia and Saiveiinus fontinaiis. Bull. Environ.
Contam. Toxicol. 54(1): 29-35.

Spehar, R.L. and J.T. Fiandt. 1986. Acute and chronic effects of water quality criteria-based metal mixtures on
three aquatic species. Environ. Toxicol. Chem. 5(10): 917-31.

Goettl, J.P., et al. 1972. Laboratory water pollution studies. Colorado Fisheries Research Review.

Sauter, S., K. S. Buxton, K.J. Macek and S.R. Petrocelli. 1976. Effects of exposure to heavy metals on
selected freshwater fish. Toxicity of copper, cadmium, chromium and lead to eggs and fry of seven fish species.
EPA-600/3-76-105. National Technical Information Service, Springfield, VA.

Davies, P.H., J.P. Goettl, Jr., J.R. Sinley and N.F. Smith. 1976. Acute and chronic toxicity of lead to rainbow
trout (Oncorhynchus mykiss) in hard and soft water. Water Res. 10: 199-206.

Holcombe, G.W., D.A. Benoit, E.N. Leonard and J.M. McKim. 1976. Long term effects of lead exposure on
three generations of brook trout (Saiveiinus fontinaiis). J. Fish. Res. Board Can. 33: 1731-1741.

Coughlan, D.J., S.P. Gloss and J. Kubota. 1986. Acute and sub-chronic toxicity of lead to the early life stages of
smallmouth bass (Micropterus dolomieui). Water Air Soil Pollut. 28(3-4): 265-75.

B. Studies That EPA Considered But Did Not Utilize In This Determination

1) For the studies that were not utilized, but the most representative SMAV/2 or
most representative SMCV fell below the criterion, or, if the studies were for a
species associated with one of the four most sensitive genera used to calculate the
FAV in the most recent national ambient water quality criteria dataset used to
derive the CMC24, EPA is providing a transparent rationale as to why they were
not utilized (see below).

24 U.S. EPA. 1984. Ambient Water Quality Criteria Documents for Lead. EPA-440/5-84-027.

-------
2.1.9 LINDANE (GAMMA-BHC)

2.1.9.1 Evaluation of the Acute Freshwater Criterion Concentration for Lindane
A. Presentation of Toxicological Data

Oregon adopted a freshwater acute criterion concentration of 0.95 |ig/L for lindane (gamma-
BHC). This concentration is the same as the freshwater CMC recommended for use nationally by

EPA for the protection of aquatic life . EPA developed the recommended criterion in
accordance with the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.1.9-1 provides available GMAVs based on available acute toxicity data for lindane to
aquatic life from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Table 2.1.9-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values
(GMAVs) for Lindane

Most

Acute References

Representative
SMAV

GMAV

(used in the
calculation of the

Genus

Species

Common name

(MS)"-)

SMAV)

Bufo

woodhousei

Fowler's toad

3752

1,32

Pseudacris

triseriata

Western chorus frog

2675

1,32

Simocephalus

serrulatus

Cladoceran

676.5

Anguilla

anguilla

Common eel

512.9

28,29,30

Limnodrilus

hoffmeisteri

Tubificid worm,
Oligochaete

430.0

Physa

fontinalis

Bladder snail

430.0

Polycelis

tenuis

Turbellarian

430.0

Hydropsyche

angustipennis

Caddisfly

330.0

Daphnia

magna

Cladoceran

630.2

13,16,31

Daphnia

pulex

Cladoceran

460.0

1,27

Daphnia

carinata

Cladoceran

100.0

307.2

Anabas

testudineus

Climbing perch

240.3

25,26

Hypophthalm ichthys

nobilis

Carp

170.0

Poecilia

reticulata

Guppy

138.0

Cyprinus

carpio

Carp

134.2

5,23

Gambusia

affinis

Western mosquitofish

130.0

Leuctra

moselyi

Stonefly

130.0

Protonemura

meyeri

Stonefly

130.0

Carassius

auratus

Goldfish

117.0

1,5,20

Pimephales

promelas

Fathead minnow

111.0

Chironomus

thummi

Midge

235.0

Chironomus

tentans

Midge

207.0

Chironomus

plumosus

Midge

20.59

100.1

Lepomis

microlophus

Redear sunfish

83.00

Lepomis

cyanellus

Green sunfish

76.22

Lepomis

macrochirus

Bluegill

50.40

68.32

1,15,16

Ameiurus

melas

Black bullhead

64.00

Gammarus

pulex

Scud

225.0

Gammarus

lacustris

Scud

64.99

1,17

25See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.

The data which serve as the basis for the current nationally-recommended criteria are from: U.S. EPA. 1980.

Ambient Water Quality Criteria for Hexachlorocyclohexane. EPA-440/5-80-054.

-------

Most

Acute References

Representative
SMAV

GMAV

(used in the
calculation of the

Genus

Species

Common name

(MS)"-)

SMAV)

Gammarus

fasciatus

Scud

10.49

53.53

Tilapia

zillii

Tilapia

50.27

Cloeon

sp.

Mayfly

50.00

Ictalurus

punctatus

Channel catfish

46.43

1,5

Perca

flavescens

Yellow perch

40.00

Salvelinus

fontinalis

Brook trout

44.30

Salvelinus

namaycush

Lake trout, siscowet

27.71

35.04

Oncorhynchus

tshawytscha

Chinook salmon

40.00

Oncorhynchus

kisutch

Coho salmon

37.29

1,5,12

Oncorhynchus

mykiss

Rainbow trout

25.69

33.71

10,11

Micropterus

salmoides

Largemouth bass

32.00

Hyalella

azteca

Scud

23.50

Lestes

congener

Damselfly

20.00

Peltodytes

sp.

Beetle

20.00

Asellus

brevicaudus*

Aquatic sowbug

10.00

Salmo

trutta

Brown trout

8.519

1,5,6

Chaoborus

flavicans

Midge

4.000

Chaoborus

sp.

Phantom midge

3.300

3.633

Lymnaea

stagnalis

Great pond snail

3.300

Notonecta

undulata

Backswimmer

3.000

Pteronarcys

californica

Stonefly

2.121

Note 1: Species that are bold and italicized indicate those associated with the four most sensitive genera used to derive the FAV in
the 1980 ALC document. Underlined species with an asterisk (*) indicate known or suspected Oregon non-resident species, and for
this evaluation, only those non-resident species below the criterion or related to the four most sensitive genera used in the derivation
of the 304(a) criteria are identified as such.

B. Evaluation of the Protectiveness of the Oregon Freshwater Acute Criterion

Following review of GMAV values in Table 2.1.9-1, all tested genera and species had values
greater than Oregon's acute criterion concentration for lindane. Further, all SMAV/2 values are
greater than the criterion. Therefore, EPA concluded that acute effects to these species are not
expected to occur at concentrations equal to or lower than the criterion and thus these species and
the aquatic life designated use would be fully protected by the lindance acute criterion.

2.1.9.2 References for Lindane

A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the acute table, and are the source from which EPA obtained SMAVs
(acute table).

Reference No.

Used Reference Citation

(associated with reference numbers and provided above in Table 2.1.9-1)

Acute References

Federle, P.F. and W.J. Collins. 1976. Insecticide toxicity to three insects from Ohio ponds. Ohio J. Sci. 76(1): 19-

-------
Reference No.

Used Reference Citation

(associated with reference numbers and provided above in Table 2.1.9-1)

24.

Bluzat, R. and J. Seuge. 1979. Effects of three insecticides (lindane, fenthion, and carbaryl) on the acute toxicity
to four aquatic invertebrate species and the chronic toxicity. Environ. Pollut. 18(1): 51-70 (FRE) (ENG ABS)

Maund, S.J., A. Peither, E.J. Taylor, I. Juttner, R. Beyerle-Pfnur, J.P. Lay and D. Pascoe. 1992. Toxicity of
lindane to freshwater insect larvae in compartments of an experimental pond. Ecotoxicol. Environ. Saf. 23: 76-88
(OECDG Data File)

Macek, K.J. and W.A. McAllister. 1970. Insecticide susceptibility of some common fish family representatives.
Trans. Am. Fish. Soc. 99(1): 20-27 (Publ in Part As 6797)

Office of Pesticide Programs. 2000. Pesticide Ecotoxicity Database (Formerly: Environmental Effects Database
(EEDB)). Environmental Fate and Effects Division, U.S. EPA, Washington, D.C.

Sanders, H.O. 1972. Toxicity of some insecticides to four species of malacostracan crustaceans. U.S. Bur. Sport
Fish. Wildl. Tech. Pap. 66: 3.

Hooftman, R.N., D.M.M. Adema and J. Kauffman-Van Bommel. 1989. Developing a Set of Test Methods for the
Toxicological Analysis of the Pollution Degree of Waterbottoms. Rep. No. 16105, Netherlands Organization for
Applied Scientific Research: 68 p.(DUT)

Blockwell, S.J., S.J. Maund and D. Pascoe. 1998. The Acute toxicity of lindane to Hyaiella azteca and the
development of a sublethal bioassay based on precopulatory guarding behavior. Arch. Environ. Contam. Toxicol.
35(3):432-440

Tooby, T.E. and F.J. Durbin. 1975. Lindane residue accumulation and elimination in rainbow trout (Saimo
qairdnerii Richardson) and roach (Rutiius rutiius Linnaeus). Environ. Pollut. 8(2): 79-89

Tooby, T.E., P.A. Hursey and J.S. Alabaster. 1975. The acute toxicity of 102 pesticides and miscellaneous
substances to fish. Chem. Ind. (Lond.) 21: 523-526

Katz, M. 1961. Acute toxicity of some organic insecticides to three species of salmonids and to the threespine
stickleback. Trans. Am. Fish. Soc. 90(3): 264-268

Macek, K.J., K.S. Buxton, S.K. Derr, J.W. Dean and S. Sauter. 1976. Chronic Toxicity of Lindane to Selected
Aquatic Invertebrates and Fishes. EPA-600/3-76-046, U.S. EPA, Duluth, MN: 50 p.

El Sebae, A.H., M.A. El Amayem, I. Sharaf and M. Massod. 1986. Factors affecting acute and chronic toxicity of
chlorinated pesticides and their biomagnification in Alexandria Region. In: Papers Presented at the FAO/UNEP
Meeting on the Toxicity and Bioaccumulation of Selected Substances in Marine Organisms, Rovinj, Yugoslavia,
5-9 Nov., 1984, FAO Fish. Rep. No. 334 (Suppl.): 73-79.

Macek, K.J., C. Hutchinson and O.B. Cope. 1969. The effects of temperature on the susceptibility of bluegills and
rainbow trout to selected pesticides. Bull. Environ. Contam. Toxicol. 4(3): 174-183 (Publ in Part As 6797)

Randall, W.F., W.H. Dennis and M.C. Warner. 1979. Acute toxicity of dechlorinated DDT, chlordane and lindane
to bluegill (Lepomis macrochirus) and Daphnia maqna. Bull. Environ. Contam. Toxicol. 21 (6): 849-854

Sanders, H.O. 1969. Toxicity of pesticides to the crustacean Gammarus iacustris. Tech. Pap. No. 25, Bur. Sports
Fish. Wildl., Fish Wildl. Serv., U.S.D.I., Washington, D.C.: 18 p. (Author Communication Used) (Used with
Reference 732) (Publ in Part As 6797)

Santharam, K.R., B. Thayumanavan and S. Krishnaswamy. 1976. Toxicity of some insecticides to Daphnia
carinata King, an important link in the food chain in the freshwater ecosystems. Indian J. Ecol. 3(1): 70-73
(OECDG Data File)

Call, D.J., L.T. Brooke, N. Ahmad and D.D. Vaishnav. 1981. Aquatic Pollutant Hazard Assessments and
Development of a Hazard Prediction Technology by Quantitative Structure-Activity Relationships. Second
Quarterly Report, U.S. EPA Cooperative Agreement No. CR 809234-01-0, Center for Lake Superior
Environmental Studies, University of Wisconsin, Superior, Wl: 74 p. (Publ in Part As 12448)

Henderson, C., Q.H. Pickering and C.M. Tarzwell. 1959. Relative toxicity often chlorinated hydrocarbon
insecticides to four species offish. Trans. Am. Fish. Soc. 88(1): 23-32

Nunogawa, J.H., N.C. Burbank Jr., R.H.F. Young and L.S. Lau. 1970. Relative Toxicities of Selected Chemicals
to Several Species of Tropical Fish. Water Resour. Res. Center, University of Hawaii, Honululu, HI: 38 p. (U.S.
NTIS PB-196312)

Green, D.W.J., K.A. Williams and D. Pascoe. 1986. Studies on the acute toxicity of pollutants to freshwater
macroinvertebrates. 4. Lindane (gamma-Hexachlorocyclohexane). Arch. Hydrobiol. 106(2): 263-273

Chin, Y.N. and K.I. Sudderuddin. 1979. Effect of methamidophos on the growth rate and esterase activity of the
common carp Cyprinus carpio L. Environ. Pollut. 18(3): 213-220.

Zhang, F. and X. Li. 1987. Toxicity of HCH towards the eggs and larvas of pond frog and fish. C. A. Sel.-Environ.
Pollut. 25: 107-213 327B / China Environ. Sci.(Zhongguo Huanjing Kexue) 7(2): 39-42 (CHI)

Bakthavathsalam, R. and Y.S. Reddy. 1982. Toxicity and behavioural responses of Anabas testudineus (Bloch)
exposed to pesticides. Indian J. Environ.Health 24(1): 65-68.

Zayapragassarazan, A. and V. Anandan. 1996. Effect of gamma-HCH on the protein profiles of selected tissues
of the air-breathing fish Anabas testudineus (Bloch). Environ. Ecol. 14(1): 55-59.

Sanders , H.O and O.B. Cope. 1966. Toxicities of several pesticides to tow species of clacoderns. Trans. Am.
Soc. 95: 165.

Ferrando, M.D., E. Andreu-Moliner, M.M. Almar, C. Cebrian and A. Nunez. 1987. Acute toxicity of
organochlorined pesticides to the European eel, Anguiiia anguiiia: The dependency on exposure time and
temperature. Bull. Environ. Contam. Toxicol. 39(3): 365-369 (OECDG Data File)

-------
Reference No.

Used Reference Citation

(associated with reference numbers and provided above in Table 2.1.9-1)

Ferrando, M.D., E. Sancho and E. Andreu-Moliner. 1991. Comparative acute toxicities of selected pesticides to
Anguiiia anguiiia. J. Environ. Sci. Health B26(5/6): 491-498.

Ferrando, M.D., M.M. Almar and E. Andreu. 1988. Lethal toxicity of lindane on a teleost fish, Anguiiia anguiiia
from Albufera Lake (Spain): Hardness and temperature effects. J. Environ. Sci. Health B23(1): 45-52

Hermens, J., H. Canton, N. Steyger and R. Wegman. 1984. Joint effects of a mixture of 14 chemicals on mortality
and inhibition of reproduction of Daphnia magna. Aquat. Toxicol. 5(4): 315-322.

Sanders, H.O. 1970. Pesticide toxicities to tadpoles of the Western chorus frog Pseudacris triseriata and Fowler's
toad Bufo woodhousii fowieri. Copeia 2: 246-251 (Author Communication Used) (Publ in Part As 6797)

B. Studies That EPA Considered But Did Not Utilize In This Determination

1) For the studies that were not utilized, but the most representative SMAV/2 fell
below the criterion, or, if the studies were for a species associated with one of the
four most sensitive genera used to calculate the FAV in the most recent national
ambient water quality criteria dataset used to derive the CMC26, EPA is providing
a transparent rationale as to why they were not utilized (see below).

26 U.S. EPA. 1980. Ambient Water Quality Criteria for Hexachlorocyclohexane. EPA-440/5-80-054.

-------
2.1.10 NICKEL

2.1.10.1 Evaluation of the Acute Freshwater Criterion Concentration for Nickel
A. Presentation of Toxicological Data

Oregon adopted a freshwater acute criterion concentration of 470 |ig/L for nickel that is
expressed as a function of total hardness in the water column and in terms of the dissolved
concentration of the metal. This dissolved metal concentration reflects the criterion normalized
to a total hardness of 100 mg/L as CaCC>3 and is the same as the freshwater CMC recommended

for use nationally by EPA for the protection of aquatic life . EPA developed the recommended
criterion in accordance with the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.1.10-1 provides available SMAVs and GMAVs based on available acute toxicity data for
nickel to aquatic animals from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Table 2.1.10-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values
(GMAVs) for Nickel

Genus

Species

Common name

Most
Representative
SMAV
(Mg/L)

GMAV
(Mg/L)

Acute References

(used in the calculation
of the SMAV)

Asellus

aquaticus

Aquatic sowbug

213476

Chironomus

tentans

Midge

224108

Chironomus

riparis

Midge

131329

171557

Salmo

salar

Atlantic salmon

161455

Gambusia

affinis

Mosquitofish

142295

Crangonyx

pseudogracilis

Amphipod

118578

Fundulus

diaphanus

Banded killifish

77582

13,14

Acroneuria

lycorias

Stonefly

72582

Carassius

auratus

Goldfish

44470

21,25

Tubifex

tubifex

Tubificid worm

31214

Oncorhynchus

kisutch

Coho salmon

34655

Oncorhynchus

mykiss

Rainbow trout

24003

28841

Nais

sp.

Oligochaete

25294

Gammarus

sp.

Scud, Amphipod

23321

Amnicola

sp.

Spire snail

22908

Lepomis

macrochirus

Bluegill

38695

Lepomis

gibbosus

Pumpkinseed

13533

22884

Anguilla

rostrata

American eel

21850

13,14

Poecilia

reticulata

Guppy

17331

Thymallus

arcticus

Arctic grayling

16882

Morone

americana

White perch

22944

13,14

Morone

saxatilis

Striped bass

10609

15602

12,13,14

Bufo

melanostictus

Common Indian
toad

15016

Philodina

acuticornis

Rotifer

14436

Dugesia

tigrina

Turbellarian,

12904

15,16

27 See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.

The data which serve as the basis for the current nationally-recommended criteria are from the 1995 Great Lakes Initiative Updates to these
criteria as cited in: U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient Water.
EPA-820-B-96-001.

-------

Most

Representative
SMAV

GMAV

Acute References

(used in the calculation

Genus

Species

Common name

(Mg/L)

(M9/L)

of the SMAV)

Flatworm

Eohemerella

subvaria*

Mayfly

8317

Am bl oolites

ruoestris*

Rock bass

7735

Cyprinus

carpio

Common carp

2681

Daphnia

puiicaria

Cladoceran

3663

Daphnia

magna

Cladoceran

1977

7,8,9

Daphnia

pulex

Cladoceran

743.8

1753

Pimephales

promelas

Fathead minnow

1230

5,6

Moina

macrocopa40

Cladoceran

921.5

Physa

gyrina

Snail

746.3

Utterbackia

imbecillis*

Mussel

259.8

Note 2: The reporting of calculated values has been limited to a minimum of four significant figures for convenience and use in this
evaluation with the exception of very high values, which are reported as whole numbers - see text in section 2.2 of this evaluation for
an explanation of this decision, particularly for metals such as nickel which are normalized to a water hardness of 100 mg/L as
CaC03 and expressed on a dissolved metal basis for a comparison with the acute criterion concentration.

B. Evaluation of the Protectiveness of the Oregon Freshwater Acute Criterion

Following review of GMAV values in Table 2.1.10-1, 28 of 29 genera have values greater than
Oregon's acute criterion concentration for nickel. The most sensitive genera is not expected to
reside in the state, indicating all resident genera are protected by the criterion. Therefore, EPA
concluded that acute effects to these genera are not expected to occur at concentrations equal to
or lower than the criterion, and thus these genera and the aquatic life designated use would be
protected by the criterion.

When compared to Oregon's acute criterion concentration for nickel, SMAV/2 values for four
test species (the mussel Utterbackia (=Anodonta) imbecillis, the cladocerans Daphniapulex and
Moina macrocopa, and the gastropod Physa gyrina) were lower than the acute criterion
concentration of 470.0 |ig/L dissolved nickel. Three of these species (I). pulex, P. gyrina, andM
macrocopa) are expected to reside in Oregon waters. Therefore, EPA reviewed the data from the
studies that make up the most representative SMAV for these three resident species and
determined whether the SMAV/2 values are quantitatively different from the criterion value of
470.0 |ig/L.

The overall hardness adjusted SMAV for D. pulex was 743.8 |ig/L, with 5 and 95 percent
confidence intervals of 688.8 and 803.3 |ig/L. When divided by two, the SMAV/2 for D. pulex
was 371.9 |ig/L (text box A -D. pulex acute).

The overall hardness adjusted SMAV fori5, gyrina was 746.3 |ig/L. Five and 95 percent
confidence intervals were not reported for the single test run used to determine the SMAV for
this species. When divided by two, the SMAV/2 fori5, gyrina was 373.1 |ig/L

-------
The overall hardness adjusted SMAV for M. macrocopa was 921.5 |ig/L, with 5 and 95 percent
confidence intervals of 575.5 and 1475 |ig/L. When divided by two, the SMAV/2 forM
macrocopa was 460.7 |ig/L (text box B -M. macrocopa acute). Given that uncertainty bounds at
the low end of the acute toxicity spectra are generally expected to be broader than the bounds
around the central value, this SMAV/2 value of 460.7 |ig/L maybe be statistically
indistinguishable from the criterion value of 470 |ig/L. Thus it is likely that the acute criterion
value would be sufficiently protective of this species.

Because the Oregon acute criterion for nickel is greater SMAV/2 for D. pulex, P. gyrina, andM
macrocopa, the occurrence of ambient concentrations equal to or greater than the Oregon CMC
for nickel may result in acute toxicity to some individuals of these species. However, as noted
above, 29 of 30 genera have values greater than Oregon's acute criterion concentration for
nickel, indicating that all except a small proportion of genera are protected at ambient
concentrations equal to or lower than the chronic criterion and thus the aquatic life designated
use would be expected to be protected by the criterion.

Freshwater nickel acute criterion comparison

Text Box A (acute) - Basis for the meta analysis comparing the SMAV/2 for the cladoceran (D.
pulex) to the acute criterion for nickel (470.0 |ig/L dissolved metal concentration normalized to a
hardness of 100 mg/L as CaCOs).

Daphnia pulex

Reported Values

Hardness Normalized Values

Hardness Normalized Values/2

Hardness LC50 5% CI

95% CI

LC50 5% CI 95% CI

LC50/2

CMC

130 912.3 844.9

985.3

743.8 688.8 803.3

371.9

470

(SMAV)

(SMAV/2)

Text Box B (acute) - Basis for the meta analysis comparing the SMAV/2 for the cladoceran (M
macrocopa) to the acute criterion for nickel (470.0 |ig/L dissolved metal concentration
normalized to a hardness of 100 mg/L as CaCOs).

Moina macrocopa

Reported Values

Hardness Normalized Values

Hardness Normalized Values/2

95%

Hardness LC50 5% CI

LC50 5% CI 95% CI

LC50/2

CMC

44 461.0 288.0

738.0

921.5 575.7 1475

460.7

470

(SMAV)

(SMAV/2)

2.1.10.2 Evaluation of the Chronic Freshwater Criterion Concentration for Nickel
A. Presentation of Toxicological Data

-------
Oregon adopted a freshwater chronic criterion concentration of 52 |ig/L for nickel expressed as
the dissolved metal concentration at a total hardness of 100 mg/L CaCC>3 in the water column.
This concentration is the same as the freshwater CCC recommended for use nationally by EPA

for the protection of aquatic life . EPA developed the recommended criterion in accordance
with the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.1.10-2 presents a compilation of the GMAVs from Table 2.1.10-1, any experimentally
determined SMCVs obtained from the criteria document and EPA ECOTOX download used for
the BE, and estimated GMCVs based on the GMAV/ACR. The 1995 update of the criteria

document for nickel reported an FACR of 17.99, which EPA calculated as the geometric mean
of three experimentally determined ACRs ranging from 5.478 for a saltwater invertebrate, the
mysid (Americamysis bahia) to 35.58 for a fish, Pimephalespromelas. EPA determined the
FACR of 17.99 with the ACRs from two freshwater species (Daphnia magna, Pimephales
promelas) and one saltwater species (Americamysis bahia). Since no additional acceptable ACRs
are available, EPA calculated the predicted SMCVs for nickel in Table 2.1.10-2 using an FACR
of 17.99 and the following equation: Predicted GMCV = GMAV/FACR.

EPA compared the GMCVs for each species to Oregon's nickel chronic criterion to determine
whether the chronic criterion will protect the species.

Table 2.1.10-2: Genus Mean Chronic Values (GMCVs) for Nickel

Genus

Species

Common name

GMAV
(M9/L)

SMCV
(Mg/L)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(Mg/L)

Asellus

aquaticus

Aquatic sowbug

213476

11866

Chironomus

tentans

Midge

Chironomus

riparis

Midge

171557

9536

Salmo

salar

Atlantic salmon

161455

8975

Gambusia

affinis

Mosquitofish

142295

7910

Crangonyx

pseudogracilis

Amphipod

118578

6591

Fundulus

diaphanus

Banded killifish

77582

4312

Acroneuria

lycorias

Stonefly

72582

4035

Carassius

auratus

Goldfish

44470

2472

Tubifex

tubifex

Tubificid worm

31214

1735

Oncorhynchus

kisutch

Coho salmon

Oncorhynchus

mykiss

Rainbow trout

28841

263.1

1603
(263.1)

Nais

sp.

Oligochaete

25294

1406

Gammarus

sp.

Scud, Amphipod

23321

1296

Amnicola

sp.

Spire snail

22908

1273

Lepomis

macrochirus

Bluegill

Lepomis

gibbosus

Pumpkinseed

22884

1272

Anguilla

rostrata

American eel

21850

1215

Poecilia

reticulata

Guppy

17331

963.4

Thymallus

arcticus

Arctic grayling

16882

938.4

Morone

americana

White perch

Morone

saxatilis

Striped bass

15602

867.3

Bufo

melanostictus

Common Indian

15016

834.7

28 See footnote 29 above.

29 U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient
Water. EPA-820-B-96-001.

-------

toad

Philodina

acuticornis

Rotifer

14436

802.5

Dugesia

tigrina

Turbellarian,
Flatworm

12904

717.3

Eohemerella

subvaria*

Mayfly

8317

462.3

Am bl oolites

ruoestris*

Rock bass

7735

430.0

Clistoronia

magnifica

Caddisfly

215.6

(215.6)

Cyprinus

carpio

Common carp

2681

149.0

Daphnia

puiicaria

Cladoceran

Daphnia

magna

Cladoceran

84.05

Daphnia

pulex

Cladoceran

1753

97.44
(84.05)

Pimephales

promelas

Fathead minnow

1230

345.5

4, 5

68.37
(345.5)

Moina

macrocopa

Cladoceran

921.5

51.22

Physa

gyrina

Snail

746.3

41.48

Utterbackia

imbecillis*

Mussel

259.8

14.44

See same notes as above under Table 2.1.10-1.

B. Evaluation of the Protectiveness of the Oregon Freshwater Chronic Criterion

Following the review of the measured SMCV values in Table 2.1.10-2, all tested species were
shown to have chronic values greater than Oregon's chronic criterion of 52 |ig/L for nickel.
Therefore, EPA concluded that all species with measured chronic data would be protected by the
chronic criterion. In extrapolating chronic values from acute data using the ACR, 27 of the 30
genera tested had predicted GMCVs greater than Oregon's chronic criterion for nickel.
Therefore, EPA concluded that chronic effects are not expected to occur at concentrations equal
to or lower than the criterion for these 27 genera, and all except a small proportion of genera are
protected at ambient concentrations equal to or lower than the chronic criterion, and thus the
designated use would be protected at ambient concentrations equal to or lower than the chronic
criterion.

When compared to Oregon's chronic criterion concentration for nickel, SMCV values for four
test species (the mussel Utterbackia (=Anodonta) imbecillis, the cladocerans Daphniapulex and
Moina macrocopa, and the gastropod Physa gyrina) were lower than the chronic criterion
concentration of 52.0 |ig/L dissolved nickel. Three of these species (I). pulex, P. gyrina, andM
macrocopa) are expected to reside in Oregon waters. Therefore, EPA reviewed the data from the
studies that make up the most representative SMAV for these three resident species and after
applying the ACR for nickel to these values, examined the SMCV values to determine whether
the SMCV values are quantitatively different from the criterion value of 52.0 |ig/L.

The SMCV for D. pulex was estimated by applying the ACR of 17.99 described above to the
hardness normalized SMAV of 743.9. The final SMCV was 41.35 |ig/L (text box C - D. pulex
chronic).

The SMCV fori5, gyrina was estimated by applying the ACR of 17.99 described above to the
SMAV. The final SMCV was 41.48 |ig/L. Five and ninety five percent confidence intervals
were not reported for the single test used to calculate the SMAV for this test species.

-------
The SMCV for M macrocopa was estimated by applying the ACR of 17.99 described above to
the SMAV. The final SMCV was 51.22 |ig/L (text box D -M. macrocopa chronic).

Because the Oregon acute criterion for nickel is greater than the SMCV for D. pulex, P. gyrina,
andM. macrocopa, EPA concludes that the occurrence of ambient concentration at or above the
Oregon CCC for nickel for more than 4 days every 3 years, may result in chronic effects in
individuals within these species.

EPA concluded that chronic effects not expected to occur for any species with actual chronic test
data , nor are chronic effects predicted to occur in 27 of 30 genera for which predicted chronic
values were generated, at concentrations equal to or lower than the criterion.

Freshwater nickel chronic criterion comparison

Text Box C (chronic) - Basis for the meta analysis comparing the SMCV for the cladoceran (D.
pulex) to the chronic criterion for nickel (52.0 |ig/L dissolved metal concentration normalized to
a hardness of 100 mg/L as CaC03).

Daphnia pulex

Reported Values

Hardness Normalized Values

Hardness Normalized SMCV

Hardness

LC50 5% CI

95% CI

LC50

5% CI

95% CI

ACR

(LC50 / ACR)

CCC

130

912.3 844.9

985.3

743.8

688.8

803.3

17.99

41.35

(SMCV)

Text Box D (chronic) - Basis for the meta analysis comparing the SMCV for the cladoceran (M
macrocopa) to the chronic criterion for nickel (52.0 |ig/L dissolved metal concentration
normalized to a hardness of 100 mg/L as CaCOs).

Moina macrocopa

Reported Values

Hardness Normalized Values

Hardness Normalized SMCV

Hardness LC50 5% CI

95% CI

LC50 5% CI 95% CI ACR

(LC50 / ACR)

CCC

44 461.0 288.0

738.0

921.5 575.7 1475 17.99

51.22

(SMCV)

2.1.10.3 References for Nickel

A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the acute and chronic tables, and are the source from which EPA
obtained SMAVs (acute table) and experimentally-derived SMCVs (chronic table).

Reference No.

Used Reference Citation

(associated with reference numbers and provided above in Tables 2.1.10-1 and 2.1.10-2)

Acute References

-------
1

Used Reference Citation

(associated with reference numbers and provided above in Tables 2.1.10-1 and 2.1.10-2)

Keller, A.E. and S.G. Zam. 1991. The acute toxicity of selected metals to the freshwater mussel, Anodonta

imbecilis. Environ. Toxicol. Chem. 10(4): 539-546.

Jindal, R. and A. Verma. 1990. Heavy metal toxicity to Daphnia puiex. Indian J. Environ. Health 32(3): 289-

292.

Nebeker, A.V., A. Stinchfield, C. Savonen and G.A. Chapman. 1986. Effects of copper, nickel and zinc on

three species of Oregon freshwater snails. Environ. Toxicol. Chem. 5(9): 807-811.

Pokethitiyook, P., E.S. Upatham and O. Leelhaphunt. 1987. Acute toxicity of various metals to Moina

macrocopa. Nat. Hist. Bull. Siam. Soc. 35(1/2): 47-56.

Lind, D., K. Alto and S. Chatterton. 1978. Regional Copper-Nickel Study. Draft Report, Minnesota

Environmental Quality Board, St. Paul, MN: 54 p.

Pickering, Q.H. 1974. Chronic toxicity of nickel to the fathead minnow. J. Water Pollut. Control Fed. 46: 760-

765.

Biesinger, K.E. and G.M. Christensen. 1972. Effects of various metals on survival, growth, reproduction and

metabolism of Daphnia magna. J. Fish Res. Board Can. 29: 1691-1700.

Call, D.J., L.T. Brooke, N. Ahmad and J.E. Richter. 1983. Toxicity and Metabolism Studies with EPA Priority
Pollutants and Related Chemicals in Freshwater Organisms. EPA 600/3-83-095, U.S. EPA, Duluth, MN: 120

p. (U.S. NTIS PB83-263665).

Chapman, G.A., S. Ota and F. Recht. 1980. Effects of Water Hardness on the Toxicity of Metals to Daphnia

magna. Manuscript. U.S. EPA, Corvallis, OR: 17 p.(Author Communication Used).

Virk, S. and R.C. Sharma. 1995. Effect of nickel and chromium on various life stages of Cyprinus carpio

Linn. Indian J. Ecol. 22(2): 77-81.

Warnick, S. L. and H. L. Bell. 1969. The acute toxicity of some heavy metals to different species of aquatic

insects. J. Water Pollut. Control Fed. 41(2): 280-284.

Palawski, D., J.B. Hunn and F.J. Dwyer. 1985. Sensitivity of young striped bass to organic and inorganic

contaminants in fresh and saline waters. Trans. Am. Fish. Soc. 114: 748-753.

Rehwoldt, R., G. Bida and B. Nerrie. 1971. Acute toxicity of copper, nickel, and zinc ions to some Hudson

River fish species. Bull. Environ. Contam. Toxicol. 6(5): 445-448.

Rehwoldt, R., L.W. Menapace, B. Nerrie and D. Allessandrello. 1972. The effect of increased temperature

upon the acute toxicity of some heavy metal ions. Bull. Environ. Contam. Toxicol. 8(2): 91-96.

See, C.L. 1976. The Effect of Sublethal Concentrations of Selected Toxicants on the Negative Phototactic
Response of Dugesia tigrina. Ph.D. Thesis, Virginia Polytechnic Institute and State University, Blacksburg,

VA: 79 p.

See, C.L., A.L. Buikema, Jr. and J. Cairns, Jr. 1974. The effects of selected toxicants on survival of Dugesia

tigrina (Turbellaria). ASB (Assoc. Southeast. Biol.) Bull. 21(2): 82.

Cairns, J., Jr., K.W. Thompson and A.C. Hendricks. 1981. Effects of Fluctuating, Sublethal Applications of
Heavy Metal Solutions upon the Gill Ventilation Response of Bluegills (Lepomis macrochirus). EPA-600/3-

81-003, U.S. EPA, Cincinnati, OH: 104 p. (U.S. NTIS PB81-150997).

Buikema, A.L., Jr., J. Cairns, Jr. and G.W. Sullivan. 1974. Evaluation of Phiiodina acuticornis (Rotifera) as

bioassay organisms for heavy metals. Water Resour. Bull. Am. Water Res. Assoc. 10(4): 648-661.

Khangarot, B.S. and P.K. Ray. 1987. Sensitivity of toad tadpoles, Bufo meianostictus (Schneider), to heavy

metals. Bull. Environ. Contam. Toxicol. 38(3): 523-527.

Buhl, K.J. and S.J. Hamilton. 1991. Relative sensitivity of early life stages of Arctic grayling, Coho salmon,

and rainbow trout to nine inorganics. Ecotoxicol. Environ. Saf. 22: 184-197.

Pickering, Q.H. and C. Henderson. 1966. The acute toxicity of some heavy metals to different species of

warmwater fishes. Air Water pollut. Int. J. 10: 453-463.

Rehwoldt, R., L. Lasko, C. Shaw and E. Wirhowski. 1973. The acute toxicity of some heavy metal ions

toward benthic organisms. Bull. Environ. Contam. Toxicol. 10(5): 291-294.

Nebeker, A.V., C. Savonen and D.G. Stevens. 1985. Sensitivity of rainbow trout early life stages to nickel

chloride. Environ. Toxicol. Chem. 4(2): 233-239.

Khangarot, B.S. 1991. Toxicity of metals to a freshwater tubificid worm, Tubifex tubifex (Muller). Bull.

Environ. Contam. Toxicol. 46: 906-912.

Ding, S.R. 1980. Acute toxicities of vanadium, nickel and cobalt to several species of aquatic organisms.

Environ. Qual. 1: 17-21 (CHI) (ENG ABS).

Martin, T.R. and D.M. Holdich. 1986. The acute lethal toxicity of heavy metals to peracarid crustaceans

(with particular reference to fresh-water asellids and gammarids). Water Res. 20(9): 1137-1147.

Powlesland, C. and J. George. 1986. Acute and chronic toxicity of nickel to larvae of Chironomus riparis

(Meigan). Environ. Poll., (Series A). 42: 47-64.

Kallanagoudar, Y.P. and H.S. Patil. 1997. Influence of water hardness on copper, zinc and nickel toxicity to

Gambusia affinis (B&G). J. Environ. Biol. 18(4): 409-413.

Grande, M. and S. Andersen. 1983. Lethal effects of hexavalent chromium, lead and nickel on young

stages of Atlantic salmon (Salmo salar L.) in soft water. Vatten 39(4): 405-416.

Khangarot, B.S. and P.K. Ray. 1989. Sensitivity of midge larvae of Chironomus tentans Fabricius (Diptera
Chironomidae) to heavy metals. Bull. Environ. Contam. Toxicol. 42(3): 325-330.

-------
Reference No.

Used Reference Citation

(associated with reference numbers and provided above in Tables 2.1.10-1 and 2.1.10-2)

Chronic References

Chapman, G.A., S. Ota and F. Recht. 1980. Effects of Water Hardness on the Toxicity of Metals to Daphnia
maqna. Manuscript. U.S. EPA, Corvallis, OR.

Nebeker, A.V., C. Savonen, R.J. Baker and J.K. McCrady. 1984. Effects of copper, nickel, and zinc on the
life cycle of the caddisfly Ciistoronia maqnifica (Limnephilidae). Environ. Toxicol. Chem. 3: 645-649.

Nebeker, A.V., C. Savonen and D.G. Stevens. 1985. Sensitivity of rainbow trout early life stages to nickel
chloride. Environ. Toxicol. Chem. 4(2): 233-239.

Lind, D., K. Alto and S. Chatterton. 1978. Regional Copper-Nickel Study. Draft Report, Minnesota
Environmental Quality Board, St.Paul, MN: 54 p.

Pickering, Q.H. 1974. Chronic toxicity of nickel to the fathead minnow. J. Water Pollut. Control Fed. 46: 760-
765.

B. Studies That EPA Considered But Did Not Utilize In This Determination

derive the CMC , EPA is providing a transparent rationale as to why they were
not utilized (see below).

30 U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient
Water. EPA-820-B-96-001.

-------
2.1.11 PENTACHLOROPHENOL

2.1.11.1 Evaluation of the Acute Freshwater Criterion Concentration for
Pentachlorophenol

A. Presentation of Toxicological Data

Oregon adopted a freshwater acute criterion concentration of 19 |ig/L (at pH 7.8) for
pentachlorophenol that is expressed as a function of pH. This concentration is the same as the
freshwater acute criterion concentration recommended for use nationally by EPA for the
protection of aquatic life31. EPA developed the recommended criterion in accordance with the
1985 Guidelines pursuant to CWA section 304(a).

Table 2.1.11-1 provides available SMAVs and GMAVs based on available acute toxicity data for
arsenic to aquatic life from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Table 2.1.11-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values

(GMAVs) for Pentachloropheno

Genus

Species

Common name

Most
Representative
SMAV
(MS)"-)

GMAV
(Mg/L)

Acute References

(used in the calculation
of the SMAV)

Orconectes

immunis

Crayfish

162206

Caenorhabditis

elegans

Nematode

56093

Mysis

relicta

Opossum shrimp

44249

Tanytarsus

dissimilis

Midge

41586

Sepedon

fuscipennis

Marsh fly

39185

Asellus

intermedius

Aquatic sowbug

13680

Lumbriculus

variegatus

Oligochaete, worm

4326

Pteronarcys

dorsata

Stonefly

1809

Brachionus

calyciflorus

Rotifer

1771

Rhyacodrilus

montana

Tubificid worm

1543

Stylodrilus

heringianus

Oligochaete

1508

15,42

Gillia

altilis

Buffalo pebblesnail

1489

Utterbackia

imbecillis

Mussel

1363

Spirosperma

nikolskyi

Oligochaete

2016

Spirosperma

ferox

Tubificid worm

884.5

1335

Quistadrilus

multisetosus

Oligochaete

1173

Jordanella

floridae

Flagfish

1133

Tubifex

tubifex

Tubificid worm

828.0

15,42,49

Helisoma

trivolvis

Ramshorn snail

740.5

Xenopus

laevis

Clawed toad

736.2

Poecilia

reticulata

Guppy

721.7

43,44,45,46,47

Limnodrilus

hoffmeisteri

Tubificid worm,
Oligochaete

674.0

15,42,49

Crangonyx

pseudogracilis

Amphipod

635.6

Branchiura

sowerbyi

Oligochaete

575.8

31 See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.

The data which serve as the basis for the current nationally-recommended criteria are from: U.S. EPA. 1996. 1995

Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient Water. EPA-820-B-96-

001.

-------

Most

Representative
SMAV

GMAV

Acute References

(used in the calculation

Genus

Species

Common name

(MS)"-)

(Mg/L)

of the SMAV)

Pontoporeia

hoyi

Scud

490.7

Physa

gyrina

Pouch snail

487.9

Micropterus

salmoides

Largemouth bass

387.8

Gammarus

fasciatus

Scud

429.2

Gammarus

pseudolimnaeus

Scud

337.9

380.8

18,38

Daphnia

pulex

Cladoceran

312.6

26,32,33,34,37

Daphnia

magna

Cladoceran

270.4

290.8

4,26,27,28,29,30,31,32,
33,34,35,36,37

Salmo

salar

Atlantic salmon

264.9

Pimephales

promelas

Fathead minnow

260.8

3,4,10,16,18,19,20,21,
22,23,24

Ceriodaphnia

reticulata

Cladoceran

247.9

Nais

communis

Oligochaete

245.8

Carassius

auratus

Goldfish

242.0

3,4,16

Xyrauchen

texanus

Razorback sucker

229.0

Gambusia

affinis

Western
mosquitofish

223.4

Aplexa

hypnorum

Snail

223.2

Varichaeta

pacifica

Worm

215.9

Simocephalus

vetulus

Cladoceran

213.2

Lepomis

macrochirus

Bluegill

208.3

3,4

Gila

elegans

Bonytail

188.1

Salvelinus

fontinalis

Brook trout

126.0

Ran a

catesbeiana

Bullfrog

125.2

Ptychocheilus

lucius

Colorado squawfish

114.5

Ictalurus

punctatus

Channel catfish

98.02

3,4

Oncorhynchus

clarki (henshawi)

Lahontan cutthroat
trout

139.0

Oncorhynchus

mykiss

Rainbow trout

130.5

4,11,12,13

Oncorhynchus

nerka

Sockeye salmon

121.3

5,9

Oncorhynchus

tshawytscha

Chinook salmon

118.6

7,8

Oncorhynchus

kisutch

Coho salmon

117.5

5,6

Oncorhvnchus

ailae*

Apache trout

89.97

clarki

Oncorhynchus

(includes 1 henshawi
and 1 stomias)

Cutthroat trout

33.72

Oncorhvnchus

clarki (stomias)*

Greenback
cutthroat trout

8.179

93.5332

Cyprinus

carpio

Common carp

16.08

B. Evaluation of the Protectiveness of the Oregon Freshwater Acute Criterion

Following review of GMAV values in Table 2.1.11-1, 45 of the 46 genera had values greater
than Oregon's acute criterion concentration for pentachlorophenol. The most sensitive genera is
not expected to reside in Oregon indicating all resident tested genera are protected by the

32 This value was calculated as the geometric mean of Oncorhynchus clarki combined (33.72), (). gilae (89.97), ().
kisutch (117.5), O. tshawytscha (118.6), O. nerka (121.3), and O. mykiss (130.5). Subspecies SMAVs retained for
transparency.

-------
criterion. Therefore, EPA concluded that acute effects to these species are not expected to occur
at concentrations lower than the criterion, and thus these species and the designated use would be
protected by the criterion.

When compared to Oregon's acute criterion concentration for pentachlorophenol, SMAV/2
values for two test species were lower than the acute criterion concentration of 19 |ig/L
pentachlorophenol. The first SMAV/2 value lower than the acute criterion concentration pertains
to the common carp. This species is exotic to, but currently residing in, Oregon waters. The
subspecies O. clarkii henshaw are expected to reside in Oregon waters, however the subspecies
0. clarki stomias is not. Therefore, EPA reviewed the data from the studies that make up the
most representative SMAV for the resident species and compared the confidence intervals of the
SMAV for these species to determine whether the SMAV/2 values are quantitatively different
from the criterion value of 19 |ig/L.

The pH normalized SMAV for C. carpio was 16.08 |ig/L. This value was based on a single study
by Verna et al. (1981), and no confidence intervals were reported. The pH normalized SMAV/2
of 8.042 |ig/L was less than the criterion for pentachlorophenol of 19 |ig/L.

The overall pH normalized SMAV/2 for cutthroat trout of 16.86 |ig/L is based on the geometric
mean of one LC50 value for each of two subspecies - 0. clarki stomias (greenback cutthroat
trout, and O. clarki henshawi (Lahontan cutthroat trout), respectively. The greenback cutthroat
trout is not expected to reside in Oregon waters, and thus, exclusion of this LC50 value from the
SMAV for the species increases the SMAV to well above the criterion; i.e, the SMAV for
cutthroat trout based on O. clarki henshawi alone is 139.01 ug/L, SMAV/2 = 69.52 ug/L (see
Table 3.1.14-1 above).

Because the Oregon acute criterion for pentachlorophenol is greater than the SMAV/2 for the
invasive Cyprinus carpio, EPA concludes that the Oregon CMC for pentachlorophenol may not
be protective of all individuals within this species. Because the Oregon acute criterion for
pentachlorophenol is substantially lower than the SMAV/2 for the Oregon resident
Onchorhynchus clarki henshawi, EPA concludes that the Oregon CMC for pentachlorophenol is
protective of this species.

2.1.11.2 Evaluation of the Chronic Freshwater Criterion Concentration for
Pentachlorophenol

A. Presentation of Toxicological Data

Oregon adopted a freshwater chronic criterion concentration of 15 |ig/L (at pH 7.8) for
pentachlorophenol that is expressed as a fuction of pH. This concentration is the same as the
freshwater chronic criterion concentration recommended for use nationally by EPA for the

-------
33

protection of aquatic life . EPA developed the recommended criterion in accordance with the
1985 Guidelines pursuant to CWA section 304(a).

Table 2.1.11-2 presents a compilation of the GMAVs from Table 2.1.11-1, any experimentally
determined SMCVs obtained from the criteria document and the BE, and estimated GMCVs
based on the GMAV/ACR. The 1986 criteria document for pentachlorophenol34 reported an
FACR of 3.166, which EPA calculated as the geometric mean of five experimentally determined
ACRs ranging from 0.8945 for the cladoceran (Simocephalus vetulus) to 6.873 for the saltwater
fish species Cyprinodon variegatus. Note: the 1995 GLI Update to the freshwater criteria for
pentachlorophenol excludes this ACR for sheepshead minnow (C. variegatus) because the
update was for the freshwater criterion only. Since no additional acceptable ACRs are available,
EPA calculated the predicted GMCVs for pentachlorophenol in Table 2.1.11-2 using an FACR
of 3.166 and the following equation: Predicted GMCV = GMAV/FACR.

EPA compared the GMCVs for each species to Oregon's pentachlorophenol chronic criterion to
determine whether the chronic criterion will protect the genera.

Table 2.1.11-2: Genus Mean Chronic Values (GMCVs) for Pentachlorophenol

Chronic

SMCV

References

Genus

Species

Common name

GMAV
(MS)"-)

(Mg/L)

('experimentally
derived}

(used in the
calculation of
the SMCV)

Predicted
GMCV
(MS)"-)

Orconectes

immunis

Crayfish

162206

51234

Caenorhabditis

elegans

Nematode

56093

17717

Mysis

relicta

Opossum shrimp

44249

13976

Tanytarsus

dissimilis

Midge

41586

13135

Sepedon

fuscipennis

Marsh fly

39185

12377

Asellus

intermedius

Aquatic sowbug

13680

4321

Lumbriculus

variegatus

Oligochaete, worm

4326

1366

Pteronarcys

dorsata

Stonefly

1809

571.3

Brachionus

calyciflorus

Rotifer

1771

559.4

Rhyacodrilus

montana

Tubificid worm

1543

487.3

Stylodrilus

heringianus

Oligochaete

1508

476.2

Gillia

altilis

Buffalo pebblesnail

1489

470.3

Utterbackia

imbecillis

Mussel

1363

430.5

Spirosperma

nikolskyi

Oligochaete

Spirosperma

ferox

Tubificid worm

1335

421.8

Quistadrilus

multisetosus

Oligochaete

1173

370.4

Jordanella

floridae

Flagfish

1133

357.8

Tubifex

tubifex

Tubificid worm

828.0

261.5

Helisoma

trivolvis

Ramshorn snail

740.5

233.9

Xenopus

laevis

Clawed toad

736.2

232.5

Poecilia

reticulata

Guppy

721.7

227.9

Limnodrilus

hoffmeisteri

Tubificid worm,
Oligochaete

674.0

212.9

Crangonyx

pseudogracilis

Amphipod

635.6

200.8

Branchiura

sowerbyi

Oligochaete

575.8

181.9

Pontoporeia

hoyi

Scud

490.7

155.0

Physa

gyrina

Pouch snail

487.9

<31.79

154.1
(<31.79)

Micropterus

salmoides

Largemouth bass

387.8

122.5

Gammarus

fasciatus

Scud

33 See footnote 34 above.

34 U.S. EPA. 1986. Ambient Water Quality Criteria Document for Pentachlorophenol-1986. EPA 440/5-86-005.

-------
Genus

Species

Common name

GMAV
(MS)"-)

SMCV
(Mg/L)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(MS)"-)

Gammarus

pseudolimnaeus

Scud

380.8

120.3

Daphnia

pulex

Cladoceran

Daphnia

magna

Cladoceran

290.8

91.84

Salmo

salar

Atlantic salmon

264.9

83.67

Pimephales

promelas

Fathead minnow

260.8

64.19

3,4,5

82.37
(64.19)

Ceriodaphnia

reticulata

Cladoceran

247.9

<6.780

78.31
(<6.780)

Nais

communis

Oligochaete

245.8

77.63

Carassius

auratus

Goldfish

242.0

76.44

Xyrauchen

texanus

Razorback sucker

229.0

72.34

Gambusia

affinis

Western
mosquitofish

223.4

70.57

Aplexa

hypnorum

Snail

223.2

70.49

Varichaeta

pacifica

Worm

215.9

68.21

Simocephalus

vetulus

Cladoceran

213.2

208.6

67.33
(208.6)

Lepomis

macrochirus

Bluegill

208.3

65.80

Gila

elegans

Bonytail

188.1

59.42

Salvelinus

fontinalis

Brook trout

126.0

39.81

Ran a

catesbeiana

Bullfrog

125.2

39.56

Ptychocheilus

lucius

Colorado squawfish

114.5

36.17

Ictalurus

punctatus

Channel cattish

98.02

30.96

Oncorhynchus

clarki
(henshawi)

Lahontan cutthroat
trout

Oncorhynchus

my kiss

Rainbow trout

20.93

Oncorhynchus

nerka

Sockeye salmon

Oncorhynchus

tshawytscha

Chinook salmon

Oncorhynchus

kisutch

Coho salmon

Oncorhvnchus

ailae*

Apache trout

Oncorhynchus

clarki
(includes 1
henshawi and 1
stomias)

Cutthroat trout

Oncorhvnchus

clarki (stomias)*

Greenback
cutthroat trout

93.53

29.54
(20.93)

Cyprinus

carpio

Common carp

16.08

5.080

See same notes as above under Table 2.1.11-1.

B. Evaluation of the Protectiveness of the Oregon Freshwater Chronic Criterion

Following the review of the GMCV values in Table 2.1.11-2, 45 of the 46 genera had values
greater than Oregon's chronic criterion for pentachlorophenol. No test data is below the criterion.
Therefore, EPA concluded that chronic effects are not expected to occur at concentrations lower
than the criterion and thus these species and designated use would be protected by the criterion.

When compared to Oregon's chronic criterion concentration for pentachlorophenol, SMCV
values for three test species were lower than the acute criterion concentration of 15 |ig/L
pentachlorophenol. The first SMCV value lower than the acute criterion concentration pertains to
the common carp. This species is expected to reside in Oregon waters. The second SMCV is for
Ceriodaphnia reticulate, which is also expected to reside in Oregon waters. The subspecies of
Onchorhynchus clarki, 0. clarki henshawi is expected to reside in Oregon waters, however the

-------
subspecies 0. clarki stomias is not. Therefore, EPA reviewed the data from the studies that make
up the most representative SMCVs for this species and compared the confidence intervals of
these SMCVs to determine whether the SMCV values were quantitatively different from the
criterion value of 15 |ig/L.

Of the test species with SMCV values lower than the chronic criterion concentration for
pentachlorophenol, the cutthroat trout ((). clarki) is excluded from consideration for reasons
described above in section 3.1.16.1.B. Although the overall SMCV for cutthroat trout of 10.65
|ig/L is lower than the CCC for pentachlorophenol of 15 |ig/L, when the SMCV of the non-
resident greenback cutthroat trout (O. clarki stomias) is excluded from the analysis, the SMCV
for the resident Lahontan cutthroat trout subspecies (O. clarki henshawi) is well above the CCC
for pentachlorophenol (43.92 |ig/L vs. 15 |ig/L).

The SMCV for the common carp was estimated by applying the FACR of 3.166 to the SMAV of
16.08 |ig/L described in section 3.1.14.1.B to obtain a pH-normalized SMCV of 5.079 |ig/L (see
Verna et al. 1981).

The SMCV for the freshwater cladoceran Ceriodaphnia reticulata was determined to be less
than the pH normalized LOEC value of 6.780 |ig/L (text box A - C. reticulata chronic). Because
the NOEC value in the single study used to determine the SMCV for this test species was the
control or nominal "zero" concentration (Hedtke et al. 1986), a SMCV based on the geometric
mean could not be calculated. However, the pH normalized LOEC, which represents the upper
boundary of the probable "true" SMCV for C. reticulata, falls below the CCC.

Because the Oregon chronic criterion for pentachlorophenol is substantially lower than the
SMCV for the Oregon resident 0. clarki henshawi, EPA concludes that the Oregon CCC for
pentachlorphenol is protective of this species. Because the Oregon chronic criterion for
pentachlorophenol is greater than the SMCV for Cyprinus carpio, EPA concludes that the
Oregon CMC for pentachlorophenol may not be protective of all individuals within this species.
Because the Oregon chronic criterion for pentachlorophenol is greater than the LOEC for
Ceriodaphnia reticulata, Oregon's chronic WQC for pentachlorophenol may not be protective of
all individuals within this species.

Freshwater pentachlorophenol chronic criterion comparison

Text Box A - Basis for the meta analysis comparing the SMCV for the cladoceran (C. reticulata)
to the acute criterion for pentachlorophenol (15.0 |ig/L).

Ceriodaphnia reticulata

Reported Values

pH Normalized Values

pH NOEC LOEC

CV NOEC LOEC CV

CCC

7.3 0 4.100

<4.100 0 6.780 <6.780

(SMCV)

-------
2.1.11.3 References for Pentachlorophenol

A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the acute and chronic tables, and are the source from which EPA
obtained SMAVs (acute table) and experimentally-derived SMCVs (chronic table).

Reference No.

Used Reference Citation

(associated with reference numbers and provided above in tables 2.1.11-1 and 2.1.11-2)

Acute References

Sappington, L.C., F.L. Mayer, F.J. Dwyer, D.R. Buckler, J.R. Jones and M.R. Ellersieck. 2001. Contaminant
sensitivity of threatened and endangered fishes compared to standard surrogate species. Environ. Toxicol.
Chem. 20(12): 2869-2876.

Verma, S.R., I.P. Tonk and R.C. Dalela. 1981. Determination of the maximum acceptable toxicant
concentration (MATC) and the safe concentration for certain aquatic pollutants. Acta Hydrochim. Hydrobiol.
9(3): 247-254.

Phipps, G.L. and G.W. Holcombe. 1985. A method for aquatic multiple species toxicant testing: Acute
toxicity of 10 chemicals to 5 vertebrates and 2 invertebrates. Environ. Pollut. Ser. A Ecol. Biol. 38(2): 141-
157 (Author Communication Used) (OECDG Data File).

Thurston, R.V., T.A. Gilfoil, E.L. Meyn, R.K. Zajdel, T.L. Aoki and G.D. Veith. 1985. Comparative toxicity of
ten organic chemicals to ten common aquatic species. Water Res. 19(9): 1145-1155.

Davis, J.C. and R.A.W. Hoos. 1975. Use of sodium pentachlorophenate and dehydroabietic acid as
reference toxicants for salmonid bioassays. J. Fish. Res. Board Can. 32(3): 411-416.

Iwama, G.K. and G.L. Greer. 1980. Effect of a bacterial infection on the toxicity of sodium
pentachlorophenate to juvenile Coho salmon. Trans. Am. Fish. Soc. 109(2): 290-292.

Johnson, W.W. and M.T. Finley. 1980. Handbook of Acute Toxicity of Chemicals to Fish and Aquatic
Invertebrates. Resorce Publ. 137. U.S. Fish and Wildlife Service, Washington, DC: 58.

Webb, P.W. and J.R. Brett. 1973. Effects of sublethal concentrations of sodium pentachlorophenate on
growth rate, food conversion efficiency and swimming performance in underyearling sockeye salmon
(Oncorhynchus nerka). J. Fish. Res. Board Can. 30(4): 499-507.

Cardwell, R.D., D.G. Foreman, T.R. Payne and D.J.Wilbur. 1976. Acute Toxicity of Selected Toxicants to
Six Species of Fish. EPA-600/3-76-008, U.S. EPA, Duluth, MN: 125 p. (Publ in Part As 2149).

Fogels, A. and J.B. Sprague. 1977. Comparative short-term tolerance of zebrafish, blagfish, and rainbow
trout to five poisons including potential reference toxicants. Water Res. 11(9): 811-817.

Hodson, P.V., D.G. Dixon and K.L.E. Kaiser. 1984. Measurement of median lethal dose as a rapid
indication of contaminant toxicity to fish. Environ. Toxicol. Chem. 3(2): 243-254.

McCarty, L.S., P.V. Hodson, G.R. Craig and K.L.E. Kaiser. 1985. The use of quantititative structure activity
relationships to predict the acute and chronic toxicities of organic chemcials to fish. Environ. Toxicol. Chem.
4: 595-606.

Hedtke, S.F., C.W. West, K.N. Allen, T.J. Norberg-King and D.I. Mount. 1986. Toxicity of pentachlorophenol
to aquatic organisms under naturally varying and controlled environmental conditions. Environ. Toxicol.
Chem. 5(6): 531-542.

Chapman, P.M., M.A. Farrell and R.O. Brinkhurst. 1982a. Relative tolerances of selected aquatic
oligochaetes to individual pollutants and environmental factors. Aquat. Toxicol. 2(1): 47-67.

Adelman, I.R., Jr. 1976. Standard Test Fish Development. Part I. Fathead Minnows (Pimephaies promeias)
and Goldfish (Carassius auratus) as Standard Fish in Bioassays and Their Reaction to Potential Reference
Toxicants. EPA-600/3-76-061A, U.S. EPA, Duluth, MN: 77.

Chapman, P.M. and D.G. Mitchell. 1986. Acute tolerance tests with the oligochaetes Nais communis
(Naididae) and liyodriius frantzi (Tubificidae). Hydrobiologia 137(1): 61-64.

Spehar, R.L., H.P. Nelson, M.J. Swanson and J.W. Renoos. 1985. Pentachlorophenol toxicity to amphipods
and fathead minnows at different test pH values. Environ. Toxicol. Chem. 4: 389-397.

Phipps, G.L., G.W. Holcombe and J.T. Fiandt. 1981. Acute toxicity of phenol and substituted phenols to the
fathead minnow. Bull. Environ. Contam. Toxicol. 26(5): 585-593 (Author Communication Used) (OECDG
Data File).

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Used Reference Citation

(associated with reference numbers and provided above in tables 2.1.11-1 and 2.1.11-2)

Ruesink, R.G. and L.L. Smith, Jr. 1975. The relationship of the 96-hour LC50 to the lethal threshold
concentration of hexavalent chromium, phenol, and sodium pentachlorophenate for fathead minnows
(Pimephaies promeias Rafinesque). Trans. Am. Fish. Soc. 104: 567-570.

Broderius, S.J., M.D. Kahl and M.D. Hoglund. 1995. Use of joint toxic response to define the primary mode
of toxic action for diverse industrial organic chemicals. Environ. Toxicol. Chem. 14(9): 1591-1605 (Author
Communication Used).

Geiger, D.L., C.E. Northcott, D.J. Call and L.T. Brooke. 1985. Acute Toxicities of Organic Chemicals to
Fathead Minnows (Pimephaies promeias), Vol. 2. Center for Lake Superior Environmental Stud., Univ. of
Wisconsin-Superior, Superior, Wl: 326.

Geiger, D.L., L.T. Brooke and D.J. Call. 1990. Acute Toxicities of Organic Chemicals to Fathead Minnows
(Pimephaies promeias), Vol. 5. Center for Lake Superior Environmental Stud., Univ. of Wisconsin-Superior,
Superior, Wl: 332.

Hall, L.H., L.B. Kierand G. Phipps. 1984. Structure-activity relationship studies on the toxicities of benzene
derivatives: I. An additivity model. Environ. Toxicol. Chem. 3: 355-365.

Burridge, L.E. and K. Haya. 1990. Seasonal lethality of pentachlorophenol to juvenile Atlantic salmon. Bull.
Environ. Contam. Toxicol. 45(6):888-892.

Canton, J.H. and D.M.M. Adema. 1978. Reproducibility of short-term and reproduction toxicity experiments
with Daphnia magna and comparison of Daphnia magna with Daphnia pulex and Daphnia cucullata in
short-term experiments. Hydrobiologia 59: 135-140.

LeBlanc, G.A. 1980. Acute toxicity of priority pollutants to Water Flea (Daphnia magna). Bull. Environ.
Contam. Toxicol. 24(5): 684-691 (OECDG Data File).

Adema, D.M.M. 1978. Daphnia magna as a test animal in acute and chronic toxicity tests. Hydrobiologia 59:
125-134

Adema, D.M.M. and G.J. Vink. 1981. A comparative study of the toxicity of 1,1,2-trichloroethane, dieldrin,
pentachlorophenol and 3,4-dicloroaniline for marine and fresh water organisms. Chemosphere 10: 533-
554.

Hermens, J., P. Leuwangh and A. Musch. 1984. Joint toxicity of mixtures of groups of organic aquatic
pollutants to the guppy (Poecilia reticulata). Ecotoxicol. Environ. Safety 9: 321-326.

Mount, D.I. and T.J. Norberg. 1984. A seven-day life-cycle cladoceran toxicity test. Environ. Toxicol. Chem.
3(3): 425-434 (Author Communication Used).

Lewis, P.A. and C.I. Weber. 1985. A study of the reliability of Daphnia acute toxicity tests. In: R.D. Cardwell,
R. Purdy and R.C. Bahner (Eds.), Aquatic Toxicology and Hazard Assessment, 7th Symposium, ASTM
STP 854, Philadelphia, PA: 73-86.

Hall, W.S., R.L. Paulson, L.W. Hall, Jr. and D.T. Burton. 1986. Acute toxicity of cadmium and sodium
pentachlorophenate to daphnids and fish. Bull. Environ. Contam. Toxicol. 37(2): 308-316.

Elnabarawy, M., A.N. Welter and R.R. Robideau. 1986. Relative sensitivity of three daphnid species to
selected organic and inorganic chemcials. Environ. Toxicol. Chem. 5: 393-398.

Brooke, L.T., D.J. Call, D.E. Hammermeister, A. Hoffman and C.E. Northcott. Manuscript. Acute Toxicities
of Five Chemicals in Different Natural Waters. Center for Lake Superior Environmental Studies, University
of Wisconsin-Superior, Superior, Wl.

Kuhn, R., M. Pattard, K. Pernak and A. Winter. 1989. Results of the harmful effects of selected water
pollutants (anilines, phenols, aliphatic compounds) to Daphnia magna. Water Res. 23(4): 495-499 (OECDG
Data File).

Lewis, P.A. and W.B. Horning II. 1991. Differences in acute toxicity test results of three reference toxicants
on Daphnia at two temperatures. Environ. Toxicol. Chem. 10: 1351-1357.

Call, D.J., L.T. Brooke, N. Ahmad, and J.E. Richter. 1983. Toxicity and Metabolism Studies with EPA
Priority Pollutants and Related Chemicals in Freshwater Organisms. EPA 600/3-83-095, U.S.EPA, Duluth,
MN :120 p.(U.S.NTIS PB83-263665).

Johansen, P.H., R.A.S. Mathers, J.A. Brown and P.W. Colgan. 1985. Mortality of early life stages of
largemouth bass, Micropterus salmoides due to pentachlorophenol exposure. Bull. Environ. Contam.
Toxicol. 34(3): 377-384.

Landrum, P.F. and W.S. Dupuis. 1990. Toxicity and toxicokinetics of pentachlorophenol and carbaryl to
Pontoporeia hoyi and Mysis relicta. In: W.G. Landis and W.H. Van der Schalie (Eds.), Aquatic Toxicology
and Risk Assessment, 13th Volume, ASTM STP 1096, Philadelphia, PA: 278-289.

Chapman, P.M., M.A. Farrell and R.O. Brinkhurst. 1982b. Relative tolerances of selected aquatic
oligochaetes to combinations of pollutants and environmental factors. Aquat. Toxicol. 2(1): 69-78.

Brown, J.A., P.H. Johansen, P.W. Colgan and R.A. Mathers. 1985. Changes in the predator-avoidance
behavior of juvenile guppies (Poecilia reticulata) exposed to pentachlorophenol. Can. J. Zool. 63: 2001-
2005.

Khangarot, B.S. 1983. Acute toxicity of pentachlorophenol and antimycin to common guppy (Lebistes
reticulatus Peters). Indian J. Phys. Nat. Sci. 3: 25-29.

Gupta, P.K., V.S. Mujumdar, P.S. Rao and V.S. Durve. 1982a. Toxicity of phenol, pentachlorophenol and

-------
Reference No.

Used Reference Citation

(associated with reference numbers and provided above in tables 2.1.11-1 and 2.1.11-2)

sodium pentachlorophenolate to a freshwater teleost Lebistes reticuiatus (Peters). Acta Hydrochim.
Hydrobiol. 10(2): 177-181.

Saarikoski, J. and M. Viluksela. 1981. Influence of pH on the toxicity of substituted phenols to fish. Arch.
Environ. Contam. Toxicol. 10(6): 747-753.

Salkinoja-Salonen, M., M. Saxelin and J. Pere. 1981. Analysis of toxicity and biodegradability of
organochlorine compounds released into the environment in bleaching effluents of kraft pulping. In: L. H.
Keith (Ed.), Advances in the Identification and Analysis of Organic Pollutants in Water, Butterworth,
Stoneham, MA 2: 1131-1164.

Fort, D.J., E.L. Stover and J.A. Bantle. 1996. Integrated ecological hazard assessment of waste site soil
extracts using FETAXand short-term fathead minnow teratogenesis assay. In: T.W. La Point, F.T. Price,
and E.E. Little (Eds.), Environmental Toxicology and Risk Assessment, 4th Volume, ASTM STP 1262,
Philadelphia, PA: 93-109.

Chapman, P.M., M.A. Farrell and R.O. Brinkhurst. 1982c. Effects of species interactions on the survival and
respiration of Limnodriius hoffmeisteri and Tubifex tubifex (Oligochaeta, Tubificidae) exposed to various
pollutants and environmental factors. Water Res. 16: 1405-1408.

Keller, A.E. 1993. Acute toxicity of several pesticides, organic compounds, and a wastewater effluent to the
freshwater mussel, Anodonta imbeciiis, Ceriodaphnia dubia, and Pimephaies promeias. Bull Environ.
Contam. Toxicol. 51(5): 696-702.

Stuart, R.J. and J.B. Robertson. 1985. Acute toxicity of pentachlorophenol to the freshwater snail, Giilia
altilis. Bull. Environ. Contam. Toxicol. 35(5): 633-640.

Call, D.J. and L.T. Brooke. 1982. Report on Stonefly Toxicity Tests with Priority Pollutants. Center for Lake
Superior Environmental Stud., Univ. of Wisconsin-Superior, Superior, Wl: 2.

Mccoy, L.E. and J.E. Joy. 1977. Tolerance of Sepedon fuscipennis and Dictya sp. larvae (Diptera:
Sciomyzidae) to the molluscicides Bayer 73 and sodium pentachlorophenate. Environ. Entomol. 6(2): 198-
202.

Kammenga, J.E., C.A.M. Van Gestel and J. Bakker. 1994. Patterns Of sensitivity To cadmium and
pentachlorophenol among nematode species From different taxonomic and ecological groups. Arch.
Environ. Contam. Toxicol. 27(1): 88-94.

Radix, P., M. Leonard, C. Papantoniou, G. Roman, E. Saouter, S. Gallotti-Schmitt, H. Thiebaud and P.
Vasseur. 1999. Comparison of Brachionus caiycifiorus 2-d and microtox chronic 22-h tests with Daphnia
magna 21-d test for the chronic toxicity assessment of chemicals. Environ. Toxicol. Chem. 18(10): 2178-
2185.

Chronic References

Dominguez, S.E. and G.A. Chapman. 1984. Effect of pentachlorophenol on the growth and mortality of
embryonic and juvenile steelhead trout. Arch. Environ. Contam. Toxicol. 13: 739-743.

Holcombe, G.W., G.L. Phipps and J.T. Fiandt. 1982. Effects of phenol, 2,4-dimethylphenol, 2,4-
dichlorophenol, and pentachlorophenol on embryo, larval, and juvenile fathead minnows (Pimephaies
promeias). Arch. Environ. Contam. Toxicol. 11(1): 73-78

Spehar, R.L., H.P. Nelson, M.J. Swanson and J.W. Renoos. 1985. Pentachlorophenol toxicity to amphipods
and fathead minnows at different test pH values. Environ. Toxicol. Chem. 4: 389-397.

Arthur, A.D. and D.G. Dixon. 1994. Effects of rearing density on the growth response of juvenile fathead
minnow (Pimephaies promeias) under toxicant-induced stress. Can. J. Fish. Aquat. Sci. 51 (2): 365-371.

B. Studies That EPA Considered But Did Not Utilize In This Determination

1) For the studies that were not utilized, but the most representative SMAV/2 or
most representative SMCV fell below the criterion, or, if the studies were for
a species associated with one of the four most sensitive genera used to
calculate the FAY in the most recent national ambient water quality criteria

-------
35

dataset used to derive the CMC , EPA is providing a transparent rationale as
to why they were not utilized (see below).

2) For the studies that were not utilized because they were not found to be

pertinent to this determination (including failing the QA/QC procedures listed
in Appendix A) upon initial review of the download from ECOTOX, EPA is
providing the code that identifies why EPA determined that the results of the
study were not reliable (see Appendix K).

35 U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient
Water. EPA-820-B-96-001.

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2.1.12 SELENIUM (SELENATE AND SELENITE)

Please see the primary decision document regarding the disapproval of this criterion.

-------
2.1.13 SILVER

2.1.13.1 Evaluation of the Acute Freshwater Criterion Concentration for Silver
A. Presentation of Toxicological Data

Oregon adopted a freshwater acute criterion concentration of 3.2 |ig/L for silver that is expressed
as a function of total hardness in the water column and in terms of the dissolved concentration of
the metal. This dissolved metal concentration reflects the criterion normalized to a total hardness
of 100 mg/L as CaCC>3 and is the same as the freshwater CMC recommended for use nationally
by EPA for the protection of aquatic life36. EPA developed the recommended criterion in
accordance with the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.1.13-1 provides available SMAVs and GMAVs based on available acute toxicity data for
silver to aquatic life from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Table 2.1.13-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values
(GMAVs) for Silver

Most

Acute References

Representative
SMAV

GMAV

(used in the
calculation of the

Genus

Species

Common name

(Mg/L)

SMAV)

Orconectes

immunis

Crayfish

1901

Tanytarsus

dissimilis

Midge

1426

Aplexa

hypnorum

Snail

433.1

3,12

Gambusia

affinis

Western
mosquitofish

120.3

Nephelopsis

obscura

Leech

98.47

Chironomus

tentans

Midge

95.94

Hydra

sp.

Hydra

82.18

Ictalurus

punctatus

Channel catfish

59.42

Simocephalus

vetulus

Water flea

50.35

Lepomis

macrochirus

Bluegill

44.14

Oncorhynchus

kisutch

Coho salmon

46.40

Oncorhynchus

mykiss

Rainbow trout

31.81

38.42

3,11,14,15,16

Isonychia

bicolor

Mayfly

34.82

Thymallus

arcticus

Arctic grayling

33.97

Jordanella

floridae*

Flagfish

31.72

Pimephales

promelas

Fathead minnow

23.23

3,10,11,12,13

Gammarus

oseudolimnaeus*

Scud

15.52

Crangonyx

pseudogracilis

Amphipod

14.00

Leptophlebia

sp.

Mayfly

13.88

Cottus

bairdi

Mottled sculpin

9.242

Rhinichthys

osculus

Speckled dace

8.887

Tubifex

tubifex

Tubificid worm

5.642

Daphnia

pulex

Cladoceran

4.103

4,5

Daphnia

magna

Cladoceran

3.056

3.541

Cyprinus

carpio

Common Carp

1.543

36 See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.

The data which serve as the basis for the current nationally-recommended criteria are from: U.S. EPA. 1980.
Ambient Water Quality Criteria Documents for Silver. Unpublished document authored by W. A. Brungs and D.J.
Hansen, U.S. EPA ERL-Narragansett and Gulf Breeze, respectively.

-------

Most

Acute References

Representative
SMAV

GMAV

(used in the
calculation of the

Genus

Species

Common name

(Mg/L)

(M9/L)

SMAV)

Ceriodaphnia

reticulata

Cladoceran

3.122

4,5

Ceriodaphnia

dubia

Cladoceran

0.4211

1.147

Poecilia

reticulata*

Guppy

1.132

Note 1: Species that are bold and italicized indicate those associated with the four most sensitive genera used to derive the FAV in
the 1980 unpublished ALC document. Underlined species with an asterisk (*) indicate known or suspected Oregon non-resident
species, and for this evaluation, only those non-resident species below the criterion or related to the four most sensitive genera used
in the derivation of the 304(a) criteria are identified as such.

Note 2: The reporting of calculated values has been limited to a minimum of four significant figures for convenience and use in this
evaluation with the exception of very high values, which are reported as whole numbers - see text in section 2.2 of this evaluation for
an explanation of this decision, particularly for metals such as silver which are normalized to a water hardness of 100 mg/L as
CaC03 and expressed on a dissolved metal basis for a comparison with the acute criterion concentration.

B. Evaluation of the Protectiveness of the Oregon Freshwater Acute Criterion

Following review of GMAV values in Table 2.1.13-1, 22 of the 25 tested genera have values
greater than Oregon's acute criterion concentration for silver. Therefore, EPA concluded that
acute effects to these species and genera are not expected to occur at concentrations equal to or
lower than the acute criterion. P. reticulata is an exotic not expected to reside in Oregon waters.

C. carpio is a non-native, invasive species. When these two values are removed from the table,
22 of 23 genera have values greater than Oregon's acute criterion concentration for silver.

When compared to Oregon's acute criterion concentration for silver, SMAV/2 values for five test
species (four planktonic cladocerans and a tubificid worm) were lower than the acute criterion
concentration of 3.2 |ig/L dissolved silver. Ceriodaphnia dubia, Daphnia magna, C. reticulata,

D. pulex and T. tubifex are expected to reside in Oregon waters. Therefore, EPA reviewed the
data from the studies that make up the most representative SMAV for these five species and
compared the SMAV for this species to determine whether the SMAV/2 values are quantitatively
different from the criterion value of 3.2 |ig/L.

The hardness normalized dissolved SMAV for Ceriodaphnia dubia was 0.4211 |ig/L, with 5 and
95 percent confidence intervals of 0.4211 and 0.5264 |ig/L. When divided by two, the SMAV/2
for C. dubia was 0.2106 |ig/L (text box A - C. dubia).

The hardness normalized dissolved SMAV for Daphnia magna was 3.056 |ig/L, with 5 and 95
percent confidence intervals of 2.716 and 3.395 |ig/L. When divided by two, the SMAV/2 for I),
magna was 1.528 |ig/L (text box B - I), magna).

The hardness normalized dissolved SMAV for Ceriodaphnia reticulata was 3.122 |ig/L, with 5
and 95 percent confidence intervals of 2.358 and 3.881 |ig/L. When divided by two, the SMAV/2
for C. reticulata was 1.561 |ig/L (text box C - C. reticulata).

The hardness normalized dissolved SMAV for Daphnia pulex was 4.103 |ig/L. For the one study
with confidence intervals, the hardness normalized dissolved SMAV was 0.3583 |ig/L, with 5
and 95 percent confidence intervals of 0.3206 and 0.4337 |ig/L. When divided by two, the

-------
SMAV/2 for D. pulex was 2.052 |ig/L. For the study with confidence intervals, the SMAV/2 was
0.1792 |ig/L (text box D - I). pulex).

The hardness normalized dissolved SMAV for Tubifex tubifex was 5.642 |ig/L, with 5 and 95
percent confidence intervals of 3.822 and 10.01 |ig/L. When divided by two, the SMAV/2 for T.
tubifex was 2.821 |ig/L (text box E - T. tubifex).

Because the Oregon CMC for silver is greater than the SMAV/2 values for C. dubia, D. magna,
C. reticulata, D. pulex, and T. tubifex, EPA concludes that the occurrence of ambient
concentrations equal to or greater than the Oregon CMC for silver may result in acute toxicity to
some individuals within these species. As noted above, however, 22 of the 23 native, tested
genera have values greater than Oregon's acute criterion concentration for silver, and all except a
small proportion of genera are expected to be protected at ambient concentrations equal to or
lower than the chronic criterion, therefore EPA believes the aquatic life designated use will be
protected.

Freshwater silver acute criterion comparison

Text Box A (acute) - Basis for the meta analysis comparing the SMAV/2 for the cladoceran (C.
dubia) to the acute criterion for silver (3.2 |ig/L dissolved metal concentration normalized to a
hardness of 100 mg/L as CaCOs).

Ceriodaphnia dubia

Reported Values

Hardness Normalized Values

Hardness Normalized Values/2

Hardness LC50 5% CI

95% CI

LC50 5% CI 95% CI

LC50/2

CMC

88.30 0.40 0.40

0.50

0.4211 0.4211 0.5264

0.2106

3.2

(SMAV)

(SMAV/2)

Text Box B (acute) - Basis for the meta analysis comparing the SMAV/2 for the cladoceran (D.
magna) to the acute criterion for silver (3.2 |ig/L dissolved metal concentration normalized to a
hardness of 100 mg/L as CaCOs).

Daphnia magna

Reported Values

Hardness Normalized Values

Hardness Normalized Values/2

Hardness LC50 5% CI

95% CI

LC50 5% CI 95% CI

LC50/2

CMC

44.70 0.90 0.80

1.00

3.056 2.716 3.395

1.528

3.2

(SMAV)

(SMAV/2)

Text Box C (acute) - Basis for the meta analysis comparing the SMAV/2 for the cladoceran (C.
reticulata) to the acute criterion for silver (3.2 |ig/L dissolved metal concentration normalized to
a hardness of 100 mg/L as CaCOs).

Ceriodaphnia reticulata
Reported Values

Hardness LC50 5% CI

95% CI

Hardness Normalized Values

LC50 5% CI 95% CI

Hardness Normalized Values/2

LC50/2

CMC

240 1.40 1.10

1.70

0.26 0.21 0.32

0.13

3.2

-------
45

11.00

8.00

14.00

36.92

26.85

46.99

18.46

Geomean
(all)

3.92

2.97

4.88

SMAV

3.122

2.358

3.881

SMAV/2

1.561

Text Box D (acute) - Basis for the meta analysis comparing the SMAV/2 for the cladoceran (D.
pulex) to the acute criterion for silver (3.2 |ig/L dissolved metal concentration normalized to a
hardness of 100 mg/L as CaCC^).

Daphnia pulex

Reported Values

Hardness Normalized Values

Hardness Normalized Values/2

Hardness

LC50

5% CI

95% CI

SMAV

5% CI

95% CI

SMAV/2

CMC

240

1.90

1.70

2.30

0.36

0.32

0.43

0.18

3.2

14.00

46.99

23.50

Geomean

(all)

5.16

4.103

2.052

CI Only

1.90

1.70

2.30

0.3583

0.3206

0.4337

0.1792

Text Box E (acute) - Basis for the meta analysis comparing the SMAV/2 for the oligochaete (T.
tubifex) to the acute criterion for silver (3.2 |ig/L dissolved metal concentration normalized to a
hardness of 100 mg/L as CaCCb).

Tubifex tubifex

Reported Values

Hardness Normalized Values

Hardness Normalized Values/2

Hardness LC50 5% CI

95% CI

LC50 5% CI 95% CI

LC50/2

CMC

245.00 31.00 21.00

55.00

5.642 3.822 10.01

2.821

3.2

(SMAV)

(SMAV/2)

2.1.13.2 Evaluation of the Chronic Freshwater Criterion Concentration for Silver
A. Presentation of Toxicological Data

Oregon adopted a freshwater chronic criterion concentration of 0.10 |ig/L for silver expressed as
the dissolved metal concentration in the water column. This concentration is effectively the same
as the freshwater CCC (0.12 |ig/L) recommended in the 1987 draft silver criterion produced by

EPA that was never finalized .

Table 2.1.13-2 presents a compilation of the GMAVs from Table 2.1.13-1, any experimentally
determined SMCVs obtained from the criteria document and EPA ECOTOX download used for
the BE, and estimated GMCVs based on the GMAV/ACR. The 1980 criteria document for silver
did not report an FACR for silver because of the "variation in the results of chronic tests with
rainbow trout and the problem with determining an acute-chronic ratio for Daphnia magna" in
which case an FACR was not determined. A recent draft of the silver ALC document, however,
did provide an FACR for silver based on the values of three experimentally determined ACRs

37 Ambient Aquatic LifeWater Quality Criteria for Silver. Draft. 1987. EPA publication # 440/5-87-011.

-------
(expressed on a total recoverable metal basis) of 7.719, 13.66, and 33.37 for the saltwater shrimp
species Americamysis bahia, the fathead minnow, and rainbow trout, respectively. Thus, since
no additional acceptable ACRs are available, EPA calculated the predicted GMCVs for silver in
Table 2.1.13-2 using an FACR of 15.21 and the following equation: Predicted GMCV =
GMAV/FACR.

EPA compared the GMCVs for each species to Oregon's silver chronic criterion to determine
whether the chronic criterion will protect the aquatic life designated use.

Table 2.1.13-2: Genus Mean Chronic Values (GMCVs) for Silver

Genus

Species

Common name

GMAV
(MS)"-)

SMCV

(Mg/L)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV

(Mg/L)

Orconectes

immunis

Crayfish

1901

125.0

Tanytarsus

dissimilis

Midge

1426

93.75

Aplexa

hypnorum

Snail

433.1

28.48

Gambusia

affinis

Western
mosquitofish

120.3

7.912

Nephelopsis

obscura

Leech

98.47

6.474

Chironomus

tentans

Midge

95.94

6.308

Hydra

sp.

Hydra

82.18

5.403

Ictalurus

punctatus

Channel catfish

59.42

3.907

Simocephalus

vetulus

Water flea

50.35

3.310

Lepomis

macrochirus

Bluegill

44.14

2.902

Oncorhynchus

kisutch

Coho salmon

Oncorhynchus

mykiss

Rainbow trout

38.42

0.1596

1,2

2.526
(0.1596)

Isonychia

bicolor

Mayfly

34.82

2.290

Thymallus

arcticus

Arctic grayling

33.97

2.233

Jordanella

floridae*

Flagfish

31.72

2.086

Pimephales

promelas

Fathead minnow

23.23

0.4168

1.527
(0.4168)

Gammarus

oseudolimnaeus*

Scud

15.52

1.020

Crangonyx

pseudogracilis

Amphipod

14.00

0.9205

Leptophlebia

sp.

Mayfly

13.88

0.9123

Cottus

bairdi

Mottled sculpin

9.242

0.6076

Rhinichthys

osculus

Speckled dace

8.887

0.5843

Tubifex

tubifex

Tubificid worm

5.642

0.3709

Daphnia

pulex

Cladoceran

Daphnia

magna

Cladoceran

3.541

6.722

0.2328
(6.722)

Cyprinus

carpio

Common Carp

1.543

0.1014

Ceriodaphnia

reticulata

Cladoceran

Ceriodaphnia

dubia

Cladoceran

1.147

0.07541

Poecilia

reticulata*

Guppy

1.132

0.07442

See same notes as above under Table 2.1.13-1. Also note that the chronic criterion for silver is not hardness normalized, therefore,
the hardness-normalized SMAV cannot be used with the ACR to calculate the SMCV. Instead, the SMAV expressed only on a
dissolved metal basis is used here with the ACR to calculate the most representative SMCV (the SMAV expressed only a dissolved
metal basis is not provided in the table above).

B. Evaluation of the Protectiveness of the Oregon Freshwater Chronic Criterion

Following the review of the GMCV values in Table 2.1.13-2, 23 of 25 genera have GMCVs
greater than Oregon's chronic criterion for silver. Therefore, EPA concluded that acute effects to

-------
these species and genera are not expected to occur at concentrations equal to or lower than the
acute criterion. Two of the two genera (P. reticulata and C. carpid) are not native. The guppy is
not expected to reside in Oregon and the common carp is considered invasive, therefore these
species will not be considered further.

When compared to Oregon's chronic criterion concentration for silver, SMCV values for one test
species (Ceriodaphnia dubia) expected to reside in Oregon waters was lower than the chronic
criterion concentration of 0.10 |ig/L dissolved silver. Therefore, EPA reviewed the data from the
study that makes up the most representative SMCV for this species and compared the SMCV to
determine whether the SMCV value was quantitatively different from the criterion value of 0.10
Hg/L.

The dissolved SMCV for C. dubia was estimated by applying the ACR of 15.21 described above
to the dissolved SMAV obtained from Brooke et al. (1993). The dissolved SMCV for C. dubia
was 0.02235 |ig/L (text box F (chronic) - C. dubia).

Because the Oregon CCC for dissolved silver is greater than the SMCV for C. dubia, EPA
concludes that the occurrence of ambient concetraitons equal to or greater than Oregon CCC for
silver may result in chronic effects tosome individuals of this species. As noted above, 23 of 25
genera have GMCVs greater than Oregon's chronic criterion for silver, and all except a small
proportion of genera are expected to be protected at ambient concentrations equal to or lower
than the chronic criterion, therefore EPA believes the aquatic life designated use will be
protected.

Freshwater silver chronic criterion comparison

Text Box F (chronic) - Basis for the meta analysis comparing the SMCV for the cladoceran (C.
dubia) to the chronic criterion for silver (0.10 |ig/L dissolved metal concentration).

Ceriodaphnia dubia

Reported Values Dissolved Normalized Values Dissolved Normalized Chronic Values

Hardness LC50 5% CI 95% CI LC50 5% CI 95% CI ACR (LC50/ACR) CCC
88.30 0.4000 0.4000 0.5000 0.3400 0.3400 0.4250 15.21 0.02235 0.10
(SMCV)

2.1.13.3 References for Silver

A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the acute and chronic tables, and are the source from which EPA
obtained SMAVs (acute table) and experimentally-derived SMCVs (chronic table).

Used Reference Citation

Ref No.

(associated with reference numbers and provided above in Tables 2.1.13-1 and 2.1.13-2)

Acute References

Brooke, L.T. 1993. Effects of Food and Test Solution Age on the Toxicity of Silver to Three Freshwater Organisms.

-------
Ref No.

Used Reference Citation

(associated with reference numbers and provided above in Tables 2.1.13-1 and 2.1.13-2)

Progress Report to U.S. EPA for Contract No. 68-C1-0034, Work Assignment 1-10, September. Environmental
Health Laboratory, University of Wisconsin-Superior, Superior, Wl.

Khangarot, B.S. and P.K. Ray. 1988. The acute toxicity of silver to some freshwater fishes. Acta Hydrochim.
Hydrobiol. 16(5): 541-545.

Holcombe, G.W., G.L. Phipps, A.H. Sulaiman and A.D. Hoffman. 1987. Simultaneous multiple species testing: Acute
toxicity of 13 chemicals to 12 diverse freshwater families. Arch. Environ. Contam. Toxicol 16: 697-710.

Elnabarawy, M.T., A.N. Welter and R.R. Robideau. 1986. Relative sensitivity of three daphnid species to selected
organic and inorganic chemicals. Environ. Toxicol. Chem. 5: 393-398.

Mount, D.I. and T.J. Norberg. 1984. Aseven-day life-cycle cladoceran toxicity test. Environ. Toxicol. Chem. 3: 425-
434.

Khangarot, B.S. 1991. Toxicity of metals to a freshwater tubificid worm, Tubifex tubifex (Muller). Bull. Environ.
Contam. Toxicol. 46: 906-912.

Goettl, J.P., Jr. and P.H. Davies. 1978. Water Pollution Studies. Job Progress Report. Colorado Division of Wildlife,
Department of Natural Resources, Boulder, CO.

Brooke, L.T., D.J. Call, C.A. Lindberg, T.P. Markee, S.H. Poirier and D.J. McCauley. 1986. Acute Toxicity of Silver to
Selected Freshwater Invertebrates. Center for Lake Superior Environmental Studies, University of Wisconsin-
Superior, Superior, Wl. Report to Battelle Memorial Research Institute, Columbus, OH.

Martin, T.R. and D.M. Holdich. 1986. The acute lethal toxicity of heavy metals to peracarid crustaceans (with
particular reference to freshwater asellids and gammarids). Water Res. 20: 1137-1147.

Lima, A.R., C. Curtis, D.E. Hammermeister, D.J. Call and T.A. Felhaber. 1982. Acute toxicity of silver to selected fish
and invertebrates. Bull. Environ. Contam. Toxicol. 29: 184-189.

Lemke, A.E. 1981. Interlaboratory comparison acute testing set. EPA 600/3-81-005 or PB81-160772. National
Technical Information Service, Springfield, VA.

Holcombe, G.W., G.L. Phipps and J.T. Fiandt. 1983. Toxicity of selected priority pollutants to various aquatic
organisms. Ecotoxicol. Environ. Safety 7: 400-409.

EG & G Bionomics. 1979. The acute toxicity of various silver compounds to the fathead minnow (Pimephales
promelas). Report No. BW-79-12-576. Wareham, MA.

Davies, P.H., J.P. Goettl, Jr. and J.R. Winley. 1978. Toxicity of silver to rainbow trout (Saimo gairdneri). Water Res.
12:113-117.

Karen, D.J., D.R. Ownby, B.L. Forsythe, T.P. Bills, T.W. La Point, G.B. Cobb and S.J. Klaine. 1999. Influence of
water quality on silver toxicity to rainbow trout (O. mykiss), fathead minnows (P. promelas), and the waterflea (D.
magna). Environ. Toxicol. Chem. 18(1): 63-70.

Nebeker, A.V., C.K. McAuliffe, R. Msharand D.G. Stevens. 1983. Toxicity of silver to steelhead and rainbow trout,
fathead minnows and Daphnia magna. Environ. Toxicol. Chem. 2:95-104.

Buhl, K.J. and S.J. Hamilton. 1991. Relative sensitivity of early life stages of Arctic grayling, coho salmon, and
rainbow trout to nine inorganics. Ecotoxicol. Environ. Saf. 22:184-197.

Diamond, J.M., D.G. Mackler, M. Collins and D. Gruber. 1990. Derivation of a freshwater silver criteria for the New
River, Virginia, using representative species. Environ. Toxicol. Chem. 9(11): 1425-1434.

Khangarot, B.S. and P.K. Ray. 1987. Sensitivity of toad tadpoles, Bufo melanostrictus (Schneider), to heavy metals.
Bull. Environ. Contam. Toxicol. 38: 523-527.

Rao, T.S., M.S. Rao and S.B.S.K. Prasad. 1975. Median tolerance limits of some chemicals to the fresh water fish
"Cyprinus carpio." Indian J. Environ. Health 17(2): 140-146.

Chronic References

Davies, P.H., J.P. Goettl, Jr. and J.R. Winley. 1978. Toxicity of silver to rainbow trout (Salmo gairdneri). Water Res.
12: 113-117.

Nebeker, A.V., C.K. McAuliffe, R. Msharand D.G. Stevens. 1983. Toxicity of silver to steelhead and rainbow trout,
fathead minnows and Daphnia magna. Environ. Toxicol. Chem. 2: 95-104.

Holcombe, G.W., G.L. Phipps and J.T. Fiandt. 1983. Toxicity of selected priority pollutants to various aquatic
organisms. Ecotoxicol. Environ. Safety 7: 400-409.

Nebeker, A.V. 1982. Evaluation of a Daphnia magna renewal life-cycle test method with silver and endosulfan.
Water Res. 16: 739-744.

B. Studies That EPA Considered But Did Not Utilize In This Determination

-------
1) For the studies that were not utilized, but the most representative SMAV/2 or
most representative SMCV fell below the criterion, or, if the studies were for a
species associated with one of the four most sensitive genera used to calculate the
FAV in the most recent national ambient water quality criteria dataset used to

derive the CMC , EPA is providing a transparent rationale as to why they were
not utilized (see below).

38 U.S. EPA. 1980. Ambient Water Quality Criteria Documents for Silver. Unpublished document authored by W.
A. Brungs and D.J. Hansen, U.S. EPA ERL-Narragansett and Gulf Breeze, respectively.

-------
2.1.14 TRIBUTYLTIN

2.1.14.1 Evaluation of the Acute Freshwater Criterion Concentration for Tributyltin
A. Presentation of Toxicological Data

Oregon adopted a freshwater acute criterion concentration of 0.46 |ig/L for tributyltin. This
concentration is the same as the freshwater CMC recommended for use nationally by EPA for

the protection of aquatic life . EPA developed the recommended criterion in accordance with
the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.1.14-1 provides available SMAVs and GMAVs based on available acute toxicity data for
tributyltin to aquatic life from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Table 2.1.14-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values
(GMAVs) for Tributyltin

Most

Acute References

Representative
SMAV

GMAV

(used in the
calculation of the

Genus

Species

Common name

(MS)"-)

SMAV)

Elliptio

complanata

Mussel,
Eastern elliptio

24600

Salvelinus

naymaycush

Lake Trout

12.73

Culex

sp.

Mosquito

10.20

Lepomis

macrochirus

Bluegill

8.300

Ictalurus

punctatus

Channel catfish

5.500

Lumbriculus

variegatus

Annelid

5.400

Oncorhynchus

mykiss

Rainbow trout

4.571

3,4,5

Daphnia

magna

Cladoceran

4.300

Gammarus

oseudolimnaeus*

Scud

3.700

Pimephales

promelas

Fathead minnow

2.600

Chlorohvdra

viridissima*

Hydra

1.800

Hvdra

littoralis*

Hydra

1.201

1,2

Hvdra

oliaactis*

Hydra

1.140

1.170

Note 1: Species that are bold and italicized indicate those associated with the four most sensitive genera used to derive the FAV in
the 2003 ALC document. Underlined species with an asterisk (^indicate known or suspected Oregon non-resident species, and for
this evaluation, only those non-resident species below the criterion or related to the four most sensitive genera used in the derivation
of the 304(a) criteria are identified as such.

B. Evaluation of the Protectiveness of the Oregon Freshwater Acute Criterion

Following review of GMAV and SMAV/2 values in Table 2.1.14-1, all tested genera and species
had values greater than Oregon's acute criterion concentration for tributyltin. Therefore, EPA
concluded that acute effects to these genera are not expected to occur at concentrations equal to

39 U.S. EPA. 2003. Ambient Water Quality Criteria Document for Tributyltin (TBT) - Final. EPA-822/R-03-031.

-------
or lower than the criterion, and thus these genera and the aquatic life designated use would be
protected, by the criterion.

2.1.14.2 Evaluation of the Chronic Freshwater Criterion Concentration for Tributyltin
A. Presentation of Toxicological Data

Oregon adopted a freshwater chronic criterion concentration of 0.063 |ig/L for tributyltin. This
concentration is the same as the freshwater chronic criterion concentration recommended for use
nationally by EPA for the protection of aquatic life40. EPA developed the recommended
criterion in accordance with the 1985 Guidelines pursuant to CWA section 304(a). The process
used in the criteria document clearly outlines the consideration of sublethal effects data from
which this criterion was derived.

Table 2.1.14-2 presents a compilation of the GMAVs from Table 2.1.14-1, any experimentally
determined SMCVs obtained from the criteria document and EPA ECOTOX download used for
the BE, and estimated SMCVs based on the GMAV/ACR. The 2003 criteria document for
tributyltin41 reported an FACR of 12.69, which EPA calculated as the geometric mean of four
experimentally determined ACRs ranging from 4.7 for an acutely sensitive saltwater
invertebrate, the mysid (Acanthomysis sculpta) to 36.6 for an acutely sensitive invertebrate,
Daphnia magna. EPA determined the FACR of 12.69 with the ACRs from two freshwater
species {Daphnia magna, Pimephalespromelas) and two saltwater species (Acanthomysis
sculpta, Eurytemora affinis). Since no additional acceptable ACRs are available, EPA calculated
the predicted GMCVs for tributyltin in Table 2.1.14-2 using the FACR of 12.69 and the
following equation: Predicted GMCV = GMAV/FACR.

EPA compared the SMCVs for each species to Oregon's tributyltin chronic criterion to
determine whether the chronic criterion will protect the aquatic life designated use.

Table 2.1.14-2: Species Mean Chronic Values (SMCVs) for Tributyltin

Genus

Species

Common name

GMAV
(ng/L)

SMCV
(MS)"-)

(experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(M9/L)

Elliptio

complanata

Mussel,
Eastern elliptio

24600

1939

Salvelinus

naymaycush

Lake Trout

12.73

1.003

Culex

sp.

Mosquito

10.20

0.8038

Lepomis

macrochirus

Bluegill

8.300

0.6541

Ictalurus

punctatus

Channel catfish

5.500

0.4334

Lumbriculus

variegatus

Annelid

5.400

0.4255

Oncorhynchus

mykiss

Rainbow trout

4.571

0.3602

Daphnia

magna

Cladoceran

4.300

0.1896

1,2

0.3388
(0.1896)

Gammarus

oseudolimnaeus*

Scud

3.700

0.2916

40 See footnote 41 above.

41 U.S. EPA. 2003. Ambient Water Quality Criteria Document for Tributyltin (TBT) - Final. EPA-822/R-03-031.

-------
Genus

Species

Common name

GMAV
(MQ/L)

SMCV
(MS)"-)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(MQ/L)

Pimephales

promelas

Fathead minnow

2.600

0.2598

0.2049
(0.2598)

Chlorohvdra

viridissima*

Hydra

1.800

0.1418

Hvdra

littoralis*

Hydra

Hvdra

oliaactis*

Hydra

1.170

0.09220

See same notes as above under Table 2.1.14-1.

B. Evaluation of the Protectiveness of the Oregon Freshwater Chronic Criterion

Following the review of the SMCV values in Table 2.1.14-2, all tested genera and species had
values greater than Oregon's chronic criterion for tributyltin. Therefore, EPA concluded that
chronic effects are not expected to occur at concentrations lower than the criterion and thus these
species would be protected.

2.1.14.3 References for Tributyltin

A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the acute and chronic tables, and are the source from which EPA
obtained SMAVs (acute table) and experimentally-derived SMCVs (chronic table).

Reference No.

Used Reference Citation

(associated with reference numbers and provided above in Tables 2.1.14-1 and 2.1.148-2)

Acute References

TAI Environmental Sciences Inc. 1989a. Toxicity of Tri-butyl Tin Oxide to Two Species of Hydra. Mobile, AL: 31

pp.

TAI Environmental Sciences Inc. 1989b. Toxicity of Tri-butyl Tin Oxide to Hydra littoralis and Chlorohydra
viridissima. Mobile, AL: 25 pp.

Brooke, L.T., D.J. Call, S.H. Poirier, T.P. Markee, C.A. Lindberg, D.J. McCauley and P.G. Simonson. 1986. Acute
Toxicity and Chronic Effects of Bis(tri-n-butyltin) Oxide to Several Species of Freshwater Organisms. Center for
Lake Superior Environmental Studies, University of Wisconsin-Superior, Superior, Wl: 20 pp.

ABC Laboratories, Inc. 1990a. Acute 96-hour Flow-Through Toxicity of Bis(tri-n-butyltin) Oxide to Rainbow Trout
(Oncorhynchus mykiss). ABC study number 38306. Analytical Bio-Chemistry Laboratories, Inc., Columbia, MO:
277 pp.

Martin, R.C., D.G. Dixon, R.J. Maguire, P.J. Hodson and R.J. Tkacz. 1989. Acute toxicity, uptake, depuration and
tissue distribution of tri-n-butyltin in rainbow trout, Salmo gardneri. Aquat. Toxicol. 15: 37-52.

ABC Laboratories, Inc. 1990b. Acute 96-hour Flow-through Toxicity of Bis(tri-n-butyltin) Oxide to Bluegill (Lepomis
macrochirus). ABC study number 38307. Analytical Bio-Chemistry Laboratories, Inc.,Columbia, MO: 279 pp.

Buccafusco, R. 1976a. Acute Toxicity of Tri-n-butyltin Oxide to Channel Catfish (Ictalurus punctatus), the
Freshwater Clam (Elliptio camplanatus), the Common Mummichog (Fundulus heteroclitus) and the Eastern
Oyster (Crassostrea virginica). U.S. EPA-OPP Registration Standard.

Chronic References

ABC Laboratories, Inc. 1990d. Chronic Toxicity of Bis(tributyltin) Oxide to Daphnia magna. ABC report number
38310. Analytical Bio-Chemistry Laboratories, Inc., Columbia, MO: 318 pp.

-------
B. Studies That EPA Considered But Did Not Utilize In This Determination

derive the CMC , EPA is providing a transparent rationale as to why they were
not utilized (see below).

42 U.S. EPA. 2003. Ambient Water Quality Criteria Document for Tributyltin (TBT) - Final. EPA-822/R-03-031.

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2.1.15 ZINC

2.1.15.1 Evaluation of the Acute Freshwater Criterion Concentration for Zinc
A. Presentation of Toxicological Data

Oregon adopted a freshwater criterion concentration of 120 |ig/L for zinc that is expressed as a
function of total hardness in the water column and in terms of the dissolved concentration of the
metal. This dissolved metal concentration reflects the criterion normalized to a total hardness of
100 mg/L as CaCC>3 and is the same as the freshwater CMC recommended for use nationally by
EPA for the protection of aquatic life43. EPA developed the recommended criterion in
accordance with the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.1.15-1 provides available GMAVs based on available acute toxicity data for zinc to
aquatic life from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Table 2.1.15-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values
(GMAVs) for Zinc

Most

Representative
SMAV

GMAV

Acute References

(used in the calculation of

Genus

Species

Common name

(Mg/L)

the SMAV)

Argia

sp.

Damselfly

156530

Gambusia

affinis

Mosquitofish

57309

Crangonyx

pseudogracilis

Amphipod

34839

Xenopus

laevis

Clawed toad

33741

Nais

sp.

worm

32376

Fundulus

diaphanus

Banded killifish

31566

53,54

Amnicola

sp.

Spire snail

29596

Carassius

auratus

Goldfish

29256

49,50,59,60

Chironomus

tentans

Midge

25958

Anguilla

rostrata

American eel

23983

53,54

Asellus

aquaticus

Aquatic sowbug

32024

Asellus

communis

Isopod

20428

Asellus

bicrenata

Isopod

10084

18755

Lepomis

gibbosus

Pumpkinseed

33062

53,54

Lepomis

macrochirus

Bluegill

10446

18584

47,48

Lumbriculus

variegatus

Oligochaete, worm

17089

Gammarus

sp.

Scud, Amphipod

14252

Cyprinus

carpio

Common carp

12727

53,54,55

Poecilia

reticulata

Guppy

10651

49,50,51

Notemigonus

crysoleucas

Golden shiner

10557

Corbicula

manilensis

Asiatic clam

8622

44,45

Xiphophorus

maculatus

Southern platyfish

7638

Ptychocheilus

oregonensis

Northern squawfish

11578

Ptychocheilus

lucius

Colorado squawfish

3026

5919

32,33,34

Lirceus

alabamae

Isopod

5745

Pimephales

promelas

Fathead minnow

5185

36,37,38,39,40,41

See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.

The data which serve as the basis for the current nationally-recommended criteria are from the 1995 Great Lakes Initiative Updates to these
criteria as cited in: U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient Water.
EPA-820-B-96-001.

-------

Most

Representative
SMAV

GMAV

Acute References

(used in the calculation of

Genus

Species

Common name

(M9/L)

the SMAV)

Salmo

salar

Atlantic salmon

3829

Xyrauchen

texanus

Razorback sucker

3816

32,33,34

Salvelinus

fontinalis

Brook trout

3695

Gila

elegans

Bonytail

3229

33,34

Catostomus

commersoni

White sucker

9199

Catostomus

latipinnis

Flannelmouth sucker

1063

3127

Lophopodella

carteri

Bryozoa

3004

Jordanella

floridae*

Flagfish

2942

29,30

Plumatella

emarginata

Bryozoan

2828

Helisoma

campanulatum

Snail

2777

Physa

gyrina

Pouch snail

2961

Physa

heterostropha

Snail

1914

2381

24,25,26,27

Pectinatella

magnifica

Bryozoa

2300

Limnodrilus

hoffmeisteri

Tubificid worm

2224

Oncorhynchus

kisutch

Coho salmon

2865

Oncorhynchus

nerka

Sockeye salmon

2643

12,29

Oncorhynchus

mykiss

Rainbow trout

1135

12,13,16,17,18,19,20,21,22

Oncorhynchus

tshawytscha

Chinook salmon

785.5

1612

12,13,14

Oreochromis

mossambica

Mozambique tilapia

1390

Utterbackia

imbecillis

Mussel

582.1

Daphnia

magna

Water flea

625.5

Daphnia

pulex

Water flea

445.0

527.6

1,9

Aaosia

chrvsoaaster*

LongTin dace

400.8

Morone

saxatilis

Striped bass

210.1

Ceriodaphnia

dubia

Water flea

117.0

3,4,5,6

Ceriodaphnia

reticulata

Water flea

89.21

102.2

1,2

Note 2: The reporting of calculated values has been limited to a minimum of four significant figures for convenience and use in this
evaluation with the exception of very high values, which are reported as whole numbers - see text in section 2.2 of this evaluation for
an explanation of this decision, particularly for metals such as zinc which are normalized to a water hardness of 100 mg/L as CaC03
and expressed on a dissolved metal basis for a comparison with the acute criterion concentration.

B. Evaluation of the Protectiveness of the Oregon Freshwater Acute Criterion

Following review of GMAV values in Table 2.1.15-1, 40 of the 41 tested genera had values
greater than Oregon's acute criterion concentration for zinc. Therefore, EPA concluded that
acute effects to these genera are not expected to occur at concentrations equal to or lower than
the criterion, and thus these genera and the aquatic life designated use would be expected to be
protected.

When compared to Oregon's acute criterion concentration for zinc, SMAV/2 values for three test
species (two planktonic cladocerans and one non-salmonid fish) were lower than the acute
criterion concentration of 120 |ig/L dissolved zinc. All three of these species are expected to
reside in Oregon waters. Therefore, EPA reviewed the data from the studies that make up the
most representative SMAV for C. reticulata, C. dubia, and M saxatilis and compared the
confidence intervals of the SMAV for these species to determine whether the SMAV/2 values
are quantitatively different from the criterion value of 120 |ig/L.

-------
The overall hardness adjusted SMAV for C. reticulata was 89.21 |ig/L, with 5 and 95 percent
confidence intervals of 71.23 and 111.3 |ig/L. When divided by two, the SMAV/2 for C.
reticulata was 44.60 |ig/L (text box A - C. reticulata acute), less than the Oregon criterion
concentration of 120 |ig/L.

The overall hardness adjusted SMAV for C. dubia was 117.0 |ig/L, with 5 and 95 percent
confidence intervals of 96.29 and 142.8 |ig/L. When divided by two, the SMAV/2 for C.
reticulata was 58.52 |ig/L (text box B - C. dubia acute) , less than the Oregon criterion
concentration of 120 |ig/L.

The overall hardness adjusted SMAV forM saxatilis was 210.1 |ig/L, with 5 and 95 percent
confidence intervals of 118.4 and 272.4 |ig/L. When divided by two, the SMAV/2 for C.
reticulata was 105.0 |ig/L (text box C-M. saxatilis acute), less than the Oregon criterion
concentration of 120 |ig/L.

Because the Oregon acute criterion for zinc is greater than the SMAV/2 for C. reticulata ,C.
dubia, andM saxatilis, EPA concludes that the occurrence of ambient concentrations equal to or
greater than the Oregon CMC for zinc may result in some level of acute toxicity to individuals
of this species.

Freshwater zinc acute criterion comparison

Text Box A (acute) - Basis for the meta analysis comparing the SMAV/2 for the cladoceran (C.
reticulata) to the acute criterion for zinc (120 |ig/L dissolved metal concentration normalized to
a hardness of 100 mg/L as CaCOs).

Ceriodaphnia reticulata

Reported Values

Hardness Normalized Values

Hardness Normalized Values/2

Hardness

LC50

5% CI

95% CI

LC50

5% CI

95% CI

LC50/2

CMC

41.00

32.00

52.00

78.88

61.56

100.0

39.44

120

32.00

26.00

40.00

61.56

50.02

76.95

30.78

76.00

61.00

93.00

146.2

117.4

178.9

73.11

SMAV

SMAV/2

Geomean

46.37

37.02

57.83

89.21

71.23

111.3

44.60

Text Box B (acute) - Basis for the meta analysis comparing the SMAV/2 for the cladoceran (C.
dubia) to the acute criterion for zinc (120 |ig/L dissolved metal concentration normalized to a
hardness of 100 mg/L as CaCOs).

Ceriodaphnia dubia

Reported Values Hardness Normalized Values Hardness Normalized Values/2

Hardness LC50 5% CI 95% CI LC50 5% CI 95% CI LC50/2 CMC

100

-------
207

360

300

440

190.1

158.4

232.3

95.04

120

180

105

305

306.4

178.7

519.1

153.2

114

57.06

35.99

81.64

28.53

114

120

101

162

105.3

88.66

142.2

52.67

114

131

112

154

115.0

98.32

135.2

57.50

182

105

115

61.83

56.53

67.71

30.91

182

123

108

140

72.42

63.59

82.43

36.21

182

153

147

164

90.09

86.56

96.57

45.04

69.88

59.90

80.87

34.94

101

112

100.8

91.85

111.8

50.42

109

126

108.8

92.85

125.8

54.41

207

500

410

620

264.0

216.5

327.4

132.0

199

170

229

235.5

200.3

270.7

117.7

SMAV

SMAV/2

Geomean

142.6

117.3

173.9

117.0

96.29

142.8

58.52

Text Box C (acute) - Basis for the meta analysis comparing the SMAV/2 for the striped bass (M
saxatilis) to the acute criterion for zinc (120 |ig/L dissolved metal concentration normalized to a
hardness of 100 mg/L as CaCC^).

Monroe saxatilis

Reported Values

Hardness Normalized Values

Hardness Normalized Values/2

Hardness

LC50

5% CI

95% CI

LC50

5% CI

95% CI

LC50/2

CMC

120

170

255.1

96.65

361.4

127.5

120

285

430

360

510

173.1

145.0

205.4

86.55

SMAV

SMAV/2

Geomean

227.2

169.7

294.4

210.1

118.4

272.4

105.0

2.1.15.2 Evaluation of the Chronic Freshwater Criterion Concentration for Zinc
A. Presentation of Toxicological Data

Oregon adopted a freshwater chronic criterion concentration of 120 |ig/L for zinc expressed as
the dissolved metal concentration at a total hardness of 100 mg/L CaCC>3 in the water column.
This concentration is the same as the freshwater CCC recommended for use nationally by EPA
for the protection of aquatic life44. EPA developed the recommended criterion in accordance
with the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.1.15-2 presents a compilation of the GMAVs from Table 2.1.15-1, any experimentally
determined SMCVs obtained from the criteria document and EPA ECOTOX download used for
the BE, and estimated GMCVs based on the GMAV/ACR. The 1995 update of the criteria
document for zinc45 reported an FACR of 2.0. Because of the large range in ACRs (0.7027 to
41.20) and trend of lower ACRs for the most acutely sensitive species, EPA determined that only
the experimentally- determined ACRs for the freshwater Daphnia magna, chinook salmon, and

44 See footnote 45 above.

45 U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient
Water. EPA-820-B-96-001.

101

-------
rainbow trout, were the most appropriate ACRs to protect sensitive species in general. The
geometric mean of the three species ACRs is 1.994. However, according to the 1985 Guidelines,
the FACR cannot be less than 2.0. Since no additional acceptable ACRs are available, EPA
calculated the predicted GMCVs for zinc in Table 2.1.15-2 using an ACR of 2.0 and the
following equation: Predicted GMCV = GMAV/FACR.

EPA compared the GMCVs for each species to Oregon's zinc chronic criterion to determine
whether the chronic criterion will protect Oregon's aquatic life designated use.

Table 2.1.15-2: Genus Mean Chronic Values (GMCVs) for Zinc

Genus

Species

Common name

GMAV
(ng/L)

SMCV
(MS)"-)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(M9/L)

Argia

sp.

Damselfly

156530

78265

Gambusia

affinis

Mosquitofish

57309

28655

Crangonyx

pseudogracilis

Amphipod

34839

17420

Xenopus

laevis

Clawed toad

33741

16871

Nais

sp.

worm

32376

16188

Fundulus

diaphanus

Banded killifish

31566

15783

Amnicola

sp.

Spire snail

29596

14798

Carassius

auratus

Goldfish

29256

14628

Clistoronia

magnifica

Caddisfly

>13945

(>13945)

Chironomus

tentans

Midge

25958

12979

Anguilla

rostrata

American eel

23983

11991

Asellus

aquaticus

Aquatic sowbug

Asellus

communis

Isopod

Asellus

bicrenata

Isopod

18755

9377

Lepomis

gibbosus

Pumpkinseed

Lepomis

macrochirus

Bluegill

18584

9292

Lumbriculus

variegatus

Oligochaete, worm

17089

8544

Gammarus

sp.

Scud, Amphipod

14252

7126

Cyprinus

carpio

Common carp

12727

6363

Poecilia

reticulata

Guppy

10651

<473.1

5325
(<473.1)

Notemigonus

crysoleucas

Golden shiner

10557

5279

Corbicula

manilensis

Asiatic clam

8622

4311

Xiphophorus

maculatus

Southern platyfish

7638

3819

Ptychocheilus

oregonensis

Northern
squawfish

Ptychocheilus

lucius

Colorado
squawfish

5919

2959

Lirceus

alabamae

Isopod

5745

2872

Pimephales

promelas

Fathead minnow

5185

268.2

5,6

2593
(268.2)

Salmo

salar

Atlantic salmon

3829

1914

Xyrauchen

texanus

Razorback sucker

3816

1908

Salvelinus

fontinalis

Brook trout

3695

1630

1848
(1630)

Gila

elegans

Bonytail

3229

1615

Catostomus

commersoni

White sucker

Catostomus

latipinnis

Flannelmouth
sucker

3127

1563

Lophopodella

carteri

Bryozoa

3004

1502

Jordanella

floridae*

Flagfish

2942

71.99

1,2

1471
(71.99)

Plumatella

emarginata

Bryozoan

2828

1414

Helisoma

campanulatum

Snail

2777

1388

102

-------
Genus

Species

Common name

GMAV
(MS)"-)

SMCV
(MS)"-)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(MQ/L)

Physa

gyrina

Pouch snail

Physa

heterostropha

Snail

2381

1190

Pectinatella

magnifica

Bryozoa

2300

1150

Limnodrilus

hoffmeisteri

Tubificid worm

2224

1112

Oncorhynchus

kisutch

Coho salmon

Oncorhynchus

nerka

Sockeye salmon

>595.2

Oncorhynchus

mykiss

Rainbow trout

1282

10,11

Oncorhynchus

tshawytscha

Chinook salmon

1612

1184

8,9

805.9
(>966.9)

Oreochromis

mossambica

Mozambique
tilapia

1390

695.0

Utterbackia

imbecillis

Mussel

582.1

291.0

Daphnia

magna

Water flea

100.1

3,4

Daphnia

pulex

Water flea

527.6

263.8
(100.1)

Aaosia

chrvsoaaster*

LongTin dace

400.8

200.4

Morone

saxatilis

Striped bass

210.1

105.0

Ceriodaphnia

dubia

Water flea

Ceriodaphnia

reticulata

Water flea

102.2

51.09

See same notes as above under Table 2.1.15-1.

B. Evaluation of the Protectiveness of the Oregon Freshwater Chronic Criterion

Following the review of the GMCV values in Table 2.1.15-2, 39 of the 41 genera have GMCVs
greater than Oregon's chronic criterion for zinc. Therefore, EPA concluded that chronic effects
are not expected to occur at concentrations lower than the criterion and thus these species and
designated use would be protected.

When compared to Oregon's CCC for zinc, SMCV values for four Oregon resident test species
(three planktonic cladocerans - C. reticulata, C. dubia, and D. magna, and the striped bass M
saxatilis) were lower than the CCC of 120 |ig/L for zinc. Therefore, EPA reviewed the data from
the studies that make up the most representative SMCVs for each of those species and,
depending on whether the SMCV was estimated based on the use of the ACR or experimentally
determined based on NOEC and LOECs, compared the confidence intervals (ACR approach) or
LOEC values surrounding these SMCVs to determine whether the SMCV values were
quantitatively different from the chronic criterion value for zinc of 120 |ig/L. A fifth species, the
flagfish J. floridae, also had a SMCV below the CCC for zinc, but it is not resident in Oregon
waters and was therefore not included in this analysis.

The SMCV for C. reticulata was estimated by applying the ACR of 2.0 described above to the
SMAV and the 5 and 95 percent confidence intervals surrounding the SMAV for each test
performed by Carlson and Roush (1985), and taking the geometric mean of the values. The final
SMCV was 44.60 |ig/L (text box D - C. reticulata chronic).

The SMCV for C. dubia was estimated by applying the ACR of 2.0 described above to the
SMAV and the 5 and 95 percent confidence intervals surrounding the SMAV for all studies with

103

-------
this test species, and taking the geometric mean of the values. The final SMCV was 58.52 |ig/L
(text box E - C. dubia chronic).

The SMCV for D. magna was calculated as the geometric mean of the measured LOEC and
NOEC for two replicate tests in Biesenger et al. (1986) and three tests across a water hardness
gradient by Chapman et al. (1980). The final hardness normalized dissolved SMCV was 100.1
|ig/L, with hardness normalized dissolved NOEC and LOEC values of 79.08 and 126.7 |ig/L,
respectively (text box F - D. magna chronic).

The SMCV forM saxatilis was estimated by applying the ACR of 2.0 described above to the
SMAV and the 5 and 95 percent confidence intervals surrounding the SMAV for both tests with
this species, and taking the geometric mean of the values. The final SMCV was 105.0 |ig/L (text
box G - M saxatilis chronic).

Because the Oregon chronic criterion for zinc is greater than the SMCV for C. reticulata and C.
dubia, EPA concludes that the Oregon CMC for silver may not protect all individuals of this
species. Because the Oregon chronic criterion for zinc is below the upper confidence interval
surrounding the SMCV for M. saxatilis, EPA concludes that the Oregon CCC for zinc is
protective of this species. Finally, because the Oregon chronic criterion for zinc is below the
LOEC for D. magna, EPA concludes that the Oregon CCC for zinc is protective of this species.

Freshwater zinc chronic criterion comparison

Text Box D (chronic) - Basis for the meta analysis comparing the SMCV for the cladoceran (C.
reticulata) to the chronic criterion for zinc (120 |ig/L dissolved metal concentration normalized
to a hardness of 100 mg/L as CaCOs).

Ceriodaphnia reticulata
Reported Values

Hardness LC50 5% CI

95% CI

Hardness Normalized Values

LC50 5% CI 95% CI ACR

Hardness Normalized Chronic Values

LC50 / ACR 5% CI / ACR 95% CI / ACR

CCC

78.88

61.56

100.0 2.0

39.44

30.78

50.02

120

61.56

50.02

76.95

30.78

25.01

38.48

146.2

117.4

178.9

73.11

58.68

89.46

Geomean

46.37

37.02

57.83

89.21

71.23

111.3

SMCV

44.60

35.61

55.63

Text Box E (chronic) - Basis for the meta analysis comparing the SMCV for the cladoceran (C.
dubia) to the chronic criterion for zinc (120 |ig/L dissolved metal concentration normalized to a
hardness of 100 mg/L as CaCOs).

Ceriodaphnia dubia

Reported Values

Hardness Normalized Values

Hardness Normalized Chronic Values

Hardness

LC50 5% CI

95% CI

LC50

5% CI

95% CI ACR

LC50/ACR

CCC

207

360 300

440

190.1

158.4

232.3 2.0

95.04

120

180 105

305

306.4

178.7

519.1

153.2

114

65 41

57.06

35.99

81.64

28.53

104

-------
114

120

101

162

105.3

88.66

142.2

52.67

114

131

112

154

115.0

98.32

135.2

57.50

182

105

115

61.83

56.53

67.71

30.91

182

123

108

140

72.42

63.59

82.43

36.21

182

153

147

164

90.09

86.56

96.57

45.04

69.88

59.90

80.87

34.94

101

112

100.8

91.85

111.8

50.42

109

126

108.8

92.85

125.8

54.41

207

500

410

620

264.0

216.5

327.4

132.0

199

170

229

235.5

200.3

270.7

117.7

SMCV

Geomean

142.6

117.3

173.9

117.0

96.3

142.8

58.52

Text Box F (chronic) - Basis for the meta analysis comparing the SMCV for the cladoceran (D.
magna) to the chronic criterion for zinc (120 |ig/L dissolved metal concentration normalized to a
hardness of 100 mg/L as CaCC^).

Daphnia magna

Reported Chronic Values

Hardness NOEC LOEC

Hardness Normalized Chronic Values

NOEC LOEC CV

ccc

140.3

101.9

143.5

272.1

197.6

120

140.3

101.9

143.5

272.1

197.6

190

135.8

166.4

326.0

233.0

104

47.29

41.01

49.60

45.10

211

46.73

22.00

27.23

24.48

Geomean

62.57

100.2

79.19

79.08

126.7

SMCV

100.1

Text Box G (chronic) - Basis for the meta analysis comparing the SMCV for the striped bass (M
saxatilis) to the chronic criterion for zinc (120 |ig/L dissolved metal concentration normalized to
a hardness of 100 mg/L as CaCC^).

Monroe saxatilis

Reported Values

Hardness Normalized Values

Hardness Normalized Chronic Values

Hardness

LC50

5% CI

95% CI

LC50

5% CI

95% CI

ACR

LC50/ACR

CCC

120

170

255.1

96.65

361.4

2.0

127.5

120

285

430

360

510

173.2

145.0

205.4

86.58

SMCV

Geomean

227.2

169.7

294.4

210.1

118.4

272.4

105.0

2.1.15.3 References for Zinc

A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the acute and chronic tables, and are the source from which EPA
obtained SMAVs (acute table) and experimentally-derived SMCVs (chronic table).

105

-------
Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in tables 2.1.15-1 and 2.1.15-2)

Acute References

Mount, D.I. and T.J. Norberg. 1984. A seven-day life-cycle cladoceran toxicity test. Environ. Toxicol. Chem. 3(3):
425-434 (Author Communication Used).

Carlson, A.R. and T.H. Roush. 1985. Site-specific Water Quality Studies of the Straight River, Minnesota:
Complex Effluent Toxicity, Zinc Toxicity, and Biological Survey Relationships. EPA-600/3-85-005. National
Technical Information Service, Springfield, VA.

Carlson, A.R., H. Nelson and D. Hammermeister. 1986. Evaluation of Site-Specific Criteria for Copper and Zinc:
An Integration of Metal Addition Toxicity, Effluent and Receiving Water Toxicity, and Ecological Survey Data.
EPA-600/3-86-026, U.S. EPA, Duluth, MN: 68 p. (U.S. NTIS PB86-183928) (Publ in Part As 12161).

Magliette, R.J., F.G. Doherty, D. McKinney and E.S. Venkataramani. 1995. Need for environmental quality
guidelines based on ambient freshwater quality criteria in natural waters-Case study "zinc". Bull. Environ.
Contam. Toxicol. 54(4): 626-632.

Belanger, S.E. and D.S. Cherry. 1990. Interacting effects of pH acclimation, pH, and heavy metals on acute and
chronic toxicity to Ceriodaphnia dubia (Cladocera). J. Crustac. Biol. 10(2): 225-235

Diamond, J.M., D.E. Koplish, J. McMahon III and R. Rost. 1997. Evaluation of the water-effect ratio procedure for
metals in a riverine system. Environ. Toxicol. Chem. 16(3): 509-520.

Palawski, D., J.B. Hunn and F.J. Dwyer. 1985. Sensitivity of young striped bass to organic and inorganic
contaminants in fresh and saline waters. Trans. Am. Fish. Soc. 114: 748-753

Lewis, M. 1978. Acute toxicity of copper, zinc, and manganese in single and mixed salt solutions to juvenile
longfin dace, Aqosia chrysoqaster. J. Fish Biol. 13(6): 695-700.

Cairns, J., Jr., A.L. Buikema, A.G. Heath and B.C. Parker. 1978. Effects of Temperature on Aquatic Organism
Sensitivity to Selected Chemicals. Va. Water Resour. Res. Center, Bull. 106, Office ofWater Res. and Technol.,
OWRT Project B-084-VA, VA. Polytech. Inst. State Univ., Blacksburg, VA: 1-88

Keller, A.E. and S.G. Zam. 1991. The acute toxicity of selected metals to the freshwater mussel, Anodonta
imbeciiis. Environ. Toxicol. Chem. 10(4): 539-546

Attar, E.N. and E.J. Maly. 1982. Acute toxicity of cadmium, zinc, and cadmium-zinc mixtures to Daphnia magna.
Arch. Environ. Contam. Toxicol. 11(3): 291-296.

Chapman, G.A. 1975. Toxicity of Copper, Cadmium and Zinc to Pacific Northwest Salmonids. Interim report. U.S.
EPA, Corvallis, OR. Available from: C.E. Stephan, U.S. EPA, Duluth, MN.

Chapman, G.A. 1978b. Toxicities of cadmium, copper, and zinc to four juvenile stages of Chinook salmon and
steelhead. Trans. Am. Fish. Soc. 107(6): 841-847

Finlayson, B.J. and K.M. Verrue. 1982. Toxicities of copper, zinc, and cadmium mixtures to juvenile Chinook
salmon. Trans. Am. Fish. Soc. 111(5): 645-650.

Hamilton, S.J. and K.J. Buhl. 1997a. Hazard evaluation of inorganics, singly and in mixtures, to flannelmouth
sucker Catostomus iatipinnis in the San Juan River, New Mexico. Ecotoxicol. Environ. Saf. 38(3): 296-308

Alsop, D.H. and C.M. Wood. 1999. Influence of waterborne cations on zinc uptake and toxicity in rainbow trout,
Oncorhynchus mykiss. Can. J. Fish. Aquat. Sci. 56(11): 2112-2119

Goettl, J.P., Jr., J.R. Sinley and P.H. Davies. 1974. Water pollution studies. In: Colorado Fisheries Research
Review. Review No. 9. Colorado Division of Wildlife, Fort Collins, CO: 36-44.

Goettl, J.P., Jr., P.H. Davies and J.R. Sinley. 1976. Water pollution studies. In: D.B. Cope (Ed.), Colorado
Fisheries Research Review 1972-1975, DOW-R-R-F72-75, Colorado Division of Wildlife, Boulder, CO :68-75

Chapman, G.A. and D.G. Stevens. 1978. Acute lethal levels of cadmium, copper, and zinc to adult male Coho
salmon and steelhead. Trans. Am. Fish. Soc. 107(6): 837-840.

Sinley, J.R., J. P. Goettl, Jr. and P.H. Davies, 1974. The effects of zinc on rainbow trout (Saimo gairdneri) in hard
and soft water. Bull. Environ. Contam. Toxicol. 12(2): 193-201.

Holcombe, G.W. and R.W. Andrew. 1978. The Acute Toxicity of Zinc to Rainbow and Brook Trout: Comparisons
in Hard and Soft Water. EPA-600/3-78-094, U.S. EPA, Duluth, MN.

Cusimano, R.F., D.F. Brakke and G.A. Chapman. 1986. Effects of pH on the toxicities of cadmium, copper, and
zinc to steelhead trout (Saimo gairdneri). Can. J. Fish. Aquat. Sci. 43(8): 1497-1503.

Qureshi, S.A. and A.B. Saksena. 1980. The acute toxicity of some heavy metals to Tiiapia mossambica (Peters).
Aqua 1: 19-20.

Wurtz, C.B. 1962. Zinc effects on fresh water mollusks. Nautilus 76: 53-61.

Wurtz, C.B. and C.H. Bridges. 1961. Preliminary results from macroinvertebrate bioassays. Proc. Pa. Acad. Sci.
35: 51-56.

Cairns, J., Jr. and A. Scheier. 1958. The effects of temperature and hardness ofwater upon the toxicity of zinc to
the pond snail, Physa heterostropha (Say). Notulae Naturae, No. 308-1-11.

Academy of Natural Sciences. 1960. The Sensitivity of Aquatic Life to Certain Chemical Commonly Found in
Industrial Wastes. Philadelphia, PA.

Pardue, W.J. and T.S. Wood. 1980. Baseline toxicity data for freshwater bryozoa exposed to copper, cadmium,
chromium, and zinc. J. Tenn. Acad. Sci. 55(1): 27-31

Chapman, G.A. 1978a. Effects of continuous zinc exposure on sockeye salmon during adult-to-smolt freshwater
residency. Trans. Am. Fish. Soc. 107(6): 828-836

Spehar, R.L. 1976a. Cadmium and Zinc Toxicity to Jordaneiia fioridae. EPA-600/3-76-096. National Technical

106

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Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in tables 2.1.15-1 and 2.1.15-2)

Information Service, Springfield, VA.

Nebeker, A.V., A. Stinchfield, C. Savonen and G.A. Chapman. 1986. Effects of copper, nickel and zinc on three
species of Oregon freshwater snails. Environ. Toxicol. Chem. 5(9): 807-811.

Hamilton, S.J. and K.J. Buhl. 1997b. Hazard assessment of inorganics, individually and in mixtures, to two
endangered fish in the San Juan River, New Mexico. Environ. Toxicol. Water Qual. 12: 195-209

Hamilton, S.J. 1995. Hazard assessment of inorganics to three endangered fish in the Green River, Utah.
Ecotoxicol. Environ. Saf. 30(2): 134-142.

Buhl, K.J. and S.J. Hamilton. 1996. Toxicity of inorganic contaminants, individually and in environmental mixtures,
to three endangered fishes (Colorado squawfish, bonytail, and razorback sucker). Arch. Environ.Contam. Toxicol.
30(1): 84-92

Carson, W.G. and W.V. Carson. 1972. Toxicity of Copper and Zinc to Juvenile Atlantic Salmon in the Presence of
Humic Acid and Lignosulfonates. Fisheries Research Board of Canada Manuscript Report Series No. 1181.
Biological Stations, St. Andrews, N.B., Canada.

Pickering, Q.H. and W.N. Vigor. 1965. The acute toxicity of zinc to eggs and fry of the fathead minnow. Prog.
Fish-Cult. 27(3): 153-157.

Mount, D.I. 1966. The effect of total hardness and pH on acute toxicity of zinc to fish. Int. J. Air Water Pollut. 10:
49-56.

Brungs, W.A. 1969. Chronic toxicity of zinc to the fathead minnow. Trans. Am. Fish. Soc. 98(2): 272-279.

Benoit, D.A. and G.W. Holcombe. 1978. Toxic effects of zinc on fathead minnows (Pimephaies promeias) in soft
water. J. Fish Biol. 13(6): 701-708.

Broderius, S.J. and L.L. Smith, Jr. 1979. Lethal and sublethal effects of binary mixtures of cyanide and hexavalent
chromium, zinc, or ammonia to the fathead minnow and rainbow trout. J. Fish. Res. Board Can. 36(2): 164-172.

Norberg-King, T.J. 1987. An Evaluation of the Fathead Minnow Seven-Day Subchronic Test for Estimating
Chronic Toxicity. M.S. Thesis, University of Wyoming, Laramie, WY: 80 p.

Bosnak, A.D. and E.L. Morgan. 1981. Acute toxicity of cadmium, zinc, and total residual chlorine to epigean and
hypogean isopods (Asellidae). Natl. Speleological Soc. Bull. 43: 12-18.

Rachlin, J.W. and A. Perlmutter. 1968. Response of an inbred strain of platyfish and the fathead minnow to zinc.
Prog. Fish-Cult. 30(4): 203-207.

Cherry, D.S., J.H. Rodgers, Jr., R.L. Graney and J. Cairns, Jr. 1980. Dynamics and control of the Asiatic clam in
the New River, Virginia. Bull. Va. Water Resour. Res. Cent. 123: 72.

Rodgers, J.H., Jr., D.S. Cherry, R.L. Graney, K.L. Dickson and J. Cairns, Jr. 1980. Comparison of heavy metal
interactions in acute and artificial stream bioassay techniques for the Asiatic clam (Corbicuia fiuminea). In: Aquatic
toxicology. Eaton, J.G., P.R. Parrish and A.C. Hendricks (Eds.). ASTM STP 707. American Society for Testing
and Materials, Philadelphia, PA: 266-280.

Cairns, J., Jr., T.K. Bahns, D.T. Burton, K.L. Dickson, R.E. Sparks and W.T. Waller. 1971. The effects of pH,
solubility and temperature upon the acute toxicity of zinc to the bluegill sunfish (Lepomis macrochirus Raf.). Trans.
Kans. Acad. Sci. 74: 81-92.

Cairns, J., Jr. and A. Scheier. 1959. The Relationship of Bluegill Sunfish Body Size to Tolerance for Some
Common Chemicals. Proc. Ind. Waste Conf. Purdue Univ. 13: 243-252.

Cairns, J., Jr., W.T. Waller and J.C. Smrchek. 1969. Fish bioassays contrasting constant and fluctuating input of
toxicants. Rev. Biol. 7: 75-91.

Pickering, Q.H. and C. Henderson. 1966. The acute toxicity of some heavy metals to different species to
warmwater fishes. Air Water Pollut. Int. J. 10: 453-463.

Pierson, K.B. 1981. Effects of chronic zinc exposure on the growth, sexual maturity, reproduction, and
bioaccumulation of the guppy, Poeciiia reticulata. Can. J. Fish. Aquat. Sci. 38: 23-31.

Andros, J.D. and R.R. Garton. 1980. Acute lethality of copper, cadmium, and zinc to Northern squawfish. Trans.
Am. Fish. Soc. 109(2): 235-238.

Rehwoldt, R., G. Bida and B. Nerrie. 1971. Acute Toxicity of copper, nickel, and zinc ions to some Hudson River
fish species. Bull. Environ. Contam. Toxicol. 6(5): 445-448.

Rehwoldt, R., L.W. Menapace, B. Nerrie and D. Allessandrello. 1972. The effect of increased temperature upon
the acute toxicity of some heavy metal ions. Bull. Environ. Contam. Toxicol. 8(2): 91-96.

Khangarot, B.S., A. Sehgal and M.K. Bhasin. 1983. Man and the biosphere-studies on Sikkim Himalayas. Part 1:
Acute toxicity of copper and zinc to common carp Cyprinus carpio (Linn.) in soft water. Acta Hydrochim. Hydrobiol.
11(6):667-673.

Rehwoldt, R., L. Lasko, C. Shaw and E. Wirhowski. 1973. The acute toxicity of some heavy metal ions toward
benthic organisms. Bull. Environ. Contam. Toxicol. 10(5): 291-294.

Bailey, H.C. and D.H.W. Liu. 1980. Lumbriculus variegatus, a benthic oligochaete, as a bioassay organism. In:
J.C. Eaton, P.R. Parrish and A.C. Hendricks (Eds.), Aquatic Toxicology and Hazard Assessment, 3rd Symposium,
ASTM STP 707, Philadelphia, PA: 205-215.

Khangarot, B.S. and P.K. Ray. 1989. Sensitivity of midge larvae of Chironomus tentans fabricius (Diptera
Chironomidae) to heavy metals. Bull. Environ. Contam. Toxicol. 42(3): 325-330.

107

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Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in tables 2.1.15-1 and 2.1.15-2)

Pickering, Q.H. and C. Henderson. 1964. The acute toxicity of some heavy metals to different species of warm
water fishes. Proc. 19th Ind. Waste Conf., Purdue University, West Lafayette, IN: 578-591; Int. J. Air Water
Pollut.10: 453-463 (1966) (Author Communication Used).

Nor, Y.M. 1990. Effects of organic ligands on toxicity of copper and zinc to Carassius auratus. Chem. Spec.
Bioavail. 3(3): 111-115.

Martin, T.R. and D.M. Holdich. 1986. The acute lethal toxicity of heavy metals to peracarid crustaceans (with
particular reference to fresh-water asellids and gammarids). Water Res. 20(9):1137-1147.

Dawson, D.A., E.F. Stebler, S.L. Burks and J.A. Bantle. 1988. Evaluation of the developmental toxicity of metal-
contaminated sediments using short-term fathead minnow and frog embryo-larval assays. Environ. Toxicol.
Chem. 7: 27-34.

Kallanagoudar, Y.P. and H.S. Patil. 1997. Influence of water hardness on copper, zinc and nickel toxicity to
Gambusia affinis (B&G). J. Environ. Biol. 18(4): 409-413.

Chronic References

Spehar, R.L. 1976a. Cadmium and Zinc Toxicity to Jordaneiia fioridae. EPA-600/3-76-096, U.S.EPA, Duluth, MN:
34 (1976) / M.S. Thesis, Univ. of Minnesota, Minneapolis, MN: 67 p.

Spehar, R.L. 1976b. Cadmium and zinc toxicity to flagfish, Jordaneiia fioridae. J. Fish. Res. Board. Can. 33: 1939-
1945.

Biesinger, K.E., G.M. Christensen and J.T. Fiandt. 1986. Effects of metal salt mixtures on Daphnia magna.
Ecotoxicol. Environ. Saf. 11: 9-14.

Chapman, G.A., S. Ota and F. Recht. Manuscript. Effects of Water Hardness on the Toxicity of Metals to Daphnia
magna. Available from: C.E. Stephan, U.S. EPA, Duluth, MN.

Benoit, D.A. and G.W. Holcombe. 1978. Toxic effects of zinc on fathead minnows (Pimephales promelas) in soft
water. J. Fish Biol. 13(6): 701-708.

Norberg-King, T.J. 1987. An Evaluation of the Fathead Minnow Seven-Day Subchronic Test for Estimating
Chronic Toxicity. M.S. Thesis, University of Wyoming, Laramie, WY: 80 p.

Pierseon, K.B. 1981. Effects of chronic zinc exposure on the growth, sexual maturity, reproduction, and
bioaccumulation of the guppy, Poecilia reticulata. Can. J. Fish. Aquat. Sci. 38: 23-31.

Chapman, G.A. 1978. Effects of continuous zinc exposure on sockeye salmon during adult-to-smolt freshwater
residency. Trans. Am. Fish. Soc. 107(6): 828-836.

Chapman, G.A. 1975. Toxicity of copper, cadmium and zinc to Pacific northwest salmonids. Interim report. U.S.
EPA, Corvallis, OR. Available from: C.E. Stephan, U.S. EPA, Duluth, MN.

Sinley, J.R., J. P. Goettl, Jr. and P.H. Davies. 1974. The effects of zinc on rainbow trout (Salmo gairdneri) in hard
and soft water. Bull. Environ. Contam. Toxicol. 12(2): 193-201.

Cairns, M.A., R.R. Garton and R.A. Tubb. 1982. Use offish ventilation frequency to estimate chronically safe
toxicant concentrations. Trans. Am. Fish. Soc. 111(1): 70-77.

Holcombe, G.W., D.A. Benoit and E.N. Leonard. 1979. Long-term effects of zinc exposures on brook trout
(Salvelinus fontinalis). Trans. Am. Fish. Soc. 108(1): 76-87.

Nebeker, A.V., C. Savonen, R.J. Baker and J.K. McCrady. 1984. Effects of copper, nickel and zinc on the life
cycle of the caddisfly Clistoronia magnifica (Limnephilidae). Environ. Toxicol. Chem. 3(4): 645-649.

B. Studies That EPA Considered But Did Not Utilize In This Determination

1) For the studies that were not utilized, but the most representative SMAV/2 or
most representative SMCV fell below the criterion, or, if the studies were for a
species associated with one of the four most sensitive genera used to calculate the
FAV in the most recent national ambient water quality criteria dataset used to
derive the CMC46, EPA is providing a transparent rationale as to why they were
not utilized (see below).

U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient Water. EPA-820-B-96-001.

108

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2) For the studies that were not utilized because they were not found to be pertinent
to this determination (including failing the QA/QC procedures listed in Appendix
A) upon initial review of the download from ECOTOX, EPA is providing the
code that identifies why EPA determined that the results of the study were not
reliable (see Appendix N).

109

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2.2 Saltwater

2.2.1 CADMIUM

2.2.1.1 Evaluation of the Acute Saltwater Criterion Concentration for Cadmium
A. Presentation of Toxicological Data

Oregon adopted a saltwater acute criterion concentration of 40 |ig/L for cadmium that is
expressed in terms of the dissolved concentration of the metal. This dissolved metal
concentration is the same as the saltwater CMC recommended for use nationally by EPA for the
protection of aquatic life47. EPA developed the recommended criterion in accordance with the
1985 Guidelines pursuant to CWA section 304(a).

Table 2.2.1-1 provides available GMAVs based on available acute toxicity data for cadmium to
aquatic animals from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Table 2.2.1-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values
(GMAVs) for Cadmium

Most

Representative
SMAV

GMAV

Acute References

(used in the calculation

Genus

Species

Common name

(ng/L)

of the SMAV)

Monopylephorus

cuticulatus

Tubificid

134190

Tilapia

mossambica

Mozambique tilapia

79520

Scorpaena

guttata

Scorpionfish

61628

Cyprinodon

variegatus

Sheepshead minnow

49700

Eohaustorius

estuarius

Amphipod

27824

Tautogolabrus

adspersus

Cunner

25745

Tubificoides

gabriellae

Oligochaete

23856

Ilea

pugilator

Fiddler crab

21111

Fundulus

majalis

Striped killifish

20874

Fundulus

heteroclitus

Mummichog

18091

19433

Nassarius

obsoletus

Eastern mud snail

19055

24,25

Neanthes

arenaceodentata

Polychaete worm

12759

16,59

Cymatogaster

aggregata

Shiner perch

10934

Loligo

opalescens

California market squid

10139

Lagodon

rhomboides

Pinfish

9940

Limnodriloides

verrucosus

Oligochaete

9940

Mugil

curema

White mullet

11928

Mugil

cephalus

Striped mullet

7037

9161

Excirolana

sp.

Isopod

7952

Dendraster

excentricus

Sand dollar

7356

Limnoria

tripunctata

Wood borer

7077

Nereis

virens

Polychaete worm

10054

24,25

Nereis

grubei

Polychaete

4672

6853

Diporeia

spp.

Amphipod

6660

Urosalpinx

cinerea

Atlantic oyster drill

6560

47 See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.

The data which serve as the basis for the current nationally-recommended criteria are from the 2001 ALC document
as cited in: U.S. EPA. 2001. 2001 Update of Ambient Water Quality Criteria for Cadmium. EPA-822-R-01-001.

110

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Genus

Species

Common name

Most
Representative
SMAV
(MS)"-)

GMAV
(Mg/L)

Acute References

(used in the calculation
of the SMAV)

Eurypanopeus

depressus

Mud crab

4871

Carcinus

maenas

Green crab

4075

Marinogammarus

obtusatus

Scud

3479

Ctenodrilus

serratus

Polychaete worm

3149

Pseudopleuronectes

americanus

Winter flounder

2916

Ampelisca

abdita

Amphipod

2883

Pectinaria

californiensis

Cone worm

2584

Callinectes

sapidus

Blue crab

2578

Asterias

forbesii

Common starfish

2398

24,25

Ophryotrocha

diadema

Polychaete

2155

56,57

Emerita

analoga

Pacific sand crab

2097

Morula

granulata

Gastropod

2048

Perna

viridis

Green mussel

1969

52,53

Perna

indica

Brown mussel

1933

1951

50,51

Nematostella

vectensis

1926

Pseudodiaptomus

coronatus

Copepod

1698

Mya

arenaria

Soft shell clam

1662

24,25,48

Oncorhynchus

kisutch

Coho salmon

1491

Litopenaeus

vannamei

1622

46,47

Litopenaeus

setiferus

Northern white shrimp

984.1

1264

Palaemonetes

pugio

Daggerblade grass
shrimp

1972

43,44

Palaemonetes

vulgaris

Marsh grass shrimp

755.4

1220

Grandidierella

japonica

Scud

1163

Corophium

insidiosum

Scud

1056

22,27,41

Strongylocentrotus

droebachiensis

Green sea urchin

1789

Strongylocentrotus

purpuratus

Purple sea urchin

411.2

857.8

17,40

Crangon

sp.

Caridean shrimp

2246

Crangon

septemspinosa

Bay shrimp,
Sand shrimp

318.1

845.3

Crassostrea

virginica

Eastern oyster

3777

Crassostrea

gigas

Pacific oyster

172.1

806.3

19,37

Rivulus

marmoratus

Rivulus

795.2

Nitocra

spinipes

Harpacticoid copepod

789.7

34,35

Palaemon

elegans

Rockpool prawn

775.3

Menidia

menidia

Atlantic silverside

775.2

Argopecten

irradians

Bay scallop

1471

Argopecten

ventricosus

Pacific calico scallop

393.6

761.0

Mytilus

edulis

Common bay mussel,
blue mussel

1067

19,29

Mytilus

trossolus

502.0

731.8

Elasmopus

bampo

Scud

711.9

22,27

Mytilopsis

sallei

Santo Domingo, or
falsemussel

705.7

Pagurus

longicarpus

Longwrist hermit crab

641.1

24,25

Chelura

terebrans

Amphipod

626.2

Leptocheirus

plumulosus

Amphipod

587.0

Jaeropsis

sp.

Isopod

407.5

Penaeus

duorarum

Northern pink shrimp

308.6

Cancer

irroratus

Rock crab

248.5

Cancer

magister

Dungeness crab

220.9

234.3

17,19

Amphiascus

tenuiremis

Harpacticoid copepod

222.7

Capitella

capitata

Polychaete worm

198.8

Scorpaenichthys

marmoratus

Cabezon

198.8

Tresus

nuttalli

Horse clam,
Pacific gaper

586.5

Tresus

capax

Horse clam

55.66

180.7

Limulus

polyphemus

Horseshoe crab

166.7

Balanus

improvisus

Barnacle

159.0

Eurytemora

affinis

Calanoid copepod

146.8

Ill

-------

Most

Representative
SMAV

GMAV

Acute References

(used in the calculation

Genus

Species

Common name

(MS)"-)

(Mg/L)

of the SMAV)

Acartia

clausi

Copepod

143.1

Acartia

tonsa

Calanoid copepod

118.0

129.9

9,10

Homarus

americanus

American lobster

77.53

Morone

saxatilis

Striped bass

74.55

Americamysis

bigeiowi*

Shrimp

109.3

Americamysis

bahia*

Opossum shrimp

42.59

68.24

3,4,5,6

Nucella

laoillus*

Dog whelk,
Atlantic dogwinkle

23.06

Praunus

flexuosus*

13.86

Neomvsis

inteaer*

8.434

Note 1: Species that are bold and italicized indicate those associated with the four most sensitive genera used to derive the FAV or
FCV in the 2001 ALC document. Underlined species with an asterisk (*) indicate known or suspected Oregon non-resident species,
and for this evaluation, only those non-resident species below the criterion or related to the four most sensitive genera are identified
as such.

Note 2: The reporting of calculated values has been limited to a minimum of four significant figures for convenience and use in this
evaluation with the exception of very high values, which are reported as whole numbers - see text in section 2.2 of this evaluation for
an explanation of this decision, particularly for metals such as cadmium which are expressed on a dissolved metal basis for a
comparison with the acute criterion concentration.

B. Evaluation of Protectiveness of the Oregon Saltwater Acute Criterion

Following review of GMAV values in Table 2.2.1-1, 71 of the 74 tested genera have values
greater than Oregon's acute criterion concentration for cadmium. Therefore, EPA concluded that
acute effects to these species are not expected to occur at concentrations lower than the criterion
and thus these species would be protected. The three most acutely sensitive tested species are
non-resident. Removing those from the data set indicates that 72 of 75 resident genera are above
the criterion. EPA believes Oregon's aquatic life designated use will be protected.

When compared to Oregon's acute criterion concentration for cadmium, SMAV/2 values for
seven test species (dog whelk, Nucella lapillus; opossum shrimp, Americamysis bahia; horse
clam, Tresus capax; striped bass, Morone saxatilis; and American lobster, Homarus americanus)
were lower than the acute criterion concentration of 40 |ig/L dissolved cadmium. Of the seven,
only four of these species (horse clam, striped bass, American lobster, and the oyster) are
expected to reside in Oregon waters. Therefore, EPA reviewed the data from the studies which
make up the most representative SMAV for these four species, and compared the confidence
intervals of the SMAV for the species to determine whether the SMAV/2 values are
quantitatively different from the criterion value of 40 |ig/L.

The SMAV for horse clam (Tresus capax) was based on a single LC50 of 55.66 |ig/L dissolved
cadmium, with 5 and 95 percent confidence intervals of 46.72 and 66.60 |ig/L. When divided by
two, the SMAV/2 for T. capax was 27.83 |ig/L (text box A - T. capax acute).

The SMAV for striped bass (Morone saxatilis) was based on a single LC50 of 74.55 |ig/L
dissolved cadmium, with 5 and 95 percent confidence intervals of 58.65 and 95.42 |ig/L. The
SMAV/2 forM. saxatilis was 37.28 |ig/L (text box B -M. saxatilis acute).

112

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The SMAV for American lobster (Homarus americanus) was based on a single LC50 of 77.53
|ig/L dissolved cadmium. The 5 and 95 percent confidence intervals were not reported for the
test. The SMAV/2 for H. americanus was 38.77 |ig/L.

Because the Oregon acute criterion for cadmium is greater than SMAV/2 for the horse clam,
Tresus capax , EPA concludes that the ambient concentrations equal to or greater than the
Oregon CMC for cadmium may result in acute toxicity to some individuals of this species.
Because the Oregon acute criterion for cadmium is approximately equal to the SMAV/2 for
striped bass, M. saxatilis, and Homarus americanus, it is EPA's judgement that these populations
would be unlikely to be affected.

Saltwater cadmium acute criterion comparison

Text Box A (acute) - Basis for the meta analysis comparing the SMAV/2 for the horse clam
(.Tresus capax) to the acute criterion for cadmium (40 |ig/L dissolved metal concentration).

Tresus capax

Reported Values

Dissolved Normalized Values

Dissolved Normalized Values/2

LC50 5% CI

95% CI

LC50 5% CI 95% CI

LC50/2

CMC

56.00 47.00

67.00

55.66 46.72 66.60

27.83

(SMAV)

(SMAV/2)

Text Box B (acute) - Basis for the meta analysis comparing the SMAV/2 for the striped bass
(Morone saxatilis) to the acute criterion for cadmium (40 |ig/L dissolved metal concentration).

Morone saxatilis

Reported Values

Dissolved Normalized Values

Dissolved Normalized Values/2

LC50 5% CI

95% CI

LC50 5% CI 95% CI

LC50/2

CMC

75.00 59.00

96.00

74.55 58.65 95.42

37.28

(SMAV)

(SMAV/2)

2.2.1.2 Evaluation of the Chronic Saltwater Criterion Concentration for Cadmium
A. Presentation of Toxicological Data

Oregon adopted a saltwater chronic criterion concentration of 8.8 |ig/L for cadmium expressed
as the dissolved metal concentration in the water column. This concentration is the same as the

saltwater CCC recommended for use nationally by EPA for the protection of aquatic life . EPA
developed the recommended criterion in accordance with the 1985 Guidelines pursuant to CWA
section 304(a).

Table 2.2.1-2 presents a compilation of the GMAVs from Table 2.2.1-1, any experimentally
determined SMCVs obtained from the criteria document and EPA ECOTOX download used for
the BE, and estimated GMCVs based on the GMAV/ACR. The 2001 criteria document for

48 See Footnote 49 above.

113

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cadmium49 reported an FACR of 9.106 for saltwater species. EPA determined that the
experimentally-determined ACRs of 5.384 and 15.40 |ig/L for the saltwater mysids,
Americamysis bahia and Americamysis bigelowi, respectively, were the most appropriate ACRs
to protect sensitive saltwater species in general. The decision to use only the two ACRs from the
saltwater mysids was made because the wide range of ACRs available for freshwater organisms
seemed inappropriate. Since no additional acceptable ACRs are available for saltwater species,
EPA calculated the predicted GMCVs for cadmium in Table 2.2.1-2 using an ACR of 9.106 and
the following equation: Predicted GMCV = GMAV/FACR.

EPA compared the SMCVs for each species to Oregon's cadmium chronic criterion to determine
whether the chronic criterion will protect Oregon's aquatic life designated use.

Table 2.2.1-2: Species Mean Chronic Values

SMCVs) for Cadmium

Genus

Species

Common name

GMAV
(ng/L)

SMCV
(MS)"-)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(M9/L)

Monopylephorus

cuticulatus

Tubificid

134190

14736

Tilapia

mossambica

Mozambique
tilapia

79520

8733

Scorpaena

guttata

Scorpionfish

61628

6768

Cyprinodon

variegatus

Sheepshead
minnow

49700

5458

Eohaustorius

estuarius

Amphipod

27824

3056

Tautogolabrus

adspersus

Cunner

25745

2827

Tubificoides

gabriellae

Oligochaete

23856

2620

Ilea

pugilator

Fiddler crab

21111

2318

Fundulus

majalis

Striped killifish

Fundulus

heteroclitus

Mummichog

19433

2134

Nassarius

obsoletus

Eastern mud snail

19055

2093

Neanthes

arenaceodentata

Polychaete worm

12759

1401

Cymatogaster

aggregata

Shiner perch

10934

1201

Loligo

opalescens

California market
squid

10139

1113

Lagodon

rhomboides

Pinfish

9940

1092

Limnodriloides

verrucosus

Oligochaete

9940

1092

Mugil

curema

White mullet

Mugil

cephalus

Striped mullet

9161

1006

Excirolana

sp.

Isopod

7952

873.3

Dendraster

excentricus

Sand dollar

7356

807.8

Limnoria

tripunctata

Wood borer

7077

777.2

Nereis

virens

Polychaete worm

Nereis

grubei

Polychaete

6853

752.6

Diporeia

spp.

Amphipod

6660

731.4

Urosalpinx

cinerea

Atlantic oyster
drill

6560

720.4

Eurypanopeus

depressus

Mud crab

4871

534.9

Carcinus

maenas

Green crab

4075

447.6

Marinogammarus

obtusatus

Scud

3479

382.1

Ctenodrilus

serratus

Polychaete worm

3149

345.8

Pseudopleuronectes

americanus

Winter flounder

2916

320.2

Ampelisca

abdita

Amphipod

2883

316.6

Pectinaria

californiensis

Cone worm

2584

283.8

Callinectes

sapidus

Blue crab

2578

283.1

Asterias

forbesii

Common starfish

2398

263.4

49 U.S. EPA. 2001. 2001 Update of Ambient Water Quality Criteria for Cadmium. EPA-822-R-01-001.

114

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Genus

Species

Common name

GMAV
(Mg/L)

SMCV
(MS)"-)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(Mg/L)

Ophryotrocha

diadema

Polychaete

2155

236.6

Emerita

analoga

Pacific sand crab

2097

230.3

Morula

granulata

Gastropod

2048

224.9

Perna

viridis

Green mussel

Perna

indica

Brown mussel

1951

214.3

Nematostella

vectensis

1926

211.5

Pseudodiaptomus

coronatus

Copepod

1698

186.4

Mya

arenaria

Soft shell clam

1662

182.5

Oncorhynchus

kisutch

Coho salmon

1491

163.7

Litopenaeus

vannamei

Litopenaeus

setiferus

Northern white
shrimp

1264

138.8

Palaemonetes

pugio

Daggerblade
grass shrimp

Palaemonetes

vulgaris

Marsh grass
shrimp

1220

134.0

Grandidierella

japonica

Scud

1163

127.7

Corophium

insidiosum

Scud

1056

116.0

Strongylocentrotus

droebachiensis

Green sea urchin

Strongylocentrotus

purpuratus

Purple sea urchin

857.8

94.20

Crangon

sp.

Caridean shrimp

Crangon

septemspinosa

Bay shrimp,
Sand shrimp

845.3

92.83

Crassostrea

virginica

Eastern oyster

Crassostrea

gigas

Pacific oyster

806.3

88.55

Rivulus

marmoratus

Rivulus

795.2

87.33

Nitocra

spinipes

Harpacticoid
copepod

789.7

86.73

Palaemon

elegans

Rockpool prawn

775.3

85.14

Menidia

menidia

Atlantic silverside

775.2

85.13

Argopecten

irradians

Bay scallop

Argopecten

ventricosus

Pacific calico
scallop

761.0

83.57

Mytilus

edulis

Common bay
mussel,
blue mussel

Mytilus

trossolus

731.8

80.36

Elasmopus

bampo

Scud

711.9

78.18

Mytilopsis

sallei

Santo Domingo,
or

falsemussel

705.7

77.50

Pagurus

longicarpus

Longwrist hermit
crab

641.1

70.41

Chelura

terebrans

Amphipod

626.2

68.77

Leptocheirus

plumulosus

Amphipod

587.0

64.46

Jaeropsis

sp.

Isopod

407.5

44.76

Penaeus

duorarum

Northern pink
shrimp

308.6

33.89

Cancer

irroratus

Rock crab

Cancer

magister

Dungeness crab

234.3

25.73

Amphiascus

tenuiremis

Harpacticoid
copepod

222.7

24.45

Capitella

capitata

Polychaete worm

198.8

21.83

Scorpaenichthys

marmoratus

Cabezon

198.8

21.83

Tresus

nuttalli

Horse clam,
Pacific gaper

Tresus

capax

Horse clam

180.7

19.84

Limulus

polyphemus

Horseshoe crab

166.7

18.31

Balanus

improvisus

Barnacle

159.0

17.47

Eurytemora

affinis

Calanoid

146.8

16.12

115

-------

Chronic

SMCV

References

Genus

Species

Common name

GMAV
(Mg/L)

(MS)"-)

('experimentally
derived}

(used in the
calculation of
the SMCV)

Predicted
GMCV
(Mg/L)

copepod

Acartia

clausi

Copepod

Acartia

tonsa

Calanoid
copepod

129.9

14.27

Homarus

americanus

American lobster

77.53

8.514

Morone

saxatilis

Striped bass

74.55

8.187

Americamysis

bigelowi*

Shrimp

7.098

Americamysis

bahia*

Opossum shrimp

68.24

6.136

1,2,3

7.494
(6.599)

Nucella

lapillus*

Dog whelk,
Atlantic dogwinkle

23.06

2.532

Praunus

flexuosus*

13.86

1.522

Neomvsis

inteaer*

8.434

0.9262

See same notes as above under Table 2.2.1-1.

B. Evaluation of the Protectiveness of the Oregon Saltwater Chronic Criterion

Following the review of the GMCV values in Table 2.2.1-2, 72 of 78 genera had GMCVs greater
than Oregon's chronic criterion for cadmium. The three most acutely sensitive tested species are
non-resident. Removing those from the data set indicates that 72 of 75 resident genera are above
the criterion. Therefore, EPA concluded that chronic effects to nearly all genera are not expected
to occur at concentrations equal to or lower than the criterion, and thus the aquatic life
designated use would be protected by the chronic criterion.

When compared to Oregon's CCC for cadmium, the SMCV value for eight test species
(Nassarius festivus, Nucella lapillus, Americamysis bahia, Americamysis bigelowi, Tresus capax,
Morone saxatilis, Homarus americanus, and Saccostrea cuccullata) were lower than the chronic
criterion concentration of 8.8 |ig/L cadmium. Only four of these species (Tresus capax, Morone
saxatilis, Homarus americanus, and Saccostrea cuccullata) are expected to reside in Oregon
waters. Therefore, EPA reviewed the data from the studies that make up the most representative
SMCVs for these resident species and compared the confidence intervals of these SMCVs to
determine whether the SMCV values were quantitatively different from the criterion value of 8.8
Hg/L-

The SMCV for horse clam (T. capax) was estimated by applying the ACR of 9.106 described
above to the SMAV and the 5 and 95 percent confidence intervals surrounding the SMAV for the
single test with this test species. The final SMCV was 6.113 |ig/L (text box C-T. capax
chronic).

The SMCV for striped bass (M saxatilis) was estimated by applying the ACR of 9.106 to the
SMAV and the 5 and 95 percent confidence intervals surrounding the SMAV for the single test
with this test species. The final SMCV was 8.187 |ig/L (text box D -M. saxatilis chronic).

116

-------
The SMCV for American lobster (H. americanus) was estimated by applying the ACR of 9.106
to the SMAV for the single test with this test species. The 5 and 95 percent confidence intervals
were not reported for the test. The final SMCV was 8.514 |ig/L.

The SMCV for oyster (S. cuccullata) was estimated by applying the ACR of 9.106 to the SMAV
for the single test with this test species. The 5 and 95 percent confidence intervals were not
reported for the test. The final SMCV was 8.733 |ig/L.

Because the Oregon chronic criterion for cadmium is greater than the SMCV for the horse clam,
Tresus capax , EPA concludes that the occurance of ambient concentration equal to or greater
than the Oregon CCC for cadmium may not protect all individuals of this species. Because the
Oregon chronic criterion for cadmium is approximately equal to the SMCV for striped bass, M
saxatilis, Homarus americanus and Saccostrea cuccullata, it is EPA's professional judgement
that these populations would not be significantly negatively affected.

Saltwater cadmium chronic criterion comparison

Text Box C (chronic) - Basis for the meta analysis comparing the SMCV estimated for the horse
clam (Tresus capax) to the chronic criterion for cadmium (8.8 |ig/L dissolved metal
concentration).

Tresus capax
Reported Value

LC50 5% CI

95% CI

Dissolved Normalized Value

LC50 5% CI 95% CI

ACR

Chronic Dissolved Value

LC50/ACR

CCC

56.00 47.00

67.00

55.66 46.72 66.60

9.106

6.113
(SMCV)

8.8

Text Box D (chronic) - Basis for the meta analysis comparing the SMCV estimated for the
striped bass (Morone saxatilis) to the chronic criterion for cadmium (8.8 |ig/L dissolved metal
concentration).

Morone saxatilis

Reported Values

Dissolved Normalized Values

Chronic Dissolved Values

LC50 5% CI 95% CI

ACR

LC50/ACR

CCC

75.00 59.00 96.00

74.55 58.65 95.42

9.106

8.187

8.8

(SMCV)

2.2.1.3 References for Cadmium

A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the acute and chronic tables, and are the source from which EPA
obtained SMAVs (acute table) and experimentally-derived SMCVs (chronic table).

117

-------
Reference
No.

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Leung, K.M.Y., and R.W. Furness. 1999. Induction of Metallothionein in Dogwhelk Nucella lapillus During and After
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Nimmo, D.R., L.H. Bahner, R.A. Rigby, J.M. Sheppard, and A.J. Wilson Jr. 1977a. Mysidopsis Bahia: An Estuarine
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Gentile, S.M., J.H. Gentile, J. Walker, and J.F. Heltshe. 1982. Chronic Effects of Cadmium on Two Species of Mysid
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Gentile, S. M. 1982. Memorandum to John H. Gentile. U.S. EPA, Narragansett, Rhode Island.

Sullivan, B.K., E. Buskey, D.C. Miller, and P.J. Ritacco. 1983. Effects of Copper and Cadmium on Growth, Swimming
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Cardwell, R.D., C.E. Woelke, M.I. Carr, and E.W. Sanborn. 1979. Toxic Substances and Water Quality Effects on
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Green, A.S., G.T. Chandler, and E.R. Blood. 1993. Aqueous-, Pore-Water-, and Sediment-Phase Cadmium: Toxicity
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Martin, M., K.E. Osborn, P. Billig, and N. Glickstein. 1981. Toxicities of Ten Metals to Crassostrea gigas and Mytilus
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Eisler, R., and R.J. Hennekey. 1977. Acute Toxicities of Cd2+, Cr+6, Hg2+, Ni2+ and Zn2+ to Estuarine Macrofauna.
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Eisler, R. 1971. Cadmium Poisoning in Fundulus heteroclitus (Pisces: Cyprinodontidae) and Other Marine Organisms.
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Cardin, J.A. 1982. Memorandum to J.H. Gentile. U.S. EPA, Narragansett, Rhode Island.

Lorenzon, S., M. Francese and E.A. Ferrero. 2000. Heavy metal toxicity and differential effects on the hyperglycemic
stress response in the shrimp Palaemon elegans. Arch. Environ. Contam. Toxicol. 39(2): 167-176.

Bengtsson, B.E., and B. Bergstrom. 1987. A Flowthrough Fecundity Test with Nitocra spinipes (Harpacticoidea
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Bengtsson, B.E. 1978. Use of a Harpacticoid Copepod in Toxicity Tests. Mar.Pollut.Bull. 9:238-241.

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Watling, H.R. 1982. Comparative Study of the Effects of Zinc, Cadmium, and Copper on the Larval Growth of Three
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Wright, D.A., and J.W. Frain. 1981. Cadmium Toxicity in Marinogammarus obtusatus: Effect of External Calcium.
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Hilmy, A.M., M.B. Shabana, and A.Y. Daabees. 1985. Bioaccumulation of Cadmium: Toxicity in Mugil cephalus.
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Chung, K.S. 1978. Cadmium Tolerance of the White Mullet (Mugil curema) and Its Use to Predict Survival Probability in
Polluted Sea Waters. Bol.lnst.Oceanogr.Univ.Oriente 17(1 /2):105-107.

Sharp, J.R. 1988. The Effect of Salinity on Cadmium Toxicity and Fin Regeneration of Penfish, Lagodon rhomboides.
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Lin, H.C., and W.A. Dunson. 1993. The Effect of Salinity on the Acute Toxicity of Cadmium to the Tropical, Estuarine,
Hermaphroditic Fish, Rivulus marmoratus: A Comparison of Cd, Cu, and Zn tolerance with Fundulus heteroclitus.
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O'Hara, J. 1973. The Influence of Temperature and Salinity on the Toxicity of Cadmium to the Fiddler Crab, Uca
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Robohm, R.A. 1986. Paradoxical Effects of Cadmium Exposure on Antibacterial Antibody Responses in Two Fish
Species: Inhibition in Cunners (Tautogolabrus adspersus), and and enhancement in striped bass (Morone saxatilis).
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Meador, J.P. 1993. The Effect of Laboratory Holding on the Toxicity Response of Marine Infaunal Amphipods to
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Brown, D.A., S.M. Bay, J.F. Alfafara, G.P. Hershelman and K.D. Rosenthal. 1984. Detoxification/Toxification of
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Chronic References

Nimmo, D.R., L.H. Bahner, R.A. Rigby, J.M. Sheppard and A.J. Wilson, Jr. 1977. Mysidopsis Bahia: An estuarine
species suitable for life-cycle toxicity tests to determine the effects of a pollutant. In: F.L. Mayer and J.L. Hamelink
(Eds.), Aquatic Toxicology and Hazard Evaluation, 1st Symposium, ASTM STP 634, Philadelphia, PA: 109-116.

Gentile, S.M., J.H. Gentile, J. Walker and J.F. Heltshe. 1982. Chronic effects of cadmium on two species of mysid
shrimp: Mysidopsis bahia and Mysidopsis bigeiowi. Hydrobiologia 93(1/2): 195-204.

Carr, R.S., J.W. Williams, F.I. Saksa, R.L. Buhl and J.M. Neff. 1985. Bioenergetic alterations correlated with growth,
fecundity and body burden of cadmium for mysids (Mysidopsis bahia). Environ. Toxicol. Chem. 4: 181-188.

B. Studies That EPA Considered But Did Not Utilize In This Determination

1) For the studies that were not utilized, but the most representative SMAV/2 or
most representative SMCV fell below the criterion, or, if the studies were for a
species associated with one of the four most sensitive genera used to calculate the
FAV in the most recent national ambient water quality criteria dataset used to
derive the CMC50, EPA is providing a transparent rationale as to why they were
not utilized (see below).

2) For the studies that were not utilized because they were not found to be pertinent
to this determination (including failing the QA/QC procedures listed in Appendix

50 U.S. EPA. 2001. 2001 Update of Ambient Water Quality Criteria for Cadmium. EPA-822-R-01-001.

120

-------
A) upon initial review of the download from ECOTOX, EPA is providing the
code that identifies why EPA determined that the results of the study were not
reliable (see Appendix O).

121

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2.2.2 COPPER

2.2.2.1 Evaluation of the Acute Saltwater Criterion Concentration for Copper
A. Presentation of Toxicological Data

Oregon adopted a saltwater acute criterion concentration of 4.8 |ig/L for copper that is expressed
in terms of the dissolved concentration of the metal. This dissolved metal concentration is the
same as the saltwater CMC recommended for use nationally by EPA for the protection of aquatic
life51. EPA developed the recommended criterion in accordance with the 1985 Guidelines
pursuant to CWA section 304(a).

Table 2.2.2-1 provides available GMAVs based on available acute toxicity data for copper to
aquatic animals from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Table 2.2.2-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values
(GMAVs) for Copper

Most

Acute References

Representative
SMAV

GMAV

(used in the
calculation of the

Genus

Species

Common name

(ng/L)

SMAV)

Gammarus

duebeni

Scud

8300

Rangia

cuneata

Common rangia or clam

6386

Morone

saxatilis

Striped bass

5107

64,65

Micropogonias

undulatus

Atlantic croaker

4698

Portunus

pelagicus

Crab

1919

Nitocra

spinipes

Harpacticoid copepod

1494

Monhystera

disjuncta

Nematode

>1453

1453

Fundulus

heteroclitus

Killifish

1403

Rivulus

marmoratus

Rivulus

1177

Metapenaeus

dobsoni

Kadal shrimp

1141

Eurythoe

complanata

Fireworm

1079

57,58

Archosargus

probatocephalus

Sheepshead

946.2

Citharichthys

stigmaeus

Speckled sanddab

664.0

Oncorhynchus

kisutch

Coho salmon

498.8

Carcinus

maenas

Green or Europeon shore
crab

498.0

Sciaenops

ocellatus

Red drum

430.0

Crangon

sp.

Caridean shrimp

745.3

Crangon

crangon

Common shrimp, sand
shrimp

240.7

423.6

Hediste

diversicolor

Ragworm

420.2

52,53

Allorchestes

compressa

Scud, Amphipod

398.4

Cymatogaster

aggregata

Shiner perch

346.9

Trachinotus

carolinus

Florida pompano

341.7

Cyprinodon

variegatus

Sheepshead minnow

305.4

Loligo

opalescens

California market squid

256.5

Nereis

diversicolor

Polychaete worm

302.0

51 See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.

The data which serve as the basis for the current nationally-recommended criteria are from the 1995 draft addendum
to the saltwater criteria as cited in: U.S. EPA. 1995. Ambient Water Quality Criteria - Saltwater Copper Addendum.
U.S. EPA, Narragansett, RI.

122

-------

Most

Acute References

Representative
SMAV

GMAV

(used in the
calculation of the

Genus

Species

Common name

(MS)"-)

SMAV)

Nereis

virens

Polychaete worm

>206.7

249.8

Ctenodrilus

serratus

Polychaete worm

249.0

Penaeus

setiferus

Northern white shrimp

296.4

Penaeus

duorarum

Northern pink shrimp

207.5

248.0

Leiostomus

xanthurus

Spot

232.4

Caenorhabditis

elegans

Nematode

215.8

Elasmopus

bampo

Amphipod

207.5

Atherinops

affinis

Topsmelt

201.7

Tigriopus

californicus

Harpacticoid copepod

195.8

Pectinaria

californiensis

Cone worm

166.0

Pseudodiaptomus

coronatus

Calanoid copepod

150.1

22,23

Americamysis

bahia

Opossum shrimp

150.2

Americamysis

bigelowi

Mysid

117.0

132.6

Capitella

capitata

Polychaete worm

128.6

28,38,39

Menidia

peninsulae

Tidewater silverside

116.2

Menidia

menidia

Atlantic silverside

112.5

Menidia

beryllina

Inland silverside

111.1

113.3

Neomysis

mercedis

Opposum Shrimp

112.6

Pleuronectes

americanus

Winter flounder

107.0

Neanthes

arenaceodentata

Polychaete worm

125.0

Neanthes

grubei

Polychaete

83.00

101.9

Anaitides

maculata

Polychaete worm

99.60

Corophium

insidiosum

Amphipod

498.0

Corophium

sp.

Euryhaline amphipod

13.29

81.35

Scorpaenichthys

marmoratus

Cabezon

78.85

Ophryotrocha

diadema

Polychaete

132.8

Ophryotrocha

labronica

Polychaete

41.50

74.24

Tisbe

battagliai

Harpacticoid copepod

62.29

Homarus

americanus

American lobster

57.50

29,30

Cancer

magister

Dungeness or edible crab

56.93

3,24

Haliotis

rufescens

Red abalone

71.45

Haliotis

cracherodii

Black abalone

41.50

54.45

Spisula

solidissima

Surf clam

42.33

Mya

arenaria

Soft shell clam

32.37

Pandalus

danae

Coon stripe shrimp

31.98

Acartia

clausi

Calanoid copepod

41.81

22,23

Acartia

tonsa

Calanoid copepod

24.28

31.86

15,21,22,23

Dend raster

excentricus

Sand dollar

27.39

Argopecten

irradians

Bay scallop

24.07

Eurytemora

affinis

Calanoid copepod

23.95

18,19

Crassostrea

madrasensis*

Oyster

73.04

Crassostrea

virainica*

Eastern oyster

14.35

Crassostrea

gigas

Pacific oyster

12.38

23.50

3,9,10,11,12

Arbacia

punctulata

Sea urchin

21.40

Acanthomysis

costata

Mysid

17.85

16,17

Mulinia

lateralis

Clam

17.70

Metamysidopsis

elongata

Mysid

14.94

Strongylocentrotus

purpuratus

Purple sea urchin

11.84

Paralichthys

dentatus

Summer Flounder

11.56

Mytilus

edulis

Common bay mussel, blue
mussel

7.374

2,3,4,5,6,7

Isoanomon

californicum*

Black purse shells

5.810

Note 1: Species that are bold and italicized indicate those associated with the four most sensitive genera used to derive the FAV or
FCV in the 1995 ALC draft addendum. Underlined species with an asterisk (*) indicate known or suspected Oregon non-resident
species, and for this evaluation, only those non-resident species below the criterion or related to the four most sensitive genera are
identified as such.

Note 2: The reporting of calculated values has been limited to a minimum of four significant figures for convenience and use in this
evaluation with the exception of very high values, which are reported as whole numbers - see text in section 2.2 of this evaluation for
an explanation of this decision, particularly for metals such as copper which are expressed on a dissolved metal basis for a
comparison with the acute criterion concentration.

123

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B. Evaluation of the Protectiveness of the Oregon Saltwater Acute Criterion

Following review of GMAV and SMAV/2 values in Table 2.2.2-1, all genera have GMAVs
greater than Oregon's acute criterion concentration for copper. Thus the aquatic life designated
use would be protected by the chronic criterion.

When compared to Oregon's acute criterion concentration for copper, SMAV/2 values for two
test species (both bivalve mollusks) were lower than the acute criterion concentration of 4.8 |ig/L
dissolved copper. Only one of these species is known to reside in Oregon waters: the common
(blue) mussel, Mytilus edulis. Therefore, EPA reviewed the data from the studies that make up
the most representative SMAV for the resident species and the SMAV values to determine
whether the SMAV/2 values are quantitatively different from the criterion value of 4.8 |ig/L.

Confidence intervals were reported for 31 of the 37 tests used to calculate the SMAV for Mytilus
edulis. The SMAV for dissolved copper was 7.374 |ig/L, and the SMAV for the subset of
studies with reported confidence intervals was 6.663 |ig/L, with 5 and 95 percent confidence
intervals of 6.352 |ig/L and 7.133 |ig/L, respectively (text box A-M. edulis). When divided by
two, the SMAV/2 was 3.687.

Because the Oregon acute criterion for copper is greater than the the SMAV/2 for the common
mussel, Mytilus edulis, EPA concludes that the occurrence of ambient concentration equal to or
greater than the Oregon CMC for copper may result in acute toxicity to some individuals within
this species.

124

-------
Saltwater copper acute criterion comparison

Text Box A (acute) - Basis for the meta analysis comparing the SMAV/2 for common mussel
(Mytilus edulis) to the acute criterion for copper (4.8 |ig/L dissolved metal concentration).

Mytillus edulis

Reported Values

LC50 5% CI

95% CI

Dissolved Normalized Values

LC50 5% CI 95% CI

Dissolved Normalized Values/2

LC50 / 2 CMC

5.800

3.840

7.760

4.814

3.187

6.441

2.407 4.8

17.46

15.11

19.06

14.49

12.54

15.82

7.246

22.81

19.15

36.13

18.93

15.89

29.99

9.466

27.37

24.08

54.86

22.72

19.99

45.54

11.36

19.14

9.568

4.679

2.340

5.393

2.697

22.07

11.03

20.75

10.38

16.85

8.425

7.210

6.820

7.620

5.984

5.661

6.325

2.992

6.400

6.070

6.740

5.312

5.038

5.594

2.656

5.840

5.740

5.940

4.847

4.764

4.930

2.424

12.45

11.98

12.82

12.45

11.98

12.82

6.225

14.10

13.50

14.61

14.10

13.50

14.61

7.050

11.30

10.90

11.58

11.30

10.90

11.58

5.650

11.90

11.28

12.17

11.90

11.28

12.17

5.950

5.560

5.457

5.665

4.392

4.311

4.475

2.196

8.479

8.332

8.629

7.497

7.367

7.630

3.749

7.362

7.259

7.466

6.789

6.694

6.885

3.395

9.500

9.355

9.648

7.806

7.687

7.928

3.903

7.159

7.024

7.293

5.587

5.481

5.691

2.793

5.847

5.808

5.886

4.890

4.857

4.922

2.445

5.028

4.958

5.099

4.745

4.679

4.812

2.373

3.821

3.749

3.894

3.523

3.456

3.590

1.761

4.696

4.609

4.784

3.571

3.505

3.638

1.785

6.418

6.290

6.548

4.662

4.569

4.756

2.331

6.215

6.112

6.320

5.374

5.285

5.465

2.687

6.205

6.121

6.290

5.481

5.407

5.556

2.741

5.874

5.965

5.107

5.186

2.553

5.404

5.337

5.471

4.456

4.401

4.511

2.228

5.998

5.894

6.105

4.788

4.705

4.873

2.394

9.049

8.898

9.204

7.795

7.665

7.928

3.897

7.194

7.035

7.356

4.717

4.613

4.823

2.359

8.019

7.892

8.148

6.405

6.304

6.508

3.203

7.291

7.165

7.420

5.249

5.159

5.342

2.625

8.932

8.658

9.214

5.963

5.780

6.151

2.982

Geomean
(all)

Geomean
(CI only)

8.546
7.946

7.574

8.506

SMAV

7.374
6.663

6.352

7.133

SMAV/2

3.687
3.332

2.2.2.2 Evaluation of the Chronic Saltwater Criterion Concentration for Copper
A. Presentation of Toxicological Data

125

-------
Oregon adopted a saltwater CCC of 3.1 |ig/L for copper expressed as the dissolved metal
concentration in the water column. This concentration is the same as the saltwater chronic
criterion concentration recommended for use nationally by EPA for the protection of aquatic
life52. EPA developed the recommended criterion in accordance with the 1985 Guidelines
pursuant to CWA section 304(a).

Table 2.2.2-2 presents a compilation of the GMAVs from Table 2.2.2-1, any experimentally
determined SMCVs obtained from the criteria document and EPA ECOTOX download used for
the BE, and estimated SMCVs based on the SMAV/ACR. The 1995 saltwater addendum to the

criteria document for copper reported an FACR of 3.127. This FACR represents the geometric
mean of four species, including two freshwater species with GMAVs within a factor of two of
the freshwater FAV, Daphnia magna and Gammaruspseudolimnaeus (ACR of 2.418 and 3.297,
respectively), a sensitive freshwater mollusk, Physa integra (ACR of 3.585), and a saltwater
mysid, Americamysis bahia (ACR of 3.346). Since no additional acceptable ACRs are available,
EPA calculated the predicted GMCVs for copper in Table 2.2.2-2 using an ACR of 3.127 and the
following equation: Predicted GMCV = GMAV/FACR

EPA compared the GMCVs for each species to Oregon's copper chronic criterion to determine
whether the chronic criterion will protect Oregon's aquatic life designated use.

Table 2.2.2-2: <

jenus Mean Chronic Values

GMCVs) for Copper

Genus

Species

Common name

GMAV
(ng/L)

SMCV
(MS)"-)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(M9/L)

Gammarus

duebeni

Scud

8300

2654

Rangia

cuneata

Common rangia or
clam

6386

2042

Morone

saxatilis

Striped bass

5107

1633

Micropogonias

undulatus

Atlantic croaker

4698

1502

Portunus

pelagicus

Crab

1919

613.7

Nitocra

spinipes

Harpacticoid
copepod

1494

477.8

Monhystera

disjuncta

Nematode

>1453

>464.5

Fundulus

heteroclitus

Killifish

1403

448.7

Rivulus

marmoratus

Rivulus

1177

376.5

Metapenaeus

dobsoni

Kadal shrimp

1141

364.9

Eurythoe

complanata

Fireworm

1079

345.1

Archosargus

probatocephalus

Sheepshead

946.2

302.6

Citharichthys

stigmaeus

Speckled sanddab

664.0

212.3

Oncorhynchus

kisutch

Coho salmon

498.8

159.5

Carcinus

maenas

Green or
Europeon shore
crab

498.0

159.3

Sciaenops

ocellatus

Red drum

430.0

137.5

Crangon

sp.

Caridean shrimp

Crangon

crangon

Common shrimp,
sand shrimp

423.6

135.5

Hediste

diversicolor

Ragworm

420.2

134.4

Allorchestes

compressa

Scud, Amphipod

398.4

127.4

52 See footnote 53 above.

53 U.S. EPA. 1995. Ambient Water Quality Criteria -

Saltwater Copper Addendum. U.S. EPA, Narragansett, RI.
126

-------
Genus

Species

Common name

GMAV
(MS)"-)

SMCV
(MS)"-)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV

(Mg/L)

Cymatogaster

aggregata

Shiner perch

346.9

110.9

Trachinotus

carolinus

Florida pompano

341.7

109.3

Cyprinodon

variegatus

Sheepshead
minnow

305.4

207.1

97.67
(207.1)

Loligo

opalescens

California market
squid

256.5

82.02

Nereis

diversicolor

Polychaete worm

Nereis

virens

Polychaete worm

249.8

79.89

Ctenodrilus

serratus

Polychaete worm

249.0

79.63

Penaeus

setiferus

Northern white
shrimp

Penaeus

duorarum

Northern pink
shrimp

248.0

79.30

Leiostomus

xanthurus

Spot

232.4

74.32

Caenorhabditis

elegans

Nematode

215.8

69.01

Elasmopus

bampo

Amphipod

207.5

66.36

Atherinops

affinis

Topsmelt

201.7

64.50

Tigriopus

californicus

Harpacticoid
copepod

195.8

62.61

Pectinaria

californiensis

Cone worm

166.0

53.09

Pseudodiaptomus

coronatus

Calanoid copepod

150.1

48.01

Americamysis

bahia

Opossum shrimp

44.89

Americamysis

bigelowi

Mysid

132.6

42.40
(44.89)

Capitella

capitata

Polychaete worm

128.6

41.12

Menidia

peninsulae

Tidewater
silverside

Menidia

menidia

Atlantic silverside

Menidia

beryllina

Inland silverside

113.3

36.22

Neomysis

mercedis

Opposum Shrimp

112.6

36.02

Pleuronectes

americanus

Winter flounder

107.0

34.22

Neanthes

arenaceodentata

Polychaete worm

Neanthes

grubei

Polychaete

101.9

32.57

Anaitides

maculata

Polychaete worm

99.60

31.85

Corophium

insidiosum

Amphipod

Corophium

sp.

Euryhaline
amphipod

81.35

26.02

Scorpaenichthys

marmoratus

Cabezon

78.85

25.22

Ophryotrocha

diadema

Polychaete

Ophryotrocha

labronica

Polychaete

74.24

23.74

Tisbe

battagliai

Harpacticoid
copepod

62.29

19.92

Homarus

americanus

American lobster

57.50

18.39

Cancer

magister

Dungeness or
edible crab

56.93

18.21

Haliotis

rufescens

Red abalone

Haliotis

cracherodii

Black abalone

54.45

17.41

Spisula

solidissima

Surf clam

42.33

13.54

Mya

arenaria

Sand gaper, soft
shell clam

32.37

10.35

Pandalus

danae

Coon stripe
shrimp

31.98

10.23

Acartia

clausi

Calanoid copepod

Acartia

tonsa

Calanoid copepod

31.86

10.19

Dend raster

excentricus

Sand dollar

27.39

8.759

Argopecten

irradians

Bay scallop

24.07

7.697

Eurytemora

affinis

Calanoid copepod

23.95

7.659

Crassostrea

madrasensis*

Oyster

Crassostrea

virainica*

Eastern oyster

127

-------
Genus

Species

Common name

GMAV
(MS)"-)

SMCV
(MS)"-)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(MQ/L)

Crassostrea

gigas

Pacific oyster

23.50

7.515

Arbacia

punctulata

Sea urchin

21.40

6.844

Acanthomysis

costata

Mysid

17.85

5.708

Mulinia

lateralis

Clam

17.70

5.660

Metamysidopsis

elongata

Mysid

14.94

4.778

Strongylocentrotus

purpuratus

Purple sea urchin

11.84

3.786

Paralichthys

dentatus

Summer
Flounder

11.56

3.697

Mytilus

edulis

Common bay
mussel, blue
mussel

7.374

2.358

Isoanomon

californicum*

Black purse shells

5.810

1.858

See same notes as above under Table 2.2.2-1.

B. Evaluation of the Protectiveness of the Oregon Saltwater Chronic Criterion

Following the review of the SMCV values in Table 2.2.2-1, 43 of 45 genera have GMCVs
greater than Oregon's chronic criterion for copper. Therefore, EPA concluded that chronic
effects to nearly all genera are not expected to occur at concentrations equal to or lower than the
criterion, and thus the aquatic life designated use would be protected by the chronic criterion.

When compared to Oregon's chronic criterion concentration for copper, SMCV values for two
test species (both bivalve mollusks) were lower than the chronic criterion concentration of 3.1
|ig/L dissolved copper. Only one of these species is known to reside in Oregon waters: the
common (blue) mussel, Mytilus edulis. Therefore, EPA reviewed the data from the studies that
make up the most representative SMAV for the resident species and after applying the ACR for
copper to these values, compared the confidence intervals of the SMCV values to determine
whether the SMCV values are quantitatively different from the criterion value of 3.1 |ig/L.

The SMCV for Mytilus edulis was estimated by applying the ACR of 3.127 (see above) to acute
values (dissolved copper) for all tests, and to the 5 and 95 percent confidence intervals for the 31
acute tests with reported confidence intervals. The overall SMCV for copper was 2.358 |ig/L,
and the SMCV for the subset of studies with reported confidence intervals was 2.131 |ig/L (text
box B - M edulis chronic).

Because the Oregon acute criterion for copper is greater than the SMCV for the common mussel,
Mytilus edulis, EPA concludes that the Oregon CCC for copper may not be protective of all
individuals within this species.

Saltwater copper chronic criterion comparison

128

-------
Text Box B - Basis for the meta analysis comparing the SMCV for the common mussel (M
edulis) to the chronic criterion for copper (3.1 |ig/L dissolved metal concentration).

Mytillus edulis

Reported Values

LC50 5% CI

95% CI

Dissolved Normalized Values

LC50 5% CI 95% CI

ACR

Dissolved Chronic Values

LC50/ACR CCC

5.800

3.840

7.760

4.814

3.187

6.441

3.127

1.539 3.1

17.46

15.11

19.06

14.49

12.54

15.82

4.634

22.81

19.15

36.13

18.93

15.89

29.99

6.054

27.37

24.08

54.86

22.72

19.99

45.54

7.265

19.14

6.119

4.679

1.496

5.393

1.725

22.07

7.057

20.75

6.636

16.85

5.388

7.210

6.820

7.620

5.984

5.661

6.325

1.914

6.400

6.070

6.740

5.312

5.038

5.594

1.699

5.840

5.740

5.940

4.847

4.764

4.930

1.550

12.45

11.98

12.82

12.45

11.98

12.82

3.981

14.10

13.50

14.61

14.10

13.50

14.61

4.509

11.30

10.90

11.58

11.30

10.90

11.58

3.614

11.90

11.28

12.17

11.90

11.28

12.17

3.806

5.560

5.457

5.665

4.392

4.311

4.475

1.405

8.479

8.332

8.629

7.497

7.367

7.630

2.398

7.362

7.259

7.466

6.789

6.694

6.885

2.171

9.500

9.355

9.648

7.806

7.687

7.928

2.496

7.159

7.024

7.293

5.587

5.481

5.691

1.787

5.847

5.808

5.886

4.890

4.857

4.922

1.564

5.028

4.958

5.099

4.745

4.679

4.812

1.518

3.821

3.749

3.894

3.523

3.456

3.590

1.127

4.696

4.609

4.784

3.571

3.505

3.638

1.142

6.418

6.290

6.548

4.662

4.569

4.756

1.491

6.215

6.112

6.320

5.374

5.285

5.465

1.719

6.205

6.121

6.290

5.481

5.407

5.556

1.753

5.874

5.965

5.107

5.186

1.633

5.404

5.337

5.471

4.456

4.401

4.511

1.425

5.998

5.894

6.105

4.788

4.705

4.873

1.531

9.049

8.898

9.204

7.795

7.665

7.928

2.493

7.194

7.035

7.356

4.717

4.613

4.823

1.509

8.019

7.892

8.148

6.405

6.304

6.508

2.048

7.291

7.165

7.420

5.249

5.159

5.342

1.679

8.932

8.658

9.214

5.963

5.780

6.151

1.907

Geomean
(all)

Geomean
(CI only)

8.546
7.946

7.574

8.506

7.374
6.663

6.352

7.133

SMCV

2.358
2.131

2.2.2.3 References for Copper

129

-------
A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the acute and chronic tables, and are the source from which EPA
obtained SMAVs (acute table) and experimentally-derived SMCVs (chronic table).

Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in Tables .2.2-1 and 2.2.2-2)

Acute References

Ringwood, A.H. 1992. Comparative sensitivity of gametes and early developmental stages of a sea urchin
species (Echinometra mathaei) and a bivalve species (Isognomon). Arch. Environ. Contam. Toxicol. 22: 288-
295.

City of San Jose. 1998. Toxicities often metals to Crassostrea gigas and Mytiius eduiis embryos and Cancer
magister larvae. Mar. Pollut. Bull. 12(9): 305-308 (Author Communication Used).

Martin, M., K.E. Osborn, P. Billig and N. Glickstein. 1981. Toxicities of ten metals to Crassostrea gigas and
Mytiius eduiis embryos and Cancer magister larvae. Mar. Pollut. Bull. 12(9): 305-308 (Author Communication
Used).

CH2M Hill. 1999. Bioassy Report Acute Toxicity of Copper to Blue Mussel (Mytiius eduiis). Final Report.
Prepared for U.S. Navy. Norfolk, VA.

Tucker, D.W. 1998. Development of a Site-Specific Water Quality Criterion for Copper in South San Francisco
Bay. Copper Site-Specific WQC Report, San Jose/Santa Clara Water Pollution Control Plant, Environmental
Services Department, San Jose, CA: 171 p.

ToxScan. 1991. Toxicities often metals to Crassostrea gigas and Mytiius eduiis embryos and Cancer magister
larvae. Mar. Pollut. Bull. 12(9): 305-308 (Author Communication Used).

SAIC. 1993. Toxicities often metals to Crassostrea gigas and Mytiius eduiis embryos and Cancer magister
larvae. Mar. Pollut. Bull. 12(9): 305-308 (Author Communication Used).

Cardin, J.A. 1985. Results of Acute Toxicity Tests Conducted with Copper at ERL, Narragansett. U.S. EPA,
Narragansett, Rl: 10 p.

Knezovich, J.P., F.L. Harrison and J.S. Tucker. 1981. The Influence of organic chelators on the toxicity of
copper to embryos of the Pacific oyster, Crassostrea gigas. Arch. Environ. Contam. Toxicol. 10(2): 241-249.

Coglianese, M. and M. Martin. 1981. Individual and interactive effects of environmental stress on the
embryonic development of the Pacific oyster, Crassostrea gigas. Parti. Toxicity of copper and silver. Mar.
Environ. Res. 5: 13.

Dinnel, P.A., Q.J. Stober, J.M. Link, M.W. Letourneau, W.E. Roberts, S.P. Felton and R.E. Nakatani. 1983.
Methodology and Validation of a Sperm Cell Toxicity Test for Testing Toxic Substances in Marine Waters.
Final Report, FRI-UW-8306, Fisheries Research Inst., School of Fisheries, University of Washington, Seattle,
WA: 208.

S.R. Hansen and Associates. 1992. Devlopment of site-specific criterion for copper for San Fransico Bay-Final
report. Prepared for California Regional Water Quality Control Board, Oakland, CA. October.

Hyne, R.V. and D.A. Everett. 1998. Application of a benthic euryhaline amphipod, Corophium sp., as a
sediment toxicity testing organism for both freshwater and estuarine systems. Arch. Environ. Contam. Toxicol.
34(1): 26-33.

Maclnnes, J.R. and A. Calabrese. 1978. Response of Embryos of the American Oyster, Crassostrea virginica,
to Heavy Metals at Different Temperatures. In: D.S. McLusky and A.J. Berry (Eds.), Physiology and Behaviour
of Marine Organisms, Permagon Press, New York, NY: 195-202.

Salazar, M.H. and S.M. Salazar. 1989. Acute Effects of (bis)Tributyltin Oxide on Marine Organisms. Tech. Rep.
No. 1299, Naval Ocean Systems Center, San Diego, CA: 87 p. (U.S. NTIS AD-A214005).

Martin, M., J.W. Hunt, B.S. Anderson and S.L. Turpen. 1989. Experimental evaluation of the mysid
Holmesimysis costata as a test organism for effluent toxicity testing. Environ. Toxicol. Chem. 8(11): 1003-1012.

Hunt, J.W., B.S. Anderson, S.L. Turpen, A.R. Coulon, M. Martin, F.H. Palmer and J.J. Janik. 1989. Marine
Bioassay Project. 4th Report. Experimental Evaluation of Effluent Toxicity Testing Protocols with Giant Kelp,
Mysids, Red Abalone. No. 89-5WQ, State Water Resources Control Board, State of California, Sacramento,
CA: 144.

Sullivan, B.K., E. Buskey, D.C. Miller and P.J. Ritacco. 1983. Effects of copper and cadmium on growth,
swimming and predator avoidance in Eurytemora affinis (Copepoda). Mar. Biol. 77(3): 299-306.

Hall, L.W., Jr., R.D. Anderson, J.V. Kilian, B.L. Lewis and K. Traexler. 1997. Acute and chronic toxicity of
copper to the estuarine copepod Eurytemora affinis: Influence of organic complexation and speciation.
Chemosphere 35(7): 1567-1597.

Nelson, D.A., J.E. Miller and A. Calabrese. 1988. Effect of heavy metals on bay scallops, surf clams, and blue
mussels in acute and long-term exposures. Arch. Environ. Contam. Toxicol. 17(5): 595-600.

Sosnowski, S.L. and J.H. Gentile. 1978. Toxicological comparison of natural and cultured populations of
Acartia tonsa to cadmium, copper, and mercury. J. Fish. Res. Board Can. 35(10): 1366-1369.

Gentile, S. and J. Cardin. 1982. Unpublished Laboratory Data. U.S. EPA, Narragansett, Rl: 5 p.

130

-------
Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in Tables .2.2-1 and 2.2.2-2)

Lussier, S.M. and J.A. Cardin. 1985. Results of Acute Toxicity Tests Conducted with Copper at ERL,
Narragansett. U.S. EPA, Narragansett, Rl: 3.

Dinnel, P.A., J.M. Link, Q.J. Stober, M.W. Letourneau and W.E. Roberts. 1989. Comparative sensitivity of sea
urchin sperm bioassaysto metals and pesticides. Arch. Environ. Contam. Toxicol. 18(5): 748-755.

Gibson, C.I., T.O. Thatcher and C.W. Apts. 1976. Some Effects of Temperature, Chlorine, and Copper on the
Survival and Growth of the Coon Stripe Shrimp. In: G.W. Esch and R.W. McFarlane (Eds.), Rep. No. CONF-
750425, Thermal Ecology II, Proc. 1975 Symp., U.S. ERDA: 88-92.

Eisler, R. 1977. Acute toxicities of selected heavy metals to the softshell clam, Mya arenaria. Bull. Environ.
Contam. Toxicol. 17(2): 137-145.

Martin, M., M.D. Stephenson and J.H. Martin. 1977. Copper toxicity experiments in relation to abalone deaths
observed in a power plant's cooling waters. Calif. Fish Game 63(2): 95-100.

Reish, D.J. and J.A. Lemay. 1991. Toxicity and bioconcentration of metals and organic compounds by
polychaeta. Ophelia (Suppl.) 5: 653-660.

Johnson, M.W. and J.H. Gentile. 1979. Acute toxicity of cadmium, copper, and mercury to larval American
lobster Homarus americanus. Bull. Environ. Contam. Toxicol. 22(1/2): 258-264.

McLeese, D.W. 1974. Toxicity of copper at two temperatures and three salinities to the American lobster
(Homarus americanus). J. Fish. Res. Board Can. 31(12): 1949-1952.

Hutchinson, T.H., T.D. Williams and G.J. Eales. 1994. Toxicity of cadmium, hexavalent chromium and copper
to marine fish larvae (Cypinodon variegatus) and copepods (Tisbe battagiiai). Mar. Environ. Res. 38(4): 275-
290.

Kumaraguru, A.K. and K. Ramamoorthi. 1978. Toxicity of copper to three estuarine bivalves. Mar. Environ.
Res. 1(1): 43-48.

McLusky, D.S. and C.N.K. Phillips. 1975. Some effects of copper on the polychaete Phyiiodoce macuiata.
Estuar. Coast. Mar. Sci. 3(1): 103-108.

Brandt, O.M., R.W. Fujimuraand B.J. Finlayson. 1993. Use of Neomysis mercedis (Crustacea: Mysidacea) for
estuarine toxicity tests. Trans. Am. Fish. Soc. 122(2): 279-288.

Hansen, D.J. 1983. Section on Acute Toxicity Tests to be Inserted in the April 1983 Report on Site Specific
FAV's. U.S. EPA, Narragansett, Rl: 7.

Gentile, S.M. 1982. Memorandum to John H. Gentile. U.S. EPA, Narragansett, Rl.

Pesch, C.E. and D. Morgan. 1978. Influence of sediment in copper toxicity tests with the polychaete Neanthes
arenaceodentata. Water Res. 12(10): 747-751.

Reish, D.J. 1978. The effects of heavy metals on polychaetous annelids. Rev. Int. Oceanogr. Med. 49(3): 99-
104.

Reish, D.J., J.M. Martin, F.M. Piltz and J.Q. Word. 1976. The effect of heavy metals on laboratory populations
of two polychaetes with comparisons to the water quality conditions and standards in Southern CA. Water Res.
10: 299-302.

Lussier, S.M., J.H. Gentile and J. Walker. 1985. Acute and chronic effects of heavy metals and cyanide on
Mysidopsis bahia (Crustacea: Mysidacea). Aquat. Toxicol. 7(1-2): 25-35.

O'Brien, P., H. Feldman, E.V. Grill and A.G. Lewis. 1988. Copper tolerance of the life history stages of the
splashpool copepod Tigriopus caiifornicus (Copepoda, Harpacticoida). Mar. Ecol. Prog. Ser. 44(1): 59-64.

Anderson, B.S., D.P. Middaugh, J.W. Hunt and S.L. Turpen. 1991. Copper Toxicity to sperm, embryos and
larvae of topsmelt Atherinops affinis, with notes on induced spawning. Mar. Environ. Res. 31(1): 17-35.

Raymont, J. E.G. and J. Shields. 1963. Toxicity of copper and chromium in the marine environment. Int. J. Air
Water. Poll. 7: 435-443

Reish, D.J. 1993. Effects of metals and organic compunds on survival and bioaccumulation in two species of
marine gammaridean amphipod, together with a summary of toxicological research on this group. J. Nat. Hist.
27(4): 781-794

Johnson, S.K. 1974. Toxicity of Several Management Chemicals to Penaeid Shrimp. Tex. Agric. Ext. Serv.
Fish. Dis. Diagn. Lab, Report FDDL-S (FDDL- S3): 12.

Williams, P.L. and D.B. Dusenbery. 1990. Aquatic toxicology testing using the nematode, Caenorhabditis
eiegans. Environ. Toxicol. Chem. 9(10): 1285-1290

Bowmer, T., R.G.V. Boelens, B.F. Keegan and J. O'Neill. 1986. The use of marine benthic 'key' species in
ecotoxicological testing: Amphiura fiiiformis (O.F. Muller) (Echinodermata: Ophiuroidea). Aquat. Toxicol. 8(2):
93-109.

Jones, L.H., N.V. Jones and A.J. Radlett. 1976. Some effects of salinity on the toxicity of copper to the
polychaete Nereis diversicoior. Estuar. Coast. Mar. Sci. 4: 107-111.

Hughes, M.M., M.A. Heber, G.E. Morrison, S.C. Schimmel and W.J. Berry. 1989. An evaluation of a short-term
chronic effluent toxicity test using sheepshead minnow (Cyprinodon variegatus) Larvae. Environ. Pollut. 60(1):
1-14.

Birdsong, C.L. and J.W. Avault, Jr. 1971. Toxicity of certain chemicals to juvenile pompano. Prog. Fish-Cult.
33(2): 76-80.

Ahsanullah, M., M.C. Mobley and P. Rankin. 1988. Individual and combined effects of zinc, cadmium and
copper on the marine amphipod Aiiorchestes compressa. Aust. J. Mar. Freshwater Res. 39(1): 33-37.

131

-------
Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in Tables .2.2-1 and 2.2.2-2)

Ozoh, P.T.E. 1992a. The effects of salinity, temperature and sediment on the toxicity of copper to juvenile
Hediste (Nereis) diversicoior(O.FMu\\er). Environ. Monit. Assess. 21(1): 1-10.

Ozoh, P.T.E. 1992b. The importance of adult Hediste (Nereis) diversicoior in managing heavy metal pollution
in shores and estuaries. Environ. Monit. Assess. 21(3): 165-171.

Peppard, E.M., W.R. Wolters and J.W. Avault, Jr. 1991. Toxicity of chelated copper to juvenile red drum
Sciaenops oceiiatus. J. World Aquacult. Soc. 22(2): 101-108.

Connor, P.M. 1972. Acute toxicity of heavy metals to some marine larvae. Mar. Pollut. Bull. 3(12): 190-192.

Steele, C.W. 1983. Comparison of the behavioural and acute toxicity of copper to sheepshead, Atlantic croaker
and pinfish. Mar. Pollut. Bull. 14(11): 425-428.

Marcano, L., O. Nusetti, J. Rodriguez-Grau and J. Vilas. 1996. Uptake and depuration of copper and zinc in
relation to metal-binding protein in the polychaete Eurythoe campianata. Comp. Biochem. Physiol. C 114(3):
179-184.

Nusetti, O., R. Salazar-Lugo, J. Rodriguez-Grau and J. Vilas. 1998. Immune and biochemical responses of the
polychaete Eurythoe compianata exposed to sublethal concentration of copper. Comp. Biochem. Physiol. C
119(2): 177-183.

Sivadasan, C.R., P.N.K. Nambisan and R. Damodaran. 1986. Toxicity of mercury, copper and zinc to the
prawn Metapenaeus dobsoni (Mier). Curr. Sci. 55(7): 337-340.

Lin, H.C. and W.A. Dunson. 1993. The effect of salinity on the acute toxicity of cadmium to the tropical,
estuarine, hermaphroditic fish, Rivuius marmoratus: A comparison of Cd, Cu, and Zn tolerance with Funduius
heterociitus. Arch. Environ. Contam. Toxicol. 25: 41-47.

Vranken, G., R. Vandergaeghen and C. Heip. 1991. Effects of pollutants on life-history parameters of the
marine nematode Monhystera disjuncta. ICES J. Mar. Sci. 48: 325-334.

Bengtsson, B.E. 1978. Use of a harpacticoid copepod in toxicity tests. Mar. Pollut. Bull. 9: 238-241.

Hilmy, A.M., N.F. Abdel-Hamid and K.S. Ghazaly. 1985. Toxic effects of both zinc and copper on size and sex
of Portunus peiaqicus (L) (Crustacea: Decapoda). Bull. Inst. Oceanogr. Fish. (Cairo) 11: 207-215.

Reardon, I.S. and R.M. Harrell. 1990. Acute toxicity of formalin and copper sulfate to striped bass fingerlings
held in varying salinities. Aquaculture 87(3/4): 255-270.

Hetrick, F.M., B.S. Roberson and C.F. Tsai. 1982. Effect of Heavy Metals on the Susceptibility and Immune
Response of Striped Bass to Bacterial Pathogens. NOAA-8211 2603, NOAA, Office Mar. Pollut., Rockville,
MD: 26 p. (U.S. NTIS PB83-151936).

Olson, K.R. and R.C. Harrel. 1973. Effect of salinity on acute toxicity of mercury, copper, and chromium for
Rangia cuneata (Pelecypoda, Mactridae). Contrib. Mar. Sci. 17: 9-13.

Moulder, S.M. 1980. Combined Effect of the chlorides of mercury and copper in sea water on the euryhaline
amphipod Gammarus duebeni. Mar. Biol. 59(4): 193-200.

Chronic References

Lussier, S.M., J.H. Gentile and J. Walker. 1985. Acute and chronic effects of heavy metals and cyanide on
Mysidopsis bahia (Crustacea: Mysidacea). Aquat. Toxicol. 7(1-2): 25-35.

B. Studies That EPA Considered But Did Not Utilize In This Determination

1) For the studies that were not utilized, but the most representative SMAV/2 or
most representative SMCV fell below the criterion, or, if the studies were for a
species associated with one of the four most sensitive genera used to calculate the
FAV in the most recent national ambient water quality criteria dataset used to
derive the CMC54, EPA is providing a transparent rationale as to why they were
not utilized (see below).

54 U.S. EPA. 1995. Ambient Water Quality Criteria - Saltwater Copper Addendum. U.S. EPA, Narragansett, RI.

132

133

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2.2.3 LEAD

2.2.3.1 Evaluation of the Acute Saltwater Criterion Concentration for Lead
A. Presentation of Toxicological Data

Oregon adopted a saltwater acute criterion concentration of 210 |ig/L for lead that is expressed in
terms of the dissolved concentration of the metal. This dissolved metal concentration is the same
as the saltwater CMC recommended for use nationally by EPA for the protection of aquatic
life55. EPA developed the recommended criterion in accordance with the 1985 Guidelines
pursuant to CWA section 304(a).

Table 2.2.3-1 provides available SMAVs based on available acute toxicity data for lead to
aquatic life from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Table 2.2.3-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values
(GMAVs) for Lead

Genus

Species

Common name

Most
Representative
SMAV
(MS)"-)

GMAV
(Mg/L)

Acute
References

(used in the
calculation of
the SMAV)

Pandalus

montagui

Aesop shrimp

356625

Fundulus

heteroclitus*

Mummichog

299565

Mya

arenaria

Soft-shell clam

25677

Epinephelus

sp.

Rockcod, Grouper

16167

Polyodon

spathula

Paddlefish

14227

Ctenodrilus

serratus

Polychaete worm

11742

Elasmopus

bampo

Amphipod

>9510

Nereis

arenaceodentata

Polychaete worm

8541

8,16

Argopecten

irradians

Bay scallop

8179

Menidia

menidia

Atlantic silverside

>9510

Menidia

beryllina

Inland silverside

>2986

>5329

11,12

Corophium

insidiosum

Amphipod

>4755

Pectinaria

californiensis

Cone worm

>4755

Onisimus

litoralis

Amphipod

>3329

Cyprinodon

variegatus

Sheepshead minnow

>2986

11,12

Americamysis

bahia

Opossum shrimp

2977

Ophryotrocha

labronica

Polychaete

>4755

Ophryotrocha

diadema

Polychaete

1643

>2795

Crangon

sp.

Caridean shrimp

>1997

Loligo

opalescens

California market squid

>1988

2,3

Scorpaenichthys

marmoratus

Cabezon

1441

2,3

Crassostrea

virginica

Eastern oyster

2330

Crassostrea

gigas

Pacific oyster

587.3

1170

1,3,4

Mercenaria

mercenaria

Northern quahog or Hard
clam

741.8

Cancer

anthonvi*

Yellow rock crab

>951.0

Cancer

magister

Dungeness or edible crab

558.6

>728.8

1,2

Acartia

clausi

Copepod

635.3

Mytilus

edulis

Common bay mussel,

452.7

55 See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.

The data which serve as the basis for the current nationally-recommended criteria are from: U.S. EPA. 1984. Ambient Water Quality Criteria for
Lead. EPA-440/5-84-027.

134

-------
Genus

Species

Common name

Most
Representative
SMAV
(MS)"-)

GMAV
(MQ/L)

Acute
References

(used in the
calculation of
the SMAV)

blue mussel

Note 1: Species that are bold and italicized indicate those associated with the four most sensitive genera used to derive the FAV in
the 1984 ALC document. Underlined species with an asterisk (*) indicate known or suspected Oregon non-resident species, and for
this evaluation, only those non-resident species below the criterion or related to the four most sensitive genera are identified as
such.

Note 2: The reporting of calculated values has been limited to a minimum of four significant figures for convenience and use in this
evaluation with the exception of very high values, which are reported as whole numbers - see text in section 2.2 of this evaluation for
an explanation of this decision, particularly for metals such as lead which are expressed on a dissolved metal basis for a
comparison with the acute criterion concentration.

B. Evaluation of the Protectiveness of the Oregon Saltwater Acute Criterion

Following review of GMAV and SMAV/2 values in Table 2.2.33-1, all tested genera and species
values are greater than Oregon's acute criterion concentration for lead. Therefore, EPA
concluded that acute effects are not expected to occur at concentrations equal to or lower than the
criterion, and thus the aquatic life designated use would be protected by the criterion.

2.2.3.2 Evaluation of the Chronic Saltwater Criterion Concentration for Lead
A. Presentation of Toxicological Data

Oregon adopted a saltwater chronic criterion concentration of 8.1 |ig/L for lead expressed as the
dissolved metal concentration in the water column. This concentration is the same as the
saltwater CCC recommended for use nationally by EPA for the protection of aquatic life56. EPA
developed the recommended criterion in accordance with the 1985 Guidelines pursuant to CWA
section 304(a).

Table 2.2.3-2 presents a compilation of the GMAVs from Table 2.2.3-1, any experimentally
determined SMCVs obtained from the criteria document and EPA ECOTOX download used for
the BE, and estimated GMCVs based on the GMAV/ACR. The 1984 criteria document for lead57
reported an FACR of 51.29, which EPA calculated as the geometric mean of experimentally
determined ACRs for three freshwater species and one saltwater species ranging from 18.13 for
an acutely sensitive freshwater invertebrate, the cladoceran Daphnia magna, to 124.8 for a
relatively insensitive saltwater invertebrate species, Americamysis bahia. However, considering
an update of the lead dataset in 1998, the number of ACRs was increased to six freshwater and
one saltwater species, although the smallmouth bass ratio was not definitive. The five remaining
valid freshwater Species Mean ACRs range from 4.77 to 61.97, whereas the saltwater mysid
ratio remains 124.8. For the six acceptable ACRs (4.77, 6.38, 18.13, 49.35, 61.97 and 124.8) the
highest ACR is 26 fold greater than the lowest value. If the saltwater mysid ratio is deleted, the

56 See footnote 57 above.

57 U.S. EPA. 1984. Ambient Water Quality Criteria Document for Lead. EPA-440/5-84-027.

135

-------
ratios differ by a factor of only 13. Since the mysid is acutely insensitive but chronically
sensitive to lead, inclusion of the mysid ratio provides the necessary safety margin to be
chronically protective of sensitive saltwater invertebrates. Thus, the EPA calculated the predicted
GMCVs for lead in Table 2.2.3-2 using the FACR of 24.39 (geomean of the six ACRs above)
and the following equation: Predicted GMCV = GMAV/FACR.

EPA compared the SMCVs for each species to Oregon's lead chronic criterion to determine
whether the chronic criterion will protect Oregon's aquatic life designated use.

Table 2.2.3-2: Genus Mean Chronic Values (SMCVs) for Lead

Genus

Species

Common name

GMAV
(MS)"-)

SMCV
(MS)"-)

('experimentally
derived)

Chronic
References

(used in the
calculation
of the
SMCV)

Predicted
GMCV
(MS)"-)

Pandalus

montagui

Aesop shrimp

356625

14622

Fundulus

heteroclitus*

Mummichog

299565

12282

Mya

arenaria

Soft-shell clam

25677

1053

Epinephelus

sp.

Rockcod, Grouper

16167

662.9

Polyodon

spathula

Paddlefish

14227

583.3

Ctenodrilus

serratus

Polychaete worm

11742

481.4

Elasmopus

bampo

Amphipod

>9510

>389.9

Nereis

arenaceodentata

Polychaete worm

8541

350.2

Argopecten

irradians

Bay scallop

8179

335.3

Menidia

menidia

Atlantic silverside

Menidia

beryllina

Inland silverside

>5329

>218.5

Corophium

insidiosum

Amphipod

>4755

>195.0

Pectinaria

californiensis

Cone worm

>4755

>195.0

Onisimus

litoralis

Amphipod

>3329

>136.5

Cyprinodon

variegatus

Sheepshead minnow

>2986

>122.4

Americamysis

bahia

Opossum shrimp

2977

23.85

122.0
(23.85)

Ophryotrocha

labronica

Polychaete

Ophryotrocha

diadema

Polychaete

>2795

>114.6

Crangon

sp.

Caridean shrimp

>1997

>81.88

Loligo

opalescens

California market
squid

>1988

>81.49

Scorpaenichthys

marmoratus

Cabezon

1441

59.07

Crassostrea

virginica

Eastern oyster

Crassostrea

gigas

Pacific oyster

1170

47.96

Mercenaria

mercenaria

Northern quahog or
Hard clam

741.8

30.41

Cancer

anthonvi*

Yellow rock crab

Cancer

magister

Dungeness or
edible crab

>728.8

>29.88

Acartia

clausi

Copepod

635.3

26.05

Mytilus

edulis

Common bay
mussel, blue
mussel

452.7

18.56

See same notes as above under Table 3.2.5-1.

B. Evaluation of the Protectiveness of the Oregon Saltwater Chronic Criterion

136

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Following the review of the SMCV values in Table 2.2.3-2, all of the genera and species had
values greater than Oregon's chronic criterion for lead. Therefore, EPA concluded that chronic
effects are not expected to occur at concentrations equal to or lower than the criterion, and thus
the aquatic life designated use would be protected by the chronic criterion.

2.2.3.3 References for Lead

A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the acute and chronic tables, and are the source from which EPA
obtained SMAVs (acute table) and experimentally-derived SMCVs (chronic table).

Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in Tables 2.2.3-1 and 2.2.3-2)

Acute References

Martin, M., K.E. Osborn, P. Billig and N. Glickstein. 1981. Toxicities often metals to Crassostrea gigas and Mytiius
eduiis embryos and Cancer magister larvae. Mar. Pollut. Bull. 12(9): 305-308 (Author Communication Used).

Dinnel, P.A., J.M. Link, Q.J. Stober, M.W. Letourneau and W.E. Roberts. 1989. Comparative sensitivity of sea urchin
sperm bioassays to metals and pesticides. Arch. Environ. Contam. Toxicol. 18(5): 748-755.

Dinnel, P.A., Q.J. Stober, J.M. Link, M.W. Letourneau, W.E. Roberts, S.P. Felton and R.E. Nakatani. 1983.
Methodology and validation of a sperm cell toxicity test for testing toxic substances in marine waters. Final Rep. FRI -
UW-8306, Fish. Res. Inst., School of Fish., Univ. of Washington, Seattle, WA: 208 p.

Chapman, P.M. and C. McPherson. 1993. Comparative zinc and lead toxicity tests with arctic marine invertebrates
and implications for toxicant discharges. Polar Record 29(168): 45-54.

Gentile, S.M. 1982. Memorandum to John H. Gentile. U.S. EPA, Narragansett, Rl.

Calabrese, A. and D.A. Nelson. 1974. Inhibition of embryonic development of the hard clam, Mercenaria mercenaria,
by heavy metals. Bull. Environ. Contam. Toxicol. 11(1): 92-97.

Macdonald, J.M., J.D. Shields and R.K. Zimmer-Faust. 1988. Acute toxicities of eleven metals to early life-history
stages of the yellow crab Cancer anthonyi. Mar. Biol. (Berlin) 98(2): 201-207.

Reish, D.J., T.V. Gerlinger, C.A. Phillips and P.D. Schmidtbauer. 1977. Toxicity of formulated mine tailings on
marine polychaete. Marine Biological Consultants, Costa Mesa, CA: 133 p.

Calabrese, A., R.S. Collier, D.A. Nelson and J.R. Mac Innes. 1973. The toxicity of heavy metals to embryos of the
American oyster Crassostrea virginica. Mar. Biol. 18(3): 162-166.

Lussier, S.M., J.H. Gentile and J. Walker. 1985. Acute and chronic effects of heavy metals and cyanide on
Mysidopsis bahia (Crustacea: Mysidacea). Aquat. Toxicol. 7(1-2): 25-35.

Cardin, J.A. 1981. Memorandum to John H. Gentile. U.S. EPA, Narragansett, Rl.

Cardin, J.A. 1985. Results of acute toxicity tests conducted with lead at ERL, Narragansett. U.S. EPA, Narragansett,
Rl: 2 p.

Reish, D.J. 1993. Effects of metals and organic compounds on survival and bioaccumulation in two species of
marine gammaridean amphipod, together with a summary of toxicological research on this group. J. Nat. Hist. 27(4):
781-794.

Reish, D.J. and J.E. LeMay. 1991. Toxicity and bioconcentration of metals and organic compounds by polychaeta.
Ophelia (Suppl) 5: 653-660.

Nelson, D.A., J.E. Miller and A. Calabrese. 1988. Effect of heavy metals on bay scallops, surf clams and blue
mussels in acute and long-term exposures. Arch. Environ. Contam. Toxicol. 17(5): 595-600.

Reish, D.J. and T.V. Gerlinger. 1984. The effects of cadmium, lead, and zinc on survival and reproduction in the
polychaetous annelid Neanthes arenaceodentata (F. nereididae). In: P. A. Hutchings (Ed.), Proc. of the First Int.
Polychaete Conf., Sydney, Aust., July 1983, The Linnean Society of New South Wales, Australia: 383-389.

Berry, W.J. 1981. Memorandum to John H. Gentile. U.S. EPA, Narragansett, Rl.

Siammai, H. and S. Chiayvareesajja. 1988. Acute toxicity of lead on grouper (Epinepheius spp.). Songklanakarin J.
Sci. Technol.10(2): 179-184.

Eisler, R. 1977. Acute toxicities of selected heavy metals to the soft-shell clam, Mya arenaria. Bull. Environ. Contam.
Toxicol. 17: 137.

Dorfman, D. 1977. Tolerance of Funduius heterociitus to different metals in salt waters. Bull. N.J. Acad. Sci. 22(2):
21-23.

Portmann, J.E. and K.W. Wilson. 1971. The toxicity of 140 substances to the brown shrimp and other marine
animals. Shellfish Information Leaflet No. 22 (2nd Ed.), Ministry of Agric. Fish. Food, Fish. Lab. Burnham-on-Crouch,

137

-------
Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in Tables 2.2.3-1 and 2.2.3-2)

Essex, and Fish Exp. Station Conway, North Wales: 12 p

Chronic References

Lussier, S.M., J.H. Gentile and J. Walker. 1985. Acute and chronic effects of heavy metals and cyanide on
Mysidopsis bahia (Crustacea: Mysidacea). Aquat. Toxicol. 7(1-2): 25-35.

B. Studies That EPA Considered But Did Not Utilize In This Determination

most recent national ambient water quality criteria dataset used to derive the CMC ,
EPA is providing a transparent rationale as to why they were not utilized (see below).

2) For the studies that were not utilized because they were not found to be pertinent to
this determination (including failing the QA/QC procedures listed in Appendix A)
upon initial review of the download from ECOTOX, EPA is providing the code that
identifies why EPA determined that the results of the study were not reliable (see
Appendix Q).

58 U.S. EPA. 1984. Ambient Water Quality Criteria Documents for Lead. EPA-440/5-84-027.

138

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2.2.4 NICKEL

2.2.4.1 Evaluation of the Acute Saltwater Criterion Concentration for Nickel
A. Presentation of Toxicological Data

Oregon adopted a saltwater acute criterion concentration of 74 |ig/L for nickel that is expressed
in terms of the dissolved concentration of the metal. This dissolved metal concentration is the
same as the saltwater acute criterion concentration recommended for use nationally by EPA for
the protection of aquatic life59. EPA developed the recommended criterion in accordance with
the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.2.4-1 provides available GMAVs based on available acute toxicity data for nickel to
aquatic animals from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Table 2.2.4-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values
(GMAVs) for Nickel

Most

Acute References

Representative
SMAV

GMAV

(used in the
calculation of the

Genus

Species

Common name

(ng/L)

SMAV)

Mya

arenaria

Sand gaper,
soft shell clam

316800

Macoma

balthica

Balthica macoma or clam

291555

Asterias

forbesii

Common starfish

148500

Fundulus

heteroclitus

Mummichog

148401

13,17

Penaeus

duorarum

Northern pink shrimp

110880

Nassarius

obsoletus

Eastern mud snail

71280

Leiostomus

xanthurus

Spot

69300

Capitella

capitata

Polychaete worm

>49500

Neanthes

arenaceodentata

Polychaete worm

48510

Pagurus

longicarpus

Longwrist hermit crab

46530

Allorchestes

compressa

Scud, Amphipod

34333

Atherinops

affinis

Topsmelt

26294

Nereis

viridis

Polychaete worm

24750

Morone

saxatilis

Striped bass

20790

Corophium

volutator

Scud

18761

Menidia

peninsulae

Tidewater silverside

37620

Menidia

menidia

Atlantic silverside

7878

17216

Ctenodrilus

serratus

Polychaete worm

16830

Monhystera

disjuncta

Nematode

14850

Eurytemora

affinis

Calanoid copepod

10586

2,7

Nitocra

spinipes

Harpacticoid copepod

5940

Acartia

clausi

Calanoid copepod

2656

2,7

Strongylocentrotus

purpuratus

Purple sea urchin

2475

Mytilus

edulis

Common bay mussel,
Blue mussel

882.1

Crassostrea

virainica*

Eastern oyster

1168

Crassostrea

gigas

Pacific oyster

345.5

635.3

Americamvsis

biaelowi*

Shrimp

627.7

59 See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.

The data which serve as the basis for the current nationally-recommended criteria are from: U.S. EPA. 1986. Ambient Water Quality Criteria for
Nickel - 1986. EPA 440-5-86-004.

139

-------
Genus

Species

Common name

Most
Representative
SMAV
(MS)"-)

GMAV
(MQ/L)

Acute References

(used in the
calculation of the
SMAV)

Americamvsis

bahia*

Opossum shrimp

502.9

561.8

Mercenaria

mercenaria*

Northern quahog or
Hard clam

306.9

Heteromvsis

formosa*

Opossom Shrimp

150.2

Mvsidoosis

intii*

Shrimp

147.1

Haliotis

rufescens

Red abalone

144.0

Note 1: Species that are bold and italicized indicate those associated with the four most sensitive genera used to derive the FAV or
FCV in the 1986 ALC document. Underlined species with an asterisk (*) indicate known or suspected Oregon non-resident species,
and for this evaluation, only those non-resident species below the criterion or related to the four most sensitive genera are identified
as such.

Note 2: The reporting of calculated values has been limited to a minimum of four significant figures for convenience and use in this
evaluation with the exception of very high values, which are reported as whole numbers - see text in section 2.2 of this evaluation for
an explanation of this decision, particularly for metals such as nickel which are expressed on a dissolved metal basis for a
comparison with the acute criterion concentration.

B. Evaluation of the Protectiveness of the Oregon Saltwater Acute Criterion

Following review of GMAV values in Table 2.2.4-1, all tested genera have values greater than
Oregon's acute criterion concentration for nickel. Therefore, EPA concluded that acute effects to
nearly all genera are not expected to occur at concentrations equal to or lower than the criterion,
and thus the aquatic life designated use would be protected by the criterion.

When compared to Oregon's acute criterion concentration for nickel, SMAV/2 values for two
test species (the red abalone, Haliotis rufescens, and the shrimp, Mysidopsis intii) were lower
than the acute criterion concentration of 74|ig/L dissolved nickel. Of these two species, only the
red abalone is expected to reside in Oregon waters. Therefore, EPA reviewed the data from the
study that makes up the most representative SMAV for this resident species and compared the
SMAV value to determine whether the SMAV/2 value is quantitatively different from the
criterion value of 74 |ig/L.

The SMAV based on a single LC50 for Haliotis rufescens was 144.0 |ig/L dissolved nickel, with
5 and 95 percent confidence intervals of 135.6 and 152.5 |ig/L. When divided by two, the
SMAV/2 for H. rufescens is 72.00 |ig/L (text box A -H. rufescens acute).

Because the Oregon acute criterion for nickel is approximately equal to the SMAV/2, a value
estimated to represent an effect concentration indistinguishable from control levels for this
species it is expected that the criterion would be sufficiently protective of this species, especially
when considering the uncertainty in the low range of toxicity curve being considered.

Saltwater nickel acute criterion comparison

Text Box A (acute) - Basis for the meta analysis comparing the SMAV/2 for the red abalone (H.
rufescens) to the acute criterion for nickel (74 |ig/L dissolved metal concentration).

140

-------
Haliotis rufescens

Reported Values

Dissolved Normalized Values

Dissolved Normalized Values/2

LC50 5% CI

95% CI

LC50 5% CI 95% CI

LC50/2

CMC

145.5 137.0

154.0

144.0 135.6 152.5

72.00

(SMAV)

(SMAV/2)

2.2.4.2 Evaluation of the Chronic Saltwater Criterion Concentration for Nickel
A. Presentation of Toxicological Data

Oregon adopted a saltwater chronic criterion concentration of 8.2 |ig/L for nickel expressed as
the dissolved metal concentration in the water column. This concentration is the same as the
saltwater CCC recommended for use nationally by EPA for the protection of aquatic life60. EPA
developed the recommended criterion in accordance with the 1985 Guidelines pursuant to CWA
section 304(a).

Table 2.2.4-2 presents a compilation of the GMAVs from Table 2.2.4-1, any experimentally
determined SMCVs obtained from the criteria document and EPA ECOTOX download used for
the BE, and estimated GMCVs based on the GMAV/FACR. The 1986 criteria document for
nickel61 reported an FACR of 17.99, which EPA calculated as the geometric mean of the ACRs
29.86 and 35.58 from two freshwater species {Daphnia magna and Pimephalespromelas,
respectively) and the ACR of 5.478 for one acutely sensitive saltwater species (Americamysis
bahia). However, new ACRs were recently made available in the literature for three new
saltwater species: red abalone, Haliotis rufescens (ACR of 5.505), Mysidopsis intii (ACR of
6.727) and topsmelt, Atherinops affinis (ACR of 6.220). The new ACR for saltwater species
correspond well the ACR of 5.478 for A. bahia, which is in contrast to the freshwater ACR
values used in the 1986 nickel criteria document, which are 29.86 for Daphnia magna and 35.58
for Pimephales promelas. The FACR calculated as the geometric mean of only the four
saltwater ACR values is 5.960, compared to the 17.99 ACR presented in the 1986 criteria
document. Because the freshwater ACRs were an order of magnitude larger than the saltwater
ACRs, EPA calculated the predicted GMCVs for nickel in Table 2.2.4-2 using an FACR of
5.960 and the following equation: Predicted GMCV = GMAV/FACR.

EPA compared the SMCVs for each species to Oregon's nickel chronic criterion to determine
whether the chronic criterion will protect Oregon's aquatic life designated use.

Table 2.2.4-2: <

jenus Mean Chronic Values

(GMCVs) for Nickel

Genus

Species

Common name

GMAV
(MS)"-)

SMCV

(Mg/L)

('experimentally
derived)

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(MS)"-)

Mya

arenaria

Sand gaper, soft
shell clam

316800

53154

Macoma

balthica

Balthica macoma

291555

48919

60 See footnote 61 above.

61 U.S. EPA. 1986. Ambient Water Quality Criteria for Nickel - 1986. EPA 440-5-86-004.

141

-------
Genus

Species

Common name

GMAV
(MS)"-)

SMCV

(Mg/L)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(MS)"-)

or clam

Asterias

forbesii

Common starfish

148500

24916

Fundulus

heteroclitus

Mummichog

148401

24899

Penaeus

duorarum

Northern pink
shrimp

110880

18604

Nassarius

obsoletus

Eastern mud snail

71280

11960

Leiostomus

xanthurus

Spot

69300

11628

Capitella

capitata

Polychaete worm

>49500

>8305

Neanthes

arenaceodentata

Polychaete worm

48510

8139

Pagurus

longicarpus

Longwrist hermit
crab

46530

7807

Allorchestes

compressa

Scud, Amphipod

34333

5761

Atherinops

affinis

Topsmelt

26294

4228

4412
(4228)

Nereis

viridis

Polychaete worm

24750

4153

Morone

saxatilis

Striped bass

20790

3488

Corophium

volutator

Scud

18761

3148

Menidia

peninsulae

Tidewater
silverside

Menidia

menidia

Atlantic silverside

17216

2889

Ctenodrilus

serratus

Polychaete worm

16830

2824

Monhystera

disjuncta

Nematode

14850

2492

Eurytemora

affinis

Calanoid copepod

10586

1776

Nitocra

spinipes

Harpacticoid
copepod

5940

996.6

Acartia

clausi

Calanoid copepod

2656

445.6

Strongylocentrotus

purpuratus

Purple sea urchin

2475

415.3

Mytilus

edulis

Common bay
mussel, Blue
mussel

882.1

148.0

Crassostrea

virainica*

Eastern oyster

Crassostrea

gigas

Pacific oyster

635.3

106.6

Americamvsis

biaeiowi*

Shrimp

Americamvsis

bahia*

Opossum shrimp

561.8

91.81

2,3

94.27
(91.81)

Mercenaria

mercenaria*

Northern quahog
or Hard clam

306.9

51.49

Heteromvsis

formosa*

Opossom
Shrimp

150.2

25.20

Mvsidopsis

intii*

Shrimp

147.1

21.87

24.68
(21.87)

Haliotis

rufescens

Red abalone

144.0

26.17

24.16
(26.17)

See same notes as above under Table 2.2.4-1.

B. Evaluation of the Protectiveness of the Oregon Saltwater Chronic Criterion

Following the review of the GMCV values in Table 2.2.4-2, all genera and species have values
greater than Oregon's chronic criterion for nickel. Therefore, EPA concluded that chronic effects
are not expected to occur at concentrations lower than the criterion and thus these species would
be protected.

142

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2.2.4.3 References for Nickel

A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the acute and chronic tables, and are the source from which EPA
obtained SMAVs (acute table) and experimentally-derived SMCVs (chronic table).

Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in Tables 2.2.4-1 and 2.2.4-2)

Acute References

Hunt, J.W., B.S. Anderson, B.M. Phillips, R.S. Tjeerdema, H.M. Puckett, M. Stephenson, D.W. Tucker and D.
Watson. 2002. Acute and chronic toxicity of nickel to marine organisms: Implications for water quality criteria.
Environ. Toxicol. Chem. 21(11): 2423-2430

Gentile, S. and J. Cardin. 1982. Unpublished Laboratory Data. U.S. EPA, Narragansett, Rl: 5 p.

Calabrese, A. and D.A. Nelson. 1974. Inhibition of embryonic development of the hard clam, Mercenaria
mercenaria, by heavy metals. Bull. Environ. Contam. Toxicol. 11(1): 92-97.

Martin, M., K.E. Osborn, P. Billig and N. Glickstein. 1981. Toxicities often metals to Crassostrea gigas and
Mytiius eduiis embryos and Cancer magister larvae. Mar. Pollut. Bull. 12(9): 305-308 (Author Communication
Used).

Calabrese, A., R.S. Collier, D.A. Nelson and J.R. Mac Innes. 1973. The toxicity of heavy metals to embryos of
the American oyster Crassostrea virginica. Mar. Biol. 18(3): 162-166.

Garman, G.D., S.L. Anderson and G.N. Cherr. 1997. Developmental abnormalities and DNA-protein crosslinks in
sea urchin embryos exposed to three metals. Aquat. Toxicol. 39: 247-265

Lussier, S.M. and J.A. Cardin. 1985. Results of Acute Toxicity Tests Conducted with Nickel at ERL,
Narragansett. U.S. EPA, Narragansett, Rl: 4.

Bengtsson, B.E. 1978. Use of a harpacticoid copepod in toxicity tests. Mar. Pollut. Bull. 9: 238-241.

Vranken, G., R. Vandergaeghen and C. Heip. 1991. Effects of pollutants on life-history parameters of the marine
nematode Monhystera disjuncta. ICES J. Mar. Sci. 48: 325-334.

Petrich, S.M. and D.J. Reish. 1979. Effects of aluminum and nickel on survival and reproduction in polychaetous
annelids. Bull. Environ. Contam. Toxicol. 23(4/5): 698-702.

Bryant, V., D.M. Newbery, D.S. McLusky and R. Campbell. 1985. Effect of temperature and salinity on the
toxicity of nickel and zinc to two estuarine invertebrates (Corophium voiutator, Macoma baithica). Mar. Ecol. Prog.
Ser. 24(1-2): 139-153.

Palawski, D., J.B. Hunn and F.J. Dwyer. 1985. Sensitivity of young striped bass to organic and inorganic
contaminants in fresh and saline waters. Trans. Am. Fish. Soc. 114: 748-753.

Eisler, R. and R.J. Hennekey. 1977. Acute toxicities of Cd2+, Cr+6, Hg2+, Ni2+ and Zn2+ to estuarine
macrofauna. Arch. Environ. Contam. Toxicol. 6(2/3): 315-323.

Ahsanullah, M. 1982. Acute toxicity of chromium, mercury, molybdenum and nickel to the amphipod Aiiorchestes
compressa. Aust. J. Mar. Freshwater Res. 33(3): 465-474.

Hansen, D.J. 1983. Section on Acute Toxicity Tests to be Inserted in the April 1983 Report on Site Specific
FAV's. U.S. EPA, Narragansett, Rl :7.

Bentley, R.E., T. Heitmuller, B.H. Sleight III and P.R. Parrish. 1975. Acute Toxicity of Nickel to Bluegill (Lepomis
macrochirus), Rainbow Trout (Saimo gairdneri), and Pink Shrimp (Penaeus duorarum). U.S. EPA, Criteria
Branch, WA-6-99-1414-B, Washington, D.C.: 14.

Dorfman, D. 1977. Tolerance of Funduius heterociitus to different metals in salt water. Bull. N.J. Acad. Sci. 22:
21-23.

Chronic References

Gentile, J.H., S.M. Gentile, N.G. Hairston Jr. and B.K. Sullivan. 1982. The use of life-tables for evaluating the
chronic toxicity of pollutants to Mysidopsis bahia. Hydrobiologia 93(1/2): 179-182.

Lussier, S.M., J.H. Gentile and J. Walker. 1985. Acute and chronic effects of heavy metals and cyanide on
Mysidopsis bahia (Crustacea: Mysidacea). Aquat. Toxicol. 7: 25-35.

B. Studies That EPA Considered But Did Not Utilize In This Determination

143

-------
EPA evaluated the studies and determined that the results were not reliable for use in this
determination, either because they were not pertinent to this determination or they failed the
QA/QC procedures listed in Appendix A. For full descriptions, see Appendix R.

1) For the studies that were not utilized, but the most representative SMAV/2 or most
representative SMCV fell below the criterion, or, if the studies were for a species
associated with one of the four most sensitive genera used to calculate the FAV in the
most recent national ambient water quality criteria dataset used to derive the CMC62,
EPA is providing a transparent rationale as to why they were not utilized (see below).

2) For the studies that were not utilized because they were not found to be pertinent to
this determination (including failing the QA/QC procedures listed in Appendix A)
upon initial review of the download from ECOTOX, EPA is providing the code that
identifies why EPA determined that the results of the study were not reliable.

62 U.S. EPA. 1986. Ambient Water Quality Criteria for Nickel - 1986. EPA 440-5-86-004.

144

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2.2.5 PENTACHLOROPHENOL

2.2.5.1 Presentation of Acute Saltwater Data in Support of Chronic Pentachlorophenol
A. Presentation of Toxicological Data

Table 2.2.5-1 provides available GMAVs based on available acute toxicity data for
pentachlorophenol to aquatic life from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE. This information is provided
to support the analysis of the chronic criterion.

Table 2.2.5-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values
(GMAVs) for Pentachlorophenol

Acute

Most

References

Representative
SMAV

GMAV

(used in the
calculation of the

Genus

Species

Common name

(MS)"-)

(Mg/L)

SMAV)

Crangon

crangon

Common shrimp, Sand shrimp

7800

Monhystera

disjuncta

Nematode

2100

Crepidula

fornicata

Slipper limpet

1200

Penaeus

duorarum

Northern pink shrimp

5600

Penaeus

aztecus

Brown shrimp

>195.0

>1045

Brachionus

plicatilis

Rotifer

900.0

Ophryotrocha

diadema

Polychaete

862.6

11,20

Arbacia

punctulata

Purple-spined sea urchin

785.9

Platichthys

flesus

Starry, European flounder

728.9

Monopylephorus

cuticulatus

Tubificid

598.2

Neanthes

succinea

Clam worm

>672.0

Neanthes

arenaceodentata

Polychaete worm

435.0

>540.7

Palaemonetes

pugio

Daggerblade grass shrimp

491.3

4,18

Mulinia

lateralis

Clam

482.0

Solea

solea

Dover sole

450.0

Peloscolex

gabriellae

Oligochaete

423.4

Limnodriloides

verrucosus

Oligochaete worm

403.1

Gammarus

tigrinus

Scud

371.0

Ensis

minor

Jackknife clam

344.0

Mytilus

edulis

Common bay mussel, Blue
mussel

328.8

Fundulus

similis

Longnose killifish

>306.0

Mercenaria

mercenaria

Northern quahog or Hard clam

<250.0

Cyprinodon

variegatus

Sheepshead minnow

442.0

Cyprinodon

bovinus

Leon Springs pupfish

80.00

188.0

Temora

longicornis

Calanoid copepod

170.0

Laevicardium

mortoni

Morton's egg cockle

163.0

Mugil

cephalus

Striped mullet

112.1

Nitocra

spinipes

Harpacticoid copepod

102.5

Corophium

acherusicum

Scud

82.00

Heteromastus

filiformis

Capitellid thread worm

67.00

Pseudodiaotomus

coronatus*

Calanoid copepod

62.81

Haliotis

rufescens

Red abalone

56.02

Laaodon

rhomboides*

Pinfish

53.20

Crassostrea

virainica*

Eastern oyster

42.55

3,4

Crassostrea

gigas

Pacific oyster

40.83

41.68

CI u pea

pallasii

Pacific herring

25.29

Note 1: Species that are bold and italicized indicate those associated with the four most sensitive genera used to derive the FAV in
the 1986 ALC document. Underlined species with an asterisk (*) indicate known or suspected Oregon non-resident species, and for

145

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this evaluation, only those non-resident species below the criterion or related to the four most sensitive genera are identified as
such.

2.2.5.2 Evaluation of the Chronic Saltwater Criterion Concentration for
Pentachlorophenol

A. Presentation of Toxicological Data

Oregon adopted a saltwater chronic criterion concentration of 7.9 |ig/L for pentachlorophenol.
This concentration is the same as the saltwater chronic criterion concentration recommended for
use nationally by EPA for the protection of aquatic life63. EPA developed the recommended
criterion in accordance with the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.2.5-2 presents a compilation of the GMAVs from Table 2.2.5-1, any experimentally
determined SMCVs obtained from the criteria document and EPA ECOTOX download used for
the BE, and estimated GMCVs based on the GMAV/ACR. The 1986 criteria document for
pentachlorophenol reported an FACR of 3.166, which EPA calculated as the geometric mean of
five experimentally determined ACRs ranging from 0.8945 for the cladoceran (Simocephalus
vetulus) to 6.873 for the saltwater fish species Cyprinodon variegatus. Since no additional
acceptable ACRs are available, and since there is only one ACR available for a saltwater species,
and this one ACR is probably not sufficiently representative of all saltwater species, especially
when the freshwater ACRs suggest lower values possible for invertebrates, EPA calculated the
predicted GMCVs for pentachlorophenol in Table 2.2.5-2 using an FACR of 3.166 and the
following equation: Predicted GMCV = GMAV/FACR.

EPA compared the GMCVs for each species to Oregon's pentachlorophenol chronic criterion to
determine whether the chronic criterion will protect Oregon's aquatic life designated use.

63 See Footnote 64 above.

146

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Table 2.2.5-2: Genus Mean Chronic Values (SMCVs) for Pentachlorophenol

Genus

Species

Common name

GMAV

(Mg/L)

SMCV
(MS)"-)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(Mg/L)

Crangon

crangon

Common shrimp,
Sand shrimp

7800

2464

Monhystera

disjuncta

Nematode

2100

663.3

Crepidula

fornicata

Slipper limpet

1200

379.0

Penaeus

duorarum

Northern pink
shrimp

Penaeus

aztecus

Brown shrimp

>1045

>330.1

Americamysis

bahia

Opossum shrimp

298.4

(298.4)

Brachionus

plicatilis

Rotifer

900.0

284.3

Ophryotrocha

diadema

Polychaete

862.6

272.4

Arbacia

punctulata

Purple-spined sea
urchin

785.9

248.2

Platichthys

flesus

Starry, European
flounder

728.9

230.2

Monopylephorus

cuticulatus

Tubificid

598.2

189.0

Neanthes

succinea

Clam worm

Neanthes

arenaceodentata

Polychaete worm

>540.7

>170.8

Palaemonetes

pugio

Daggerblade grass
shrimp

491.3

155.2

Mulinia

lateralis

Clam

482.0

152.2

Solea

solea

Dover sole

450.0

142.1

Peloscolex

gabriellae

Oligochaete

423.4

133.7

Limnodriloides

verrucosus

Oligochaete worm

403.1

127.3

Gammarus

tigrinus

Scud

371.0

117.2

Ensis

minor

Jackknife clam

344.0

108.7

Mytilus

edulis

Common bay
mussel, Blue
musse"

328.8

103.9

Fundulus

similis

Longnose killifish

>306.0

>96.65

Mercenaria

mercenaria

Northern quahog or
Hard clam

<250.0

<78.96

Cyprinodon

variegatus

Sheepshead
minnow

64.31

Cyprinodon

bovinus

Leon Springs
pupfish

188.0

59.39
(64.31)

Temora

longicornis

Calanoid copepod

170.0

53.70

Laevicardium

mortoni

Morton's egg cockle

163.0

51.48

Mugil

cephalus

Striped mullet

112.1

35.41

Nitocra

spinipes

Harpacticoid
copepod

102.5

32.37

Corophium

acherusicum

Scud

82.00

25.90

Heteromastus

filiformis

Capitellid thread
worm

67.00

21.16

Pseudodiaptomus

coronatus*

Calanoid copepod

62.81

19.84

Haliotis

rufescens

Red abalone

56.02

17.69

Laaodon

rhomboides*

Pinfish

53.20

16.80

Crassostrea

virainica*

Eastern oyster

Crassostrea

gigas

Pacific oyster

41.68

13.17

CI u pea

pallasii

Pacific herring

25.29

7.988

See same notes as above under Table 2.2.5-1.

B. Evaluation of the Protectiveness of the Oregon Saltwater Chronic Criterion

147

-------
Following the review of the GMCV values in Table 2.2.5-2, all genera and species have values
greater than Oregon's chronic criterion for pentachlorophenol. Therefore, EPA concluded that
chronic effects are not expected to occur at concentrations equal to or lower than the criterion
and thus these genera, species, and Oregon's aquatc life designated use would be protected by
the criterion.

2.2.5.3 References for Pentachlorophenol

A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the acute and chronic tables, and are the source from which EPA
obtained SMAVs (acute table) and experimentally-derived SMCVs (chronic table).

Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in Tables 2.2.5-1 and 2.2.5-2)

Acute References

Vigers, G.A., J.B. Marliave, R.G. Janssen and P. Borgmann. 1978. Use of larval herring in bioassays. In: J.C.
Davis, G.L. Greer and I.K. Birtwell (Eds.), Proc. 4th Annual Aquatic Toxicol. Workshop, Nov. 8-10, 1977, Vancouver,
B.C., Can. Fish. Mar. Serv. Tech. Rep. No. 818: 31-52.

Woelke, C.E. 1972. Development of a Receiving Water Quality Bioassay Criterion Based on the 48-Hour Pacific
Oyster (Crassostrea gigas) Embryo. Wash. Dep. Fish. Tech. Rep. No. 9, Seattle, WA: 93p.

Office of Pesticide Programs. 2000. Pesticide Ecotoxicity Database (Formerly: Environmental Effects Database
(EEDB)). Environmental Fate and Effects Division, U.S. EPA, Washington, D.C.

Borthwick, P.W. and S.C. Schimmel. 1978. Toxicity of pentachlorphenol and related compounds to early life stages
of selected estuarine animals. In: K.R. Rao (Ed.), Pentachlorophenol: Chemistry, Pharmacology, and Environmental
Toxicology, Plenium Press, NY: 141-146/ EPA-600/J-78-076, Environ. Res. Lab., U.S. Environ. Prot. Agency, Gulf
Breeze, FL.

Schimmel, S.C., J.M. Patrick, Jr. and L.F. Faas. 1978. Effects of sodium pentachlorophenate on several estuarine
animals: Toxicity, uptake, and depuration. In: K.R. Rao (Ed.), Pentachlorophenol, Plenum Publ. Corp., New York,
NY: 147-155; EPA-600/J-78/078, U.S.EPA, Gulf Breeze, FL: 147-155 (U.S. NTIS PB-291127/9ST).

Hunt, J.W., B.S. Anderson, S. Tudor, M.D. Stephenson, H.M. Puckett, F.H. Palmer and M.W. Reeve. 1996. Marine
Bioassay Project. 8th Report: Refinement and Implementation of Four Effluent Toxicity Testing Methods Using
Indigenous Marine Species. Report #94-4. State Water Resources Control Board, Sacramento, CA. pp. 85-104.

Hauch, R.G., D.R. Norris and R.H. Pierce, Jr. 1980. Acute and chronic toxicity of sodium pentachlorophenate to the
copepod, Pseudodiaptomus coronatus. Bull. Environ. Contam. Toxicol.25(4): 562-568 / Fla. Sci. 43 (Suppl.1): 36
(ABS).

Tagatz, M.E. and R.S. Stanley. 1987. Sensitivity Comparisons of Estuarine Benthic Animals Exposed to Toxicants
in Single Species Acute Tests and Community Tests. EPA 600/X-87-167, U.S. EPA, Gulf Breeze, FL: 16.

Bengtsson, B.E. and B. Bergstrom. 1987. A flow through fecundity test with Nitocra spinipes (Harpacticoidea
Crustacea) for aquatic toxicity. Ecotoxicol. Environ. Saf. 14: 260-268.

Adema, D.M.M. and G.J. Vink. 1981. A comparative study of the toxicity of 1,1,2-trichloroethane, dieldrin,
pentacholorophenol, and 3,4 dichloroaniline for marine and fresh water. Chemosphere 10(6): 533-554 (OECDG
Data File).

Davis, H.C. and H. Hidu. 1969. Effects of pesticides on embryonic development of clams and oysters and on
survival and growth of the larvae. Fish. Bull. 67(2): 393-404.

Kierstead, W.G. and F. Barlocher. 1989. Ecological effects of pentachlorophenol on the brackish-water amphipod
Gammarus tigrinus. Arch. Hydrobiol. 115(1): 149-156.

Chapman, P.M., M.A. Farrell and R.O. Brinkhurst. 1982. Relative tolerances of selected aquatic oligochaetes to
combinations of pollutants and environmental factors. Aquat. Toxicol. 2(1): 69-78.

Rubinstein, N. 1981. Effect of PCP on Neanthes areaceodentata. Memorandum to S. Tagatz, U.S. EPA, Gulf
Breeze, FL.: 2p.

Parrish, P.R., E.E. Dyar, J.M. Enos and W.G. Wilson. 1978. Chronic toxicity of chlordane, trifluralin, and
pentachlorophenol to sheepshead minnows (Cyprinodon variegatus). EPA-600/3-78-010, U.S. EPA, Gulf Breeze,
FL: 53 p. (U.S. NTIS PB-278269).

148

-------
Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in Tables 2.2.5-1 and 2.2.5-2)

Smith, S., V.J. Furay, P.J. Layiwola and J.A. Menezes-Filho. 1994. Evaluation of the toxicity and quantitative
structure-activity relationships (QSAR) of chlorophenols to the copepodid stage of a marine copepod (Tisbe
battagiiai) and two species of benthic flatfish, the flounder (Piatichthys fiesus) and sole (So/ea solea). Chemosphere
28(4): 825-836.

Conklin, P.J. and K.R. Rao. 1978. Toxicity of sodium pentachlorophenate (NA-PCP) to the grass shrimp,
Paiaemonetes puqio, at different stages of the molt cycle. Bull. Environ. Contam. Toxicol. 20(2): 275-279.

Jackim, E. and D. Nacci. 1984. A rapid aquatic toxicity assay utilizing labeled thymidine incorporation in sea urchin
embryos. Environ. Toxicol. Chem. 3(4): 631-636.

Hooftman, R.N. and G.J. Vink. 1980. The determination of toxic effects of pollutants with the marine polychaete
worm Ophryotrocha diadema. Ecotoxicol. Environ. Saf. 4(3): 252-262.

Snell, T.W., B.D. Moffat, C. Janssen and G. Persoone. 1991. Acute toxicity tests using rotifers. III. Effects of
temperature, strain, and exposure time on the sensitivity of Brachionus piicatiiis. Environ. Toxicol. Water Qual. 6:
63-75.

Vranken, G., R. Vandergaeghen and C. Heip. 1991. Effects of pollutants on life-history parameters of the marine
nematode Monhystera disjuncta. ICES J Mar Sci 48: 325-334.

Bentley, R.E., T. Heitmuller, B.H. Sleight III and P.R. Parrish. 1975. Acute Toxicity of Pentachlorophenol to Bluegill
(.Lepomis macrochirus), Rainbow Trout (Saimo gairdneri), and Pink Shrimp (Penaeus duorarum). U.S. EPA, Criteria
Branch, WA-6-99-1414-B, Washington, D.C.: 13.

Chronic References

Parrish, P.R., E.E. Dyar, J.M. Enos and W.G. Wilson. 1978. Chronic Toxicity of Chlordane, Trifluralin, and
Pentachlorophenol to Sheepshead Minnows (Cyprinodon variegatus). EPA-600/3-78-010, U.S. EPA, Gulf Breeze,
FL: 53 p. (U.S. NTIS PB-278269).

Goodfellow, Jr., W.L. and W.J. Rue. 1989. Evaluation of a chronic estimation toxicity test using Mysidopsis bahia.
In: U.M. Cowgill and L.R. Williams (Eds.), Aquatic Toxicology and Hazard Assessment, 12th Volume, ASTM STP
1027, Philadelphia, PA: 333-344.

B. Studies That EPA Considered But Did Not Utilize In This Determination

1) For the studies that were not utilized, but the most representative SMAV/2 or most
representative SMCV fell below the criterion, or, if the studies were for a species
associated with one of the four most sensitive genera used to calculate the FAV in the
most recent national ambient water quality criteria dataset used to derive the CMC64,
EPA is providing a transparent rationale as to why they were not utilized (see below).

2) For the studies that were not utilized because they were not found to be pertinent to
this determination (including failing the QA/QC procedures listed in Appendix A)
upon initial review of the download from ECOTOX, EPA is providing the code that
identifies why EPA determined that the results of the study were not reliable (see
Appendix S).

64 U.S. EPA. 1986. Ambient Water Quality Criteria for Pentachlorophenol - 1986. EPA-440-5-86-009.

149

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2.2.6 SELENIUM

2.2.6.1 Evaluation of the Acute Saltwater Criterion Concentration for Selenium
A. Presentation of Toxicological Data

Oregon adopted a saltwater CMC of 290 |ig/L for selenium that is expressed in terms of the
dissolved concentration of the metal. This dissolved metal concentration is the same as the
saltwater acute criterion concentration recommended for use nationally by EPA for the
protection of aquatic life65. EPA developed the recommended criterion in accordance with the
1985 Guidelines pursuant to CWA section 304(a).

Table 2.2.6.1 provides available GMAVs based on available acute toxicity data for
pentachlorophenol to aquatic life from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Table 2.2.6.1. Species Mean Acute Values (SMAVs) and GMAVs for Selenium

Acute

References

Most
Representative
SMAV

GMAV

(used in the
calculation
of the

Genus

Species

Common name

(ng/L)

(H9/L)

SMAV)

Oncorhynchus

tshawytscha

Chinook salmon

65337

Oncorhynchus

kisutch

Coho salmon,silver salmon

26963

41972

Apeltes

quadracus

Fourspine stickleback

17315

Pseudopleuronectes

americanus

Winter flounder

14620

Crassostrea

gigas

Pacific oyster

9980

4,8

Mytilus

edulis

Common bay mussel,blue mussel

9980

Menidia

menidia

Atlantic silverside

9706

Cyprinodon

variegatus

Sheepshead minnow

7385

Callinectes

sapidus

Blue crab

4591

Lagodon

rhomboides

Pinfish

4391

Paralichthys

dentatus

Summer flounder

3490

Morone

saxatilis

Striped bass

3029

6,7

Americamysis

bahia

Opossum shrimp

1497

Acartia

clausi

Copepod

2106

Acartia

tonsa

Copepod

837.3

1328

Penaeus

aztecus

Brown shrimp

1198

Cancer

m agister

Dungeness or edible crab

1038

Melanogrammus

aeglefinus

Haddock

597.8

Argopecten

irradians

Bay scallop

254.5

65 See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.
The data which serve as the basis for the current nationally-recommended criteria are cited in:
U.S. EPA. 1987. Ambient Water Quality Criteria for Selenium - 1987. EPA-440-5-87-006.

150

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Note 1: Species that are bold and italicized indicate those associated with the four most sensitive genera used to derive the FAV in
the 1987 ALC document. Underlined species with an asterisk (*) indicate known or suspected Oregon non-resident species, and for
this evaluation, only those non-resident species below the criterion or related to the four most sensitive genera are identified as
such.

Note 2: The reporting of calculated values has been limited to a minimum of four significant figures for convenience and use in this
evaluation with the exception of very high values, which are reported as whole numbers - see text in section 2.3 of this evaluation for
an explanation of this decision, particularly for metals such as selenium which are expressed on a dissolved metal basis for a
comparison with the acute criterion concentration.

B. Evaluation of Protectiveness of the Oregon Saltwater Acute Criterion

Following review of GMAV and SMAV/2 values in Table 2.2.6.1, 18 of the 19 genera and test
species had values greater than Oregon's acute criterion concentration for selenium. Therefore,
EPA concluded that acute effects to these genera and species are not expected to occur at
concentrations equal to or lower than the criterion and thus these genera, species, and aquatic life
designted use would be protected.

When compared to Oregon's acute criterion concentration for selenium, the SMAV/2 value for a
single species (bay scallop, Argopecten irradians) was lower than the acute criterion
concentration of 290 |ig/L dissolved selenium. This species is not expected to reside in Oregon
waters.

2.2.6.2. Evaluation of the Chronic Saltwater Criterion Concentration for Selenium
A. Presentation of Toxicological Data

Oregon adopted a saltwater CCC of 71 |ig/L for selenium expressed as the dissolved metal
concentration in the water column. This concentration is the same as the saltwater chronic
criterion concentration recommended for use nationally by EPA for the protection of aquatic
life66 developed in accordance with the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.2.6.2 presents a compilation of the GMAVs from Table 2.2.6.1, any experimentally
determined SMCVs obtained from the criteria document, and estimated GMCVs based on the
GMAV/ACR. The 1987 criteria document for selenium67 reported an FACR of 8.314, which
EPA calculated as the geometric mean of five experimentally determined ACRs ranging from
6.880 for an acutely sensitive freshwater fish, fathead minnow (Pimephalespromelas) to 13.31
for an acutely sensitive invertebrate, the cladoceran Daphnia magna. EPA determined the
FACR of 8.314 with the ACRs from three freshwater species (Daphnia magna, Daphniapulex,
fathead minnow) and two saltwater species (Americamysis bahia and sheepshead minnow).

Since the geometric mean of the ACRs for the two saltwater species (8.812) was so similar to the
geometric mean of ACRs for all species (8.314), and since no additional acceptable ACRs are
available, EPA calculated the predicted GMCVs for selenium in Table 2.2.6.2 using the FACR
of 8.314 and the following equation: Predicted GMCV = GMAV/FACR.

66 See footnote 67 above.

67 U.S. EPA. 1987. Ambient Water Quality Criteria Document for Selenium-1987. EPA-440/5-87-006.

151

-------
EPA compared the GMCVs for each species to Oregon's selenium chronic criterion to determine
whether the chronic criterion will protect the species.

Table 2.2.6.2. Species Mean Chronic Values (SMCVs) for Selenium

Genus

Species

Common name

GMAV
(H9/L)

SMCV
(Hg/L)

(ex perim
en tally
derived)

Chronic
References

(used in the
calculation
of the
SMCV)

Most
Representati
ve GMCV
(Hg/L)

Oncorhynchus

tshawytscha

Chinook salmon

Oncorhynchus

kisutch

Coho salmon,silver
salmon

41972

5048

Apeltes

quadracus

Fourspine stickleback

17315

2083

Pseudopleuronect
es

americanus

Winter flounder

14620

1758

Crassostrea

gigas

Pacific oyster

9980

1200

Mytilus

edulis

Common bay
mussel,blue mussel

9980

1200

Menidia

menidia

Atlantic silverside

9706

1167

Cyprinodon

variegatus

Sheepshead minnow

7385

673.8

888.3
(673.8)

Callinectes

sapidus

Blue crab

4591

552.2

Lagodon

rhomboides

Pinfish

4391

528.2

Paralichthys

dentatus

Summer flounder

3490

419.8

Morone

saxatilis

Striped bass

3029

364.4

Americamysis

bahia

Opossum shrimp

1497

211.3

180.1
(211.3)

Acartia

clausi

Copepod

Acartia

tonsa

Copepod

1328

159.7

Penaeus

aztecus

Brown shrimp

1198

144.0

Cancer

magister

Dungeness or edible
crab

1038

124.8

Melanogrammus

aeglefinus

Haddock

597.8

71.90

Argopecten

irradians

Bay scallop

254.5

30.61

See same notes as above under Table 2.2.6.1.

B. Evaluation of the Protectiveness of the Oregon Saltwater Chronic Criterion

Following the review of the GMCV values in Table 2.2.6.2, 18 of the 19 genera have GMCVs
greater than Oregon's chronic criterion for selenium. Therefore, EPA concluded that chronic
effects are not expected to occur at concentrations equal to or lower than the criterion and thus
these species would be protected.

When compared to Oregon's chronic criterion concentration for selenium, the GMCV for a
single species (bay scallop, Argopecten irradians) was lower than the chronic criterion
concentration of 71 |ig/L dissolved selenium. This species is not expected to reside in Oregon
waters.

152

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2.2.6.3 References for Selenium

A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the acute and chronic tables, and are the source from which EPA
obtained GMAVs (acute table) and experimentally-derived SMCVs (chronic table).

Reference No.

Used Reference Citation (associated with reference numbers and provided above in tables 2.2.6.1 and
2.2.6.2)

Acute References

Cardin, J.A. 1986. Memorandum to D.J. Hansen, U.S. EPA, Narragansett, Rl.

Lussier, S.M. 1986. Memorandum to D.J. Hansen, U.S. EPA, Narragansett, Rl.

Glickstein, N. 1978. Acute toxicity of mercury and selenium to Crassostrea gigas embryos and Cancer magister
larvae. Mar. Biol. 49(2): 113-117.

Ward, G.S., T.A. Hollister, P.T. Heitmuller and P.R. Parrish. 1981. Acute and chronic toxicity of selenium to
estuarine organisms. Northeast Gulf Sci. 4(2):73-78.

Chapman, D.C. 1992. Failure of gas bladder inflation in striped bass: Effect on selenium toxicity. Arch. Environ.
Contam. Toxicol. 22: 296-299

Palawski, D., J.B. Hunn and F.J. Dwyer. 1985. Sensitivity of young striped bass to organic and inorganic
contaminants in fresh and saline waters. Trans. Am. Fish. Soc. 114: 748-753.

Martin, M., K.E. Osborn, P. Billig and N. Glickstein. 1981. Toxicities often metals to Crassostrea gigas and
Mytiius eduiis embryos and Cancer magister larvae. Mar. Pollut. Bull. 12(9): 305-308 (Author Communication
Used).

Hamilton, S.J. and K.J. Buhl. 1990. Acute toxicity of boron, molybdenum, and selenium to fry of Chinook
salmon and Coho salmon. Arch. Environ. Contam. Toxicol. 19(3): 366-373.

Chronic References

Ward, G.S., T.A. Hollister, P.T. Heitmuller and P.R. Parrish. 1981. Acute and chronic toxicity of selenium to
estuarine organisms. Northeast Gulf Sci. 4(2): 73-78.

B. Studies That EPA Considered But Did Not Utilize In This Determination

1) For the studies that were not utilized, but the most representative SMAV/2 or most
representative SMCV fell below the criterion, or, if the studies were for a species
associated with one of the four most sensitive genera used to calculate the FAV in the
most recent national ambient water quality criteria dataset used to derive the CMC68,
EPA is providing a transparent rationale as to why they were not utilized (see below).

68 U.S. EPA. 1987. Ambient Water Criteria for Selenium - 1987. EPA-440-5-87-006.

153

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2) For the studies that were not utilized because they were not found to be pertinent to
this determination (including failing the QA/QC procedures listed in Appendix A)
upon initial review of the download from ECOTOX, EPA is providing the code that
identifies why EPA determined that the results of the study were not reliable.

General QA/QC failure because non-resident species in Oregon

Tests with the following species were used in the EPA BE of OR WQS for selenium in saltwater,
but were not considered in the CWA review and approval/disapproval action of the standards
because these species do not have a breeding wild population in Oregon's waters:

Argopecten

irradians

Bay scallop

Nelson et al. 1988

Melanogrammus

aeglefinus

Haddock

Cardin 1986

Penaeus

aztecus

Brown shrimp

Ward et al. 1981

Other Acute tests failins QA/QC by species
Cancer magister - Dungeness or edible crab

Glickstein, N. 1978. Acute toxicity of mercury and selenium to Crassostrea gigas embryos
and Cancer magister larvae. Mar. Biol. 49(2): 113-117.

Two LC50s from this study were used in BE: the 48 and 96 h LC50. The 1987 ALC document,
however, only included the 96 h LC50, as per the recommendations in the Guidelines.

154

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2.2.7.1 Evaluation of the Acute Saltwater Criterion Concentration for Silver
A. Presentation of Toxicological Data

Oregon adopted a saltwater acute criterion concentration of 1.9 |ig/L for silver that is expressed
in terms of the dissolved concentration of the metal in the water column. This dissolved metal
concentration is the same as the saltwater CMC recommended for use nationally by EPA for the
protection of aquatic life69. EPA developed the recommended criterion in accordance with the
1985 Guidelines pursuant to CWA section 304(a).

Table 2.2.7-1 provides available SMAVs based on available acute toxicity data for silver to
aquatic life from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Table 2.2.7-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values
(GMAVs) for Silver

Acute

Most

References

Representative
SMAV

GMAV

(used in the
calculation of the

Genus

Species

Common name

(ng/L)

SMAV)

Cyprinodon

variegatus

Sheepshead minnow

924.4

Crangon

sp.

Caridean shrimp

712.3

Parophrys

vetulus

English sole

680.0

Scorpaenichthys

marmoratus

Cabezon

680.0

Oligocottus

maculosus

Tidepool sculpin

564.4

Apeltes

guadracus

4-spine stickleback

464.6

Oncorhynchus

kisutch

Coho salmon

414.4

Oncorhynchus

mykiss

Rainbow trout

341.3

376.1

Cymatogaster

aggregata

Shiner perch

302.3

Pleuronectes

americanus

Winter flounder

166.9

Americamysis

bahia

Opossum shrimp

166.7

12,15,16

Nereis

arenaceodentata

Polychaete worm

151.8

Menidia

menidia

Atlantic silverside

93.59

Cancer

magister

Dungeness or edible
crab

36.27

3,7

Fundulus

heteroclitus

Mummichog

34.00

Araooecten

irradians*

Bay scallop

28.05

Acartia

tonsa

Calanoid copepod

30.99

2,12

Acartia

clausi

Calanoid copepod

11.31

18.72

Mercenaria

mercenaria*

Northern quahog or
Hard clam

17.85

Paralichthvs

dentatus*

Summer Flounder

15.37

Crassostrea

gigas

Pacific oyster

14.07

3,7,8

Crassostrea

virainica*

Eastern oyster

12.03

13.01

4,5,6

Mytilus

edulis

Common bay mussel,
Blue mussel

11.90

Carcinus

maenas*

Green or Europeon
shore crab

5.400

69 See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.

The data which serve as the basis for the current nationally-recommended criteria are from the 1980 ALC document

as cited in: U.S. EPA. 1980. Ambient Water Quality Criteria Document for Silver. EPA-440/5-80-071.

155

-------
this evaluation, only those non-resident species below the criterion or related to the four most sensitive genera are identified as
such.

Note 2: The reporting of calculated values has been limited to a minimum of four significant figures for convenience and use in this
evaluation with the exception of very high values, which are reported as whole numbers - see text in section 2.2 of this evaluation for
an explanation of this decision, particularly for metals such as silver which are expressed on a dissolved metal basis for a
comparison with the acute criterion concentration.

B. Evaluation of Protectiveness of the Oregon Saltwater Acute Criterion

Following review of GMAV in Table 2.2.7-1, all tested genera and species have values greater
than Oregon's acute criterion concentration for silver. Further, all SMAV/2 values are greater
than the criterion. Therefore, EPA concluded that acute effects to these genera and species are
not expected to occur at concentrations equal to or lower than the criterion and thus these genera,
species, and aquatic life designted use would be protected.

2.2.7.2 References for Silver

A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the acute and chronic tables, and are the source from which EPA
obtained SMAVs (acute table) and experimentally-derived SMCVs (chronic table).

Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in Tables 2.2.7-1)

Acute References

Amiard, J.C. 1976. Experimental study on the acute toxicity of cobalt, antimony, strontium and silver salts in some
Crustacea and their larvae and some teleostei. Rev. Int. Oceanogr. Med. 43: 79-95 (Fre) (Eng Abs).

Lussier, S.M. and J.A. Cardin. 1985. Results of Acute Toxicity Tests Conducted with Silver at ERL, Narragansett.
U.S. EPA, Narragansett, Rl: 14 p.

Martin, M., K.E. Osborn, P. Billig and N. Glickstein. 1981. Toxicities often metals to Crassostrea gigas and
Mytiius eduiis embryos and Cancer magister larvae. Mar. Pollut. Bull. 12(9): 305-308 (Author Communication
Used).

Maclnnes, J.R. and A. Calabrese. 1978. Response of embryos of the American oyster, Crassostrea virginica, to
heavy metals at different temperatures. In: D.S. McLusky and A.J. Berry (Eds.), Physiology and Behaviour of
Marine Organisms, Permagon Press, New York, NY: 195-202.

Zaroogian, G.E. Interlaboratory Comparison - Acute Toxicity Tests Using the 48 hour Oyster Embryo-larval Assay.
U.S. EPA, Narragansett, Rl.

Calabrese, A., R.S. Collier, D.A. Nelson and J.R. Maclnnes. 1973. The toxicity of heavy metals to embryos of the
American oyster Crassostrea virginica. Mar. Biol. 18(3): 162-166.

Dinnel, P.A., Q.J. Stober, J.M. Link, M.W. Letourneau, W.E. Roberts, S.P. Felton and R.E. Nakatani. 1983.
Methodology and Validation of a Sperm Cell Toxicity Test for Testing Toxic Substances in Marine Waters. Final
Report, FRI-UW-8306, Fisheries Research Inst., School of Fisheries, University of Washington, Seattle, WA: 208.

Coglianese, M.P. and M. Martin. 1981. Individual and interactive effects of environmental stress on the embryonic
development of the Pacific oyster, Crassostrea gigas. Mar. Environ. Res. 5(1): 13-27

Cardin, J.A. 1980. Unpublished Laboratory Data. U.S. EPA, Narragansett, Rl: 9.

Calabrese, A. and D.A. Nelson. 1974. Inhibition of embryonic development of the hard clam, Mercenaria
mercenaria, by heavy metals. Bull. Environ. Contam. Toxicol. 11(1): 92-97.

Nelson, D.A., A. Calabrese, B.A. Nelson, J.R. Maclnnes and D.R. Wenzloff. 1976. Biological effects of heavy
metals on juvenile bay scallops, Argopecten irradians, in short-term exposures. Bull. Environ. Contam. Toxicol.
16(3): 275-282.

Schimmel, S.C. 1981. Results: Interlaboratory Comparison - Acute Toxicity Tests Using Estuarine Animals. Final
Draft, EPA 600/4-81-003, U.S. EPA, Gulf Breeze, FL: 13 p.

Jackim, E., J.M. Hamlin and S. Sonis. 1970. Effects of metal poisoning on five liver enzymes in the killifish
(Funduius heterociitus) (Auth. communication used). J. Fish. Res. Board Can. 27(2): 383-390.

Pesch, C.E. and G.L. Hoffman. 1983. Interlaboratory comparison of a 28-day toxicity test with the polychaete

156

-------
Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in Tables 2.2.7-1)

Neanthes arenaceodentata. In: W.E. Bishop, R.D. Cardwell and B.B. Heidolph (Eds.), Aquatic Toxicology and
Hazard Assessment, 6th Symposium, ASTM STP 802, Philadelphia, PA: 482-493.

Ward and Kramer. 2002. Silver speciation during chronic toxicity tests with the mysid, Americamysis bahia.
Comar. Biochem. Physiol. Toxicol. Pharmacol.: CBP 133(1-2): 75-86

Lussier, S.M., J.H. Gentile and J. Walker. 1985. Acute and chronic effects of heavy metals and cyanide on
Mysidopsis bahia (Crustacea: Mysidacea). Aquat. Toxicol. 7(1-2): 25-35.

Ferguson, E.A. and C. Hogstrand. 1998. Acute silver toxicity to seawater-acclimated rainbow trout: Influence of
salinity on toxicity and silver speciation. Environ. Toxicol. Chem. 17(4): 589-593.

Shaw, J.R., C.M. Wood, W.J. Birge and C. Hogstrand. 1998. Toxicity of silver to the marine teleost (Oiigocottus
maculosus): Effects of salinity and ammonia. Environ. Toxicol. Chem. 17(4): 594-600.

Dinnel, P.A., J.M. Link, Q.J. Stober, M.W. Letourneau and W.E. Roberts. 1989. Comparative sensitivity of sea
urchin sperm bioassays to metals and pesticides. Arch.Environ.Contam.Toxicol. 18(5): 748-755.

B. Studies That EPA Considered But Did Not Utilize In This Determination

most recent national ambient water quality criteria dataset used to derive the CMC ,
EPA is providing a transparent rationale as to why they were not utilized (see below).

2) For the studies that were not utilized because they were not found to be pertinent to
this determination (including failing the QA/QC procedures listed in Appendix A)
upon initial review of the download from ECOTOX, EPA is providing the code that
identifies why EPA determined that the results of the study were not reliable (see
Appendix T).

70 U.S. EPA. 1980. Ambient Water Quality Criteria Document for Silver. EPA-440/5-80-071.

157

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2.2.8 TRIBUTYLTIN

2.2.8.1 Evaluation of the Acute Saltwater Criterion Concentration for Tributyltin
A. Presentation of Toxicological Data

Oregon adopted a saltwater acute criterion concentration of 0.37 |ig/L for tributyltin. Oregon
adopted EPA's draft guidance acute criterion concentration which was issued in 2002, EPA's
final guidance acute criterion concentration for tributyltin was issued in December 2003. The
saltwater acute criterion concentration recommended for use nationally by EPA for the
protection of aquatic life71 is 0.42 ug/L. EPA developed the recommended criterion in
accordance with the 1985 Guidelines pursuant to CWA section 304(a).

Table 2.2.7-1 provides available GMAVs based on available acute toxicity data for tributyltin to
aquatic life from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Table 2.2.7-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values
(GMAVs) for Tributyltin

Most

Representative
SMAV

GMAV

Acute References

(used in the calculation

Genus

Species

Common name

(MS)"-)

(Mg/L)

of the SMAV)

Ostrea

edulis

European flat oyster

204.4

Rhepoxynius

abronius

Amphipod

108.0

Hemigrapsus

nudus

Shore crab

83.28

Nucella

laoillus*

Atlantic dogwhinkle

72.70

Rhithropanopeus

harrisii

Mud crab

34.90

Armandia

brevis

Polychaete

25.00

Fundulus

heteroclitus

Mummichog

21.24

4,21

Orchestia

traskiana

Amphipod

>14.60

Platichthys

stallatus

Starry flounder

10.10

Branchiostoma

caribaeum

Caribbean lancelet

<10.00

Carcinus

maenas

Shore crab

9.732

Eohaustorius

estuarius

Amphipod

10.00

Eohaustorius

washingtonianus

Amphipod

9.000

9.487

Cyprinodon

variegatus

Sheepshead minnow

9.037

4,15,16,17

Palaemonetes

pugio

Grass shrimp

20.00

Palaemonetes

sp.

Grass shrimp

4.070

9.022

Neanthes

arenaceodentata

Polychaete

6.812

Gammarus

sp.

Amphipod

5.300

Menidia

menidia

Atlantic silverside

8.900

Menidia

beryllina

Inland silverside

3.000

5.167

Brevoortia

tyrannus

Atlantic menhaden

4.944

Arenicola

cristata

Lugworm

4.740

Metamysidopsis

elongata

Mysid

3.183

Mytilus

edulis

Blue mussel

2.238

Eurytemora

affinis

Copepod

1.975

4,10

Nitocra

spinipes

Copepod

1.911

Homarus

americanus

American lobster

1.745

Americamysis

bahia

Mysid

1.692

71 See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.

The data which serve as the basis for the current nationally-recommended criteria are from the 2003 ALC document
as cited in: U.S. EPA. 2003. Ambient Water Quality Criteria for Tributyltin (TBT) - Final. EPA-882-R-03-031.

158

-------

Most

Representative
SMAV

GMAV

Acute References

(used in the calculation

Genus

Species

Common name

(MS)"-)

(Mg/L)

of the SMAV)

Mercenaria

mercenaria*

Hard clam

1.650

Oncorhynchus

tshawytscha

Chinook salmon

1.460

Acartia

tonsa

Copepod

1.100

Crassostrea

gigas

Pacific oyster

1.557

Crassostrea

virainica*

Eastern oyster

0.7100

1.051

2,3

Holmesimysis

sculpta

Mysid

0.6100

Note 1: Species that are bold and italicized indicate those associated with the four most sensitive genera used to derive the FAV in
the 2003 ALC document. Underlined species with an asterisk (*) indicate known or suspected Oregon non-resident species, and for
this evaluation, only those non-resident species below the criterion or related to the four most sensitive genera are identified as
such.

B. Evaluation of the Protectiveness of the Oregon Saltwater Acute Criterion

Following review of GMAV values in Table 2.2.7-1, all tested genera have values greater than
Oregon's acute criterion concentration for tributyltin. Therefore, EPA concluded that these
genera and the aquatic life designated use would be protected by the criterion.

When compared to Oregon's acute criterion concentration for tributyltin, SMAV/2 values for
two test species (the mysid shrimp Holmesimysis sculpta, and the Eastern oyster Crassostrea
virginica) were lower than the acute criterion concentration of 0.37 |ig/L tributyltin. Only the
mysid shrimp is expected to reside in Oregon waters. Therefore, EPA reviewed the data from the
study that made up the most representative SMAV for the species and compared the confidence
intervals of the SMAV value to determine whether the SMAV/2 value is quantitatively different
from the criterion value of 0.37 |ig/L.

The SMAV for Holmesimysis sculpta was based on a single LC50 of 0.6100 |ig/L. The 5 and 95
percent confidence intervals around the LC50 were not reported in the study. When divided by
two, the SMAV/2 for Holmesimysis sculpta was 0.3050 |ig/L. The Oregon acute criterion for
tributyltin is greater than the SMAV/2 for Holmesimysis sculpta. Therefore, EPA concludes that
the occurrence of ambient concentrations equal to or greater than the Oregon CMC for tributyltin
may result in some acute effects to individuals within this species. However, the aquatic life
designated use would be protected by the criterion.

2.2.8.2 Evaluation of the Chronic Saltwater Criterion Concentration for Tributyltin
A. Presentation of Toxicological Data

Oregon adopted a saltwater chronic criterion concentration of 0.01 |ig/L for tributyltin. Oregon
adopted EPA's draft guidance chronic criterion concentration which was issued in 2002, EPA's
final guidance chronic criterion concentration was issued in December 2003. The saltwater
chronic criterion concentration recommended for use nationally by EPA for the protection of

159

-------
72

aquatic life . EPA developed the recommended criterion in accordance with the 1985
Guidelines pursuant to CWA section 304(a) which is 0.0074 |ig/L for tributyltin. The difference
between the 0.01 ug/L adopted value and the 0.0074 ug/L final value is negligible and orders of
magnitude below detection of environmental concentrations of this chemical and is of no
concern to EPA.

Table 2.2.7-2 presents a compilation of the SMAVs from Table 2.2.7-1, any experimentally
determined SMCVs obtained from the criteria document and EPA ECOTOX download used for
the BE, and estimated GMCVs based on the GMAV/ACR. The 2003 criteria document for
tributyltin reported an FACR of 12.69, which EPA calculated as the geometric mean of four
experimentally determined ACRs ranging from 4.7 for an acutely sensitive saltwater
invertebrate, the mysid (Acanthomysis sculpta, identified in this evaluation as Holmesimysis
sculpta) to 36.6 for an acutely sensitive invertebrate, Daphnia magna. The FACR of 12.69
included ACRs from two freshwater species (Daphnia magna and Pimephalespromelas) and
two saltwater species (Holmesimysis sculpta andEurytemora affinis). Since no additional
acceptable ACRs are available, EPA calculated the predicted GMCVs for tributyltin in Table
2.2.7-2 using the FACR of 12.69 and the following equation: Predicted GMCV = GMAV/FACR.

EPA compared the GMCVs for each species to Oregon's tributyltin chronic criterion to
determine whether the chronic criterion will protect Oregon's aquatic life designated use.

Table 2.2.7-2: Genus Mean Chronic Values (GMCVs) for Tributy

Genus

Species

Common name

GMAV
(MS)"-)

SMCV
(MS)"-)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(Mg/L)

Ostrea

edulis

European flat
oyster

204.4

16.11

Rhepoxynius

abronius

Amphipod

108.0

8.511

Hemigrapsus

nudus

Shore crab

83.28

6.563

Nucella

lapillus*

Atlantic
dogwhinkle

72.70

0.01430

5.729
(0.01430)

Rhithropanopeus

harrisii

Mud crab

34.90

2.750

Armandia

brevis

Polychaete

25.00

1.970

Fundulus

heteroclitus

Mummichog

21.24

1.674

Orchestia

traskiana

Amphipod

>14.60

>1.151

Platichthys

stallatus

Starry flounder

10.10

0.7959

Branchiostoma

caribaeum

Caribbean
lancelet

<10.00

<0.7880

Carcinus

maenas

Shore crab

9.732

0.7669

Eohaustorius

estuarius

Amphipod

Eohaustorius

washingtonianus

Amphipod

9.487

0.7476

Cyprinodon

variegatus

Sheepshead
minnow

9.037

0.7121

Palaemonetes

pugio

Grass shrimp

Palaemonetes

sp.

Grass shrimp

9.022

0.7110

Neanthes

arenaceodentata

Polychaete

6.812

0.5368

Gammarus

sp.

Amphipod

5.300

0.4177

Menidia

menidia

Atlantic silverside

Menidia

beryllina

Inland silverside

5.167

0.4072

Brevoortia

tyrannus

Atlantic

4.944

0.3896

tin

72 See Footnote 73 above.

160

-------
Genus

Species

Common name

GMAV
(MS)"-)

SMCV
(MS)"-)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(Mg/L)

menhaden

Arenicola

cristata

Lugworm

4.740

0.3735

Metamysidopsis

elongata

Mysid

3.183

0.2508

Mytilus

edulis

Blue mussel

2.238

0.1764

Eurytemora

affinis

Copepod

1.975

<0.1130

0.1556
(<0.1130)

Nitocra

spinipes

Copepod

1.911

0.1506

Homarus

americanus

American lobster

1.745

0.1375

Americamysis

bahia

Mysid

1.692

0.1333

Mercenaria

mercenaria*

Hard clam

1.650

0.1300

Oncorhynchus

tshawytscha

Chinook salmon

1.460

0.1151

Acartia

tonsa

Copepod

1.100

0.08668

Crassostrea

gigas

Pacific oyster

Crassostrea

virainica*

Eastern oyster

1.051

0.08285

Holmesimysis

sculpta

Mysid

0.6100

0.1308

3, 4

0.04807
(0.1308)

See same notes as above under Table 2.2.7-1.

B. Evaluation of the Protectiveness of the Oregon Saltwater Chronic Criterion

Following the review of the GMCV values in Table 2.2.7-2, all tested genera and species have
values greater than Oregon's chronic criterion for tributyltin. It should be noted that the saltwater
criterion for tributyltin was derived from field studies on gastropods including the uptake and
bioaccumulation properties of the metal. This evaluation found no data to indicate that Oregon's
adopted criteria, and by extension, the 304(a) nationally recommended value were not protective
of any speces. Therefore, EPA concluded that chronic effects are not expected to occur at
concentrations equal to or lower than the criterion and thus these species and the aquatic life
designated use would be protected by the criterion.

2.2.8.3 References for Tributyltin

A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the acute and chronic tables, and are the source from which EPA
obtained SMAVs (acute table) and experimentally-derived SMCVs (chronic table).

Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in Tables 2.2.7-1 and 2.2.7-2)

Acute References

Valkirs, A.O., B.M. Davidson and P.F. Seligman. 1985. Sublethal Growth Effects and Mortality to Marine Bivalves
and Fish from Long-term Exposure to Tributyltin. NOSC-TR-1042 or AD-A162-629-0. National Technical Information
Service, Springfield, VA.

Office of Pesticide Programs. 2000. Pesticide Ecotoxicity Database (Formerly: Environmental Effects Database
(EEDB)). Environmental Fate and Effects Division, U.S. EPA, Washington, D.C.

Roberts, M.H.J. 1987. Acute toxicity of tributyltin chloride to embryos and larvae of two bivalve mollusks,
Crassostrea virginica and Mercenaria mercenaria. Bull. Environ. Contam. Toxicol. 39: 1012-1019.

161

-------
Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in Tables 2.2.7-1 and 2.2.7-2)

Bushong, S.J., L.W. Hall, Jr., W.S. Hall, W.E. Johnson and R.L. Herman. 1988. Acute toxicity of tributyltin to
selected Chesapeake Bay fish and invertebrates. Water Res. 22(8): 1027-1032.

Short, J.W. and F.P. Thrower. 1987. Toxicity of tri-n-butyl-tin to Chinook salmon, Oncorhynchus tshawytscha,
adapted to seawater. Aquaculture 61(3-4): 193-200.

Thain, J.E. 1983. The Acute Toxicity of Bis(tributyltin) Oxide to the Adults and Larvae of Some Marine Organisms.
Int. Counc. Explor. Sea, Mariculture Committee E: 13. 5 pp.

Goodman, L.R., G.M. Cripe, P.H. Moody and D.G. Halsell. 1988. Acute toxicity of malathion, tetrabromobisphenol-a,
and tributyltin chloride to mysids (Mysidopsis bahia) of three ages. Bull. Environ. Contam. Toxicol. 41(5):746-753.

Laughlin, R.B.J, and W.J. French. 1980. Comparative study of the acute toxicity of a homologous series of
trialkyltins to larval shore crabs Hemigrapsus nudus, and lobster, Homarus americanus. Bull. Environ. Contam.
Toxicol. 25(5): 802-809.

Linden, E., B.E. Bengtsson, O. Svanberg and G. Sundstrom. 1979. The acute toxicity of 78 chemicals and pesticide
formulations against two brackish water organisms, the bleak (Aiburnus aiburnus) and the harpacticoid.
Chemosphere 8(11/12): 843-851 (Author Communication Used) (OECDG Data File).

Hall, L.W., Jr., S.J. Bushong, W.S. Hall and W.E. Johnson. 1988. Acute and chronic effects of tributyltin on a
Chesapeake Bay copepod. Environ. Toxicol. Chem. 7: 41-46.

Salazar, M.H. and S.M. Salazar. 1989. Acute Effects of (bis)Tributyltin Oxide on Marine Organisms. Tech. Rep. No.
1299, Naval Ocean Systems Center, San Diego, CA: 87 p. (U.S. NTIS AD-A214005).

Khan, A.T., J.S. Weis, C.E. Saharig and A.E. Polo. 1993. Effect of tributyltin on mortality and telson regeneration of
grass shrimp, Paiaemonetes puqio. Bull. Environ. Contam. Toxicol. 50(1): 152-157.

Walsh, G.E., M.K. Louie, L.L. McLaughlin and E.M. Lores. 1986. Lugworm (Arenicoia cristata) larvae in toxicity tests:
Survival and development when exposed to organotins. Environ. Toxicol. Chem. 5: 749-754.

Meador, J. P. 1997. Comparative toxicokinetics of tributyltin in five marine species and its utility in predicting
bioaccumulation and acute toxicity. Aquat. Toxicol. 37: 307-326.

EG&G Bionomics. 1979. Acute Toxicity of Three Samples of TBTO (Tributyltin Oxide) to Juvenile Sheepshead
Minnows (Cyprinodon variegatus). Report L14-500to M&T Chemicals Inc., Rahway, NJ.

EG&G Bionomics. 1981. Unpublished Laboratory Data on Acute Toxicity of Tributyltin to Sheepshead Minnow,
Cyprinodon variegatus. Pensacola, FL.

Walker, W.W. 1989a. Acute Toxicity of Bis(tributyltin)oxide to the Sheepshead Minnow in a Flow-through System.
Final Report to M&T Chemicals, Inc. and Sherex Chemical Co., Inc. 94 pp.

Clark, J.R., J.M. Patrick, Jr., J.C. Moore and E.M. Lores. 1987. Waterborne and sediment-source toxicities of six
organic chemicals to grass shrimp (Paiaemonetes pugio) and amphioxus (Branchiostoma caribaeum). Arch. Environ.
Contam. Toxicol. 16: 401-407.

Meador, J.P. 1993. The effect of laboratory holding on the toxicity response of marine infaunal amphipods to
cadmium and tributyltin. J. Exp. Mar. Biol. Ecol. 174: 227-242.

Laughlin, R.B., O. Linden and H.E. Guard. 1982. Acute Toxicity of Tributyltins and Tributyltin Leachates from Marine
Antibiofouling Paints. Office of Naval Research, Arlington, VA: 26 p. (U.S. NTIS AD-A184224).

Pinkney, A.E., D.A. Wright and G.M. Hughes. 1989. A morphometric study of the effects of tributyltin compounds on
the gills of the mummichog, Fundulus heteroclitus. J. Fish Biol. 34(5): 665-677.

Laughlin, R., W. French and H.E. Guard. 1983. Acute and sublethal toxicity of tributyltin oxide (TBTO) and its
putative environmental product, tributyltin sulfide (TBTS) to zoeal mud crabs, Rhithropanopeus harrisii. Water Air Soil
Pollut. 20(1): 69-79.

Harding, M.J.C., S.K. Bailey and I.M. Davies. 1996. Effects of TBT on the Reproductive Success of the Dogwhelk
Nucella lapillus. Napier University of Edinburgh and The Scottish Office of Agriculture, Environment and Fisheries
Department, Aberdeen, Scotland. 75 pp.

Chronic References

Hall, L.W., Jr., S.J. Bushong, W.S. Hall and W.E. Johnson. 1988. Acute and chronic effects of tributyltin on a
Chesapeake Bay copepod. Environ. Toxicol. Chem. 7: 41-46.

Davidson, B.M., A.O. Valkirs and P.F. Seligman. 1986a. Acute and Chronic Effects of Tributyltin on the Mysid
Acanthomysis sculpta (Crustacea, Mysidacea). NOSC-TR-1116 or AD-A175-294-8. National Technical Information
Service, Springfield, VA.

Davidson, B.M., A.O. Valkirs and P.F. Seligman. 1986b. Acute and Chronic Effects of Tributyltin on the Mysid
Acanthomysis sculpta (Crustacea, Mysidacea). In: Oceans 86, Vol. 4. Proceeding International Organotin
Symposium. Marine Technology Society, Washington, DC. pp. 1219-1225.

B. Studies That EPA Considered But Did Not Utilize In This Determination

162

most recent national ambient water quality criteria dataset used to derive the CMC ,
EPA is providing a transparent rationale as to why they were not utilized (see below).

2) For the studies that were not utilized because they were not found to be pertinent to
this determination (including failing the QA/QC procedures listed in Appendix A)
upon initial review of the download from ECOTOX, EPA is providing the code that
identifies why EPA determined that the results of the study were not reliable (see
Appendix U).

73 U.S. EPA. 2003. Ambient Water Quality Criteria for Tributyltin (TBT) - Final. EPA-882-R-03-031.

163

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2.2.9 ZINC

2.2.9.1 Evaluation of the Acute Saltwater Criterion Concentration for Zinc
A. Presentation of Toxicological Data

Oregon adopted a saltwater acute criterion concentration of 90 |ig/L for zinc that is expressed in
terms of the dissolved concentration of the metal. This dissolved metal concentration is the same
as the saltwater CMC recommended for use nationally by EPA for the protection of aquatic
life74. EPA developed the recommended criterion in accordance with the Guidelines pursuant to
CWA section 304(a).

Table 2.2.8-1 provides available SMAVs based on available acute toxicity data for zinc to
aquatic life from the criteria document and from EPA's ECOTOX database
(http://cfpub.epa.gov/ecotox/) subsequently used to support the BE.

Table 2.2.8-1: Species Mean Acute Values (SMAVs) and Genus Mean Acute Values
(GMAVs) for Zinc

Acute

Most

References

Representative
SMAV

GMAV

(used in the
calculation of the

Genus

Species

Common name

(Mg/L)

SMAV)

Macoma

balthica

Balthica macoma or clam

303098

Rivulus

marmoratus

Rivulus

137311

Eurythoe

complanata

Fireworm

132062

Fundulus

heteroclitus

Mummichog

122507

Nassarius

obsoletus

Eastern mud snail

47300

Asterias

forbesii

Common starfish

36894

Leiostomus

xanthurus

Spot

35948

Portunus

pelagicus

Crab

15005

Nereis

diversicolor

Polychaete worm

16990

42,43

Nereis

virens

Polychaete worm

7663

11410

Pseudopleuronectes

americanus

Winter flounder

8955

Menidia

beryllina

Inland silverside

19866

Menidia

peninsulae

Tidewater silverside

5298

Menidia

menidia

Atlantic silverside

3444

7130

Mya

arenaria

Soft-shell clam

5986

18,40

Corophium

volutator

Scud

4430

Cyprinodon

variegatus

Sheepshead minnow

4146

36,37

Eurytemora

affinis

Calanoid copepod

3854

Pectinaria

californiensis

Cone worm

2649

Capitella

capitata

Polychaete worm

2327

26,27

Ctenodrilus

serratus

Polychaete worm

2285

28,33

Argopecten

irradians

Bay scallop

2129

Allorchestes

compressa

Scud, Amphipod

1892

Loligo

opalescens

California market squid

>1816

1816

9,12

Monhystera

disjuncta

Nematode

1797

Nitocra

spinipes

Harpacticoid copepod

1785

28,29

Pseudodiaptomus

coronatus

Calanoid copepod

1687

See U.S. EPA. 2004. National Recommended Water Quality Criteria. EPA-822-H-04-001.

The data which serve as the basis for the current nationally-recommended criteria are cited in: U.S. EPA. 1987. Ambient Water Quality Criteria
for Zinc- 1987. EPA-440-5-87-003.

164

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Genus

Species

Common name

Most
Representative
SMAV

(Mg/L)

GMAV

(Mg/L)

Acute
References

(used in the
calculation of the
SMAV)

Ophryotrocha

labronica

Polychaete

1703

Ophryotrocha

diadema

Polychaete

1324

1502

Neanthes

arenaceodentata

Polychaete worm

1272

26,27

Penaeus

duorarum

Northern pink shrimp

993.3

Metapenaeus

dobsoni

Kadal shrimp

955.4

Carcinus

maenas

Green or Europeon shore
crab

946.0

Mytilus

edulis
(planulatus)

Common bay
mussel,blue mussel

3722

Mytilus

galloprovincialis

Mediterranean mussel

137.2

714.5

Acartia

clausi

Calanoid copepod

1132

16,25

Acartia

tonsa

Calanoid copepod

278.3

561.3

Cancer

m agister

Dungeness or edible crab

554.5

Americamysis

bigelowi

Shrimp

559.4

Americamysis

bahia

Opossum shrimp

472.1

513.9

Morone

saxatilis

Striped bass

406.8

Pagurus

longicarpus

Longwrist hermit crab

378.4

Homarus

americanus

American lobster

360.0

Crassostrea

virainica*

Eastern oyster

248.3

14,15

Crassostrea

gigas

Pacific oyster

179.5

211.1

8,9,10,11

Mercenaria

mercertaria*

Northern quahog or
hard clam

184.5

Scorpaenichthys

marmoratus

Cabezon

181.1

Nanosesarma

sp.*

Crab

118.3

Acanthomysis

costata

Mysid

91.02

4, 5

Haliotis

rufescens

Red abalone

50.95

1,2,3,4

Note 1: Species that are bold and italicized indicate those associated with the four most sensitive genera used to derive the FAV in
the 1987 ALC document. Underlined species with an asterisk (*) indicate known or suspected Oregon non-resident species, and for
this evaluation, only those non-resident species below the criterion or related to the four most sensitive genera are identified as
such.

Note 2: The reporting of calculated values has been limited to a minimum of four significant figures for convenience and use in this
evaluation with the exception of very high values, which are reported as whole numbers - see text in section 2.2 of this evaluation for
an explanation of this decision, particularly for metals such as zinc which are expressed on a dissolved metal basis for a comparison
with the acute criterion concentration.

B. Evaluation of Protectiveness of the Oregon Saltwater Acute Criterion

Following review of GMAV values in Table 2.2.8-1, 39 of the 42 genera have values greater
than Oregon's acute criterion concentration for zinc. Therefore, EPA concluded that acute effects
to these genera are not expected to occur at concentrations equal to or lower than the criterion
such that these nearly all genera would be protected, and thus the aquatic life designated use
would be protected.

When compared to Oregon's acute criterion concentration for zinc, SMAV/2 values for five test
species: three mollusks (Haliotis rufescens, Mytilus galloprovincialis, and Crassostrea gigas)
and two crustaceans (Acanthomysis costata and Nanosesarma sp.) were lower than the acute
criterion concentration of 90 |ig/L dissolved zinc. All but one of these species (Nanosesarma sp.)
resides in Oregon waters. Therefore, EPA reviewed the data from the studies that make up the
most representative SMAV for the four resident species and compared the SMAV for these
species to determine whether the SMAV/2 values are quantitatively different from the criterion
value of 90 |ig/L.

165

-------
The SMAV for Haliotis rufescens based on dissolved zinc was 50.95 |ig/L, and the SMAV for
the subset of studies with reported confidence intervals was 50.80 |ig/L (text box A -H.
rufescens acute). The SMAV/2 was 25.48 |ig/L.

The SMAV for Acanthomysis costata based on dissolved zinc was 91.02 |ig/L, and the SMAV
for the subset of studies with reported confidence intervals was 107.4 |ig/L (text box B - A.
costata acute). The SMAV/2 was 53.72 |ig/L.

The SMAV for Mytilus galloprovincialis was based on a single LC50 of 137.2 |ig/L dissolved
zinc. The 5 and 95 percent confidence intervals were not reported for the test. The SMAV/2 for
M galloprovincialis was 68.59 |ig/L.

The SMAV for Crassostrea gigas based on dissolved zinc was 179.5 |ig/L, and the SMAV for
the subset of studies with reported confidence intervals was 176.3 |ig/L, with 5 and 95 percent
confidence intervals of 139.5 |ig/L and 219.3 |ig/L, respectively (text box C - C. gigas acute).
The SMAV/2 is 89.75 |ig/L.

Because the Oregon acute criterion for zinc is greater than the SMAV/2 for Haliotis
rufescens Acanthomysis costata, and Mytilus galloprovincialis, EPA concludes that the
occurrence of ambient concentrations equal to or greater than the Oregon CMC for zinc may
result in mortality to some individuals within these speciesFor Crassostrea gigas, Because the
Oregon acute criterion for zinc is approximately equal to the SMAV/2, a value estimated to
represent acute effect levels indistinguishable from control levels, EPA concludes that the
Oregon CMC for zinc is sufficiently protective of this species.

Saltwater zinc acute criterion comparison

Text Box A (acute) - Basis for the meta analysis comparing the SMAV/2 for the red abalone
(Haliotis rufescens) to the acute criterion for zinc (90 |ig/L dissolved metal concentration).

Haliotis rufescens

Reported Values

LC50 5% CI

95% CI

Dissolved Normalized Values

LC50 5% CI 95% CI

Dissolved Normalized Values/2

LC50/2

CMC

40.00

39.40

41.00

37.84

37.27

38.79

18.92

55.00

52.03

26.02

76.00

68.60

83.10

71.90

64.90

78.61

35.95

64.00

56.60

71.40

60.54

53.54

67.54

30.27

64.00

58.90

69.10

60.54

55.72

65.37

30.27

47.00

41.30

52.70

44.46

39.07

49.85

22.23

44.00

38.50

49.50

41.62

36.42

46.83

20.81

50.00

45.60

54.40

47.30

43.14

51.46

23.65

Geomean
(all)

Geomean
(CI Only)

53.86
53.70

48.74

58.64

SMAV

50.95
50.80

46.11

55.48

SMAV/2

25.48
25.40

166

-------
Text Box B (acute) - Basis for the meta analysis comparing the SMAV/2 for the mysid shrimp
(Acanthomysis costatd) to the acute criterion for zinc (90 |ig/L dissolved metal concentration).

Acanthomysis costata

Reported Values

LC50 5% CI

95% CI

Dissolved Normalized Values

LC50 5% CI 95% CI

Dissolved Normalized Values/2

LC50/2

CMC

80.70

76.34

38.17

88.40

83.63

41.81

73.20

69.25

34.62

70.20

66.41

33.20

93.60

88.55

44.27

78.80

74.54

37.27

88.40

83.63

41.81

89.00

77.00

101.00

84.19

72.84

95.55

42.10

138.0

122.0

152.0

130.5

115.41

143.79

65.27

87.00

75.00

100.00

82.30

70.95

94.60

41.15

81.00

73.00

91.00

76.63

69.06

86.09

38.31

212.0

177.0

260.0

200.6

167.4

246.0

100.3

151.0

138.0

167.0

142.8

130.55

157.98

71.42

88.00

77.00

101.00

83.25

72.84

95.55

41.62

Geomean
(all)

Geomean
(CI only)

96.22
113.6

99.53

129.6

SMAV

91.02
107.4

94.15

122.6

SMAV/2

45.51
53.72

Text Box C (acute) - Basis for the meta analysis comparing the SMAV/2 for the Pacific oyster
(Crassostrea gigas) to the acute criterion for zinc (90 |ig/L dissolved metal concentration).

Crassotrea gigas
LC50

Reported Values

5% CI 95% CI

Dissolved Normalized Values

LC50 5% CI 95% CI

Dissolved Normalized Values/2

LC50/2

CMC

200.0

189.2

94.60

206.5

160.0

280.0

195.3

151.4

264.9

97.67

263.5

187.2

339.8

249.3

177.1

321.4

124.64

119.0

107.0

131.0

112.6

101.2

123.9

56.29

Geomean
(all)

Geomean
(CI only)

189.7
186.4

147.4

231.9

SMAV

179.5
176.3

139.5

219.3

SMAV/2

89.75
88.15

2.2.9.2 Evaluation of the Chronic Saltwater Criterion Concentration for Zinc
A. Presentation of Toxicological Data

Oregon adopted a saltwater chronic criterion concentration of 81 |ig/L for zinc expressed as the
dissolved metal concentration in the water column. This concentration is the same as the

saltwater CCC recommended for use nationally by EPA for the protection of aquatic life . EPA

75 See footnote 76 above.

167

-------
developed the recommended criterion in accordance with the 1985 Guidelines pursuant to CWA
section 304(a).

Table 2.2.8-2 presents a compilation of the GMAVs from Table 2.2.8-1, any experimentally
determined SMCVs obtained from the criteria document and EPA ECOTOX download used for
the BE, and estimated GMCVs based on the GMAV/ACR. The 1987 criteria document for zinc76
reported an FACR of 2.208. Because of the large range in ACRs (0.7027 to 41.20) and trend of
lower ACRs for the most acutely sensitive species, EPA determined that only the
experimentally-determined ACRs for the freshwater Daphnia magna, chinook salmon, and
rainbow trout, and the saltwater opossum shrimp, Americamysis bahia, were the most
appropriate ACRs to protect sensitive species in general. Since no additional acceptable ACRs
are available, EPA calculated the predicted GMCVs for zinc in Table 2.2.8-2 using an ACR of
2.208 and the following equation: Predicted GMCV = GMAV/FACR.

EPA compared the SMCVs for each species to Oregon's zinc chronic criterion to determine
whether the chronic criterion will protect Oregon's aquatic life designated use.

Table 2.2.8-2: Genus Mean Chronic Values (GMCVs) for Zinc

Genus

Species

Common name

GMAV
(ng/L)

SMCV
(MS)"-)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV
(M9/L)

Macoma

balthica

Balthica macoma or
clam

303098

137273

Rivulus

marmoratus

Rivulus

137311

62188

Eurythoe

complanata

Fireworm

132062

59811

Fundulus

heteroclitus

Mummichog

122507

55483

Nassarius

obsoletus

Eastern mud snail

47300

21422

Asterias

forbesii

Common starfish

36894

16709

Leiostomus

xanthurus

Spot

35948

16281

Portunus

pelagicus

Crab

15005

6796

Nereis

diversicolor

Polychaete worm

Nereis

virens

Polychaete worm

11410

5168

Pseudopleuronectes

americanus

Winter flounder

8955

4056

Menidia

beryllina

Inland silverside

Menidia

peninsulae

Tidewater silverside

Menidia

menidia

Atlantic silverside

7130

3229

Mya

arenaria

Soft-shell clam

5986

2711

Corophium

volutator

Scud

4430

2007

Cyprinodon

variegatus

Sheepshead
minnow

4146

1878

Eurytemora

affinis

Calanoid copepod

3854

1745

Pectinaria

californiensis

Cone worm

2649

1200

Capitella

capitata

Polychaete worm

2327

1054

Ctenodrilus

serratus

Polychaete worm

2285

1035

Argopecten

irradians

Bay scallop

2129

964.0

Allorchestes

compressa

Scud, Amphipod

1892

856.9

Loligo

opalescens

California market

1816

822.6

Monhystera

disjuncta

Nematode

1797

814.0

Nitocra

spinipes

Harpacticoid
copepod

1785

808.3

76 U.S. EPA. 1987. Ambient Water Criteria for Zinc - 1987. EPA-440-5-87-003.

168

-------
Genus

Species

Common name

GMAV
(MS)"-)

SMCV
(MS)"-)

('experimentally
derived}

Chronic
References

(used in the
calculation of
the SMCV)

Predicted
GMCV

(Mg/L)

Pseudodiaptomus

coronatus

Calanoid copepod

1687

763.9

Ophryotrocha

labronica

Polychaete

Ophryotrocha

diadema

Polychaete

1502

680.1

Neanthes

arenaceodentata

Polychaete worm

1272

576.0

Penaeus

duorarum

Northern pink
shrimp

993.3

449.9

Metapenaeus

dobsoni

Kadal shrimp

955.4

432.7

Carcinus

maenas

Green or Europeon
shore crab

946.0

428.4

Mytilus

edulis
(planulatus)

Common bay
mussel, blue mussel

Mytilus

galloprovincialis

Mediterranean
mussel

714.5

323.6

Acartia

clausi

Calanoid copepod

Acartia

tonsa

Calanoid copepod

561.3

254.2

Cancer

m agister

Dungeness or edible
crab

554.5

251.1

Americamysis

bigelowi

Shrimp

Americamysis

bahia

Opossum shrimp

513.9

157.5

232.7
(157.5)

Morone

saxatilis

Striped bass

406.8

184.2

Pagurus

longicarpus

Longwrist hermit
crab

378.4

171.4

Homarus

americanus

American lobster

360.0

163.0

Crassostrea

virainica*

Eastern oyster

Crassostrea

gigas

Pacific oyster

211.1

95.62

Mercenaria

mercenaria*

Northern quahog
or hard clam

184.5

83.55

Scorpaenichthys

marmoratus

Cabezon

181.1

82.00

Nanosesarma

sp.*

Crab

118.3

53.56

Acanthomysis

costata

Mysid

91.02

63.46

41.22
(63.46)

Haliotis

rufescens

Red abalone

50.95

23.08

See same notes as above under Table 2.2.8-1.

B. Evaluation of the Protectiveness of the Oregon Saltwater Chronic Criterion

Following the review of the SMCV values in Table 2.2.8-2, 39 of 42 genera, all but a small
proportion of genera, have values greater than Oregon's chronic criterion for zinc. Therefore,
EPA concluded that chronic effects to these genra are not expected to occur at concentrations
equal to or lower than the criterion and thus these genera and the aquatic life designated use
would be protected.

When compared to Oregon's chronic criterion concentration for zinc, SMCVs for four of the five
test species noted above (Haliotis rufescens, Mytilus galloprovincialis, Acanthomysis costata and
Nanosesarma sp.) were lower than the chronic criterion concentration of 81 |ig/L dissolved zinc.
All but one of these species (Nanosesarma sp.) is expected to reside in Oregon waters.

Therefore, EPA reviewed the data from the studies that make up the most representative SMCVs
for each of those species resident in Oregon waters and, depending on whether the SMCV was
estimated based on the use of the ACR or experimentally determined based on NOEC and
LOECs, compared the confidence intervals (ACR approach) or LOEC values surrounding these

169

-------
SMCVs to determine whether the SMCV values were quantitatively different from the chronic
criterion value for zinc of 81 |ig/L.

The SMCV for H. rufescens was estimated by applying the ACR of 2.208 described above to the
SMAV. The final SMCV was 23.01 (text box D -H. rufescens chronic).

The SMCV for Acanthomysis costata was calculated as the geometric mean of the measured
LOEC and NOEC for two replicate tests in Anderson et al. (1988). The final dissolved SMCV is
63.46 |ig/L (text box E -A. costata chronic).

The SMCV for M galloprovincialis was estimated by applying the ACR of 2.208 to the SMAV
Five and ninety five percent confidence intervals were not reported for the single test used to
calculate the SMAV for this test species. The final SMCV was 62.12 |ig/L.

Because the Oregon chronic criterion for zinc is greater than the SMCV for Haliotis rufescens
and Mytilus galloprovincialis, EPA concludes that the Oregon CCC for zinc may not be
protective of chronic effects for all individuals within this species. Because the Oregon chronic
criterion for zinc is below the LOEC for Acanthomysis costata, EPA concludes that the Oregon
CCC for zinc is sufficiently protective of this species.

Saltwater zinc chronic criterion comparison

Text Box D (chronic) - Basis for the meta analysis comparing the SMCV for the red abalone
(Haliotis rufescens) to the chronic criterion for zinc (81 |ig/L dissolved metal concentration).

Haliotis rufescens

Reported Values

LC50 5% CI

95% CI

Dissolved Normalized Values

LC50 5% CI 95% CI

ACR

Dissolved Chronic Values

LC50/ACR

CCC

40.00

39.40

41.00

37.84

37.27

38.79

2.208

17.14

55.00

52.03

2.208

26.02

76.00

68.60

83.10

71.90

64.90

78.61

2.208

32.56

64.00

56.60

71.40

60.54

53.54

67.54

2.208

27.42

64.00

58.90

69.10

60.54

55.72

65.37

2.208

27.42

47.00

41.30

52.70

44.46

39.07

49.85

2.208

20.14

44.00

38.50

49.50

41.62

36.42

46.83

2.208

18.85

50.00

45.60

54.40

47.30

43.14

51.46

2.208

21.42

Geomean
(all)

Geomean
(CI Only)

53.86
53.70

48.74

58.64

50.95
50.80

46.11

55.48

SMCV

23.08
23.01

Text Box E (chronic) - Basis for the meta analysis comparing the SMCV for the mysid shrimp
(Acanthomysis costata) to the chronic criterion for zinc (81 |ig/L dissolved metal concentration).

Acanthomysis costata

170

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Reported Chronic Values

Dissolved Normalized Chronic Values

NOEC LOEC

NOEC LOEC CV

ccc

45 100

67.08

42.57 94.60 63.46

(SMCV)

2.2.9.3 References for Zinc

A. Studies That EPA Utilized in this Determination

EPA determined that these studies were acceptable to be utilized in this determination based
on the data quality acceptance criteria established in the 1985 Guidelines. The studies listed
below were used in the acute and chronic tables, and are the source from which EPA
obtained SMAVs (acute table) and experimentally-derived SMCVs (chronic table).

Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in Tables 2.2.8-1 and 2.2.8-2)

Acute References

Conroy, P.T., J.W. Hunt and B.S. Anderson. 1996. Validation of a short-term toxicity test endpoint by comparison
with longer-term effects on larval red abalone Haiiotis rufescens. Environ. Toxicol. Chem. 15(7): 1245-1250.

Anderson, B.S., J.W. Hunt, M. Martin, S.L. Turpen and F.H. Palmer. 1988. Marine Bioassay Project. 3rd Report.
Protocol Development: Reference Toxicant and Initial Complex Effluent Testing. No. 88-7WQ, State Water
Resources Control Board, State of California, Sacramento, CA: 154.

Hunt, J.W. and B.S. Anderson. 1989. Sublethal effects of zinc and municipal effluents on larvae of the red
abalone Haiiotis rufescens. Mar. Biol. 101(4): 545-552.

Martin, M., J.W. Hunt, B.S. Anderson and S.L. Turpen. 1989. Experimental evaluation of the mysid Holmesimysis
costata as a test organism for effluent toxicity testing. Environ. Toxicol. Chem. 8(11): 1003-1012.

Selvakumar, S., S.A. Khan and A.K. Kumaraguru. 1996. Acute toxicity of some heavy metals, pesticides and
water soluble fractions of diesel oil to the larvae of some brachyuran crabs. J. Environ. Biol. 17(3): 221-226.

Pavicic, J., M. Skreblin, I. Kregar, M. Tusek-Znidaric and P. Stegnar. 1994. Embryo-larval tolerance of Mytilus
galloprovincialis, exposed to the elevated sea water metal concentrations -1. Toxic effects of Cd, Zn and Hg in
relation to the metallothionein level. Comp. Biochem. Physiol. C 107(2): 249-257.

Chapman, P.M. and C. McPherson. 1993. Comparative zinc and lead toxicity tests with Arctic marine
invertebrates and implications for toxicant discharges. Polar Rec. 29(168): 45-54; In: E.G.Baddaloo, S.
Ramamoorthy and J.W. Moore (Eds.), Proc. 19th Annual Aquatic Toxicity Workshop, Oct. 4-7, 1992, Edmondton,
Alberta, Can. Tech. Rep. Fish. Aquat. Sci. No. 1942: 7-22.

Dinnel, P.A., Q.J. Stober, J.M. Link, M.W. Letourneau, W.E. Roberts, S.P. Felton and R.E. Nakatani. 1983.
Methodology and Validation of a Sperm Cell Toxicity Test for Testing Toxic Substances in Marine Waters. Final
Report, FRI-UW-8306, Fisheries Research Inst., School of Fisheries, University of Washington, Seattle, WA: 208.

Nelson, V.A. 1972. Effects of Strontium-90 + Yttrium-90, Zinc-65, and Chromium-51 on the Larvae of the Pacific
Oyster Crassostrea gigas. In: A.T. Proter and D.L. Alverson (Eds.), The Columbia River Estuary and Adjacent
Ocean Waters, Chapter 32, University of Washington Press, Seattle, WA: 819-832.

Martin, M., K.E. Osborn, P. Billig and N. Glickstein. 1981. Toxicities often metals to Crassostrea gigas and
Mytilus edulis embryos and Cancer magister larvae. Mar. Pollut. Bull. 12(9): 305-308 (Author Communication
Used).

Dinnel, P.A., J.M. Link, Q.J. Stober, M.W. Letourneau and W.E. Roberts. 1989. Comparative sensitivity of sea
urchin sperm bioassays to metals and pesticides. Arch. Environ. Contam. Toxicol. 18(5): 748-755.

Calabrese, A. and D.A. Nelson. 1974. Inhibition of embryonic development of the hard clam, Mercenaria
mercenaria, by heavy metals. Bull. Environ. Contam. Toxicol. 11(1): 92-97.

Calabrese, A., R.S. Collier, D.A. Nelson and J.R. Mac Innes. 1973. The toxicity of heavy metals to embryos of the
American oyster Crassostrea virginica. Mar. Biol. 18(3): 162-166.

Lussier, S. and J. A. Cardin. 1985. Results of Acute Toxicity Tests Conducted with Zinc at ERL, Narragansett.
U.S. EPA, Narragansett, Rl: 6.

Johnson, M. 1985. Results of Acute Toxicity Tests Conducted with Zinc at ERL, Narragansett. Memo to D.
Hansen, U.S. EPA, Narragansett, Rl: 3.

171

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Reference
No.

Used Reference Citation

(associated with reference numbers and provided above in Tables 2.2.8-1 and 2.2.8-2)

Eisler, R. and R.J. Hennekey. 1977. Acute toxicities of Cd2+, Cr+6, Hg2+, Ni2+ and Zn2+ to estuarine
macrofauna. Arch. Environ. Contam. Toxicol. 6(2/3): 315-323

Palawski, D., J.B. Hunn and F.J. Dwyer. 1985. Sensitivity of young striped bass to organic and inorganic
contaminants in fresh and saline waters. Trans. Am. Fish. Soc. 114: 748-753.

Lussier, S.M., J.H. Gentile and J. Walker. 1985. Acute and chronic effects of heavy metals and cyanide on
Mysidopsis bahia (Crustacea: Mysidacea). Aquat. Toxicol. 7(1-2): 25-35.

Lussier, S. and J.H. Gentile. 1985. Results of Acute Toxicity Tests Conducted with Zinc at ERL, Narragansett.
U.S. EPA, Narragansett, Rl: 2.

Connor, P.M. 1972. Acute toxicity of heavy metals to some marine larvae. Mar. Pollut. Bull. 3(12): 190-192.

Sivadasan, C.R., P.N.K. Nambisan and R. Damodaran. 1986. Toxicity of mercury, copper and zinc to the prawn
Metapenaeus dobsoni (Mier). Curr. Sci. 55(7): 337-340.

Cripe, G.M. 1994. Comparative acute toxicities of several pesticides and metals to Mysidopsis bahia and
postlarval Penaeus duorarum. Environ. Toxicol. Chem. 13(11): 1867-1872.

Gentile, S. and J. Cardin. 1982. Unpublished Laboratory Data. U.S. EPA, Narragansett, Rl: 5 p.

Reish, D.J., J.M. Martin, F.M. Piltz and J.Q. Word. 1976. The effect of heavy metals on laboratory populations of
two polychaetes with comparisons to the water quality conditions and standards in Southern CA. Water Res. 10:
299-302.

Reish, D.J. and J.A. Lemay. 1991. Toxicity and bioconcentration of metals and organic compounds by polychaeta.
Ophelia (Suppl.) 5: 653-660.

Reish, D.J. 1978. The effects of heavy metals on polychaetous annelids. Rev. Int. Oceanogr. Med. 49(3): 99-104.

Bengtsson, B.E. 1978. Use of a harpacticoid copepod in toxicity tests. Mar. Pollut. Bull. 9: 238-241.

Vranken, G., R. Vandergaeghen and C. Heip. 1991. Effects of pollutants on life-history parameters of the marine
nematode Monhystera disjuncta. ICES J. Mar. Sci. 48: 325-334.

Ahsanullah, M., M.C. Mobley and P. Rankin. 1988. Individual and combined effects of zinc, cadmium and copper
on the marine amphipod Aiiorchestes compressa. Aust. J. Mar. Freshwater Res. 39(1): 33-37.

Reish, D.J., T.V. Gerlinger, C.A. Phillips and P.D. Schmidtbauer. 1977. Toxicity of Formulated Mine Tailings on
Marine Polychaete. Marine Biological Consultants, Coasta Mesa, CA: 133.

Cardin, J.A. 1985. Acute toxicity data for zinc and the saltwater fish, Funduius heterociitus, Menidia menidia and
Pseudopieuronectes americanus. (Memorandum to D.J. Hansen, U.S. EPA, Narragansett, Rl).

Ahsanullah, M. 1976. Acute toxicity of cadmium and zinc to seven invertebrate species from Western Port,
Victoria. Aust. J. Mar. Freshwater Res. 27(2): 187-196.

Moreau, C.J., P.L. Klerks and C.N. Haas. 1999. Interaction between phenanthrene and zinc in their toxicity to the
sheepshead minnow (Cyprinodon varieqatus). Arch. Environ. Contam. Toxicol. 37(2): 251-257.

Lewis, W. M. 1993. Acute and Chronic Responses of Menidia beryiiina, Rivuius marmoratus, and Cyprinodon
varieqatus to Malathion and Zinc Chloride. M.S. Thesis, Florida Inst, of Technol.: 71.

Bryant, V., D.M. Newbery, D.S. McLusky and R. Campbell. 1985. Effect of temperature and salinity on the toxicity
of nickel and zinc to two estuarine invertebrates (Corophium voiutator, Macoma baithica). Mar. Ecol. Prog. Ser.
24(1-2): 139-153.

Hansen, D.J. 1983. Section on Acute Toxicity Tests to be Inserted in the April 1983 Report on Site Specific FAV's.
U.S. EPA, Narragansett, Rl: 7.

Eisler, R. 1977a. Toxicities of selected heavy metals to the soft-shell clam, Mya arenaria. Bull. Environ. Contam.
Toxicol. 17: 137-145.

Hilmy, A.M., N.F. Abdel-Hamid and K.S. Ghazaly. 1985. Toxic effects of both zinc and copper on size and sex of
Portunus peiaqicus (L) (Crustacea: Decapoda). Bull. Inst. Oceanogr. Fish. (Cairo) 11: 207-215.

Bryan, G.W. and L.G. Hummerstone. 1973. Adaptation of the polychaete Nereis diversicoior to estuarine
sediments containing high concentrations of zinc and cadmium. J. Mar. Biol. Assoc. U.K. 53(4): 839-857.

Fernandez, T.V. and N.V. Jones. 1990. The influence of salinity and temperature on the toxicity of zinc to Nereis
diversicoior. Trop. Ecol. 31(1): 40-46.

Lin, H.C. and W.A. Dunson. 1993. The effect of salinity on the acute toxicity of cadmium to the tropical, estuarine,
hermaphroditic fish, Rivuius marmoratus: A comparison of Cd, Cu, and Zn tolerance with Funduius heterociitus.
Arch. Environ. Contam. Toxicol. 25: 41-47.

Marcano, L., O. Nusetti, J. Rodriguez-Grau and J. Vilas. 1996. Uptake and depuration of copper and zinc in
relation to metal-binding protein in the polychaete Eurythoe camplanata. Comp. Biochem. Physiol. C 114(3): 179-
184.

Chronic References

Lussier, S.M., J.H. Gentile and J. Walker. 1985. Acute and chronic effects of heavy metals and cyanide on
Mysidopsis bahia (Crustacea: Mysidacea). Aquat. Toxicol. 7(1-2): 25-35.

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B. Studies That EPA Considered But Did Not Utilize In This Determination

most recent national ambient water quality criteria dataset used to derive the CMC ,
EPA is providing a transparent rationale as to why they were not utilized (see below).

2) For the studies that were not utilized because they were not found to be pertinent to
this determination (including failing the QA/QC procedures listed in Appendix A)
upon initial review of the download from ECOTOX, EPA is providing the code that
identifies why EPA determined that the results of the study were not reliable (see
Appendix V).

77 U.S. EPA. 1987. Ambient Water Criteria for Zinc - 1987. EPA-440-5-87-003.

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APPENDIX A: QA/QC PROCEDURES

Sections II.B - F, IV.B - E, IV.H, and VI.B - E of the Guidelines give reasons why the results of
some toxicity tests should not be used, should be rejected, or should not be used in calculations,
whereas sections II.G, X, XI.C, XII. A. 14, and XII.B allow the use of "questionable data" and
"other data" in some situations. In other words, sections II.B - F, IV.B - E, IV.H, VI.B - E give
reasons why the results of some toxicity tests using aquatic animals should not be directly used
in the derivation of a Final Acute Value (FAV) or a Final Chronic Value (FCV), whereas
sections II.G, X, XI.C, XII. A. 14, and XII.B describe other possible uses of test results with
aquatic animals that should not be directly used in the derivation of a FAV or a FCV.

The Guidelines say the following concerning the use of results of toxicity tests using aquatic
animals:

1. General guidance:

a. All data should be available in typed, dated, and signed hard copy (publication,
manuscript, letter, memorandum, etc.) with enough supporting information to indicate
that acceptable test procedures were used and that the results are probably reliable,
(section II.B)

b. Information that is confidential or privileged or otherwise not available for distribution
should not be used, (section II.B)

c. Questionable data, whether published or unpublished, should not be used. For example,
a test result should usually be rejected if it is from:

i. a test that did not contain a control treatment.

ii. a test in which too many organisms in the control treatment died or showed signs of
stress or disease.

iii. a test in which distilled or deionized water was used as the dilution water without
addition of appropriate salts.

(section II.C)

d. A result of a test on technical-grade material may be used if appropriate, but a result of
a test on a formulated mixture or an emulsifiable concentrate of the test material should
not be used, (section II.D)

e. For some highly volatile, hydrolyzable, or degradable materials it is probably
appropriate to use only results of flow-through tests in which the concentrations of test
material in the test solutions were measured often enough using acceptable analytical
methods, (section II.E)

f. Data should be rejected if they were obtained using:

i. Brine shrimp.

ii. A species that does not have a reproducing wild population in North America.

iii. Organisms that were previously exposed to substantial concentrations of the test
material or other contaminants, (section II.F)

2. Guidance specifically regarding results of acute tests:

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g. Acute toxicity tests should have been conducted using acceptable procedures, (section
IV.B) The following two American Society for Testing and Materials (ASTM)
Standards are referenced as examples of acceptable procedures:

i. ASTM Standard E 729, Practice for Conducting Acute Toxicity Tests with Fishes,
Macroinvertebrates, and Amphibians. (The title was later changed to "Standard
Guide for Conducting Acute Toxicity Tests on Test Materials with Fishes,
Macroinvertebrates, and Amphibians".)

Some of the most important items in Standard E 729 include:

(1) "The test material should be reagent-grade or better, unless a test on a formulation,
commercial product, or technical-grade or use-grade material is specifically
needed." ("Reagent-grade" is referenced to the American Chemical Society
specifications.) (section 9.1)

(2) "If an organic solvent is used, it should be reagent-grade or better and its
concentration in any test solution must not exceed 0.5 mL/L. A surfactant must not
be used in the preparation of a stock solution because it might affect the form and
toxicity of the test material in the test solutions." (section 9.2.3)

(3) "For static tests the concentration of dissolved oxygen in each test chamber must be
from 60 to 100 % of saturation during the first 48 h of the test and must be between
40 and 100 % of saturation after 48 h. For renewal and flow-through tests the
concentration of dissolved oxygen in each test chamber must be between 60 and
100 % of saturation at all times during the test." (section 11.2.1)

ii. ASTM Standard E 724, Practice for Conducting Static Acute Toxicity Tests with
Larvae of Four Species of Bivalve Molluscs. (The title was later changed to
"Standard Guide for Conducting Static Acute Toxicity Tests Starting with Embryos
of Four Species of Saltwater Bivalve Molluscs".)

When water quality criteria for aquatic life are derived, EPA does not automatically
accept all toxicity tests that are performed according to an ASTM Standard or according
to "Standard Methods". EPA reviews results of all aquatic toxicity tests for
acceptability using best professional judgment. Although written methodologies are
very useful, no such methodology can appropriately address all aspects of toxicity tests,
especially all organism-specific and all chemical-specific aspects. In addition, written
methodologies often do not keep up with the newest information that is available.

h. Except for tests using saltwater annelids and mysids, results of acute tests during which
the test organisms were fed should not be used, unless data indicate that the food did not
affect the toxicity of the test material, (section II. C)

i. Results of acute tests conducted in unusual dilution water, e.g., dilution water in which
total organic carbon or particulate matter exceeded 5 mg/L, should not be used, unless a
relationship is developed between acute toxicity and organic carbon or particulate
matter or unless data show that organic carbon, particulate matter, etc., do not affect
toxicity, (section IV.D)

j. Acute values should be based on endpoints which reflect the total severe acute adverse
impact of the test material on the organisms used in the test. Therefore, only the
following kinds of data on acute toxicity to aquatic animals should be used:

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(1) Tests with daphnids and other cladocerans should be started with organisms less
than 24 hours old and tests with midges should be started with second- or third-
instar larvae. The result should be the 48-hr EC50 based on the percentage of
organisms immobilized plus percentage of organisms killed. If such an EC50 is not
available from a test, the 48-hr LC50 should be used in place of the desired 48-hr
EC50. An EC50 or LC50 of longer than 48 hr can be used as long as the animals
were not fed and the control animals were acceptable at the end of the test.

(2) The result of a test with embryos and larvae of barnacles, bivalve molluscs (clams,
mussels, oysters, and scallops), sea urchins, lobsters, crabs, shrimp, and abalones
should be the 96-hr EC50 based on the percentage of organisms with incompletely
developed shells plus the percentage of organisms killed. If such an EC50 is not
available from a test, the lower of the 96-hr EC50 based on the percentage of
organisms with incompletely developed shells and the 96-hr LC50 should be used
in place of the desired 96-hr EC50. If the duration of the test was between 48 and
96-hr, the EC50 or LC50 at the end of the test should be used.

(3) The acute values from tests with all other freshwater and saltwater animal species
and older life stages of barnacles, bivalve molluscs, sea urchins, lobsters, crabs,
shrimps, and abalones should be the 96-hr EC50 based on the percentage of
organisms exhibiting loss of equilibrium plus the percentage of organisms
immobilized plus the percentage of organisms killed. If such an EC50 is not
available from a test, the 96-hr LC50 should be used in place of the desired 96-hr
EC50.

(4) Tests with single-celled organisms are not considered acute tests, even if the
duration was 96 hours or less.

(5) If the tests were conducted properly, acute values reported as "greater than" values
and those which are above the solubility of the test material should be used,
because rejection of such acute values would unnecessarily lower the FAV by
eliminating acute values for resistant species.

(section IV.E)

k. The agreement of the data within and between species should be considered. Acute
values that appear to be questionable in comparison with other acute and chronic data
for the same species and for other species in the same genus probably should not be
used in the calculation of a Species Mean Acute Value (SMAV). For example, if the
acute values available for a species or genus differ by more than a factor of 10, some or
all of the values probably should not be used in calculations, (section IV.H)
3. Guidance specifically regarding results of chronic tests:

1. Chronic values should be based on results of flow-through (except renewal is acceptable
for daphnids) chronic tests in which the concentrations of test material in the test
solutions were properly measured at appropriate times during the test, (section VI.B)
m. Results of chronic tests in which survival, growth, or reproduction in the control
treatment was unacceptably low should not be used. The limits of acceptability will
depend on the species, (section VI.C)
n. Results of chronic tests conducted in unusual dilution water, e.g., dilution water in
which total organic carbon or particulate matter exceeded 5 mg/L, should not be used,
unless a relationship is developed between chronic toxicity and organic carbon or

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particulate matter or unless data show that organic carbon, particulate matter, etc., do
not affect toxicity, (section VI.D)
o. Chronic values should be based on endpoints and lengths of exposure appropriate to the
species. Therefore, only data on chronic toxicity to aquatic animals that satisfy the
species-specific requirements given in sections VI.E.l, VI.E.2, and VI.E.3 should be
used.

4. Guidance regarding other possible uses of results of toxicity tests using aquatic animals:
p. Questionable data, data on formulated mixtures and emulsifiable concentrates, and data
obtained with non-resident species or previously exposed organisms may be used to
provide auxiliary information but should not be used in the derivation of criteria,
(section II.F)

q. Pertinent information that could not be used in earlier sections might be available

concerning adverse effects on aquatic organisms and their uses. The most important of
these are data on cumulative and delayed toxicity, flavor impairment, reduction in
survival, growth, or reproduction, or any other adverse effect that has been shown to be
biologically important. Especially important are data for species for which no other
data are available. Data from behavioral, biochemical, physiological, microcosm, and
field studies might also be available. Data might be available from tests conducted in
unusual dilution water, from chronic tests in which the concentrations were not
measured, from tests with previously exposed organisms, and from tests on formulated
mixtures or emulsifiable concentrates. Such data might affect a criterion if the data
were obtained with an important species, the test concentrations were measured, and the
endpoint was biologically important, (section X)
r. The Criterion Continuous Concentration (CCC) is equal to the lowest of the Final

Chronic Value (FCV), Final Plant Value (FPV), and Final Residue Value (FRV), unless
other data show that a lower value should be used, (section XI.C)
s. Are any of the other data important? (section XII. A. 14)

t. On the basis of all available pertinent laboratory and field information, determine if the
criterion is consistent with sound scientific information. If it is not, another criterion,
either higher or lower, should be derived using appropriate modifications of these
Guidelines, (section XII.B)

In addition, the following aquatic life criteria documents published by U.S. EPA in 1985, 1986,

1987, and 1988 gave a variety of reasons for classifying specific test results as "unused":

U.S. EPA. 1985. Ambient Water Quality Criteria for Cadmium - 1984. EPA 440/5-84-032.
U.S. Environmental Protection Agency, Washington, DC.

U.S. EPA. 1985. Ambient Water Quality Criteria for Chlorine - 1984. EPA 440/5-84-030.
U.S. Environmental Protection Agency, Washington, DC.

U.S. EPA. 1985. Ambient Water Quality Criteria for Copper - 1984. EPA 440/5-84-031.
U.S. Environmental Protection Agency, Washington, DC.

U.S. EPA. 1985. Ambient Water Quality Criteria for Lead - 1984. EPA 440/5-84-027.
U.S. Environmental Protection Agency, Washington, DC.

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U.S. EPA. 1985. Ambient Water Quality Criteria for Mercury - 1984. EPA 440/5-84-026.
U.S. Environmental Protection Agency, Washington, DC.

U.S. EPA. 1986. Ambient Water Quality Criteria for Chlorpyrifos - 1986. EPA 440/5-86-

005. U.S. Environmental Protection Agency, Washington, DC.

U.S. EPA. 1986. Ambient Water Quality Criteria for Parathion - 1986. EPA 440/5-86-007.
U.S. Environmental Protection Agency, Washington, DC.

U.S. EPA. 1986. Ambient Water Quality Criteria for Pentachlorophenol - 1986. EPA
440/5-86-009. U.S. Environmental Protection Agency, Washington, DC.

U.S. EPA. 1986. Ambient Water Quality Criteria for Toxaphene - 1986. EPA 440/5-86-

006. U.S. Environmental Protection Agency, Washington, DC.

U.S. EPA. 1987. Ambient Water Quality Criteria for Selenium - 1987. EPA 440/5-87-006.
U.S. Environmental Protection Agency, Washington, DC.

U.S. EPA. 1987. Ambient Water Quality Criteria for Zinc - 1987. EPA 440/5-87-003.
U.S. Environmental Protection Agency, Washington, DC.

U.S. EPA. 1988. Ambient Water Quality Criteria for Chloride - 1988. EPA 440/5-88-001.
U.S. Environmental Protection Agency, Washington, DC.

The following is a list of common reasons why the results of some toxicity tests should not be
used. Most of these reasons can be considered to be based on items "a" through "o" listed above.

1. The document is a secondary publication of the test result.

2. The test procedures, test material, dilution water, and/or results were not adequately
described.

3. The test species is not resident in North America.

4. The test species was not obtained in North America and was not identified well enough to
determine whether it is resident in North America.

5. The test organisms were not identified specifically, for example, "crayfish" or "minnows."

6. There is reason to believe that the test organisms were possibly stressed by disease or
parasites.

7. The test organisms were exposed to elevated concentrations of the test material before the
test and/or the control organisms contained high concentrations of the test material.

8. The test organisms were obtained from a sewage oxidation pond.

9. By the end of the test, the test organisms had not been fed for too long a period of time.

10. The water quality varied too much during the test.

11. The test was conducted with brine shrimp, which are from a unique saltwater environment.

12. The exposed biological material was an enzyme, excised or homogenized tissue, tissue
extract, plasma, or cell culture.

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13. The test organisms were not acclimated to the dilution water for a sufficiently long time
period.

14. The test organisms were exposed to the test material via gavage, injection, or food.

15. There is reason to believe that the test organisms were probably crowded during the test.

16. The test organisms reproduced during an acute test, and the new individuals could not be
distinguished from the original test individuals at the end of the test.

17. The test material was a component of a mixture, effluent, fly ash, sediment, drilling mud,
sludge, or formulation.

18. In a test on zinc, the dilution water contained a phosphate buffer.

19. The test material was chlorine and it was not measured acceptably during the test.

20. The test chamber contained sediment.

21. The test was conducted in plastic test chambers without measurement of the test material.

22. The test was a field study and the concentration of test material was not measured
adequately.

23. A known volume of stock solution was placed on a wall of the test chamber and evaporated
and then dilution water was placed in the test chamber; the investigators assumed that all of
the test material dissolved in the dilution water, but the concentrations of the test material in
the test solutions were not measured.

24. The test only studied metabolism of the test material.

25. The only effects studied were biochemical, histological, and/or physiological.

26. The data concerned the selection, adaptation, or acclimation of organisms for increased
resistance to the test material.

27. The percent survival in the control treatment was too low.

28. The concentration of solvent in some or all of the test solutions was too high.

29. The study was a microcosm study.

30. The concentration of test material fluctuated too much during the exposure.

31. Too few test organisms were used in the test.

32. The dilution factor was ten.

33. There was no control treatment.

34. The pH was below 6.5.

35. The dilution water was chlorinated or "tap" water.

36. The dilution water contained an excessive amount of a chelating agent such as EDTA or
other organic matter.

37. The acceptability of the dilution water was questionable because of its origin or content.

38. The dilution water was distilled or deionized water without the addition of appropriate salts.

39. The measured test temperature fluctuated too much.

40. Neither raw data nor a clearly defined endpoint was reported.

41. The results were not adequately presented or could not be interpreted.

42. The results were only presented graphically.

43. The test was a chronic test and the concentration of test material was not measured.

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Appendix B: Procedures Used In EPA's Biological Evaluation and
Comparison to this Analysis Regarding Data Acceptability

This appendix describes the procedures that EPA used in developing the biological evaluation
(BE) for the purpose of initiating formal consultation with the U.S. Fish and Wildlife Service and
the National Marine Fisheries Services (hereafter, the Services) under section 7(a)(2) of the
Endangered Species Act (ESA) and compares the analyses and conclusions made in this
evaluation relative to EPA's CWA decision on Oregon's criteria. This BE was developed for the
purpose of providing the U.S. Fish and Wildlife Service and the National Marine Fisheries
Services (hereafter referred to as the Services) with the information that EPA understood the
Services desired in order for the Services to complete their review of EPA's action under section
7(a)(2) of the Endangered Species Act (ESA). This information consisted of a wider universe of
studies of the toxicity of chemicals to aquatic species than what was finally considered in EPA's
determination of whether Oregon's criteria are protective of Oregon's Fish and Aquatic Life
designated use. In addition, in the BE, EPA included model-based estimates or projections of
potential toxicity of chemicals to threatened and endangered aquatic species in cases where no
data existed.

Because EPA's objective in developing the BE was to be responsive and deferential to the
Services' desire to have as much information as possible to consider they developed their
Biological Opinion (BO) under the ESA, the information in the BE differs in some respects from
what EPA considered as it evaluated the protectiveness of Oregon's criteria under the CWA.

B.l Consulting Under Endangered Species Act Section 7(a)(2) on the Approval of
Oregon's Water Quality Criteria

When taking the federal action to approve Oregon's aquatic life criteria under CWA section
303(c), EPA has interpreted ESA section 7(a)(2) as applying to EPA's action. Accordingly, EPA
developed a Biological Evaluation (BE) to submit to the Services in order to initiate formal

consultation .

In order to collect the best scientific and commercial data available for the review of the effects
of the action on each of these listed species and critical habitat (50 CFR part 402.14(d)), EPA

compiled toxicological data from the ECOTOX database and its extensive literature holdings
compiled from monthly searches of online abstracting services (American Chemistry Society's
STN-CAS and Cambridge Scientific Abstracts), manual searches of table of contents from high-
impact journals, and the bibliographies of review articles. The target of these searches are
documents containing information regarding lethal and sublethal adverse effects on, and

78 US. EPA Region 10. 2008. "5.1.2 Biological Evaluation Effects Assessment Methodology", In Biological
Evaluation of Oregon's Water Quality Criteria for Toxics, (pp. 5-10 - 5-54).

79 There are over 5,000 journals, 2, 000 published books, 3,000 government reports, and 600 theses represented in
the literature holdings of ECOTOX. U.S. EPA. 2007. Ecotoxicity Database (ECOTOX) Mid-Continent Ecology
Division, National Health and Environmental Effects Research Laboratory. U.S. Environmental Protection Agency,
Office of Research and Development, http://cfpub.epa.gov/ecotox/.

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bioaccumulation by, freshwater and/or saltwater aquatic plants and animals, as well as chronic
feeding studies and long-term field studies using wildlife species that regularly consume aquatic
organisms. To ensure comprehensive coverage of the literature for these chemicals, EPA also
conducted a chemical specific using STN-CAS, Cambridge Scientific Abstract, Dissertation
Abstracts, Science Direct, and Toxline.

EPA developed, along with the Services, specific literature search strategies and QA/QC
requirements for data for inclusion in the BE. These are described in Appendix D of the BE. As
a result of the differing QA/QC requirements, and as a result of EPA's review of its prior QA/QC

determinations for potentially influential studies, some studies referenced in the BE were not
used in the development of EPA's CWA determinations on whether to approve or disapprove
Oregon's new or revised aquatic life criteria.

The literature search for the BE did not reveal data that directly tested the toxicity of each
chemical to each of the listed species. However, in order to help EPA understand whether any
listed species may be affected and to help the Services complete their BO, when toxicity data
was lacking, EPA developed model based estimates or projections of the toxicity of pollutants to
T&E species in cases where toxicity data for T&E species were lacking. Although these model-
based projections were presented in the BE to help understand the potential toxicity of these
chemicals to listed species and screen out those species where EPA and the Services could easily
conclude that they were not likely to adversely affect T&E species, EPA does not consider it
appropriate to make CWA determinations based on these model-based estimates of toxicity
because these estimates are less certain than laboratory toxicity tests at predicting the
concentrations where effects to species will be observed.

In the BE, EPA evaluated existing toxicological information and determined whether each new
or revised criteria "may affect" or was "not likely to adversely affect" each listed species. It is
important to note that EPA made these determinations in the context of the ESA in preparation
for the Services' review and their development of the BO. The BE was an analysis prepared for
purposes of formal consultation pursuant to ESA Section 7(a)(2). The ESA has a general
prohibition on the taking of individuals of listed species and requires Federal Agencies to ensure
that their actions do not jeopardize those species. The approach differs from how EPA evaluates
criteria under the CWA where EPA evaluates the protectiveness of criteria at an aquatic
ecosystem or community level. This is consistent with the purposes of the CWA, which
provides for the "protection and propagation of fish, shellfish and wildlife" and for the
"restoration and maintenance of the chemical, physical, and biological integrity of the Nation's
waters." CWA § 101(a).

Given the different goals of the ESA and CWA noted above, a determination of "may affect" in
the BE does not translate to a disapproval determination under CWA section 303. Nor does it
mean that EPA concludes that effects to listed species are likely. Rather, it means that EPA has
determined that there is at least a potential for take to occur to an individual of a given species
and that this circumstance requires consultation with the Services.

80 See Section 1.1 for additional discussion.

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B.2 Comparative Analysis of the Biological Evaluation and the CWA Decision

In January 2008, EPA submitted a 1500 page biological evaluation to the Services for the
purpose of ESA Section 7(a)(2) consultation on EPA's approval of Oregon's water quality
standards.

In the BE, EPA determined whether each criteria was either "not likely to adversely affect" or
"may affect" each of the listed species potentially affected by an approval action. For those
species where EPA could readily make a "not likely to adversely affect" determination because
the species passed the initial screen, there was no need for further analysis

For those species that did not pass the initial screen but for which EPA concluded that the criteria
were nevertheless "not likely to adversely affect" the species based on a broader assessment of
toxicity and an analysis of exposure, the detailed explanation of how EPA reached that
conclusion is available in the BE. This appendix summarizes that analysis for each applicable
criterion.

For those species and chemicals where EPA concluded in the BE that the approval of the criteria
"may affect" a listed species for the purpose of initiating formal consultation, this appendix
provides additional analysis to explain how this information is consistent with EPA's CWA
decision.

B.3 Cross-Walk of Similar and Different QA/QC Procedures for Data Acceptability in
the BE

As indicated in the introduction of this document, and further elaborated on in Section 1.1
(Sources of data and toxicity studies used in EPA determinations whether to approve or
disapprove Oregon's criteria), the BE of Oregon's criteria was developed for the purpose of
providing the information that EPA understood the Services desired in order for the Services to
complete their review of EPA's action under section 7(a)(2) of the ESA. For the reasons stated
earlier in those sections, this information consisted of a wider universe of studies of the toxicity
of chemicals to aquatic species than was considered in EPA's determination of whether Oregon's
criteria are protective of Oregon's Fish and Aquatic Life designated use. Therefore, as
previously stated, the information in the BE differs in some respects from what EPA considered
as it evaluated the protectiveness of Oregon's criteria under the CWA.

This appendix provides a cross-walk of the similarities and differences between the QA/QC
requirements described in Appendix A which establish the data acceptability requirements for
deriving ambient water quality criteria for the protection of aquatic life, and the data
acceptability criteria EPA's subcontractor utilized for supporting the effect determinations in this
BE. For nearly all the priority pollutants for which Oregon provides toxics criteria (the only
exceptions being freshwater ammonia, chromium III and chromiumVI), EPA's subcontractor

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relied on aquatic toxicity data from EPA's ECOTOX database to develop the core dataset
utilized to make the effects determinations provided in that document.

Background on EPA's ECOTOX Database

The primary literature source used in the determinations made in Oregon's criteria was from
EPA's ECOTOX literature holdings. Therefore, a brief overview of the procedures used to
establish the origin and purpose of these data is provided here to establish data use and
acceptability. A more complete documentation on the ECOTOX literature search strategy is
located at: http://lester.dul.epa.g0v/qa/s0p/#DAM.

ECOTOX Overview

ECOTOX is a comprehensive web-based database, compiled and maintained by EPA's Office of
Research and Development (ORD) that provides information on the effects of single chemical
exposures to ecologically relevant species (http://www.epa.gov/ecotox/). The database supports
research in ORD and the broader scientific community, providing data to create and evaluate
predictive effects models developed through intra- and extramural research efforts (e.g.,
advanced species, dose, and chemical extrapolation modeling). It is used by the Agency's
Regional and Program Offices, as well as other Federal, State, Tribal and local government
agencies, and the regulated community as a primary source of literature on ecological effects to
meet responsibilities under Agency-delegated programs and/or data submissions and analyses
required by EPA.

ECOTOX Literature Searches

Literature searches conducted of the ECOTOX database do not use chemical specific terms
because the purpose is to capture all the literature on the toxicity of anthropogenic substances to
ecologically relevant species. Therefore, the search includes habitat terms (e.g., pond, soil),
effect terms (e.g., mortality, reproduction, growth), species terms (e.g., bird, worm, salamander),
general chemical terms (e.g., metal, organic, pesticide), and/or sub-file category codes within
abstracting databases relevant to ecotoxicology.

The identification of studies that are potentially applicable to the ECOTOX database is
accomplished through comprehensive searches of the open literature. These searches include use
of electronic bibliographic abstracting services (e.g., STN, ScienceDirect, Cambridge Scientific
Abstracts, Dialog), the manual review of bibliographies associated with summary or review
publications, and the manual review of library holdings at EPA/ORD's Mid-Continent Ecology
Division (Duluth, MN).

ECOTOX Minimum Data Requirements

For publications identified using the manual and electronic literature search methods, citations
for potentially applicable publications (for inclusion in the database) are either manually entered
or electronically downloaded into a bibliographic file. Publications acquired using the ECOTOX

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literature searching and acquisition protocols must meet five minimum data requirements to be
considered eligible for inclusion in the database. The publication is eligible for the ECOTOX
database if it reports (1) observed biological responses related to an exposure to a single
chemical, and the chemical's name and Chemical Abstract Services Registry number can be
verified in reliable chemical reference manuals; (2) a taxonomically verifiable test species that is
an aquatic or terrestrial plant or animal with the exception of yeast, bacteria and viruses; (3)
results based on the exposure of live, intact organisms; (4) a concurrent environmental chemical
concentration/dose or application rate (e.g., the application of pesticide formulations) with the
exception of concentrations reported in the sediment without concurrent pore water
concentrations and air exposures; and (5) a duration of exposure. Those that are not considered
eligible for incorporation into the database include publications that are only available in a
language other than English, publications that are not the primary source of the effects data (i.e.,
review or summary publications), and studies that are only available in a brief abstract.

Each citation that has been identified, either through the electronic literature searches or the
manual searches, is examined to determine whether or not it is potentially applicable to the
ECOTOX database. With the exception of review/summary and methods publications,
publications that are clearly not relevant to the ECOTOX database effort are not ordered, and the
electronic bibliographic record is annotated with the reason for exclusion (See Attachment 1.) If
a clear decision of applicability cannot be made based on the information available (e.g., citation
and or abstract), then the publication is acquired. All acquired publications that are assessed as
to relevance to the ECOTOX database based on the full publication, and if excluded, the citation
is annotated with the reason.

EPA Subcontractor ECOTOX Download and Data Review and Selection Process for BE
Development

The following general procedure was used by EPA's subcontractor to conduct a screen of the
ECOTOX data for its potential use in the ESA BE of Oregon's new and proposed criteria. These
data are screened to assess their applicability for use in the BE for each chemical for which
Oregon provides criteria (see Table 1.3, Section 1.3 of this document). Useful data (referred to
as Core data hereafter) were transformed into a format suitable (MS Excel) for entry into the BE.
The entire process was performed largely by mid and senior subcontractor staff levels (P3 and P4
level).

Steps for Gathering Core Data from ECOTOX

Note: The ECOTOX database is to be used in conjunction with the ECOTOX Code List
(printable on-line at www.epa.gov/ecotox/help/codelist.htm) and Effects List (available at
www.epa.gov/cgi-bin/ecotox_effects_browse).

1. Download ECOTOX data file for the chemical of interest. Be sure to use a search term or
terms that will find all appropriate forms of the chemical (e.g., the water soluble
inorganic salts of metals). Save the file unchanged and save the amended file (below)
with a new file name as described in the procedure below:

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a. Open internet Site- www.epa.gov/ecotox

b. Click on Advanced Database Query

c. Click on Report Format (the frog picture)

d. Select Delimited Report in Aquatic and Terrestrial Report Formats

e. Add the fields (in Fields Available) to Fields Selected in Aquatic Lab
Output Selections:

1. Chemical Analysis Method

2. Chemical Comment

3. Control Type

4. Document Code

5. Hardness

6. Organic Carbon Type/Value

7. Organism Comment (this gives life stage information)

8. pH

9. Publication year

10. Salinity

11. Species Number

12. Temperature

f. Repeat for Aquatic Field Output Selections (Note: only field data with a
Test Location coded FieldA (Field Artificial) will be considered (i.e.,
mesocosm studies).

g. Add the fields (in Fields Available) to Fields Selected in Terrestrial
Field Output Selections:

Control Type

Result % dry/Wet Weight

Chemical Purity

Significance/Level

Species Number

Chemical Comment

Chemical Formulation (we do not use tests where the chemical is

applied as a spray)

Test Comments

h. Remove all fields (in Fields Selected) with the word "soil" in Terrestrial
Field Output Selections

i. Click on Test Results in Advanced Query Menu

j. Click on the Accumulation, Growth, Mortality, Reproduction, Population,
Physiology and No Effect Groups, as well as Histological and Feeding
Behavior, in Effects and Measurements
k. Click on all three boxes in Documentation Codes
1. Click on Test Conditions in Advanced Query Menu
m. Click on:

1. Lab and All Field Tests in Test Locations;

2. Fresh Water, Salt Water, and Not Reported in Water, and
Hydroponic and Not Reported in Artificial in Exposure Media;

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3. Diet, Not Reported, Flow-through, Lentic, Lotic, Renewal Aquatic,
Static Aquatic, and Tidal in Exposure Sites;

4. Measured, Unmeasured, and Not Reported in Method of Chemical
Analysis.

n. Click on Chemical in Advanced Query Menu

0. Select all appropriate forms of the chemical (for an example for some
common metals, see Attachment 2)

2. Click on Perform Query

3. Save delimited text files for aquatic and terrestrial species separately with ".tsv"
extension as "ecotoxchemical abbrevBE aq or terr for aquatic or terrestrial data-
month-day-yr.tsv" (e.g., ecotox_Cr3BE_terr_12-02-04.tsv) in a designated
SHPD, or HECD WA File Folder on c:/drive.

4. Open the data into a unique Excel Workbook (.xls) file similarly named, e.g.,
"ecotox_Cr3BE_terr_12-02-04.xls"

1. Select "delimited" option and click Next

2. Select "other" and type "|" in blank box ("|" key is above "enter" key use
the shift)

3. Select "none" in Text qualifier box and then click Finish.

5. Open and save each chemical as a separate Excel Workbook (.xls) file.

Directions for identifying useful aquatic toxicity information

1. Within each aquatic file uniquely identified by chemical name, label the tab for
worksheet #1 "All Data" then create two new worksheets and name each FH20
Core and SH20 Core, respectively.

2. Select and copy all entries in "All Data" and paste into FH20.

3. Sort data by "Aquatic Media Type" and cut and paste all saltwater data (SW) for
the chemical in SH20.

4. Add a new column A to the FH20 and SH20 worksheets for code entry. The
code in this column will be for populating your Core worksheets referred to
above.

5. Add a new column on the right side of the worksheet for comments (use liberally,
including any change to recorded ECOTOX information, i.e., unit changes or
value conversions/corrections).

6. Perform a data sort using year of publication

7. All publications approximately 6-12 months prior to the publication date of the
latest AWQC update are "new."

8. Search the "old" data and identify all papers previously cited in the AWQC
document and check the data endpoint and concentration; code the rows
containing data from the AWQC document with a letter (e.g., A-awqc = acute
data in Table 1 of the AWQC document; C-awqc = chronic data in Table 2 of the
AWQC document; P-awqc = plant data in Table 4 of the AWQC document; B-
awqc = BCF data in Table 5 of the AWQC document). Remember that some
Table 6 data (identified as other data in the AWQC document) may be of value.
Also, for the ESA BE of Oregon's new and proposed criteria, non-resident species

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to North American which do not have a naturally reproducing population in North
American waters (usually identified in the Unused List of the AWQC document)
are automatically rejected.

9. Enter data from all papers cited Tables 1, 2, 4, and 5 (and potentially useful
papers in Table 6) of the AWQC document that are not in the ECOTOX database.

10. Note all data from the AWQC document that are in the ECOTOX database, but
do not have the same endpoint or concentration. Record any changes made to the
ECOTOX entry based on what is reported in the AWQC document in the newly
added "Comments" column.

11. Review the remaining "old" data and any "new" data for potentially useful values.
Code the potentially useful lines of data with A for acute, C for chronic, P for
plant, B for bioaccumulation/bioconcentration, and D for dietary.

12. Establish blank worksheets for rejected lines of data: a worksheet for rejected FW
animal data, a worksheet for rejected SW animal data, a worksheet for rejected
BCF and bioaccumulation data (coded ACC in the Effect column) and worksheets
for rejected FW and SW plant data. Cut and paste lines of rejected data into the
appropriate worksheet. Add rejection codes (see Attachment 3 of this file) in
Column A if this has not already been done.

13. Note and reject all tests conducted with inappropriate forms of the metal, e.g., if
Concentration Type indicates use of a chemical Formulation (F), unless the
Chemical Purity and Chemical Comments columns indicate otherwise (i.e., as per
the QC/QA requirements in Appendix A).

14. Note and reject all tests without a specific test duration specified (i.e., all rows of
data where only a minimum or maximum duration has been provided).

15. Note and reject all ACC (bioacummulation) data that are of too short duration for
the chemical of interest (i.e., indicating steady-state was not achieved, this will
vary with chemical, but use 10 to 20 days as a rule of thumb).

16. Note and reject all data that are for inappropriate endpoints (e.g., this requires
scrutiny of Effect Measurement Codes and will most likely be the Physiological
endpoints coded PHY, possibly HIST).

17. Examine the rejected papers (steps 12, 13, 14, 15 and 16) for those with species or
specified or potential endpoints that might provide acute LC50s for a new taxon,
new ACRs, new BCFs, effect values near or below the AWQC criteria, and
dietary effect data. Also, for chemical criteria that are hardness or pH dependent,
to see if those required parameters values are absent in ECOTOX. (Note: dietary
effect data for aquatic organisms should be relegated to a separate worksheet
labeled as such).

18. If data look otherwise acceptable, you may wish to confirm the chemical form if
the CAS designation is ambiguous (e.g., if the CAS # provided is for the general
"Arsenic" element and not the specific salt for the desired arsenic III form).

As noted above, attachment 3 contains a list of rejection codes for use in separating data.

Most of the codes will not apply at this point because of the strict selection of initial

criteria used to create the ECOTOX download file. The most common criteria which will

be used to select/reject data in the downloaded file will be test Duration (Dur) (note: test

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durations may deviate slightly from the Guidelines as provided in the QC/QA
requirements found in Appendix A of this document, but must be of sufficient duration to
produce a reliable acute or chronic effect), and inappropriate test exposure (chronic tests
that were not flow-through, especially for those chemicals that are highly biodegradable,
hydrolyzable, oxidizable, reducible, or volatile). As a rule of thumb, consider acute and
chronic toxicity data for fish from 48 to 120 h and 21+ days, respectively. For
cladocerans, consider acute and chronic toxicity data from 24 to 96 h and 7 to 14+ days,
respectively.

All ECOTOX data records remaining in the Core fresh- and saltwater data sheets (FH20
Core and SH20 Core, respectively) will be used to support the effect determinations in
the BE.

Quality Control

1. Certify that all records have data on critical fields (see Required Toxicity Data
Fields for BE sheet below).

2. Check that all records express concentrations of the same chemical form and
fraction (e.g., total or dissolved) in the same units. Note: the national new or
proposed criteria for all metals of interest are expressed as the concentration of
dissolved metal in the water column. Use the appropriate conversion factor to
convert toxicity values expressed as total metal to dissolved metal. Appropriate
conversion factors are those provided in EPA 823-B-96-007: The Metals
Translator: Guidance for Calculating a Total Recoverable Permit Limit from a
Dissolved Criterion.

3. If appropriate, check that records have been appropriately converted.

Backup

Copy your file to an external storage media (e.g., CD-R/RW) at least once a week.

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Required Toxicity Data Fields for BE (aquatic species only)

Critical information is hig

llighted in bold.

Information

Comment

Chemical Name

Check that it is an acceptable form of the contaminant

Chemical Comment

CAS Number

Easy to find through a web search1, if not available.

Scientific Name

Records that do not identify genus and species have low priority

Common Name

Easy to find through a web search , if not available.

Organism Comment

Information on life stage

Effect + Effect Meas.

Classification of response type and response measured, respectively.

Endptl

Classify endpoint as acute or chronic (list endpoints or add column)

Habitat

NA in Ecotox. Aquatic or Terrestrial (Aquatic dependent spp.).

Plant / Animal

Not Available in Ecotox.

Media Type

Freshwater (FW) or Saltwater (SW)

Dur + Dur Unit

Duration of exposure period: value + time unit

Concentrationl mean

Endpoint value. If necessary, convert to appropriate unit.

Concentration Unit

Ecotox records values in original units.

Concentration Type

Active, Dissolved, or Total (A, D, T, respectively)

Chemical Analysis

Information on measured or unmeasured test concentrations

Temperature + Unit

Hardness + Unit

Required value if criteria are expressed as a function of hardness

Exposure Type

Static, Renewal, Flow through

Ecotox Reference #

Reference number in Ecotox series

Author + Year

Ref. Source + Title

Search for: chemical name CAS

Search atwww.itis.usda.gov/ or www.gbif.net/portal/index.jsp

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Cross-walk of Primary Differences between Data Accepted for Use in the BE versus
Data Acceptable for Criteria Derivation

The following table (replete with codes) denotes the primary differences between the
majority of toxicological data accepted for inclusion in the BE versus the toxicological
data that is accepted for criteria derivation (as per Appendix A this document) because of
the use of ECOTOX as the primary toxicological data source and instrument. ECOTOX
was selected as the primary data instrument due to the time and resource constraints
required to develop the BE of Oregon's new and proposed criteria, and also because
ECOTOX does represent a comprehensive toxicological database useful for such a
purpose. The cross-walk between the QA/QC procedures provided in Appendix A for
AWQC development and the codes denoting whether those requirements could be met
using ECOTOX is used here to identify which of the Guidelines requirements were and
were not be met in the BE. For more on the "wider universe of studies of the toxicity of
chemicals to aquatic species" EPA considered in its BE, see the subsection above
entitled: Directions for identifying useful aquatic toxicity information (last paragraph in
particular), to which the coded table below is meant to coincide.

Note: the following codes indicate which of the general and specific data requirements
given by the Guidelines were met using ECOTOX for development of the core data used
in the BE (i.e., for all chemicals except freshwater ammonia, chromium III, chromium
IV, as noted above).

X - Indicates the requirement has been met by convention of using ECOTOX
O - Indicates the requirement has not been met by convention using ECOTOX
P - Indicates the requirement only partially met by convention using ECOTOX, and
includes an explanation.

Indication of whether a
requirement was met in the BE
using ECOTOX

(codes as defined above)

General and specific requirements for ALC derivation
from APPENDIX A: QA/QC PROCEDURES

I.D.

Associated
with the
Guidelines
Requirement

General guidance:

P, as indicated above in
ECOTOX Minimum Data
Requirements

All data should be available in typed, dated, and signed hard
copy (publication, manuscript, letter, memorandum, etc.)
with enough supporting information to indicate that
acceptable test procedures were used and that the results are
probably reliable, (section II.B).

l.a

Information that is confidential or privileged or otherwise not
available for distribution should not be used, (section II.B).

l.b

Questionable data, whether published or unpublished, should
not be used. For example, a test result should usually be
rejected if it is from:

l.c

X, ECOTOX documents whether
the author(s) present information

A test that did not contain a control treatment.

l.c.i

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Indication of whether a
requirement was met in the BE
using ECOTOX

(codes as defined above)

General and specific requirements for ALC derivation
from APPENDIX A: QA/QC PROCEDURES

I.D.

Associated
with the
Guidelines
Requirement

about the type of control that
was used. Note: Many entries
exist in ECOTOX where
insufficient information was
reported to ascertain type of
control, but the toxicity value
was used to derive a criterion in
the corresponding AWQC
document

0, ECOTOX does not make
assessments on whether the
controls were satisfactory or
insufficient

A test in which too many organisms in the control treatment
died or showed signs of stress or disease

l.c.ii

P, ECOTOX does not provide
specific information on dilution
water, but does provide dilution
water chemistry values (pH,
hardness, salinity, etc).

A test in which distilled or deionized water was used as the
dilution water without addition of appropriate salts, (section
II.C)

l.c.iii

P, ECOTOX provides chemical
codes indicating grade and
formulation. Together with
chemical comments, relevant
information can be gleaned (e.g,
percentage active ingredient)

A result of a test on technical-grade material may be used if
appropriate, but a result of a test on a formulated mixture or
an emulsifiable concentrate of the test material should not be
used, (section II.D)

l.d

P, ECOTOX provides
information on exposure type
(flow-through, static, renewal,
diet, etc.) and chemical analysis
(measured, unmeasured, not
reported), but does provide
information on frequency of
measurements

For some highly volatile, hydrolyzable, or degradable
materials it is probably appropriate to use only results of
flow-through tests in which the concentrations of test
material in the test solutions were measured often enough
using acceptable analytical methods, (section II.E)

l.e

Data should be rejected if they were obtained using:

l.f

X, ECOTOX provides species
common and scientific names

Brine shrimp.

l.f.i

0, no habitat or geographical
information is provided in
ECOTOX for test species. EPA's
contractor determines residency
using specific internet searches;
databases made available to the
public, e.g., FishBase; and via
personal communication to
wildlife scientists and other
contacts

A species that does not have a reproducing wild population
in North America.

l.f.ii

P, ECOTOX does not provide
specific information on pre-
exposure. EPA's contractor,

Organisms that were previously exposed to substantial
concentrations of the test material or other contaminants,
(section II.F)

l.f.iii

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Indication of whether a
requirement was met in the BE
using ECOTOX

(codes as defined above)

General and specific requirements for ALC derivation
from APPENDIX A: QA/QC PROCEDURES

I.D.

Associated
with the
Guidelines
Requirement

does, however, screen test
location (natural field, lab) and
exposure type (lentic, lotic,
environmental)

Guidance specifically regarding results of acute tests:

0, ECOTOX does not report test
procedures

Acute toxicity tests should have been conducted using
acceptable procedures, (section IV.B) The following two
American Society for Testing and Materials (ASTM)
Standards are referenced as examples of acceptable
procedures:

2-g

0, ECOTOX does not report test
procedures

ASTM Standard E 729, Practice for Conducting Acute
Toxicity Tests with Fishes, Macroinvertebrates, and
Amphibians. (The title was later changed to "Standard
Guide for Conducting Acute Toxicity Tests on Test
Materials with Fishes, Macroinvertebrates, and
Amphibians".) Some of the most important items in Standard
E 729 include:

2.gi

P, ECOTOX provides chemical
codes indicating grade and
formulation. Together with
chemical comments, relevant
information can be gleaned (e.g,
percentage active ingredient)

(1). "The test material should be reagent-grade or better,
unless a test on a formulation, commercial product, or
technical-grade or use-grade material is specifically needed."
("Reagent-grade" is referenced to the American Chemical
Society specifications.) (section 9.1)

0, ECOTOX does not provide
specific information on dilution
water, but does provide control
type, including solvent controls.
Note, no information is provided
in ECOTOX regarding
concentration of solvent in the
test solution

(2). "If an organic solvent is used, it should be reagent-grade
or better and its concentration in any test solution must not
exceed 0.5 mL/L. A surfactant must not be used in the
preparation of a stock solution because it might affect the
form and toxicity of the test material in the test solutions."
(section 9.2.3)

0, ECOTOX does not provide
specific information on DO in
exposure chambers, but does
provide dilution water chemistry
values including DO

(3). "For static tests the concentration of dissolved oxygen in
each test chamber must be from 60 to 100 % of saturation
during the first 48 h of the test and must be between 40 and
100 % of saturation after 48 h. For renewal and flow-
through tests the concentration of dissolved oxygen in each
test chamber must be between 60 and 100 % of saturation at
all times during the test." (section 11.2.1)

0, ECOTOX does not report test
procedures

ASTM Standard E 724, Practice for Conducting Static Acute
Toxicity Tests with Larvae of Four Species of Bivalve
Molluscs. (The title was later changed to "Standard Guide
for Conducting Static Acute Toxicity Tests Starting with
Embryos of Four Species of Saltwater Bivalve Molluscs".)

2.g.ii

0, ECOTOX does not report test
procedures, but it does require
certain minimum Data
requirements, as noted above in
this Appendix.

General

192

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Indication of whether a
requirement was met in the BE
using ECOTOX

(codes as defined above)

General and specific requirements for ALC derivation
from APPENDIX A: QA/QC PROCEDURES

I.D.

Associated
with the
Guidelines
Requirement

judgment. Although written methodologies are very useful,
no such methodology can appropriately address all aspects of
toxicity tests, especially all organism-specific and all
chemical-specific aspects. In addition, written
methodologies often do not keep up with the newest
information that is available.

0, ECOTOX does not report
feeding of test organisms, only if
the exposure was oral via uptake
from food or by gavage

Except for tests using saltwater annelids and mysids, results
of acute tests during which the test organisms were fed
should not be used, unless data indicate that the food did not
affect the toxicity of the test material, (section II.C)

2.h

X, ECOTOX provides dilution
water chemistry values,
including organic carbon
concentration and type, if
reported

Results of acute tests conducted in unusual dilution water,
e.g., dilution water in which total organic carbon or
particulate matter exceeded 5 mg/L, should not be used,
unless a relationship is developed between acute toxicity and
organic carbon or particulate matter or unless data show that
organic carbon, particulate matter, etc., do not affect toxicity,
(section IV.D)

2.i

X, ECOTOX provides endpoint
codes, including LC50, EC50,
EC20, NOEC, LOEC, etc.

Acute values should be based on endpoints which reflect the
total severe acute adverse impact of the test material on the
organisms used in the test. Therefore, only the following
kinds of data on acute toxicity to aquatic animals should be
used:

X, ECOTOX provides endpoint
codes (LC50, EC50), test
duration, and organism life-stage
comments. ECOTOX does not
provide information on feeding
test organisms

(1). Tests with daphnids and other cladocerans should be
started with organisms less than 24 hours old and tests with
midges should be started with second- or third-instar larvae.
The result should be the 48-hr EC50 based on the percentage
of organisms immobilized plus percentage of organisms
killed. If such an EC50 is not available from a test, the 48-hr
LC50 should be used in place of the desired 48-hr EC50. An
EC50 or LC50 of longer than 48 hr can be used as long as
the animals were not fed and the control animals were
acceptable at the end of the test.

X, ECOTOX provides endpoint
(LC50, EC50) and effect codes
(mortality, growth,
reproduction); test duration; and
organism life-stage comments

(2). The result of a test with embryos and larvae of barnacles,
bivalve molluscs (clams, mussels, oysters, and scallops), sea
urchins, lobsters, crabs, shrimp, and abalones should be the
96-hr EC50 based on the percentage of organisms with
incompletely developed shells plus the percentage of
organisms killed. If such an EC50 is not available from a
test, the lower of the 96-hr EC50 based on the percentage of
organisms with incompletely developed shells and the 96-hr
LC50 should be used in place of the desired 96-hr EC50. If
the duration of the test was between 48 and 96-hr, the EC50
or LC50 at the end of the test should be used.

X, ECOTOX provides endpoint
(LC50, EC50) and effect codes
(mortality, growth,
reproduction); test duration; and
organism life-stage comments

(3). The acute values from tests with all other freshwater and
saltwater animal species and older life stages of barnacles,
bivalve molluscs, sea urchins, lobsters, crabs, shrimps, and
abalones should be the 96-hr EC50 based on the percentage
of organisms exhibiting loss of equilibrium plus the

193

-------
Indication of whether a
requirement was met in the BE
using ECOTOX

(codes as defined above)

General and specific requirements for ALC derivation
from APPENDIX A: QA/QC PROCEDURES

I.D.

Associated
with the
Guidelines
Requirement

percentage of organisms immobilized plus the percentage of
organisms killed. If such an EC50 is not available from a
test, the 96-hr LC50 should be used in place of the desired
96-hr EC50.

X, ECOTOX provides species
common and scientific names, as
well as test duration

(4). Tests with single-celled organisms are not considered
acute tests, even if the duration was 96 hours or less.

X, ECOTOX provides result
qualifiers such as ">" and "<"
values

(5). If the tests were conducted properly, acute values
reported as "greater than" values and those which are above
the solubility of the test material should be used, because
rejection of such acute values would unnecessarily lower the
FAV by eliminating acute values for resistant species,
(section IV.E)

X, see above. Data can
downloaded from ECOTOX and
sorted by species name, test
duration, endpoint, effect, etc.

The agreement of the data within and between species should
be considered. Acute values that appear to be questionable
in comparison with other acute and chronic data for the same
species and for other species in the same genus probably
should not be used in the calculation of a Species Mean
Acute Value (SMAV). For example, if the acute values
available for a species or genus differ by more than a factor
of 10, some or all of the values probably should not be used
in calculations, (section IV.H)

2.k

Guidance specifically regarding results of chronic tests:

Chronic values should be based on results of flow-through
(except renewal is acceptable for daphnids) chronic tests in
which the concentrations of test material in the test solutions
were properly measured at appropriate times during the test,
(section VLB)

3.1

0, ECOTOX does not make
assessments of whether the
controls were satisfactory or
insufficient

Results of chronic tests in which survival, growth, or
reproduction in the control treatment was unacceptably low
should not be used. The limits of acceptability will depend
on the species, (section VI.C)

3.m

X, ECOTOX provides dilution
water chemistry values,
including organic carbon
concentration and type, if
reported. ECOTOX does not
report on the relationship
between chronic toxicity and
organic carbon concentration

Results of chronic tests conducted in unusual dilution water,
e.g., dilution water in which total organic carbon or
particulate matter exceeded 5 mg/L, should not be used,
unless a relationship is developed between chronic toxicity
and organic carbon or particulate matter or unless data show
that organic carbon, particulate matter, etc., do not affect
toxicity, (section VI.D)

3.n

X, ECOTOX provides endpoint
(NOEC, LOEC, EC20) and
effect codes (mortality, growth,
reproduction)

Chronic values should be based on endpoints and lengths of
exposure appropriate to the species. Therefore, only data on
chronic toxicity to aquatic animals that satisfy the species-
specific requirements given in sections VI.E.l, VI.E.2, and
VI.E.3 should be used.

3.o

194

-------
Indication of whether a
requirement was met in the BE
using ECOTOX

(codes as defined above)

General and specific requirements for ALC derivation
from APPENDIX A: QA/QC PROCEDURES

I.D.

Associated
with the
Guidelines
Requirement

Guidance regarding other possible uses of results of toxicity
tests using aquatic animals:

P, ECOTOX provides chemical
codes indicating grade and
formulation, but no habitat or
geographical information is
provided in ECOTOX for test
species. EPA's contractor
determines residency using
specific internet searches;
databases made available to the
public, e.g., FishBase; and via
personal communication to
wildlife scientists and other
contacts

Questionable data, data on formulated mixtures and
emulsifiable concentrates, and data obtained with non-
resident species or previously exposed organisms may be
used to provide auxiliary information but should not be used
in the derivation of criteria, (section II.F)

X, ECOTOX provides endpoint
(LC50, EC50) and effect codes
(mortality, growth,
reproduction); test duration;
species name and organism life-
stage comments; as well as
exposure type and chemical
analysis (measured, unmeasured,
not reported)

Pertinent information that could not be used in earlier
sections might be available concerning adverse effects on
aquatic organisms and their uses. The most important of
these are data on cumulative and delayed toxicity, flavor
impairment, reduction in survival, growth, or reproduction,
or any other adverse effect that has been shown to be
biologically important. Especially important are data for
species for which no other data are available. Data from
behavioral, biochemical, physiological, microcosm, and field
studies might also be available. Data might be available
from tests conducted in unusual dilution water, from chronic
tests in which the concentrations were not measured, from
tests with previously exposed organisms, and from tests on
formulated mixtures or emulsifiable concentrates. Such data
might affect a criterion if the data were obtained with an
important species, the test concentrations were measured,
and the endpoint was biologically important, (section X)

X, ECOTOX provides acute
toxicity and bioaccumulation
results for aquatic plants and
animals, as well as for aquatic-
dependent wildlife

The Criterion Continuous Concentration (CCC) is equal to
the lowest of the Final Chronic Value (FCV), Final Plant
Value (FPV), and Final Residue Value (FRV), unless other
data show that a lower value should be used, (section XI. C)

4.r

0, ECOTOX does not provide
data subject to interpretation,
only what has been reported by
the author(s)

Are any of the other data important? (section XII. A. 14)

4.s

X, ECOTOX requires certain
Minimum Data Requirements as
indicated above, plus many
additional details and results
sufficient to ascertain sound
scientific integrity

On the basis of all available pertinent laboratory and field
information, determine if the criterion is consistent with
sound scientific information. If it is not, another criterion,
either higher or lower, should be derived using appropriate
modifications of these Guidelines, (section XII.B)

4.t

195

-------
Indication of whether a
requirement was met in the BE
using ECOTOX

(codes as defined above)

General and specific requirements for ALC derivation
from APPENDIX A: QA/QC PROCEDURES

I.D.

Associated
with the
Guidelines
Requirement

The following is a list of common reasons why the results of
some toxicity tests should not be used. Most of these reasons
can be considered to be based on items "a" through "o" listed
above.

General:

X, ECOTOX excludes secondary
data sources because they do not
meet the minimum data
requirements for inclusion into
the database

The document is a secondary publication of the test result.

X, explained elsewhere

The test procedures, test material, dilution water, and/or
results were not adequately described.

0, explained elsewhere

The test species is not resident in North America.

0, explained elsewhere

The test species was not obtained in North America and was
not identified well enough to determine whether it is resident
in North America.

X, ECOTOX provides species
common and scientific names
when reported, or to the lowest
identifiable taxon reported, i.e.,
ECOTOX does include data for
broad taxonomic groups such as
mayflies.

The test organisms were not identified specifically, for
example, "crayfish" or "minnows."

P, ECOTOX does not normally
provide information on diseased
or stressed organisms, but does
provide an organism comment
which may contain such
information

There is reason to believe that the test organisms were
possibly stressed by disease or parasites.

0, ECOTOX does not report
such specific or unique exposure
conditions

The test organisms were exposed to elevated concentrations
of the test material before the test and/or the control
organisms contained high concentrations of the test material.

0, ECOTOX does not report
such specific or unique exposure
conditions

The test organisms were obtained from a sewage oxidation
pond.

0, explained elsewhere

By the end of the test, the test organisms had not been fed for
too long a period of time.

0, ECOTOX does not report
such specific or unique exposure
conditions

The water quality varied too much during the test.

X, explained elsewhere

The test was conducted with brine shrimp, which are from a
unique saltwater environment.

X, ECOTOX only reports results
based on the exposure of live,
intact organisms

The exposed biological material was an enzyme, excised or
homogenized tissue, tissue extract, plasma, or cell culture.

0, ECOTOX does not report
such specific or unique exposure
conditions

The test organisms were not acclimated to the dilution water
for a sufficiently long time period.

X, ECOTOX reports exposure

The test organisms were exposed to the test material via

196

-------
Indication of whether a
requirement was met in the BE
using ECOTOX

(codes as defined above)

General and specific requirements for ALC derivation
from APPENDIX A: QA/QC PROCEDURES

I.D.

Associated
with the
Guidelines
Requirement

type, including gavage, injection
and oral uptake via the diet

gavage, injection, or food.

0, ECOTOX does not report
such specific or unique exposure
conditions

There is reason to believe that the test organisms were
probably crowded during the test.

0, ECOTOX does not report
such unique test results

The test organisms reproduced during an acute test, and the
new individuals could not be distinguished from the original
test individuals at the end of the test.

P, ECOTOX provides chemical
codes indicating grade and
formulation. Data from
sediment-only exposures must
provide concurrent pore water
concentrations

The test material was a component of a mixture, effluent, fly
ash, sediment, drilling mud, sludge, or formulation.

0, ECOTOX does not report
such specific or unique exposure
conditions, but chemical CAS
number is included

In a test on zinc, the dilution water contained a phosphate
buffer.

0, ECOTOX does provide
chemical analysis (measured,
unmeasured) and chemical
comment, however, data on
acceptability of analytical
chemistry measurements is not

The test material was chlorine and it was not measured
acceptably during the test.

X, ECOTOX only includes data
from sediment exposures that
also provide concurrent pore
water concentrations

The test chamber contained sediment.

P, ECOTOX provides chemical
analysis (measured, unmeasured)
and chemical comment, but not
exposure container

The test was conducted in plastic test chambers without
measurement of the test material.

X, ECOTOX provides exposure
location (natural field, lab) and
exposure type (lentic, lotic,
environmental), as well as
chemical analysis (measured,
unmeasured)

The test was a field study and the concentration of test
material was not measured adequately.

P, ECOTOX only provides
information on chemical analysis
(measured, unmeasured) and a
chemical comment

A known volume of stock solution was placed on a wall of
the test chamber and evaporated and then dilution water was
placed in the test chamber; the investigators assumed that all
of the test material dissolved in the dilution water, but the
concentrations of the test material in the test solutions were
not measured.

X, a taxonomically verifiable test
species (or group of species) is
required

The test only studied metabolism of the test material.

X, ECOTOX provides well-

The only effects studied were biochemical, histological,

197

-------
Indication of whether a
requirement was met in the BE
using ECOTOX

(codes as defined above)

General and specific requirements for ALC derivation
from APPENDIX A: QA/QC PROCEDURES

I.D.

Associated
with the
Guidelines
Requirement

defined effect codes, including
biochemical, histological and/or
physiological

and/or physiological.

0, explained elsewhere

The data concerned the selection, adaptation, or acclimation
of organisms for increased resistance to the test material.

0, explained elsewhere

The percent survival in the control treatment was too low.

0, explained elsewhere

The concentration of solvent in some or all of the test
solutions was too high.

P, ECOTOX provides test
location, but not specifically
microcosm tests

The study was a microcosm study.

0, explained elsewhere

The concentration of test material fluctuated too much during
the exposure.

0, ECOTOX does not report
such specific or unique exposure
conditions

Too few test organisms were used in the test.

0, ECOTOX only provides
information on chemical analysis
(measured, unmeasured) and a
chemical comment; not dilution
factors

The dilution factor was ten.

X, explained elsewhere

There was no control treatment.

X, explained elsewhere

The pH was below 6.5.

0, explained elsewhere

The dilution water was chlorinated or "tap" water.

0, explained elsewhere

The dilution water contained an excessive amount of a
chelating agent such as EDTA or other organic matter.

P, ECOTOX provides test
location, including natural field
or lab

The acceptability of the dilution water was questionable
because of its origin or content.

0, explained elsewhere

The dilution water was distilled or deionized water without
the addition of appropriate salts.

X, ECOTOX provides a mean,
minimum and maximum test
temperature, if reported

The measured test temperature fluctuated too much.

X, ECOTOX requires observed
biological responses related to an
exposure to a single chemical

Neither raw data nor a clearly defined endpoint was reported.

X, certain minimum data
requirements must be met as
indicated above

The results were not adequately presented or could not be
interpreted.

0, ECOTOX does not provide
data subject to interpretation,
only what has been reported by
the author(s)

The results were only presented graphically.

X, explained elsewhere

The test was a chronic test and the concentration of test
material was not measured.

198

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199

-------
Attachment 1. Guidance for marking publications "applicable" or "not applicable" to the
ECOTOX Database effort

Some publications obtained from literature searches do not meet minimum data
requirements for the ECOTOX database. For publications identified using an electronic
literature search method, the citation and abstract information are downloaded
electronically into a bibliographic file. Each citation and abstract is reviewed to
determine if the publication is potentially applicable to the ECOTOX database. When a
publication is identified as not applicable to ECOTOX, the citation entry is annotated
with the reason the study was excluded (see list of terms below), and a copy of the
publication is not acquired. Publications identified as potentially applicable to the
ECOTOX database are acquired. As publications are received, the ECOTOX eligibility
criteria are applied, and citations for rejected studies are annotated with the reason for
exclusion. For the most part, non-applicable publications are not retained, but some non-
applicable publications may be identified as useful to the ECOTOX database effort (e.g.,
review publications, methods publications), and these are assigned an ECOTOX
reference number and retained in the ECOTOX literature holdings. All citations that
have been excluded from the ECOTOX database are retained electronically in a
Reference Manager file. Procedures used in literature searches and acquisition as they
relate to the ECOTOX database can be found at: http://lester.dul.epa.g0v/qa/s0p/#DAM.

Keyword

Usage

ABSTRACT

study results published as an abstract

BACTERIA

bacteria and microbes - for microbes, enter bacteria as keyword,
Microbe in Reference Manager field 6 (Notes)

BIOLOGICAL
TOXICANT

general biological toxicants including venoms, fungal toxins, Bacillus
thuringiensis, and other plant, animal or microbial extracts or toxins
not Durified

(Purified single chemicals (with CAS numbers) of biological origin
may be applicable. See the following websites for examples of
applicable toxicants with biological origin:

www.hort.purdue.edu/newcrop/proceedingsl990/vl-511.html and
www.epa.gov/pesticides/biopesticides/ingredients/index.htm).

CAS#

UNAVAILABLE

chemical is not verifiable, no CAS # is available

DRUG

testing for drug effects and side-effects on humans (drugs used as
environmental toxicants are applicable)

EFFLUENT

includes sewage and polluted runoff

FATE

chemical distribution, metabolism

200

-------
HUMAN HEALTH

studies with human subjects or with surrogate animal subjects for
human health risk assessment

INCIDENT

reports of animal deaths by poison, etc.; lacks usable concentration
and/or duration

INCOMPLETE
CITATION

citation is not complete; order status ARCHIVE

INCORRECT
CITATION

citation is wrong; order status ARCHIVE

IN VITRO

in vitro studies, including exposure of cell cultures and excised tissues

METABOLISM

what happens to the chemical rather than to the organism

METHODS

no usable toxicity tests; describes methods for conducting tests,
purification or determination of chemicals, etc. Some methods
publications are ordered for the ECOTOX methods information file
(METHFILE); documentation provided for toxicology test methods,
experimental design, statistical methods, standard terminology, and
recently developed test methods. Methfile publications are chosen to
support development and interpretation of coding guidelines and to
assist in reviewer training.

MICROTOX

Microtox tests; studies conducted with bacteria

MIXTURE

no single chemical tests reported

MODELING

modeling only, no new organism exposure data; modeling studies may
report original toxicity tests performed as comparisons or as a basis for
extrapolation, if so, publications are ordered

201

-------
NO CONC

no usable dose or concentration reported after examination of the
entire publication; includes lead shot studies lacking dose information
and which report only the number of pellets. Concentrations reported
in log units only are not coded.

NO DURATION

no duration reported (entire publication examined)

NO EFFECT

no organism effect reported, including water quality studies with no
effect on organisms reported

NO QUANTIFIABLE
TOXICITY RESULT

no specific data values to code, authors used general statements such
as "the animals decreased in weight", used only for terrestrial
publications

NO SOURCE

source of publication undetermined; order status ARCHIVE

NO SPECIES

-no organism present or tested
-exposure of a dead organism
-reviewer unable to verify species

NO TOX DATA

- chemicals in water, sediment or soil without organism effect data

- ecological interactions with no toxicity tests

- food studies - chemicals found in foods, food safety studies

- genetics studies - including recombinant DNA and mutant strains

- physiology - effects of the level of chemicals biologically present in
an organism, including hormones and vitamins

- risk assessment publications (related to regulation and legislation)

NO TOXICANT

no chemical toxicant

- includes ambient air component chemicals (ozone, CO2, SO2) and
pollution

- includes vapor studies where the toxicant is delivered through
inhalation/respiration

-other ambient conditions including changes in conditions (other than
chemical addition), including radioactivity, ultraviolet light (UV),
temperature, pH, salinity, dissolved oxygen (DO), or other water, air
or soil parameters

NON-ENGLISH

publication in a language other than English - (these publications
receive ECOREF numbers UNLESS a second keyword is assigned);
AUTH orders only (not ILL), if not received in 6 months, citations
should be ARCHIVE

NUTRIENT

in situ chemicals tested as nutrients

202

-------
OIL

only report toxic effects associated with exposure to oil and/or
petroleum products

PUBL AS

publication was published in another journal or book, ECOREF
number of other publication listed in Reference Manager citation
Ex. PUBL AS ECOREF #####

QSAR

Quantitative Structure Activity Relationships; not primary source of
data; bibliography skimmed to identify empirical studies

REVIEW

all toxicity tests reported elsewhere; REVIEW bibliography may be
skimmed to identify relevant citations

SEDIMENT CONC

chemical concentration reported in sediment only (see applicable
conditions)

SURVEY

measured chemical present, but lacking quantification of exposure;
lacks usable concentration and/or duration

VIRUS

virus used as test organism

YEAST

yeast used as test organism

203

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Attachment 2 - CAS Numbers for Appropriate Forms of Select Metals

(Note: In general, the chloride, nitrate, and sulfate salts of most metals are acceptable, but
metal mixtures are excluded as are organic metal salts)

Chemical

Chemical Names

CAS Registry Numbers

Abbrev

arsenic, arsenite, arsenate

7440382 Arsenic

7631892 Arsenic acid, Sodium salt

7645252 Arsenic acid, Lead salt

7778394 Arsenic acid (H3As04)

7778430 Arsenic acid, Disodium salt

7784341 Arsenous trichloride

7784409 Arsenic acid, Lead(2+) salt (1:1)

7784443 Arsenic acid, Diammonium salt

7784465 Arsenenous acid, Sodium salt

10048950 Arsenic acid, Disodium salt, Heptahydrate

15120179 Sodium arsenate (NaAs03)

13464385 Sodium arsenate (Na3As04)

7631892 Sodium arsenate (generic form)

13466063 Sodium arsenite (Na2HAs03)

13464374 Sodium arsenite (Na3As03)

cadmium

7440439 Cadmium
543908 Cadmium acetate
7789426 Cadmium bromide
10108642 Cadmium chloride
7790809 Cadmium iodide (CdCI2)

10022681 Nitric acid, Cadmium salt tetrahydrate
10325947 Cadmium nitrate
10124364 Cadmium sulfate
7790785 Cadmium chloride hydrate
7790843 Cadmium sulfate 8/3H20
89759808 Cadmium acetate hydrate
34330648 Cadmium chloride hydrate

lead

7439921 Lead

301042 Lead acetate

7758954 Lead chloride

10099748 Lead nitrate

7446142 Lead sulfate

546678 Acetic acid, Lead (4+) salt

13826658 Nitrous acid, Lead (2+) salt

204

-------
Chemical
Abbrev

Chemical Names

CAS Registry Numbers

nickel

373024 Acetic acid, Nickel (2+) salt
7791200 Nickel chloride hexahydrate
69098153 Nickel chloride hydrate
15060625 Nickel (II) selenate
7440020 Nickel
7718549 Nickelous chloride
13138459 Nickelous nitrate
7786814 Sulfuric acid, nickel(2+)salt (1:1)
10101970 Nickel sulfate hexahydrate
373024 Nickelous acetate tetrahydrate
13478007 Nickel (II) chloride hydrate

silver

506649 Silver cyanide
563633 Acetic acid, Silver (1+) salt
7440224 Silver
7761888 Silver nitrate
7783906 Silver chloride
7783962 Silver iodide
10294265 Silver sulfate

zinc

7440666 Zinc

7646857 Zinc chloride

7779886 Zinc nitrate

7733020 Zinc sulfate

557346 Zinc acetate

1314223 Zinc peroxide

1314847 Zinc phosphide

7446200 Zinc sulfate heptahydrate

7699458 Zinc bromide

10139476 Zinc iodide

13597449 Sulfurous acid, Zinc salt (1:1)

10196186 Zinc nitrate hydrate

5970456 Zinc acetate dihydrate

205

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Attachment 3. BE Data Rejection Code List (from approved SHPD WA 2-18 QAPP)

(Note: This list is meant to cover the majority of test conditions for which
ecotoxicological data used in the BE might be rejected from use in ALC documents. Not
all codes will apply in this case, and new codes might be added or modified as needed).

ABIOTIC FACTOR
(AF)

Studies where an abiotic factor such as total water hardness, pH, or
temperature are not reported for a criteria for which this information is
necessary to derive a Species Mean Acute or Chronic Value, i.e.,
several freshwater metals, pentachlorophenol, ammonia.

ACELLULAR
(Ace)

Studies of acellular organisms (protozoa) and yeast.

BACTERIA
(Bact)

Studies describing only the results on bacteria.

BIOMARKER
(Biom)

Studies reporting results for a biomarker having no reported
association with a biologically significant adverse effect (survival,
growth, or reproduction of an individual or population) and an
exposure dose (or concentration).

CONTROL
(Con)

Studies where control mortality is insufficient or unsatisfactory, i.e.,
where survival is less than 90% in acute tests or 80% in chronic tests;
or where no control is used.

DETAIL
(Det)

Insufficient detail regarding test methodology or statistical analysis.

DURATION
(Dur)

Laboratory and field studies where duration of exposure is
inappropriate (e.g., too short) for the type of test (i.e., acute or
chronic), or was not reported or could not be easily estimated.

EFFLUENT
(Efflu)

Studies reporting only effects of effluent, sewage, or polluted runoff
where individual pollutants are not measured.

EFFECT
(Eff)

Studies where the biologically significant adverse effect was not
survival, growth, or reproduction of an individual or population.

ENDPOINT
(UEndp)

Studies reported in ECOTOX where an endpoint (LC50, EC50,

NOEC, LOEC, MATC, EC20, etc.) was not provided, where none of
the concentrations tested in a chronic test were deleterious (no LOEC);
or where all concentrations tested in a chronic test caused a
statistically significant adverse effect (no NOEC).

FIELD
(Field)

Chronic, long-term studies conducted in a field setting (stream
segment, pond, etc.) where source/dilution water is not characterized
for other possible contaminants.

FORMULATION
(Form)

Studies where the chemical is a primary ingredient in a commercial
formulation, e.g., biocide, fertilizer, etc.

206

-------
IN VITRO
(In Vit)

In vitro studies, including only exposure of the chemical to cell
cultures and excised tissues and not related to whole organism toxicity.

LETHAL TIME
(LT)

Laboratory studies reporting only lethal time to mortality, except
under special conditions (no other applicable information is available
for species pivotal in making a finding).

NO DOSE or CONC
(No Dose or Cone)

Studies with too few concentrations to establish a dose-response, or no
usable dose or concentration reported in either primary or sister
article(s), except under special conditions (no other applicable
information is available for species pivotal in making a finding).

NOMINAL
(Nom)

Chronic studies where test concentrations were not measured.

NON-RESIDENT
(NonRes)

Species that are not resident to North America, or where there is no
reported evidence of their reproducing naturally in North America.

NO ORGANISM
(No Org)

Laboratory and field studies where no one organism is studied (e.g.,
periphyton community) or where no scientific/common name is given
in either a primary or sister article(s).

PURITY
(Pur)

Studies where the chemical purity of the toxicant was less than 80%
pure (active ingredient).

ROUTE OF

EXPOSURE

(RouExp)

Dietary or un-natural exposure routes for aquatic chemicals, e.g.,
injection, spray, inhalation.

TOXICANT
(Tox)

Inappropriate form of toxicant used or none identified in a laboratory
or field study. Note: Inappropriate form includes mixtures.

UNACCEPTABLE

CHRONIC

(UChron)

Chronic studies which were not based on flow-through exposures
(exception for cladocerans and other small, planktonic organisms
where test water is continuously renewed) and/or where test
concentrations were not measured.

UNUSUAL
DILUTION WATER
(Dilut)

Laboratory or field studies where the dilution water contained unusual
amounts or ratios of inorganic ions or was without addition of
appropriate salts (i.e., distilled or de-ionized water).

VARIABLE
EXPOSURE
(VarExp)

Excessive variability in contaminant concentrations during the
exposure period.

WATER QUALITY
(WatQual)

Studies where the measured test pH is below 6 or greater than 9, where
dissolved oxygen was less than 40% saturation for any length of time,
or where total or dissolved organic carbon is greater than 5 mg/L.

207

-------
Appendix C Cadmium (freshwater)
Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Abbasi, S.A., and R. Soni. 1986. An Examination of
Environmentally Safe Levels of Zinc (II), Cadmium (II) and
Lead (II) with Reference to Impact on Channelfish Nuria
denricus. Environ.Pollut.Ser.A Ecol.Biol. 40(1):37-51.

11078

AF, Dur, Con

Abdelghani, A.A., Y.V. Pramar, T.K. Mandal, P.B.
Tchounwou, and L. Heyer. 1995. Levels and Toxicities of
Selected Inorganic and Organic Contaminants in a Swamp
Environment. J.Environ.Sci.Health Part B 30(5):717-731.

45166

Abel, P.D., and S.E. Papoutsoglou. 1986. Lethal Toxicity of
Cadmium to Cyprinus carpio and Tilapia aurea.

Bui I. Environ. Contam. Toxicol. 37(3):382-386.

11925

UEndp

Abel, P.D., and S.M. Garner. 1986. Comparisons of Median
Survival Times and Median Lethal Exposure Times for
Gammarus pulex Exposed to Cadmium, Permethrin and
Cyanide. Water Res. 20(5):579-582.

7616

AF, UEndp, Dur,
Con

Abel, T., and F. Baerlocher. 1988. Uptake of Cadmium by
Gammarus fossarum (Amphipoda) From Food and Water.
J.AppI.Ecol. 25(1):223-231.

6805

NonRes

Abel, T.H., and F. Barlocher. 1984. Effects of Cadmium on
Aquatic Hyphomycetes. Appl.Environ.Microbiol. 48(2):245-
251.

11030

Plant, Dur, Con

Abraham, T.J., K.Y.M. Salih, and J. Chacko. 1986. Effects
of Heavy Metals on the Filtration Rate of Bivalve Villorita
cyprinoides (Hanley) Var. Cochinensis. Indian J.Mar.Sci.
15(3): 195-196.

12315

AF, Con

208

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Achazi, R.K., G. Chroszcz, C. Duker, M. Henneken, B.
Rothe, K. Schaub, and 1. Steudel. 1995. The Effect of
Fluoranthene (Fla), Benzo(a)pyrene (BaP) and Cadmium
(Cd) upon Survival Rate and Life Cycle Parameter of Two
Terrestrial Annelids in Laboratory Test Systems.
Newslett.Enchytraeidae 4:7-14.

58146

Al Akel, A.S., M.J.K. Shamsi, H.F. Al Kahem, M.A.
Chaudhary, and Z. Ahmad. 1988. Effect of Cadmium on the
Cichlid Fish, Oreochromis niloticus: Behavioural and
Physiological Responses. J.Univ.Kuwait Sci. 15(2):341-345.

130

AF, Con

Alazemi, B.M., J.W. Lewis, and E.B. Andrews. 1996. Gill
Damage in the Freshwater Fish Gnathonemus petersii
(Family: Mormyridae) Exposed to Selected Pollutants: An
Ultrastructural Study. Environ.Technol. 17(3):225-238.

19563

UEndp, Dur

Albergoni, V., and A. Viola. 1995. Effects of Cadmium on
Catfish, Ictalurus melas, Humoral Immune Response. Fish
Shellfish Immunol. 5(2):89-95.

18698

AF, Uendp

Alkahem, H.F.. 1993. Ethological Responses and Changes
in Hemoglobin and Glycogen Content of the Common Carp,
Cyprinus carpio, Exposed to Cadmium. Asian Fish.Sci.
6(1):81-90.

4234

Con

Alkahem, H.F.. 1995. Acute and Sublethal Exposure of
Catfish (Clarias gariepinus) to Cadmium Choride: Survival,
Behavioural and Physiological Responses. Pak.J.Zool.
27(1):33-37.

18022

NonRes

Allen, P.. 1993. Accumulation Profiles of Cadmium and
Their Modification by Interaction with Lead and Mercury in
the Edible Tissues of Oreochromis aureus. Fresenius
Environ.Bull. 2(12):745-751.

16695

AF, UEndp

Allen, P.. 1995. Chronic Accumulation of Cadmium in the
Edible Tissues of Oreochromis aureus (Steindachner):
Modification by Mercury and Lead.
Arch.Environ.Contam.Toxicol. 29(1):8-14.

14920

AF, UEndp

209

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Allen, P.. 1995. Accumulation Profiles of Lead and
Cadmium in the Edible Tissues of Oreochromis aureus
During Acute Exposure. J.Fish Biol. 47(4):559-568.

16322

UEndp

Allen, Y., P. Calow, and D.J. Baird. 1995. A Mechanistic
Model of Contaminant-Induced Feeding Inhibition in
Daphnia magna. Environ.Toxicol.Chem. 14(9): 1625-1630.

10203

Acute test with
adults

Table 6 in 2001 ALC
document because
<24 h neonates
preferred

Anadu, D.I., G.A. Chapman, L.R. Curtis, and R.A. Tubb.
1989. Effect of Zinc Exposure on Subsequent Acute
Tolerance to Heavy Metals in Rainbow Trout.

Bui I. Environ. Contam. Toxicol. 43(3):329-336.

791

See note

Not used in ALC
document because
animals acclimated or
exhibited increased
resistance to
cadmium

Andaya, A.A., and E.U. Gotopeng. 1982. Cadmium Toxicity
and Uptake in Tilapia nilotica. Kalikasan (Philipp.J.Biol.)
11(2/3):390-318.

12458

AF, Dur

Anderson, B.G.. 1948. The Apparent Thresholds of Toxicity
to Daphnia magna for Chlorides of Various Metals when
Added to Lake Erie Water. Trans.Am.Fish.Soc. 78:96-113.

2054

AF, Dur

Anderson, R.L., C.T. Walbridge, and J.T. Fiandt. 1980.
Survival and Growth of Tanytarsus dissimilis
(Chironomidae) Exposed to Copper, Cadmium, Zinc, and
Lead. Arch.Environ.Contam.Toxicol. 9(3):329-335 (Author
Communication Used).

5249

Con

Angadi, S.B., and P. Mathad. 1998. Effect of Copper,
Cadmium and Mercury on the Morphological, Physiological
and Biochemical Characteristics of Scenedesmus
quadricauda (Turp.) de Breb. J.Environ.Biol. 19(2):119-124.

19132

Plant, AF, UEndp

Angadi, S.B., S. Hiremath, and S. Pujari. 1996. Toxicity of
Copper, Nickel, Manganese and Cadmium on
Cyanobacterium Hapalosiphon stuhlmannii. J.Environ.Biol.
17(2): 107-113.

17771

Plant, AF, UEndp

210

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Annune, P.A., and T.T. lyaniwura. 1993. Accumulation of
Two Trace Metals in Tissues of Freshwater Fishes,
Oreochromis niloticus and Clarias gariepinus. J.Aquat.Food
Product Technol. 2(3):5-18.

16167

AF, UEndp

Annune, P.A., S.O. Ebele, and A.A. Oladimeji. 1994. Acute
Toxicity of Cadmium to Juveniles of Clarias gariepinus
(Teugels) and Oreochromis niloticus (Trewavas).
J.Environ.Sci.Health A29(7):1357-1365.

17299

NonRes

Aoki, Y., S. Hatakeyama, N. Kobayashi, Y. Sumi, T. Suzuki,
and K.T. Suzuki. 1989. Comparison of Cadmium-Binding
Protein Induction Among Mayfly Larvae of Heavy Metal
Resistant (Baetis thermicus) and Susceptible Species (B..
Comp.Biochem.Physiol.C 93(2):345-347.

2390

AF, UEndp

Aoyama, I., and H. Okamura. 1993. Interactive Toxic Effect
and Bioconcentration Between Cadmium and Chromium
Using Continuous Algal Culture. Environ.Toxicol.Water
Qual. 8(3):255-269.

9948

Plant, AF, UEndp

Azeez, P.A., and D.K. Banerjee. 1986. Effect of Copper and
Cadmium on Carbon Assimilation and Uptake of Metals by
Algae. Toxicol.Environ.Chem. 12(1-2):77-86.

12317

Plant, AF, UEndp,
Con

Back, H.. 1983. Interactions, Uptake and Distribution of
Barium, Cadmium, Lead and Zinc in Tubificid Worms
(Annelida, Oligochaeta). In: 4th Int.Conf.on Heavy Metals in
the Environment, Heidelberg, Vol.1, Sept.1983, CEP
Consultants Ltd., Edinburgh, U.K. :370-371.

11865

AF, UEndp

Back, H.. 1990. Epidermal Uptake of Pb, Cd, and Zn in
Tubificid Worms. Oecologia 85(2):226-232.

20568

AF, UEndp

Bailey, H.C., and D.H.W. Liu. 1980. Lumbriculus variegatus,
a Benthic Oligochaete, As a Bioassay Organism. In:
J.C.Eaton, P.R.Parrish, and A.C.Hendricks (Eds.), Aquatic
Toxicology and Hazard Assessment, 3rd Symposium,

ASTM STP 707, Philadelphia, PA :205-215.

6502

Dur

211

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Baillieul, M., and R. Blust. 1999. Analysis of the Swimming
Velocity of Cadmium-Stressed Daphnia magna.
Aquat.Toxicol. 44:245-254.

20334

AF, Uendp, Eff

Baird, D.J., I. Barber, and P. Calow. 1990. Clonal Variation
in General Responses of Daphnia magna Straus to Toxic
Stress. I. Chronic Life-History Effects. Funct.Ecol. 4(3):399-
407.

3711

AF, UEndp

Ball, I.R.. 1967. Short Communication: The Toxicity of
Cadmium to Rainbow Trout (Salmo gairnderii Richardson).
Water Res. 1:805-806.

4252

Con

Balogh, K., and J. Salanki. 1984. The Dynamics of Mercury
and Cadmium Uptake Into Different Organs of Anodonta
cygnea L. Water Res. 18(11 ):1381-1387.

10766

AF, UEndp, Con,
Eff

Banerjee, V., and K. Kumari. 1988. Effect of Zinc, Mercury
and Cadmium on Erythrocyte and Related Parameters in
the Fish Anabas testudineus. Environ.Ecol. 6(3):737-739.

803

AF, Dur, Con

Barata, C., and D.J. Baird. 2000. Determining the
Ecotoxicological Mode of Action of Chemicals from
Measurements Made on Individuals: Results from Instar-
Based Tests with Daphnia magna Straus. Aquat.Toxicol.
48(2/3):195-209.

47311

AF, Eff

Barber, I., D.J. Baird, and P. Calow. 1994. Effect of
Cadmium and Ration Level on Oxygen Consumption, RNA
Concentration and RNA-DNA Ratio in Two Clones of
Daphnia magna Straus. Aquat.Toxicol. 30(3):249-258.

16639

AF, UEndp, Eff

Bartlett, L„ F.W. Rabe, and W.H. Funk. 1974. Effects of
Copper, Zinc and Cadmium on Selanastrum capricornutum.
Water Res. 8(3):179-186.

2254

UEndp

Battaglini, P., G. Andreozzi, R. Antonucci, N. Arcamone, P.
De Girolamo, L. Ferrara, and G. Gargiulo. 1993. The Effects
of Cadmium on the Gills of the Goldfish Carassius auratus
L.: Metal Uptake and Histochemical Changes.
Comp.Biochem. Physiol. C 104(2):239-247.

6879

UEndp, Eff

212

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Baudouin, M.F., and P. Scoppa. 1974. Acute Toxicity of
Various Metals to Freshwater Zooplankton.
Bull.Environ.Contam.Toxicol. 12(6):745-751.

5339

AF, Eff, Dur

Baudrimont, M., J. Metivaud, R. Maury-Brachet, F. Ribeyre,
and A. Boudou. 1997. Bioaccumulation and Metallothionein
Response in the Asiatic Clam (Corbicula fluminea) After
Experimental Exposure to Cadmium and Inorganic Mercury.
Environ. Toxicol. Chem. 16(10):2096-2105.

18269

AF, UEndp

Beach, M.J., and D. Pascoe. 1998. The Role of Hydra
vulgaris (Pallas) in Assessing the Toxicity of Freshwater
Pollutants. Water Res. 32(1): 101-106.

18616

Dur

Beattie, J.H., and D. Pascoe. 1978. Cadmium Uptake by
Rainbow Trout, Salmo gairdneri Eggs and Alevins. J.Fish
Biol. 13(5):631-637.

15554

UEndp

Beena, S., and S. Viswaranjan. 1987. Effect of Cadmium
and Mercury on the Hematological Parameters of the Fish
Cyprinus carpio. Environ.Ecol. 5(4):726-730.

7734

AF, UEndp, Eff, Dur

Belanger, S.E., and D.S. Cherry. 1990. Interacting Effects of
pH Acclimation, pH, and Heavy Metals on Acute and
Chronic Toxicity to Ceriodaphnia dubia (Cladocera).
J.Crustac.Biol. 10(2):225-235.

8661

UEndp, Eff

Bellavere, C., and J. Gorbi. 1981. A Comparative Analysis
of Acute Toxicity of Chromium, Copper, and Cadmium to
Daphnia magna, Biomphalaria glabrata, and Brachydanio
rerio. Environ.Technol.Lett. 2(3):119-128.

5268

Dur, Con

Bengtsson, B.E., and B. Bergstrom. 1987. A Flowthrough
Fecundity Test with Nitocra spinipes (Harpacticoidea
Crustacea) for Aquatic Toxicity. Ecotoxicol. Environ.Saf.
14:260-268.

2332

AF, Con

Benhra, A., C.M. Radetski, and J.F. Ferard. 1997.
Cryoalgotox: Use of Cryopreserved Alga in a Semistatic
Microplate Test. Environ.Toxicol.Chem. 16(3):505-508.

17613

Plant, AF, Dur

213

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Benson, W.H., and W.J. Birge. 1983. Heavy Metal
Tolerance and Metallothionein Induction in Fathead
Minnows: Results From Field and Laboratory Investigations.
Environ.Toxicol.Chem.4(2):209-217 (1983) /
J.Am.Coll.Toxicol. 2(2):240 (ABS).

10551

Dur, Con

Benson, W.H., K.N. Baer, R.A. Stackhouse, and C.F.
Watson. 1987. Influence of Cadmium Exposure on Selected
Hematological Parameters in Freshwater Teleost,
Notemigonus crysoleucas. Ecotoxicol.Environ.Saf. 13(1 ):92-
96.

12205

Con

Bentley, P.J.. 1991. Accumulation of Cadmium by Channel
Catfish (Ictalurus punctatus): Influx from Environmental
Solutions. Comp.Biochem.Physiol.C 99(3):527-529.

3865

AF, UEndp, Dur,
Con

Bentley, R.E., T. Heitmuller, B.H. Sleight III, and P.R.
Parrish. 1975. Acute Toxicity of Cadmium to Bluegill
(Lepomis macrochirus), Rainbow Trout (Salmo gairdneri),
and Pink Shrimp (Penaeus duorarum). U.S.EPA, Criteria
Branch, WA-6-99-1414-B, Washington, D.C ,:14.

3780

Dur, Con

Berglind, R.. 1985. The Effects of Cadmium on ALA-D
Activity, Growth and Haemoglobin Content in the Water
Flea, Daphnia magna. Comp.Biochem.Physiol.C 80(2):407-
410.

10802

AF, UEndp

Berglind, R.. 1986. Combined and Separate Effects of
Cadmium, Lead and Zinc on Ala-D Activity, Growth and
Hemoglobin Content in Daphnia magna.
Environ.Toxicol.Chem. 5:989-995.

12155

UEndp

Bervoets, L., and R. Blust. 2000. Effects of pH on Cadmium
and Zinc Uptake by the Midge Larvae Chironomus riparius.
Aquat.Toxicol. 49:145-157.

47526

AF, Uendp, Dur

Bervoets, L., R. Blust, and R. Verheyen. 1996. Effect of
Temperature on Cadmium and Zinc Uptake by the Midge
Larvae Chironomus riparius. Arch.Environ.Contam.Toxicol.
31(4):502-511.

18235

AF, UEndp, Dur

214

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Besser, J.M., C.G. Ingersoll, E.N. Leonard, and D.R. Mount.
1998. Effect of Zeolite on Toxicity of Ammonia in
Freshwater Sediments: Implications for Toxicity
Identification Evaluation Procedures. Environ.Toxicol.Chem.
17(11):2310-2317.

19610

UEndp

Bhattacharya, T., S. Bhattacharya, A.K. Ray, and S. Dey.
1989. Influence of Industrial Pollutants on Thyroid Function
in Channa punctatus (Bloch). Indian J.Exp.Biol. 27(1):65-68.

3106

AF, UEndp, Dur

Bilinski, E., and R.E.E. Jonas. 1973. Effects of Cadmium
and Copper on the Oxidation of Lactate by Rainbow Trout
(Salmo gairdneri) Gills. J.Fish.Res.Board Can. 30(10):1553-
1558.

8692

UEndp, Dur

Birge, W.J.. 1978. Aquatic Toxicology of Trace Elements of
Coal and Fly Ash. In: J.H.Thorp and J.W.Gibbons (Eds.),
Dep.Energy Symp.Ser., Energy and Environmental Stress
in Aquatic Systems, Augusta, GA 48:219-240.

5305

UEndp,Dur

Birge, W.J., A.G. Westerman, and O.W. Roberts. 1974.
Lethal and Teratogenic Effects of Metallic Pollutants on
Vertebrate Embryos. Proc.2nd Annu.NSF-Rann Trace
Contam.Environ.Conf., Springfield, VA:316-320 (U.S.NTIS
LBL-3217) (Used Ref.8703).

8488

AF, UEndp, Con

Birge, W.J., J.A. Black, A.G. Westerman, and B.A. Ramey.
1983. Fish and Amphibian Embryos - A Model System for
Evaluating Teratogenicity. Fundam.Appl.Toxicol. 3:237-242.

19124

UEndp, Dur

Birge, W.J., J.A. Black, A.G. Westerman, and J.E. Hudson.
1979. The Effects of Mercury on Reproduction of Fish and
Amphibians. In: O.Nriagu (Ed.), The Biogeochemistry of
Mercury in the Environment, Chapter 23, Elsevier/North-
Holland Biomedical Press :629-655.

10189

UEndp, Dur

215

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Birge, W.J., J.A. Black, A.G. Westerman, and J.E. Hudson.
1980. Aquatic Toxicity Tests on Inorganic Elements
Occurring in Oil Shale. In: C.Gale (Ed.), EPA-600/9-80-022,
Oil Shale Symposium: Sampling, Analysis and Quality
Assurance, March 1979, U.S.EPA, Cincinnati, OH :519-534
(U.S.NTIS PB80-221435).

11838

UEndp,Dur

Birge, W.J., J.A. Black, and A.G. Westerman. 1979.
Evaluation of Aquatic Pollutants Using Fish and Amphibian
Eggs as Bioassay Organisms. In: S.W.Nielsen, G.Migaki,
and D.G.Scarpelli (Eds.), Symp.Animals Monitors
Environ.Pollut., 1977, Storrs, CT 12:108-118.

4943

Dur

Birge, W.J., J.A. Black, and A.G. Westerman. 1985. Short-
Term Fish and Amphibian Embryo-Larval Tests for
Determining the Effects of Toxicant Stress on Early Life
Stages and Estimating Chronic Values.
Environ.Toxicol.Chem. 4(6):807-821 (Publ in Part As
10485).

12156

AF, Con

Birge, W.J., J.E. Hudson, J.A. Black, and A.G. Westerman.
1978. Embryo-Larval Bioassays on Inorganic Coal Elements
and in Situ Biomonitoring of Coal-Waste Effluents. In:
Symp.U.S.Fish Wildl.Serv., Surface Mining Fish
Wildl.Needs in Eastern U.S., W.VA :97-104.

6199

Dur

Birge, W.J., J.J. Just, A.G. Westerman, J.A. Black, and
O.W. Roberts. 1975. Sensitivity of Vertebrate Embryos to
Heavy Metals as a Criterion of Water Quality. Phase II.
Bioassay Procedures Using Developmental Stages as Test
Organisms. Res.Rep.No.84, Water Resour.Res.Inst.,
University of Kentucky, Lexington, KY :36 p.

15915

AF, UEndp, Con

Birge, W.J., W.H. Benson, and J.A. Black. 1983. The
Induction of Tolerance to Heavy Metals in Natural and
Laboratory Populations of Fish. Res.Rep.No.141, Water
Resour.Res.lnst., University of Kentucky, Lexington,
Kentucky Y: 26.

10237

Dur

216

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Bitton, G., K. Rhodes, B. Koopman, and M. Cornejo. 1995.
Short-Term Toxicity Assay Based on Daphnid Feeding
Behavior. Water Environ.Res. 67(3):290-293.

19602

AF, Eff, Dur,
RouExp

Black, J.A., and W.J. Birge. 1980. An Avoidance Response
Bioassay for Aquatic Pollutants. Res.Report No.123, Water
Resour.Res.lnst., University of Kentucky, Lexington,
Kentucky Y:34-180490.

5272

Dur

Blaise, C., R. Legault, N. Bermingham, R. Van Coillie, and
P. Vasseur. 1986. A Simple Microplate Algal Assay
Technique for Aquatic Toxicity Assessment. Toxic.Assess.
1:261-281.

12748

Plant, AF, Con

Block, M., and A.W. Glynn. 1992. Influence of Xanthates on
the Uptake of 109Cadmium by Eurasian Dace (Phoxinus
phoxinus) and Rainbow Trout (Oncorhynchus mykiss).
Environ.Toxicol.Chem. 11(7):873-879.

5908

AF, UEndp, Dur,
Con

Bodar, C.W.M., A.V.D. Zee, P.A. Voogt, H. Wynne, and D.I.
Zandee. 1989. Toxicity of Heavy Metals to Early Life Stages
of Daphnia magna. Ecotoxicol.Environ.Saf. 17(3):333-338.

3854

AF, UEndp, Dur,
Con

Bodar, C.W.M., C.J. Van Leeuwen, P.A. Voogt, and D.I.
Zandee. 1988. Effect of Cadmium on the Reproduction
Strategy of Daphnia magna. Aquat.Toxicol. 12(4):301-310.

5472

Bodar, C.W.M., E.G. Van Donselaar, and H.J. Herwig.
1990. Cytopathological Investigations of Digestive Tract and
Storage Cells in Daphnia magna Exposed to Cadmium and
Tributyltin. Aquat.Toxicol. 17(4):325-338.

3509

Af, UEndp, Eff

Bodar, C.W.M., I. Van der Sluis, J.C.P. Van Montfort, P.A.
Voogt, and D.I. Zandee. 1990. Cadmium Resistance in
Daphnia magna. Aquat.Toxicol. 16(1):33-40.

3001

AF, Dur, Con

217

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Bogaerts, P., J. Senaud, and J. Bohatier. 1998. Bioassay
Technique Using Nonspecific Esterase Activities of
Tetrahymena pyriformis for Screening and Assessing
Cytotoxicity of Xenobiotics. Environ.Toxicol.Chem.
17(8):1600-1605.

18353

Ace, AF, UEndp,
Dur

Borgmann, U.. 1980. Interactive Effects of Metals in
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5421

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Braginskiy, L.P., and E.P. Shcherban. 1979. Acute Toxicity
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5565

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Bresch, H.. 1982. Investigation of the Long-Term Action of
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10392

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Bringmann, G., and R. Kuhn. 1959. Water Toxicological
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Bringmann, G., and R. Kuhn. 1959. Comparative Water-
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61194

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Bringmann, G., and R. Kuhn. 1977. The Effects of Water
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5718

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Bringmann, G., and R. Kuhn. 1978. Investigation of
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6601

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Brkovic-Popovic, I., and M. Popovic. 1977. Effects of Heavy
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8905

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219

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ECOTOX
EcoRef#

Rejection Code(s)

Comment

Brkovic-Popovic, 1., and M. Popovic. 1977. Effects of Heavy
Metals on Survival and Respiration Rate of Tubificid Worms:
Part ll-Effects on Respiration Rate. Environ.Pollut. 13(2):93-
98.

15584

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Con

Brown, B.T., and B.M. Rattigan. 1979. Toxicity of Soluble
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2255

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Brown, E.R., L. Keith, J.J. Hazdra, and T. Arndt. 1973.
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2143

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Brown, M.W., D. Shurben, J.F.D. Solbe, A. Cryer, and J.
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12707

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Bryan, M.D., G.J. Atchison, and M.B. Sandheinrich. 1995.
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16188

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Buhringer, H., K.R. Sperling, and W. Wunder. 1990. Spinal
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RouExp

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460

96 h LC50 approx.
12,000 ug/L
dissolved cadmium
normalized to 100
mg/L as CaC03
hardness. Test was

This study appears to
provide an
appropriate 96 h
LC50 for Carassius
auratus, but the
paper should be

220

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

static, unmeasured.

secured to ensure
acceptability. Species
is relatively
insensitive to acute
cadmium exposure

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9672

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Cairns, J.Jr., J.R. Pratt, and B.R. Niederlehner. 1985. A
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2660

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9815

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19264

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20095

AF, UEndp, Eff

221

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EcoRef#

Rejection Code(s)

Comment

Calgan, D.T., and 0. Yenigun. 1996. Toxicity of Arsenic,
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19504

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Eff

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Quarterly Report, U.S.EPA Cooperative Agreement No.CR
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3690

Con

Canton, J.H., and D.M.M. Adema. 1978. Reproducibility of
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2017

AF, Con

Carlson, A.R., G.L. Phipps, V.R. Mattson, P.A. Kosian, and
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3919

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Carlson, A.R., H. Nelson, and D. Hammermeister. 1986.
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12161

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18838

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Carter, J.W., and I.L. Cameron. 1973. Toxicity Bioassay of
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15419

Ace, AF, UEndp

222

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ECOTOX
EcoRef#

Rejection Code(s)

Comment

Cassini, A., L. Tallandini, N. Favero, and V. Albergoni. 1986.
Cadmium Bioaccumulation Studies in the Freshwater
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11801

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Castren, M., and A. Oikari. 1987. Changes of the Liver
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12208

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Cearley, J.E., and R.L. Coleman. 1973. Cadmium Toxicity
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8789

UEndp

Chagnon, N.L., and S.I. Guttman. 1988. Differential
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13098

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Chagnon, N.L., and S.I. Guttman. 1989. Differential
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507

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Chandini, T.. 1988. Changes in Food [Chlorella] Levels and
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13136

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Chandini, T.. 1989. Survival, Growth and Reproduction of
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977

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Chandini, T.. 1991. Reproductive Value and the Cost of
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3605

AF, UEndp

223

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ECOTOX
EcoRef#

Rejection Code(s)

Comment

Chandra, P., and P. Garg. 1992. Absorption and Toxicity of
Chromium and Cadmium in Limnanthemum cristatum
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7115

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Chapman, G.A., and D.G. Stevens. 1978. Acute Lethal
Levels of Cadmium, Copper, and Zinc to Adult Male Coho
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Chapman, P.M., M.A. Farrell, and R.O. Brinkhurst. 1982.
Relative Tolerances of Selected Aquatic Oligochaetes to
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10602

Chapman, P.M., M.A. Farrell, and R.O. Brinkhurst. 1982.
Effects of Species Interactions on the Survival and
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15207

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Charpentier, S., J. Gamier, and R. Flaugnatti. 1987. Toxicity
and Bioaccumulation of Cadmium in Experimental Cultures
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12562

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Chatterjee, S., and S. Bhattacharya. 1986. Inductive
Changes in Hepatic Metallothionein Profile in the Climbing
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12321

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Dur, Con

Chauhan, T.P.S., M.M. Prakash, K.C. Gupta, and B.R.
Varma. 1979. Observations on the Toxicity of Cadmium
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15710

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Chawla, G., J. Singh, and P.N. Viswanathan. 1991. Effect of
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3603

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ECOTOX
EcoRef#

Rejection Code(s)

Comment

Chen, C.Y., K.C. Lin, and D.T. Yang. 1997. Comparison of
the Relative Toxicity Relationships Based on Batch and
Continuous Algal Toxicity Tests. Chemosphere 35(9):1959-
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18447

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Chen, H.C., and Y.K. Yuan. 1994. Acute Toxicity of Copper,
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18913

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Chouikhi, A.. 1979. Choice and Set Up of the Food Chains
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3521

Christensen, G.M.. 1975. Biochemical Effects of
Methylmercuric Chloride, Cadmium Chloride, and Lead
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197(Used Ref 2022, 9586).

2432

UEndp, Con

Christoffers, D., and D.E.W. Ernst. 1983. The In-Vivo
Fluorescence of Chlorella fusca as a Biological Test for the
Inhibition of Photosynthesis. Toxicol.Environ.Chem. 7:61-
71.

45160

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Chung, K.S.. 1978. Acute Toxicity of Cadmium and Copper
in the Mangrove Oyster. Acta Cient.Venez. 29(2): 14 (SPA).

8329

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Cinier, C.C., M. Petit-Ramel, R. Faure, D. Garin, and Y.
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20069

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Clubb, R.W., A.R. Gaufin, and J.L. Lords. 1975. Acute
Cadmium Toxicity Studies upon Nine Species of Aquatic
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2025

AF, UEndp, Con

225

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Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Clubb, R.W., A.R. Gaufin, and J.L. Lords. 1975. Synergism
between Dissolved Oxygen and Cadmium Toxicity in Five
Species of Aquatic Insects. Environ. Res. 9(3):285-289.

15828

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Conto Cinier, C., M. Petit-Remel, R. Faure, and D. Garin.
1997. Cadmium Bioaccumulation in Carp (Cyprinus carpio)
Tissues During Long-Term High Exposure: Analysis by
Inductively Coupled Plasma-Mass Spectrometry.
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18626

AF, UEndp

Conway, H.L.. 1978. Sorption of Arsenic and Cadmium and
Their Effects on Growth, Micronutrient Utilization, and
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15712

Plant, AF, UEndp

Cosson, R.P.. 1994. Heavy Metal Intracellular Balance and
Relationship with Metallothionein Induction in the Liver of
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4994

UEndp

Couillard, Y., P. Ross, and B. Pinel-Alloul. 1989. Acute
Toxicity of Six Metals to the Rotifer Brachionus calyciflorus,
With Comparisons to Other Freshwater Organisms.
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3091

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Craig, A., L. Hare, P.M. Charest, and A. Tessier. 1998.
Effect of Exposure Regime on the Internal Distribution of
Cadmium in Chironomus staegeri Larvae (Insecta, Diptera).
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10733

AF, UEndp

Cravedi, J.P., C. Gillet, and G. Monod. 1995. In Vivo
Metabolism of Pentachlorophenol and Aniline in Arctic Charr
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17842

AF, UEndp

Dalai, R., and S. Bhattacharya. 1994. Effect of Cadmium,
Mercury, and Zinc on the Hepatic Microsomal Enzymes of
Channa punctatus. Bull.Environ.Contam.Toxicol. 52(6):893-
897.

13692

226

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Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Daoust, P.Y.. 1981. Acute Pathological Effects of Mercury,
Cadmium and Copper in Rainbow Trout. Ph.D.Thesis,
Saskatoon, Saskatchewa n:331.

6116

Flow-through
unmeasured test

Flow-through
measured data exist
for test species; O.
mykiss

Das, B.K., and A. Kaviraj. 1990. Accumulation of Cadmium
in Heteropneustes fossilis and Changes in Haematological
Parameters. J.Nat.Conserv. 2(1):25-30.

8963

AF, UEndp

Das, K.K., and S.K. Banerjee. 1980. Cadmium Toxicity in
Fishes. Hydrobiologia 75(2):117-122.

2595

AF, Con

Das, R.C.. 1988. Cadmium Toxicity to Gonads in a
Freshwater Fish, Labeo bata (Hamilton). Arch.Hydrobiol.
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13068

AF, UEndp

Datta, D.K., and G.M. Sinha. 1987. Estimation of Acute
Toxicity of Cadmium, a Heavy Metal, in a Carnivorous
Freshwater Teleost, Mystus vittatus (Bloch). C.A.Sel.-
Environ.Pollut.2:108-17431N (1988) / Proc.Indian
Natl.Sci.Acad.Part B 53(1):43-45.

5307

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Datta, D.K., and G.M. Sinha. 1988. Response Induced on
the Mucous Cells of the Digestive Tract of a Carnivorous
Indian Freshwater Teleost, Mystus vittatus (Bloch) Due to
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5457

AF, UEndp, Eff

Dave, G., K. Andersson, R. Berglind, and B. Hasselrot.
1981. Toxicity of Eight Solvent Extraction Chemicals and of
Cadmium to Water Fleas, Daphnia magna, Rainbow Trout,
Salmo gairdneri, and Zebrafish,. Comp.Biochem.Physiol.C
69(1):83-98.

2195

Dur, Con

Davies, R.W., R.N. Singhal, and D.D. Wicklum. 1995.
Changes in Reproductive Potential of the Leech
Nephelopsis obscura (Erpobdellidae) as Biomarkers for
Cadmium Stress. Can.J.Zool. 73(12):2192-2196.

19924

AF, UEndp, Dur

227

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Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

De Coen, W.M., C.R. Janssen, and G. Persoone. 1995.
Biochemical Assessment of Cellular Energy Allocation in
Daphnia magna Exposed to Toxic Stress as an Alternative
to the Conventional "Scope for Growth". In: Proc.of the
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16782

AF, UEndp

De March, B.G.E.. 1988. Acute Toxicity of Binary Mixtures
of Five Cations (Cu2+, Cd2+, Zn2+, Mg2+, and K+) to the
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13058

De Zwart, D., and W. Slooff. 1987. Toxicity of Mixtures of
Heavy Metals and Petrochemicals to Xenopus laevis.
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12152

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Debelak, R.W.. 1975. Acute Toxicity of Mixtures of Copper,
Chromium and Cadmium to Daphnia magna. M.S.Thesis,
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3528

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Decoen, W.M., and C.R. Janssen. 1997. The Use of
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18286

AF, UEndp

Deeds, J.R., and P.L. Klerks. 1999. Metallothionein-Like
Proteins in the Freshwater Oligochaete Limnodrilus
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20336

UEndp

Del Ramo, J., A. Torreblanca, M. Martinez, A. Pastor, and J.
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16911

228

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Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Del Ramo, J., J. Diaz-Mayans, A. Torreblanca, and A.
Nunez. 1987. Effects of Temperature on the Acute Toxicity
of Heavy Metals (Cr, Cd, and Hg) to the Freshwater
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12565

See note

Not used in ALC
document because
animals acclimated or
exhibited increased
resistance to
cadmium

Delgado, M., M. Bigeriego, and E. Guardiola. 1993. Uptake
of Zn, Cr, and Cd by Water Hyacinths. Water Res.
27(2):269-272.

7114

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Den Besten, P.J., E.G. Van Donselaar, H.J. Herwig, D.I.
Zandee, and P.A. Voogt. 1991. Effects of Cadmium on
Gametogenesis in the Sea Star Asterias rubens L.
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5251

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Den Besten, P.J., H.J. Herwig, D.I. Zandee, and P.A. Voogt.
1989. Effects of Cadmium and PCBs on Reproduction of the
Sea Star Asterias rubens: Aberrations in the Early
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2395

AF, UEndp

Devi, M., D.A. Thomas, J.T. Barber, and M. Fingerman.
1996. Accumulation and Physiological and Biochemical
Effects of Cadmium in a Simple Aquatic Food Chain.
Ecotoxicol. Environ.Saf. 33:38-43.

16846

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Diamond, J.M., M.J. Parson, and D. Gruber. 1990. Rapid
Detection of Sublethal Toxicity Using Fish Ventilatory
Behavior. Environ.Toxicol.Chem. 9(1 ):3-11.

3190

AF, UEndp, Dur

Diaz-Mayans, J., A. Torreblanca, J. Del Ramo, and A.
Nunez. 1986. Oxygen Uptake by Excised Gills of
Procambarus clarkii (Girard) From Albufera Lake of
Valencia, Spain, Under Heavy Metal Treatments.
Bull.Environ.Contam.Toxicol. 36(6):912-917.

11790

AF, UEndp, Con

Diaz-Mayans, J., F. Hernandez, J. Medina, J. Del Ramo,
and A. Torreblanca. 1986. Cadmium Accumulation in the
Crayfish, Procambarus clarkii, Using Graphite Furnace
Atomic Absorption Spectroscopy.

Bui I. Environ. Contam. Toxicol. 37(5):722-729.

11947

AF, UEndp

229

-------
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ECOTOX
EcoRef#

Rejection Code(s)

Comment

Dickson, G.W., J.P. Giesy, and L.A. Briese. 1982. The
Effect of Chronic Cadmium Exposure on Phosphoadenylate
Concentrations and Adenylate Energy Charge of Gills and
Dorsal Muscle Tissue of Crayfish. Environ.Toxicol.Chem.
1(2): 147-156.

7116

AF, UEndp, Eff

Dillon, T.M., and B.C. Suedel. 1986. The Relationship
Between Cadmium Bioaccumulation and Survival, Growth,
and Reproduction in the Freshwater Crustacean, Daphnia
magna. C.A.Sel.-Environ.Pollut. 17:107-537020 (1987) / In:
Environ.Contam.2nd Int.Conf., CEP Consult., Edinburgh,
U.K. :21-23.

12770

UEndp

Dive, D., P. Vasseur, 0. Hanssen, and P.J. Gravil. 1988.
Studies on Interactions Between Components of
Electroplating Wastes. Can.Tech.Rep.Fish.Aquat.Sci.No.
1607:23-33.

4928

Ace, AF, Dur, Con

Dive, D., S. Robert, E. Angrand, C. Bel, H. Bonnemain, L.
Brun, Y. Demarque, A. Le Du, and Bouhouti El. 1989. A
Bioassay Using the Measurement of Growth Inhibition of a
Ciliate Protozoan: Colpidium campylum Stokes.
Hydrobiologia 188/189:181-188.

16260

Ace, AF, Dur

Domal-Kwiatkowska, D., B. Sosak-Swiderska, U. Mazurek,
and D. Tyrawska. 1994. The Effect of Cadmium on the
Survival and Filtering Rate of Daphnia magna, Straus 1820.
Pol .Arch. Hydrobiol. 41 (4):465-473.

17333

Donkin, S.G., and P.L. Williams. 1995. Influence of
Developmental Stage, Salts and Food Presence on Various
End Points Using Caenorhabditis elegans for Aquatic
Toxicity Testing. Environ.Toxicol.Chem. 14(12):2139-2147.

16377

AF, Dur

Dorgelo, J., H. Meester, and C. Van Velzen. 1995. Effects of
Diet and Heavy Metals on Growth Rate and Fertility in the
Deposit-Feeding Snail Potamopyrgus jenkinsi (Smith)
(Gastropoda: Hydrobiidae). Hydrobiologia 316(3): 199-210.

16506

AF, UEndp

230

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Douben, P.E.T.. 1989. Metabolic Rate and Uptake and Loss
of Cadmium From Food by the Fish Noemacheilus
barbatulus L. (Stone Loach). Environ.Pollut. 59(3):177-202.

914

AF, UEndp, RouExp

Drummond, R.A., and D.A. Benoit. 1980. Toxicity of
Cadmium to Fish - Some Observations on the Influence of
Experimental Procedures. Manuscript, U.S.EPA, Duluth,
MN:8 p.(Author Communication Used).

14381

UEndp

Edgren, M., and M. Notter. 1980. Cadmium Uptake by
Fingerlings of Perch (Perca fluviatilis) Studied by Cd-115M
at Two Different Temperatures.
Bull.Environ.Contam.Toxicol. 24(5):647-651.

9791

AF, UEndp, Con

Ellgaard, E.G., J.E. Tusa, and A.A. Malizia Jr.. 1978.
Locomotor Activity of the Bluegill Lepomis macrochirus:
Hyperactivity Induced by Sublethal Concentrations of
Cadmium, Chromium and Zinc. J.Fish Biol. 1 (1): 19-23.

15561

UEndp, Con

Enserink, L., M. De La Haye, and H. Maas. 1993.
Reproductive Strategy of Daphnia magna: Implications for
Chronic Toxicity Tests. Aquat.Toxicol. 25:111-124.

7016

Enserink, L., W. Luttmer, and H. Maas-Diepeveen. 1990.
Reproductive Strategy of Daphnia magna Affects the
Sensitivity of Its Progeny in Acute Toxicity Tests.
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3336

AF, Con

Errecalde, 0., M. Seidl, and P.G.C. Campbell. 1998.
Influence of a Low Molecular Weight Metabolite (Citrate) on
the Toxicity of Cadmium and Zinc to the Unicellular Green
Alga Selenastrum capricornutum. Water Res. 32(2):419-
429.

18646

Plant, AF, UEndp

Espina, S., A. Salibian, and F. Diaz. 2000. Influence of
Cadmium on the Respiratory Function of the Grass Carp
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10.

49075

UEndp, Eff

Fargasova, A.. 1994. Comparative Toxicity of Five Metals

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Bull.Environ.Contam.Toxicol. 53(2):317-324.

13707

Plant, AF

231

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Fennikoh, K.B., H.I. Hirshfield, and T.J. Kneip. 1978.
Cadmium Toxicity in Planktonic Organisms of a Freshwater
Food Web. Environ.Res. 15(3):357-367.

5382

Det

Ferard, J.F., J.M. Jouany, R. Truhaut, and P. Vasseur.
1983. Accumulation of Cadmium in a Freshwater Food
Chain Experimental Model. Ecotoxicol.Environ.Saf. 7(1):43-
52.

11678

AF, UEndp, Con,
RouExp

Ferard, J.F., P. Vasseur, and J.M. Jouany. 1983. Value of
Dynamic Tests in Acute Ecotoxicity Assessment in Algae.
In: W.C.McKay (Ed.), Proc.of the 9th Annu.Aquat.Toxicity
Workshop, Can.Tech.Rep.Fish.Aquat.Sci.No.1163, Univ.of
Alberta, Edmonton, Alberta, Canada :38-56.

56858

Plant, AF, Dur

Fernandez-Leborans, G., and A. Novillo. 1995. The Effects
of Cadmium on the Successional Stages of a Freshwater
Protozoa Community. Ecotoxicol.Environ.Saf. 31(1):29-36.

15308

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Fernandez-Leborans, G., and M.T. Antonio-Garcia. 1988.
Effects of Lead and Cadmium in a Community of
Protozoans. Acta Protozool. 27(2):141-159.

897

Ace, AF, UEndp

Ferrari, L., A. Salibian, and C.V. Muino. 1993. Selective
Protection of Temperature Against Cadmium Acute Toxicity
to Bufo arenarum Tadpoles. Bull.Environ.Contam.Toxicol.
50(2):212-218.

6530

AF, Dur

Ferri, S., and N. Macha. 1980. Lysosomal Enhancement in
Hepatic Cells of a Teleost Fish Induced by Cadmium. Cell
Biol.Int.Rep. 4(4):357-363.

9796

AF, UEndp, Eff,
Dur, Con

Filip, D.S., T. Peters, V.D. Adams, and E.J. Middlebrooks.
1979. Residual Heavy Metal Removal by an Algae-
Intermittent Sand Filtration System. Water Res. 13(3):305-
313.

8348

Plant, NoOrg, AF,
Con

232

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Fischer, E., J. Filip, L. Molnar, and E. Nagy. 1980.
Karyometric Studies of the Effect of Lead and Cadmium in
Relation to the Oxygen Supply in the Chloragocytes of
Tubifex tubifex Mull. Environ.Pollut.Ser.A Ecol.Biol.
21(3):203-207.

9800

AF, UEndp

Flickinger, A.L.. 1984. Chronic Toxicity of Mixtures of
Copper, Cadmium and Zinc to Daphnia pulex. Ph.D.Thesis,
Miami University, Oxford, 0 H:135.

12451

Dur

Foran, C.M., B.N. Peterson, and W.H. Benson. 2002.
Influence of Parental and Developmental Cadmium
Exposure on Endocrine and Reproductive Function in
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Comp.Biochem. Physiol. C 133(3):345-354.

62870

UEndp

Francis, P.C., W.J. Birge, and J.A. Black. 1984. Effects of
Cadmium-Enriched Sediment on Fish and Amphibian
Embryo-Larval Stages. Ecotoxicol.Environ.Saf. 8(4):378-
387.

10644

AF, UEndp

Frank, P.M., and P.B. Robertson. 1979. The Influence of
Salinity on Toxicity of Cadmium and Chromium to the Blue
Crab, Callinectes sapidus. Bull.Environ.Contam.Toxicol.
21(1/2):74-78.

5384

AF, Dur, Con

Fu, H., and R.A.C. Lock. 1990. Pituitary Response to
Cadmium During the Early Development of Tilapia
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2996

AF, UEndp, Eff

Fu, H., O.M. Steinebach, C.J.A. Van den Hamer, P.H.M.
Balm, and R.A.C. Lock. 1990. Involvement of Cortisol and
Metallothionein-Like Proteins in the Physiological
Responses of Tilapia (Oreochromis mossambicus) to
Sublethal Cadmium Stress. Aquat.Toxicol. 16(4):257-270.

3282

AF, Uendp, Eff

Gagnon, C., G. Vaillancourt, and L. Pazdernik. 1998.
Influence of Water Hardness on Accumulation and
Elimination of Cadmium in Two Aquatic Mosses Under
Laboratory Conditions. Arch.Environ.Contam.Toxicol.
34(1 ):12-20.

18999

UEndp

233

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Gale, N.L., B.G. Wixson, and M. Erten. 1992. An Evaluation
of the Acute Toxicity of Lead, Zinc, and Cadmium in
Missouri Ozark Groundwater. Trace Subst. Environ. Health
25:169-183.

9180

Gargiulo, G., P. De Girolamo, L. Ferrara, 0. Soppelsa, G.
Andreozzi, R. Antonucci, and P. Battaglini. 1996. Action of
Cadmium on the Gills of Carassius auratus L. in the
Presence of Catabolic NH3. Arch.Environ.Contam.Toxicol.
30(2):235-240.

16426

UEndp

Gavrilenko, Y.Y., and Y.Y. Zolotukhina. 1989. Accumulation
and Interaction of Copper, Zinc, Manganese, Cadmium,
Nickel and Lead Ions Absorbed by Aquatic Macrophytes.
Hydrobiol.J. 25(5):54-61.

9369

Plant, AF, UEndp,
Dur

Genin-Durbert, C., Y. Champetier, and P. Blazy. 1988.
Metallic Bioaccumulation in Aquatic Plants.
(Bioaccumulation des Metaux Dans les Vegetaux
Aquatiques). C.R.Acad.Sci.Ser.lll 307:1875-1877 (FRE)
(ENG ABS).

Plant, AF, UEndp,
Dur, Con

Gerhards, U., and H. Weller. 1977. The Uptake of Mercury,
Cadmium and Nickel by Chlorella pyrenoidosa (Die
Aufnahme von Quecksilber, Cadmium und Nickel durch
Chlorella pyrenoidosa). Z.Pflanzenphysiol.82:292-300
(GER) (ENG ABS).

14113

Plant, AF, UEndp,
Dur

Gerhardt, A.. 1992. Acute Toxicity of Cd in Stream
Invertebrates in Relation to pH and Test Design.
Hydrobiologia 239(2):93-100.

6054

AF, Con

Gerhardt, A.. 1995. Joint and Single Toxicity of Cd and Fe
Related to Metal Uptake in the Mayfly Leptophlebia
marginata (L.) (Insecta). Hydrobiologia 306(3):229-240.

16026

AF, UEndp

Ghate, H.V.. 1984. Gill Melanization and Heavy Metals in
Freshwater Prawns. Indian J.Fish. 31 (3):389-393.

9852

AF, Dur

Ghosal, T.K., and A. Kaviraj. 1996. Influence of Poultry
Litter on the Toxicity of Cadmium to Aquatic Organisms.
Bull.Environ.Contam.Toxicol. 57(6): 1009-1015.

19384

UEndp

234

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Ghosh, A.R., and P. Chakrabarti. 1990. Toxicity of Arsenic
and Cadmium to a Freshwater Fish Notopterus notopterus.
Environ.Ecol. 8(2):576-579.

3440

Dur, Con

Ghosh, A.R., and P. Chakrabarti. 1992. A Scanning
Electron Microscopic Probe into the Cellular Injury in the
Alimentary Canal of Notopterus notopterus (Pallas) After
Cadmium Intoxication. Ecotoxicol.Environ.Saf. 23:147-160.

3870

AF, UEndp, Eff

Ghosh, A.R., and P. Chakrabarti. 1993. Histopathological
and Histochemical Changes in Liver, Pancreas and Kidney
of the Freshwater Fish Heteropneustes fossilis (Bloch)
Exposed to Cadmium. Environ.Ecol. 11(1): 185-188.

13364

AF, UEndp, Eff,
Con

Ghosh, K., and S. Jana. 1988. Effects of Combinations of
Heavy Metals on Population Growth of Fish Nematode
Spinicauda spinicauda in Aquatic Environment.
Environ.Ecol. 6(4):791-794.

814

AF, UEndp, Eff

Giesy, J.P., and D.H. Smith. 1985. Cadmium Partitioning
and Related Effects in Parasitized and Non-Parasitized
Mosquitofish (Gambusia affinis: Poeciliidae).
Int.Assoc.Theor.Appl.Limnol.Proc./lnt.Ver.Theor.Angew.Lim
nol.Verh. 22:2405-2412.

11509

UEndp

Giles, M.A.. 1988. Accumulation of Cadmium by Rainbow
Trout, Salmo gairdneri, During Extended Exposure.
Can.J.Fish.Aquat.Sci. 45(6): 1045-1053.

5503

AF, UEndp

Gill, T.S., and A. Epple. 1992. Effects of Cadmium on
Plasma Catecholamines in the American Eel, Anguilla
rostrata. Aquat.Toxicol. 23(2): 107-117.

6193

AF, UEndp, Eff

Gill, T.S., C.P. Bianchi, and A. Epple. 1992. Trace Metal (Cu
and Zn) Adaptation of Organ Systems of the American Eel,
Angilla rostrata, to External Concentrations of Cadmium.
Comp.Biochem. Physiol. C 102(3):361-371.

6479

AF, UEndp

235

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Gill, T.S., J.C. Pant, and H. Tewari. 1988. Branchial
Pathogenesis in a Freshwater Fish, Puntius conchonius
Ham., Chronically Exposed to Sublethal Concentrations of
Cadmium. Ecotoxicol.Environ.Saf. 15(2): 153-161.

12880

AF, UEndp, Eff

Gill, T.S., J.C. Pant, and H. Tewari. 1989. Cadmium
Nephropathy in a Freshwater Fish, Puntius conchonius
Hamilton. Ecotoxicol.Environ.Saf. 18(2):165-172.

2374

UEndp, Eff

Gillespie, R., T. Reisine, and E.J. Massaro. 1977. Cadmium
Uptake by the Crayfish, Orconectes propinquus propinquus
(Girard). Environ.Res. 13(3):364-368.

15563

AF, UEndp, Con

Gingerich, W.H., R.M. Elsbury, and M.T. Steingraeber.
1988. Effects of Cadmium on Hatching Success, Growth,
and Osteological Development of Larval Brook Trout
(Salvelinus fontinalis) in Soft, Acidic Waters. Aquat.Toxicol.
11 (3/4):404-405 (ABS).

8196

AF, UEndp, Dur,
Con

Gipps, J.F., and P. Biro. 1978. The Use of Chlorella vulgaris
in a Simple Demonstration of Heavy Metal Toxicity.
J.BioI.Educ. 12(3):207-214.

14382

Plant, AF, UEndp

Glynn, A.W., C. Haux, and C. Hogstrand. 1992. Chronic
Toxicity and Metabolism of Cd and Zn in Juvenile Minnows
(Phoxinus phoxinus) Exposed to a Cd and Zn Mixture.
Can.J.Aquat.Sci. 49(10):2070-2079.

7097

AF, UEndp, Con

Glynn, A.W., L. Andersson, S. Gabring, and P. Runn. 1992.
Cadmium Turnover in Minnows, Phoxinus phoxinus, Fed
109Cd-Labeled Daphnia magnia. Chemosphere 24(3):359-
368.

5000

AF, UEndp, Dur,
Con

Glynn, A.W., L. Norrgren, and A. Mussener. 1994.
Differences in Uptake of Inorganic Mercury and Cadmium in
the Gills of the Zebrafish, Brachydanio rerio. Aquat.Toxicol.
30:13-26.

14422

AF, UEndp, Dur

Goerke, H., and K. Weber. 1990. Population-Dependent
Elimination of Various Polychlorinated Biphenyls in Nereis
diversicolor (Polychaeta). Mar.Environ.Res. 29(3):205-226.

5711

UEndp, Con

236

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Goettl, J.P.J., and P.H. Davies. 1976. Water Pollution
Studies. Job Progress Report, Federal Aid Project F-33-R-
11, DNR, Boulder, C 0:58.

10208

96 h LC50 approx.
9.31 ug/L dissolved
cadmium
normalized to 100
mg/L as CaC03
hardness. Test was
flow-through,
measured.

This study appears to
provide an
appropriate 96 h
LC50 for O. mykiss,
but the paper should
be secured to ensure
acceptability. Data
coincides with
existing acute values
used in his evaluation
for this species

Goettl, J.P.J., and P.H. Davies. 1978. Water Pollution
Studies. Job Progress Report, Federal Aid Project F-33-R-
13, DNR, Boulder, C :46.

7341

UEndp

Goettl, J.P.J., J.R. Sinley, and P.H. Davies. 1974. Water
Pollution Studies. Job Progress Report, Federal Aid Project
F-33-R-9, DNR, Boulder, CO :96 p..

285

Flow-through
unmeasured test

Flow-through
measured data exist
for test species; O.
mykiss

Goettl, J.P.Jr., P.H. Davies, and J.R. Sinley. 1976. Water
Pollution Studies. In: D.B.Cope (Ed.), Colorado
Fish. Res. Rev. 1972-1975, DOW-R-R-F72-75, Colorado
Div.of Wildl., Boulder, CO :68-75.

14367

UEndp

Gomot, A.. 1998. Toxic Effects of Cadmium on
Reproduction, Development, and Hatching in the
Freshwater Snail Lymnaea stagnalis for Water Quality
Monitoring. Ecotoxicol.Environ.Saf. 41 (3):288-297.

20053

AF, UEndp, Eff

Gossiaux, D.C., P.F. Landrum, and V.N. Tsymbal. 1992.
Response of the Amphipod Diporeia spp. to Various
Stressors: Cadmium, Salinity, and Temperature. J.Gt.Lakes
Res. 18(3):364-371.

9649

AF, Dur, Con

Gottofrey, J., I. Bjoerklund, and H. Tjaelve. 1988. Effect of
Sodium Isopropylxanthate, Potassium Amylxanthate and
Sodium Diethyldithiocarbamate on the Uptake and
Distribution of Cadmium in the. Aquat.Toxicol. 12(2): 171 -
184.

2501

AF, UEndp, Con

Graney, R.L.J., D.S. Cherry, and J. Cairns Jr.. 1983. Heavy
Metal Indicator Potential of the Asiatic Clam (Corbicula
fluminea) in Artificial Stream Systems. Hydrobiologia
102(2):81-88.

10815

UEndp, Field

237

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Grebe, E., and D.J. Schaeffer. 1991. Neurobehavioral
Toxicity of Cadmium Sulfate to the Planarian Dugesia
dorotocephala. Bull.Environ.Contam.Toxicol. 46:727-730.

3623

AF, UEndp, Dur,
Con

Green, D.W.J., K.A. Williams, and D. Pascoe. 1986. The
Acute and Chronic Toxicity of Cadmium to Different Life
History Stages of the Freshwater Crustacean Asellus
aquaticus (L). Arch.Environ.Contam.Toxicol. 15(5):465-471.

11953

Con

Griffiths, P.R.E.. 1980. Morphological and Ultrastructural
Effects of Sublethal Cadmium Poisoning on Daphnia.
Environ. Res. 22(2):277-284.

5280

AF, UEndp, Eff, Dur

Groenendijk, D., B. Van Opzeeland, L.M. Dionisio Pires,
and J.F. Postma. 1999. Fluctuating Life-History Parameters
Indicating Temporal Variability in Metal Adaptation in
Riverine Chironomids. Arch.Environ.Contam.Toxicol.
37(2):175-181.

20448

AF, UEndp

Guilhermino, L., 0. Sobral, C. Chastinet, R. Ribeiro, F.
Goncalves, M.C. Silva, and A.M.V.M. Soares. 1999. A
Daphnia magna First-Brood Chronic Test: An Alternative to
the Conventional 21-Day Chronic Bioassay?.

Ecotoxicol. Envi ron. Saf. 42(1):67-74.

20061

UEndp

Guilhermino, L., T.C. Diamantino, R. Ribeiro, F. Goncalves,
and A.M.V.M. Soares. 1997. Suitability of Test Media
Containing EDTAforthe Evaluation of Acute Metal Toxicity
to Daphnia magna Straus. Ecotoxicol.Environ.Saf.
38(3):292-295.

18978

AF, Eff, Dur

Gulati, R.D., C.W.M. Bodar, A.L.G. Schuurmans, J.A.J.
Faber, and D.I. Zandee. 1988. Effects of Cadmium
Exposure on Feeding of Freshwater Planktonic
Crustaceans. Comp.Biochem.Physiol.C 90(2):335-340.

5507

AF, UEndp, Eff, Dur

Gupta, A.K.. 1988. Accumulation of Cadmium in the Fishes
Heteropneustes fossilis and Channa punctatus.
Environ.Ecol. 6(3):577-580.

802

AF, Con

238

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Gupta, A.K., and V.K. Rajbanshi. 1982. Cytopathological
Studies Resulting in Cadmium Bioassay with
Heteropneustes fossilis (Bloch). Acta Hydrochim.Hydrobiol.
10(4):345-351.

11033

AF, UEndp, Eff,
Con

Gupta, A.K., and V.K. Rajbanshi. 1988. Acute Toxicity of
Cadmium to Channa punctatus (Bloch). Acta
Hydrochim.Hydrobiol. 16(5):525-535.

3448

Dur, Con

Gupta, A.K., and V.K. Rajbanshi. 1991. Toxicity of Copper
and Cadmium to Heteropneustes fossilis (Bloch). Acta
Hydrochim.Hydrobiol. 19(3):331-340.

3728

UEndp, Con

Gupta, M., and S. Devi. 1992. Cadmium Sensitivity Inducing
Structural Responses in Salvinia molesta Mitchell.

Bui I. Environ. Contam. Toxicol. 49(3):436-443.

5758

Plant, AF, UEndp,
Dur

Gupta, M., S. Devi, and J. Singh. 1992. Effects of Long-
Term Low-Dose Exposure to Cadmium During the Entire
Life Cycle of Ceratopteris thalictroides, a Water Fern.
Arch. Environ. Contam .Toxicol. 23(2): 184-189.

6366

Plant, AF, UEndp

Gupta, P., S.S. Chaurasia, A. Kar, and P.K. Maiti. 1997.
Influence of Cadmium on Thyroid Hormone Concentrations
and Lipid Peroxidation in a Fresh Water Fish, Clarias
batrachus. Fresenius Environ.Bull. 6(7/8):355-358.

59876

AF, UEndp, Eff

Gupta, P.K., B.S. Khangarot, and V.S. Durve. 1981. Studies
on the Acute Toxicity of Some Heavy Metals to an Indian
Freshwater Pond Snail Viviparus bengalensis L.
Arch.Hydrobiol. 91(2):259-264 (Publ in Part as 15716).

15745

Dur, Con

Haesloop, U., and M. Schirmer. 1985. Accumulation of
Orally Administered Cadmium by the Eel (Anguilla anguilla).
Chemosphere 14(10): 1627-1634.

2985

AF, UEndp

Hale, J.G.. 1977. Toxicity of Metal Mining Wastes.
Bull.Environ.Contam.Toxicol. 17(1):66-73.

861

239

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Halsband, E., 1. Halsband, B. Romestand, A. Dzuvic, and H.
Pump. 1986. Further Investigations on the Impact of
Cadmium, Calcium and Parathormone on Blood, Skeleton
System and Internal Organs of Rainbow Trout Salmo
gairdneri (Weitere Untersuchungen ober die Wirkung von
Cadmium, Calcium und P.

Veroeff. Inst. Kuest.Binnenfisch.Hamb. No. 91:29
p.(GER)(ENG ABS).

16871

AF, UEndp, Eff

Hameed, P.S., and A.I.M. Raj. 1989. Effects of Copper,
Cadmium and Mercury on Crystalline Style of the
Freshwater Mussel Lamellidens marginalis (Lamarck).
Indian J.Environ.Health 31 (2): 131 -136.

3311

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Dur, Con

Hamilton, S.J., P.M. Mehrle, and J.R. Jones. 1987.
Evaluation of Metallothionein Measurement As a Biological
Indicator of Stress From Cadmium in Brook Trout.
Trans.Am.Fish.Soc.116(4):551-560; Diss.Abstr.lnt.B
Sci.Eng.46(11):DA8529659 (1986);

Abstr. Pap. Am. Chem. Soc. 194:289.

12776

UEndp

Hamilton, S.J., P.M. Mehrle, and J.R. Jones. 1987.
Cadmium-Saturation Technique for Measuring
Metallothionein in Brook Trout. Trans.Am.Fish.Soc.
116(4):541-550.

12779

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Handy, R.D.. 1992. The Assessment of Episodic Metal
Pollution. II. The Effects of Cadmium and Copper Enriched
Diets on Tissue Contaminant Analysis in Rainbow Trout
(Oncorhynchus mykiss) After Short Waterborne Exposure to
Cadmium or Copper. Arch.Environ.Contam.Toxicol. 22:82-
87.

5001

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Handy, R.D.. 1992. The Assessment of Episodic Metal
Pollution. I. Uses and Limitations of Tissue Contaminant
Analysis in Rainbow Trout (Oncorhynchus mykiss) After
Short Waterborne Exposure to Cadmium or Copper.
Arch.Environ.Contam.Toxicol. 22:74-81.

5019

AF, UEndp, Dur

240

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Handy, R.D.. 1993. The Effect of Acute Exposure to Dietary
Cd and Cu on Organ Toxicant Concentrations in Rainbow
Trout, Oncorhynchus mykiss. Aquat.Toxicol. 27(1/2):1-14.

8200

AF, UEndp, Dur

Hansen, L.G., W.M. Tehseen, G.L. Foley, and D.J.
Schaeffer. 1993. Modification by Polychlorinated Biphenyls
(PCBs) of Cadmium Induced Lesions in the Planarian
Model, Dugesia dorotocephala. Biomed.Environ.Sci.
6(4):367-384.

4108

AF, UEndp, Eff

Hardy, J.K., and D.H. O'Keeffe. 1985. Cadmium Uptake by
the Water Hyacinth: Effects of Root Mass, Solution Volume,
Complexers and Other Metal Ions. Chemosphere 14(5):417-
426.

10949

Plant, AF, UEndp,
Dur, Con

Harrison, S.E., and J.F. Klaverkamp. 1989. Uptake,
Elimination and Tissue Distribution of Dietary and Aqueous
Cadmium by Rainbow Trout (Salmo gairdneri Richardson)
and Lake Whitefish. Environ.Toxicol.Chem. 8(1):87-97.

688

AF, UEndp

Harrison, S.E., and P.J. Curtis. 1992. Comparative
Accumulation Efficiency of 109Cadmium from Natural Food
(Hyalella azteca) and Artificial Diet by Rainbow Trout
(Oncorhynchus mykiss). Bull.Environ.Contam.Toxicol.
49(5):757-764.

5756

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Hart, B.A.. 1977. The Role of Phytoplankton in Cycling
Cadmium in the Environment. Project No.A-023-VT,
Vermont Water Resour. Res.Center and Office Water
Res.and Technol., U.S.D.I., Washington, D.C ,:62.

7359

AF, Eff, Con

Hart, B.A., and B.D. Scaife. 1977. Toxicity and
Bioaccumulation of Cadmium in Chlorella pyrenoidosa.
Environ. Res. 14(3):401 -413.

2174

Plant, AF, UEndp,
Eff, Dur

Hartwell, S.I., J.H. Jin, D.S. Cherry, and J. Cairns Jr.. 1989.
Toxicity Versus Avoidance Response of Golden Shiner,
Notemigonus crysoleucas, to Five Metals. J.Fish Biol.
35(3):447-456.

3286

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241

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ECOTOX
EcoRef#

Rejection Code(s)

Comment

Hatakeyama, S.. 1986. Effects of Heavy Metals Cadmium,
Copper, and Zinc on Some Aquatic Organisms Through the
Food Chain. C.A.Sel.-Environ.Pollut.22:105-147769C /
Res.Rep.Natl.Inst.Environ.Stud.(Kokuritsu Kogai Kenkyusho
Kenkyu Hokoku) 99:175-189 (JPN).

5651

AF, UEndp, Dur,
RouExp

Hatakeyama, S.. 1987. Chronic Effects of Cd on
Reproduction of Polypedilum nubifer (Chironomidae)
Through Water and Food. Environ.Pollut. 48:249-261.

12795

AF, UEndp, Eff

Hatakeyama, S., and M. Yasuno. 1982. Accumulation and
Effects of Cadmium on Guppy (Poecilia reticulata) Fed
Cadmium-Dosed Cladocera (Moina macrocopa).
Bull.Environ.Contam.Toxicol. 29(2): 159-166.

10469

AF, UEndp

Hatakeyama, S., and M. Yasuno. 1987. Chronic Effects of
Cd on the Reproduction of the Guppy (Poecilia reticulata)
Through Cd-Accumulated Midge Larvae (Chironomus
yoshimatsui). Ecotoxicol.Environ.Saf. 14:191-201.

12796

AF, UEndp, Dur

Hatakeyama, S., and Y. Sugaya. 1989. A Freshwater
Shrimp (Paratya compressa improvisa) as a Sensitive Test
Organism to Pesticides. Environ.Pollut. 59(4):325-336.

984

AF, Dur

Haynes, G.J., A.J. Stewart, and B.C. Harvey. 1989. Gender-
Dependent Problems in Toxicity Tests with Ceriodaphnia
dubia. Bull.Environ.Contam.Toxicol. 43(2):271-279.

3918

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Heinis, F., K.R. Timmermans, and W.R. Swain. 1990. Short-
Term Sublethal Effects of Cadmium on the Filter Feeding
Chironomid Larva Glyptotendipes pallens (Meigen)

(Diptera). Aquat.Toxicol. 16(1):73-86.

3002

AF, UEndp

Hemelraad, J., D.A. Holwerda, H.J. Herwig, and D.I.

Zandee. 1990. Effects of Cadmium in Freshwater Clams. III.
Interaction with Energy Metabolism in Anodonta cygnea.
Arch.Environ.Contam.Toxicol. 19(5):699-703.

3466

AF, UEndp, Eff

242

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Herkovits, J., and C.S. Perez-Coll. 1993. Stage-Dependent
Susceptibility of Bufo arenarum Embryos to Cadmium.
Bull.Environ.Contam.Toxicol. 50(4):608-611.

8053

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Herkovits, J., P. Cardellini, C. Pavanati, and C.S. Perez-
Coll. 1997. Susceptibility of Early Life Stages of Xenopus
laevisto Cadmium. Environ.Toxicol.Chem. 16(2):312-316.

17664

AF, UEndp, Dur

Herwig, H.J., F. Brands, E. Kruitwagen, and D.I. Zandee.
1989. Bioaccumulation and Histochemical Localization of
Cadmium in Dreissena polymorphs Exposed to Cadmium
Chloride. Aquat.Toxicol. 15(3):269-286.

2031

AF, UEndp, Eff

Hiraoka, Y.. 1985. A Re-Examination of the Toxicity Test for
Water Pollutants. Hiroshima J.Med.Sci. 34(3):323-326.

12270

UEndp, Dur, Con

Hiraoka, Y., S. Ishizawa, T. Kamada, and H. Okuda. 1985.
Acute Toxicity of 14 Different Kinds of Metals Affecting
Medaka Fry. Hiroshima J.Med.Sci. 34(3):327-330.

12151

UEndp, Dur

Hodson, P.V., B.R. Blunt, D.J. Spry, and K. Austen. 1977.
Evaluation of Erythrocyte Delta-Amino Levulinic Acid
Dehydratase Activity As a Short-Term Indicator in Fish of a
Harmful Exposure to Lead. J.Fish.Res.Board Can.
34(4):501-508.

15460

UEndp

Holcombe, G.W., G.L. Phipps, and J.T. Fiandt. 1983.
Toxicity of Selected Priority Pollutants to Various Aquatic
Organisms. Ecotoxicol.Environ.Saf. 7(4):400-409 (OECDG
Data File).

10417

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Hollis, L., L. Muench, and R.C. Playle. 1997. Influence of
Dissolved Organic Matter on Copper Binding, and Calcium
on Cadmium Binding, by Gills of Rainbow Trout. J.Fish Biol.
50:703-720.

17960

AF, UEndp

243

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Holwerda, D.A., J. Hemelraad, P.R. Veenhof, and D.I.
Zandee. 1988. Cadmium Accumulation and Depuration in
Anodonta anatina Exposed to Cadmium Chloride or
Cadmium-EDTA Complex. Bull.Environ.Contam.Toxicol.
40(3):373-380.

5669

AF, UEndp, Con

Hontela, A., C. Daniel, and A.C. Ricard. 1996. Effects of
Acute and Subacute Exposures to Cadmium on the
Interrenal and Thyroid Function in Rainbow Trout,
Oncorhynchus mykiss. Aquat.Toxicol. 35(3/4):171-182.

18245

UEndp, Eff

Hooftman, R.N., D.M.M. Adema, and J. Kauffman-Van
Bommel. 1989. Developing a Set of Test Methods for the
Toxicological Analysis of the Pollution Degree of
Waterbottoms. Rep. No. 16105, Netherlands Organization
for Applied Scientific Research: 68 p. (DUT).

5356

UEndp

Huebert, D.B., and J.M. Shay. 1991. The Effect of Cadmium
and Its Interaction with External Calcium in the Submerged
Aquatic Macrophyte Lemna trisulca L. Aquat.Toxicol. 20:57-
72.

5244

Plant, AF, UEndp

Huebert, D.B., and J.M. Shay. 1992. The Effect of EDTAon
Cadmium and Zinc Uptake and Toxicity in Lemna trisulca L.
Arch.Environ.Contam.Toxicol. 22:313-318.

3889

Plant, AF, UEndp

Huebert, D.B., and J.M. Shay. 1993. The Response of
Lemna trisulca L. to Cadmium. Environ.Pollut. 80:247-253.

6808

Plant, AF, UEndp

Hughes, G.M., S.F. Perry, and V.M. Brown. 1979. A
Morphometric Study of Effects of Nickel, Chromium and
Cadmium on the Secondary Lamellae of Rainbow Trout
Gills. Water Res. 13(7):665-679.

5571

UEndp, Eff

Husaini, Y., A.K. Singh, and L.C. Rai. 1991. Cadmium
Toxicity to Photosynthesis and Associated Electron
Transport System of Nostoc linckia.
Bull.Environ.Contam.Toxicol. 46(1): 146-150.

Plant, AF, UEndp,
Eff, Dur

244

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Husaini, Y., and L.C. Rai. 1991. Studies on Nitrogen and
Phosphorus Metabolism and the Photosynthetic Electron
Transport System of Nostoc linckia Under Cadmium Stress.
J.Plant Physiol. 138(4):429-435.

7157

Plant, AF, UEndp,
Dur

Iger, Y., R.A.C. Lock, J.C.A. Van der Meij, and S.E.
Wendelaar Bonga. 1994. Effects of Water-Borne Cadmium
on the Skin of the Common Carp (Cyprinus carpio).
Arch.Environ.Contam.Toxicol. 26(3):342-350.

13663

AF, UEndp

Ilangovan, K., R.O. Canizares-Villanueva, S. Gonzalez
Moreno, and D. Voltolina. 1998. Effect of Cadmium and Zinc
on Respiration and Photosynthesis in Suspended and
Immobilized Cultures of Chlorella vulgaris and
Scenedesmus acutus. Bull.Environ.Contam.Toxicol.
60(6):936-943.

19292

Plant, AF, UEndp

Indeherberg, M.B.M., N.M. Van Straalen, and E.R.
Schockaert. 1999. Combining Life-History and Toxicokinetic
Parameters to Interpret Differences in Sensitivity to
Cadmium Between Populations of Polycelis tenuis
(Platyhelminthes). Ecotoxicol.Environ.Saf. 44(1): 1-11.

20586

AF, UEndp, Dur

Inza, B., F. Ribeyre, R. Maury-Brachet, and A. Boudou.
1997. Tissue Distribution of Inorganic Mercury,
Methylmercury and Cadmium in the Asiatic Clam (Corbicula
fluminea) in Relation to the Contamination Levels.
Chemosphere 35(12):2817-2836.

18642

AF, UEndp

Jaffe, R.L. 1995. Rapid Assay of Cytotoxicity Using
Tetramitus flagellates. Toxicol.Ind.Health 11(5):543-558.

5895

Ace, AF, UEndp,
Dur

James, R. 1990. Individual and Combined Effects of Heavy
Metals on Behaviour and Respiratory Responses of
Oreochromis mossambicus. Indian J.Fish. 37(2):139-143.

9593

AF, UEndp, Eff

245

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

James, R., K. Sampath, and K.P. Ponmani. 1992. Effect of
Metal Mixtures on Activity of Two Respiratory Enzymes and
Their Recovery in Oreochromis mossambicus (Peters).
Indian J.Exp.Biol. 30(6):496-499.

8972

Jamil, K., and S. Hussain. 1992. Biotransfer of Metals to the
Insect Neochetina eichhornae Via Aquatic Plants.
Arch.Environ.Contam.Toxicol. 22(4):459-463.

6395

Plant, AF, UEndp,
Con

Jana, S., and M.A. Choudhuri. 1982. Senescence in
Submerged Aquatic Angiosperms: Effects of Heavy Metals.
New Phytol. 90:477-484.

6024

Plant, AF, UEndp,
Eff

Jana, S., and S.S. Sahana. 1989. Sensitivity of the
Freshwater Fishes Clarias batrachus and Anabas
testudineus to Heavy Metals. Environ.Ecol. 7(2):265-270.

2618

AF, UEndp

Janauer, G.A.. 1985. Heavy Metal Accumulation and
Physiological Effects on Austrian Macrophytes.
Symp.Biol.Hung. 29:21-30.

16938

Plant, AF, UEndp,
Dur

Janssen, C.R., and G. Persoone. 1993. Rapid Toxicity
Screening Tests for Aquatic Biota. 1. Methodology and
Experiments with Daphnia magna. Environ.Toxicol.Chem.
12:711-717.

6516

AF, Eff, Con

Janssen, M.P.M., C. Oosterhoff, G.J.S.M. Heijmans, and H.
Van der Voet. 1995. The Toxicity of Metal Salts and the
Population Growth of the Ciliate Colpoda cucculus.
Bull.Environ.Contam.Toxicol. 54(4):597-605.

20277

Ace, AF

Jaworska, M., A. Gorczyca, J. Sepiol, and P. Tomasik.
1997. Effect of Metal Ions on the Entomopathogenic
Nematode Heterorhabditis bacteriophora Poinar
(Nematode: Heterohabditidae) Under Laboratory
Conditions. Water Air Soil Pollut. 93:157-166.

40155

AF, UEndp

Jenner, H.A., and J.P.M. Janssen-Mommen. 1993.
Duckweed Lemna minor as a Tool for Testing Toxicity of
Coal Residues and Polluted Sediments.
Arch.Environ.Contam.Toxicol. 25(1 ):3-11.

16698

Plant, AF, UEndp

246

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Jenner, H.A., J. Hemelraad, J.M. Marquenie, and F.
Noppert. 1991. Cadmium Kinetics in Freshwater Clams
(Unionidae) Under Field and Laboratory Conditions.
Sci.Total Environ. 108(3):205-214.

3792

AF, UEndp, Con

Jennett, J.C., J.E. Smith, and J.M. Hassett. 1982. Factors
Influencing Metal Accumulation by Algae. EPA 600/2-82-
100, U.S.EPA, Cincinnati, OH :133 p..

14512

Plant, AF, UEndp,
Dur

Jindal, R., and A. Verma. 1990. Heavy Metal Toxicity to
Daphnia pulex. Indian J.Environ.Health 32(3):289-292.

7195

Acute test with
adults

Table 6 in 2001 ALC
document because
<24 h neonates
preferred

Jones, I., P. Kille, and G. Sweeney. 2001. Cadmium Delays
Growth Hormone Expression During Rainbow Trout
Development. J.Fish Biol. 59(4): 1015-1022.

62019

UEndp, Eff, Dur

Jones, J.R.E.. 1939. The Relation Between the Electrolytic
Solution Pressures of the Metals and Their Toxicity to the
Stickleback (Gasterosteus aculeatus L.). J.Exp.Biol.
16(4):425-437.

2851

AF, UEndp, Con

Jones, J.R.E.. 1940. A Further Study of the Relation
Between Toxicity and Solution Pressure, with Polycelis
nigra As Test Animal. J.Exp.Biol. 17:408-415.

10012

AF, UEndp, Dur,
Con

Jouany, J.M., J.F. Ferard, P. Vasseur, J. Gea, R. Truhaut,
and C. Rast. 1983. Interest of Dynamic Tests in Acute
Ecotoxicity Assessment in Algae. Ecotoxicol.Environ.Saf.
7:216-228.

11896

Plant, AF, UEndp,
Con

Juchelka, C.M., and T.W. Snell. 1994. Rapid Toxicity
Assessment Using Rotifer Ingestion Rate.
Arch.Environ.Contam.Toxicol. 26(4):549-554.

13660

AF, UEndp, Eff, Dur

Juchelka, C.M., and T.W. Snell. 1995. Rapid Toxicity
Assessment Using Ingestion Rate of Cladocerans and
Ciliates. Arch.Environ.Contam.Toxicol. 28(4):508-512.

14918

AF, UEndp, Eff, Dur

247

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Kammenga, J.E., C.A.M. Van Gestel, and J. Bakker. 1994.
Patterns Of Sensitivity To Cadmium And Pentachlorophenol
Among Nematode Species From Different Taxonomic And
Ecological Groups. Arch.Environ.Contam.Toxicol. 27(1 ):88-
94.

13656

AF, Dur

Kargin, F. 1996. Elimination of Cadmium from Cd-
Contaminated Tilapia zilli in Media Containing EDTA and
Freshwater: Changes in Protein Levels.
Bull.Environ.Contam.Toxicol. 57(2):211-216.

17412

AF, UEndp

Kargin, F., and H.Y. Cogun. 1999. Metal Interactions During
Accumulation and Elimination of Zinc and Cadmium in
Tissues of the Freshwater Fish Tilapia nilotica.
Bull.Environ.Contam.Toxicol. 63(4):511-519.

20648

UEndp

Karlsson-Norrgren, L., and P. Runn. 1985. Cadmium
Dynamics in Fish: Pulse Studies with 109Cd in Female
Zebrafish, Brachydanio rerio. J.Fish Biol. 27(5):571-581.

2167

AF, UEndp, Con

Karlsson-Norrgren, L., P. Runn, C. Haux, and L. Forlin.
1985. Cadmium-Induced Changes in Gill Morphology of
Zebrafish, Brachydanio rerio (Hamilton-Buchanan), and
Rainbow Trout, Salmo gairdneri Richardson. J.Fish Biol.
27(1 ):81 -95.

11497

AF, UEndp, Eff

Katti, S.R., and A.G. Sathyanesan. 1985. Chronic Effects of
Lead and Cadmium on the Testis of the Catfish Clarias
batrachus. Environ.Ecol. 3(4):596-598.

350

AF, UEndp, Eff

Kaviraj, A., and S. Das. 1995. Influence of Chelating Agent
EDTA, Adsorbent Activated Charcoal and Inorganic
Fertilizer (Single Super Phosphate) on the Histopathological
Changes in. Proc.Natl.Acad.Sci.India Sect.B 65(3):305-308.

14370

UEndp, Eff, Field

Kettle, W.D., F. DeNoyelles Jr., and C.H. Lei. 1980. Oxygen
Consumption of Zooplankton as Affected by Laboratory and
Field Cadmium Exposures. Bull.Environ.Contam.Toxicol.
25(4):547-553.

9784

AF, UEndp, Eff, Dur

248

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Khan, E.A., M.P. Sinha, N. Saxena, P.N. Panday, and P.N.
Mehrotra. 1991. Biochemical Variation During Ovarian
Vitellogenic Growth in a Hill Stream Teleost Garra mullya
(Skyes) Due to Cadmium Toxicity. J.Indian Fish.Assoc.
21:11-14.

18485

UEndp, Eff

Khangarot, B.S., and P.K. Ray. 1987. Sensitivity of Toad
Tadpoles, Bufo melanostictus (Schneider), to Heavy Metals.
Bui I. Environ. Contam. Toxicol. 38(3):523-527.

12339

Con

Khangarot, B.S., and P.K. Ray. 1988. Sensitivity of
Freshwater Pulmonate Snails, Lymnaea luteola L., to Heavy
Metals. Bull.Environ.Contam.Toxicol. 41 (2):208-213.

12943

Dur, Con

Khangarot, B.S., P.K. Ray, and H. Chandra. 1987. Daphnia
magna as a Model to Assess Heavy Metal Toxicity:
Comparative Assessment with Mouse System. Acta
Hydrochim. Hydrobiol. 15(4):427-432.

12575

Det

Khangarot, B.S., S. Mathur, and V.S. Durve. 1982.
Comparative Toxicity of Heavy Metals and Interaction of
Metals on a Freshwater Pulmonate Snail Lymnaea
acuminata (Lamarck). Acta Hydrochim.Hydrobiol. 10(4):367-
375.

11099

Dur, Con

Kislalioglu, M., E. Scherer, and R.E. NcNicol. 1996. Effects
of Cadmium on Foraging Behaviour of Lake Charr,
Salvelinus namaycush. Environ.Biol.Fish. 46(1):75-82.

17191

UEndp

Klaverkamp, J.F., and D.A. Duncan. 1987. Acclimation to
Cadmium Toxicity by White Suckers: Cadmium Binding
Capacity and Metal Distribution in Gill and Liver Cytosol.
Environ.Toxicol. Chem. 6(4):275-289.

12412

AF, UEndp, Con

Klerks, P.L., and P.R. Bartholomew. 1991. Cadmium
Accumulation and Detoxification in a Cd-Resistant
Population of the Oligochaete Limnodrilus hoffmeisteri.
Aquat.Toxicol. 19(2):97-112.

3616

UEndp, Con

249

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Knowles, C.O., and M.J. McKee. 1987. Protein and Nucleic
Acid Content in Daphnia magna during Chronic Exposure to
Cadmium. Ecotoxicol.Environ.Saf. 13(3):290-300.

12666

UEndp

Koizumi, N., and Y. Sekine. 1986. Excretion of Cadmium by
the Himedaka Oryzias latipes.

Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan Gakkaishi)
52(10): 1787-1790 (JPN) (ENG ABS).

12067

AF, UEndp, Dur,
Con

Koizumi, N., and Y. Sekine. 1988. Studies on the
Accumulation and Transfer of Pollutants Through Food
Chains. 8. Effects of Iron Contents in Himedaka (Oryzias
latipes) on the Toxicity. Sagami Joshi Daigaku Kiyo 52:27-
33 (JPN); C.A.Sel.-Environ.Pollut.20:111:110466z (1989).

3172

AF, UEndp, Dur

Kraak, M.H.S., D. Lavy, M. Toussaint, H. Schoon, W.H.M.
Peeters, and C. Davids. 1993. Toxicity of Heavy Metals to
the Zebra Mussel (Dreissena polymorpha). In: T.F.Nalepa
and D.W.Schloesser (Eds.), Zebra Mussels - Biology,
Impacts, and Control, Chapter 29, Lewis Publishers, Boca
Raton, FL :491-502.

17556

AF, UEndp

Kraak, M.H.S., D. Lavy, W.H.M. Peeters, and C. Davids.
1992. Chronic Ecotoxicity of Copper and Cadmium to the
Zebra Mussel Dreissena polymorpha.
Arch.Environ.Contam.Toxicol. 23(3):363-369.

6356

Kraak, M.H.S., M. Toussaint, D. Lavy, and C. Davids. 1994.
Short-Term Effects of Metals on the Filtration Rate of the
Zebra Mussel Dreissena polymorpha. Environ.Pollut.
84:139-143.

16692

AF, UEndp, Dur

Kraak, M.H.S., M. Toussaint, E.A.J. Bleeker, and D. Lavy.
1993. Metal Regulation in Two Species of Freshwater
Bivalves. In: R.Dallinger and P.S.Rainbow (Eds.),
Ecotoxicology of Metals in Invertebrates, Lewis Publ. :175-
186.

13830

AF, UEndp, Dur

Kraal, M.H., M.H.S. Kraak, C.J. De Groot, and C. Davids.
1995. Uptake and Tissue Distribution of Dietary and
Aqueous Cadmium by Carp (Cyprinus carpio).

Ecotoxicol. Environ.Saf. 31 (2): 179-183.

15170

AF, UEndp

250

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Kuhn, R., and M. Pattard. 1990. Results of the Harmful
Effects of Water Pollutants to Green Algae (Scenedesmus
subspicatus) in the Cell Multiplication Inhibition Test. Water
Res. 24(1):31-38 (OECDG Data File).

2997

Plant, AF

Kuhn, R., M. Pattard, K. Pernak, and A. Winter. 1989.
Results of the Harmful Effects of Water Pollutants to
Daphnia magna in the 21 Day Reproduction Test. Water
Res. 23(4):501-510 (OECDG Data File).

847

AF, UEndp

Kulkarni, K.M., and S.V. Kamath. 1980. The Metabolic
Response of Paratelphusa jacquemontii to Some Pollutants.
Geobios (Jodhpur) 7(2):70-73 (Author Communication
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5036

AF, UEndp, Eff, Dur

Kumada, H., S. Kimura, and M. Yokote. 1980. Accumulation
and Biological Effects of Cadmium in Rainbow Trout.
Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan Gakkaishi) 46(1 ):97-
103.

2028

AF, UEndp

Kumada, H., S. Kimura, M. Yokote, and Y. Matida. 1973.
Acute and Chronic Toxicity, Uptake and Retention of
Cadmium in Freshwater Organisms. Bull.Freshwater
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9245

Kungolos, A., and I. Aoyama. 1993. Interaction Effect, Food
Effect, and Bioaccumulation of Cadmium and Chromium for
the System Daphnia magna-Chlorella ellipsoidea.
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13311

Kuroshima, R.. 1992. Cadmium Accumulation in the
Mummichog, Fundulus heteroclitus, Adapted to Various
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5787

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Kuroshima, R.. 1992. Effects of Acute Exposure to
Cadmium on the Electrolyte Balance in Plasma of the Carp
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Gakkaishi) 58(6):1139-1144.

7829

AF, UEndp

251

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Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Kuroshima, R.. 1992. Comparison of Cadmium
Accumulation in Tissues Between Carp Cyprinus carpio and
Red Sea Bream Pagrus major.
Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan Gakkaishi)
58(7): 1237-1242.

7830

UEndp

Kusher, D.I., and J.W. Crim. 1991. Immunosuppression in
Bluegill (Lepomis macrochirus) Induced by Environmental
Exposure to Cadmium. Fish Shellfish Immunol. 1 (3): 157-
161.

19437

UEndp, Eff

Kwan, K.H.M., and S. Smith. 1991. Some Aspects of the
Kinetics of Cadmium and Thallium Uptake by Fronds of
Lemna minor L. New Phytol. 117(1):91 -102.

7810

Plant, AF, UEndp,
Con

Laegreid, M., J. Alstad, D. Klaveness, and H.M. Seip. 1983.
Seasonal Variation of Cadmium Toxicity Toward the Alga
Selenastrum capricornutum Printz in Two Lakes with
Different Humus Content. Environ.Sci.Technol. 17(6):357-
361.

10967

Plant, AF, Dur, Con

Lagerspetz, K.Y.H., A. Tiiska, and K.E.O. Senius. 1993.
Low Sensitivity of Ciliary Activity in the Gills of Anodonta
cygnea to Some Ecotoxicals. Comp.Biochem.Physiol.C
105(3):393-395.

8305

AF, Eff, Dur, Con

Lalande, M., and B. Pinel-Alloul. 1983. Acute Toxicity of
Cadmium, Copper, Mercury and Zinc to Chydorus
sphaericus (Cladocera) from Three Quebec Lakes. Water
Pollut.Res.J.Can. 18:103-113.

4258

Eff

Lalande, M., and B. Pinel-Alloul. 1984. Heavy Metals
Toxicity on Planktonic Crustacea of the Quebec Lakes
(Toxicite des Metaux Lourds sur les Crustaces
Planctoniques des Lacs du Quebec). Sci.Tech.Eau
17(3):253-259 (FRE) (ENG ABS).

10724

AF, Eff, Con

Lalande, M., and B. Pinel-Alloul. 1986. Acute Toxicity of
Cadmium, Copper, Mercury and Zinc to Tropocyclops
Prasinus mexicanus (Cyclopoida, Copepoda) From Three
Quebec Lakes. Environ.Toxicol.Chem. 5(1):95-102.

12292

AF, Eff, Dur, Con

252

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Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Lam, P.K.S.. 1996. Interpopulation Differences in Acute
Response of Brotia hainanensis (Gastropoda,
Prosobranchia) to Cadmium: Genetic or Environmental
Variance?. Environ.Pollut. 94(1): 1 -7.

18534

AF, UEndp, Dur

Lam, P.K.S., K.N. Yu, K.P. Ng, and M.W.K. Chong. 1997.
Cadmium Uptake and Depuration in the Soft Tissues of
Brotia hainanensis (Gastropoda: Prosobranchia:
Thiaridae): A Dynamic Model. Chemosphere 35(11):2449-
2461.

18638

AF, UEndp

Langevoord, M., M.H.S. Kraak, M.H. Kraal, and C. Davids.
1995. Importance of Prey Choice for Cd Uptake by Carp
(Cyprinus carpio) Fingerlings. J.N.Am.Benthol.Soc.
14(3):423-429.

14891

AF, UEndp, RouExp

Larsen, J., and B. Svensmark. 1991. Labile Species ofPb,
Zn and Cd Determined by Anodic Stripping Staircase
Voltammetry and Their Toxicity to Tetrahymena. Talanta
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3716

Ace, AF, Dur

Lasheen, M.R., S.A. Shehata, and G.H. AN. 1990. Effect of
Cadmium, Copper and Chromium (VI) on the Growth of Nile
Water Algae. Water Air Soil Pollut. 50(1 /2):19-30.

10326

Plant, NoOrg, AF,
UEndp

Laskowski, R., and S.P. Hopkin. 1996. Effect of Zn, Cu, Pb
and Cd on Fitness in Snails (Helix aspersa).

Ecotoxicol. Envi ron. Saf. 34(1):59-69.

45063

AF, Eff

Laube, V.M., C.N. McKenzie, and D.J. Kushner. 1980.
Strategies of Response to Copper, Cadmium, and Lead by
Blue-Green and a Green Alga. Can.J.Microbiol.
26(11): 1300-1311.

9477

Plant, AF, UEndp

Lawrence, S.G., M.H. Holoka, and R.D. Hamilton. 1989.
Effects of Cadmium on a Microbial Food Chain,
Chlamydomonas reinhardii and Tetrahymena vorax.
Sci.Total Environ. 87/88:381-395.

3127

Plant, AF, UEndp

Lee, C.L., T.C. Wang, C.H. Hsu, and A.A. Choiu. 1998.
Heavy Metals Sorption by Aquatic Plants in Taiwan.
Bull.Environ.Contam.Toxicol. 61:497-504.

19419

AF, UEndp, Dur

253

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Lee, D.R.. 1976. Development of an Invertebrate Bioassay
to Screen Petroleum Refinery Effluents Discharged into
Freshwater. Ph.D.Thesis, Virginia Polytechnic Inst.and
State University, Blacksburg, VA:108.

3402

Dur

Lee, H.L., B. Lustigman, V. Schwinge, I.Y. Chiu, and S.
Hsu. 1992. Effect of Mercury and Cadmium on the Growth
of Anacystis nidulans. Bull.Environ.Contam.Toxicol.
49(2):272-278.

6000

Plant, AF, UEndp,
Con

Lee, T.H., P.P. Hwang, and H.C. Lin. 1996. Morphological
Changes of Integumental Chloride Cells to Ambient
Cadmium During the Early Development of the Teleost,
Oreochromis mossambicus. Environ.Biol.Fish. 45(1 ):95-
102.

14912

UEndp, Eff

Lefcort, H., R.A. Meguire, L.H.Wilson, and W.F. Ettinger.
1998. Heavy Metals Alter the Survival, Growth,
Metamorphosis, and Antipredatory Behavior of Columbia
Spotted Frog (Rana luteiventris) Tadpoles.
Arch.Environ.Contam.Toxicol. 35(3):447-456.

20181

AF, UEndp

Les, A., and R.W. Walker. 1984. Toxicity and Binding of
Copper, Zinc, and Cadmium by the Blue-Green Alga,
Chroococcus paris. Water Air Soil Pollut. 23(2): 129-139.

11020

Plant, AF, Uendp

Lewander, M., M. Greger, L. Kautsky, and E. Szarek. 1996.
Macrophytes as Indicators of Bioavailable Cd, Pb and Zn
Flow in the River Przemsza, Katowice Region.
Appl.Geochem. 11 (1/2):169-173.

19971

Plant, AF, Uendp

Lewis, P.A., and C.I. Weber. 1985. A Study of the Reliability
of Daphnia Acute Toxicity Tests. In: R.D.Cardwell, R.Purdy,
and R.C.Bahner (Eds.), Aquatic Toxicology and Hazard
Assessment, 7th Symposium, ASTM STP 854, Philadelphia,
PA:73-86.

11861

AF, Con

254

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Lewis, P.A., and W.B. Horning II. 1991. Differences in Acute
Toxicity Test Results of Three Reference Toxicants on
Daphnia at Two Temperatures. Environ.Toxicol.Chem.
10:1351-1357.

3920

AF, Dur

Liao, I.C., and C.S. Hsieh. 1990. Toxicity of Three Heavy
Metals to Macrobrachium rosenbergii. In: R.Hirano and
I.Hanyu (Eds.), Proc.of the 2nd Asian Fisheries Forum, April
17-22, 1989, Tokyo, Japan, Asian Fisheries Society, Manila,
Philippines :923-926.

16218

UEndp

Lin, K.C., C.I. Lin, and C.Y. Chen. 1996. The Effect of
Limiting Nutrient on Metal Toxicity to Selenastrum
capricornutum. Toxicol.Environ.Chem. 56(1-4):47-61.

19765

AF, Dur

Lopez, J., M.D. Vazquez, and A. Carballeira. 1994. Stress
Responses and Metal Exchange Kinetics Following
Transplant of the Aquatic Moss Fontinalis antipyretica.
Freshw.Biol. 32:185-198.

45134

Plant, AF, UEndp

Loumbourdis, N.S., P. Kyriakopoulou-Sklavounou, and G.
Zachariadis. 1999. Effects of Cadmium Exposure on
Bioaccumulation and Larval Growth in the Frog Rana
ridibunda. Environ.Pollut. 104(3):429-433.

19890

UEndp, NonRes

Lowe-Jinde, L., and A.J. Niimi. 1984. Short-Term and Long-
Term Effects of Cadmium on Glycogen Reserves and Liver
Size in Rainbow Trout (Salmo gairdneri Richardson).

Arch. Environ. Contam.Toxicol. 13(6):759-764.

10428

UEndp

Lundebye, A.K., M.H.G. Berntssen, S.E. Wendelaar Bonga,
and A. Maage. 1999. Biochemical and Physiological
Responses in Atlantic Salmon (Salmo salar) Following
Dietary Exposure to Copper and Cadmium. Mar.Pollut.Bull.
39(1-12): 137-144.

20619

AF, UEndp, RouExp

Maage, A.. 1990. Comparison of Cadmium Concentrations
in Atlantic Salmon (Salmo salar) Fry Fed Different
Commercial Feeds. Bull.Environ.Contam.Toxicol. 44(5):770-
775.

3164

AF, UEndp, Con,
RouExp

255

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Mackie, G.L.. 1989. Tolerances of Five Benthic
Invertebrates to Hydrogen Ions and Metals (Cd, Pb, Al).
Arch. Environ. Contam. Toxicol. 18(1/2):215-223.

19974

MacPhee, C., and R. Ruelle. 1969. Lethal Effects of 1888
Chemicals upon Four Species of Fish From Western North
America. Univ.of Idaho Forest, Wildl.Range Exp.Station
Bull.No.3, Moscow, ID :112 p.

15148

UEndp, Dur, Con

Madoni, P., D. Davoli, and G. Gorbi. 1994. Acute Toxicity of
Lead, Chromium, and Other Heavy Metals to Ciliates from
Activated Sludge Plants. Bull.Environ.Contam.Toxicol.
53(3):420-425.

13671

Ace, AF, Dur

Madoni, P., D. Davoli, G. Gorbi, and L. Vescovi. 1996. Toxic
Effect of Heavy Metals on the Activated Sludge Protozoan
Community. Water Res. 30(1): 135-141.

16363

Ace, AF, Dur

Madoni, P., G. Esteban, and G. Gorbi. 1992. Acute Toxicity
of Cadmium, Copper, Mercury, and Zinc to Ciliates from
Activated Sludge Plants. Bull.Environ.Contam.Toxicol.
49(6):900-905.

5116

Ace, Dur

Maeda, S., M. Mizoguchi, A. Ohki, and T. Takeshita. 1990.
Bioaccumulation of Zinc and Cadmium in Freshwater Alga,
Chlorella vulgaris. Part I. Toxicity and Accumulation.
Chemosphere 21 (8):953-963.

239

Plant, AF, UEndp

Maeda, S., M. Mizoguchi, A. Ohki, J. Inanaga, and T.
Takeshita. 1990. Bioaccumulation of Zinc and Cadmium in
Freshwater Alga, Chlorella vulgaris. Part II. Association
Mode of the Metals and all Tissue. Chemosphere 21(8):965-
973.

240

Plant, AF, UEndp,
Con

Majewski, H.S., and M.A. Giles. 1981. Cardiovascular-
Respiratory Responses of Rainbow Trout (Salmo gairdneri)
During Chronic Exposure to Sublethal Concentrations of
Cadmium. Water Res. 15(10):1211-1217.

2403

AF, UEndp, Eff

256

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Malley, D.F., J.F. Klaverkamp, S.B. Brown, and P.S.S.
Chang. 1993. Increase in Metallothionein in Freshwater
Mussles Anodonta grandis grandis Exposed to Cadmium in
the Laboratory and the Field. Water Pollut.Res.J.Can.
28(1):253-273.

4305

AF, UEndp

Manson, J.M., and E.J. O'Flaherty. 1978. Effects of
Cadmium on Salamander Survival and Limb Regeneration.
Environ. Res. 16(1-3):62-69.

5404

AF, UEndp

Marshall, J.S.. 1978. Population Dynamics of Daphnia
galeata mendotae as Modified by Chronic Cadmium Stress.
J.Fish.Res.Board Can. 35(4):461-469.

8392

AF, UEndp

Marshall, J.S.. 1978. Field Verification of Cadmium Toxicity

to Laboratory Daphnia Populations.

Bull.Environ.Contam.Toxicol. 20(3):387-393.

15585

AF, Uendp

Marshall, J.S.. 1979. Cadmium Toxicity to Laboratory and
Field Populations of Daphnia galeata mendotae.
Bull.Environ.Contam.Toxicol. 21 (4-5):453-457.

8391

Marshall, J.S., J.I. Parker, D.L. Mellinger, and C. Lei. 1983.
Bioaccumulation and Effects of Cadmium and Zinc in a
Lake Michigan Plankton Community. Can.J.Fish.Aquat.Sci.
40(9):1469-1479.

11256

NoOrg, AF, UEndp

Martin, P.A., D.C. Lasenby, and R.D. Evans. 1990. Fate of
Dietary Cadmium at Two Intake Levels in the Odonate
Nymph, Aeshna canadensis. Bull.Environ.Contam.Toxicol.
44(1):54-58.

2816

AF, UEndp, Dur

Martinez, M., A. Torreblanca, J. Del Ramo, A. Pastor, and J.
Diaz-Mayans. 1993. Cadmium Induced Metallothionein in
Hepatopancreas of Procambarus clarkii: Quantification by a
Silver-Saturation Method. Comp.Biochem.Physiol.C
105(2):263-267.

8047

UEndp, Dur

Martinez, M., J. Del Ramo, A. Torreblanca, A. Pastor, and J.
Diaz-Mayans. 1996. Cadmium Toxicity, Accumulation and
Metallothionein Induction in Echinogammarus
echinosetosus. J.Environ.Sci.Health A31 (7): 1605-1617.

20393

UEndp, Dur,
NonRes

257

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Mazurek, U., T. Naglik, A. Wilczok, and M. Latocha. 1990.
Effect of Cadmium on Photosynthetic Pigments in
Synchronously Growing Chlorella Cells. Biochim.Pol.
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7214

Plant, AF, UEndp,
Dur

McCahon, C.P., and D. Pascoe. 1988. Cadmium Toxicity to
the Freshwater Amphipod Gammarus pulex (L.) During the
Moult Cycle. Freshw.Biol. 19(2):197-203.

9639

NonRes

McCahon, C.P., and D. Pascoe. 1988. Use of Gammarus
pulex (L.) in Safety Evaluation Tests: Culture and Selection
of a Sensitive Life Stage. Ecotoxicol. Environ.Saf. 15(3):245-
252.

13075

Dur, Con, NonRes

McConnell, M.A., and R.C. Harrel. 1995. The Estuarine
Clam Rangia cuneata (Gray) as a Biomonitor of Heavy
Metals Under Laboratory and Field Conditions.
Am.Malacol.Bull. 11(2):191-201.

19514

UEndp

McMahon, R.F., B.N. Shipman, and D.E. Erck. 1990. Effects
of Two Molluscicides on the Freshwater Macrofouling
Bivalve, Dreissena polymorpha, the Zebra Mussel.

Proc.Am. Power Conf. 51:1006-1011.

17063

AF, UEndp

Medina, J., J. Diaz-Mayans, F. Hernandez, A. Pastor, J. Del
Ramo, and A. Torreblanca. 1991. Study of the Toxicity and
Bioaccumulation of Some Heavy Metals in the Crayfish
Procambarus clarkii (Girard, 1852) of the Albufera Lake of
Valencia, Spain. In: Final Reports on Research Projects
Dealing with Mercury, Toxicity and Analytical Techniques,
UNEP, Athens, Greece, MAP Tech.Rep.Ser.No.51 :105-
131.

4205

AF, Eff, Con

Mersch, J., E. Morhain, and C. Mouvet. 1993. Laboratory
Accumulation and Depuration of Copper and Cadmium in
the Freshwater Mussel Dreissena polymorpha and the
Aquatic Moss Rhynchostegium ripariodes. Chemosphere
27(8):1475-1485.

8332

Plant, AF, UEndp

258

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Meyer, W., M. Kretschmer, A. Hoffmann, and G. Harisch.
1991. Biochemical and Histochemical Observations on
Effects of Low-Level Heavy Metal Load (Lead, Cadmium) in
Different Organ Systems of the Freshwater.

Ecotoxicol. Envi ron. Saf. 21 (2): 137-156.

376

AF, UEndp, Eff

Michibata, H.. 1981. Effect of Water Hardness on the
Toxicity of Cadmium to the Egg of the Teleost Oryzias
latipes. Bull.Environ.Contam.Toxicol. 27(2): 187-192.

15399

AF, NonRes

Michibata, H., S. Sahara, and M.K. Kojima. 1986. Effects of
Calcium and Magnesium Ions on the Toxicity of Cadmium to
the Egg ofthe Teleost, Oryzias latipes. Environ. Res.
40(1): 110-114.

11818

AF, UEndp, Dur,
Con, NonRes

Miliou, H., N. Zaboukas, and M. Moraitou-Apostolopoulou.
1998. Biochemical Composition, Growth, and Survival ofthe
Guppy, Poecilia reticulata, During Chronic Sublethal
Exposure to Cadmium. Arch.Environ.Contam.Toxicol.
35(1):58-63.

19310

Miller, J.C., and R. Landesman. 1978. Reduction of Heavy
Metal Toxicity to Xenopus Embryos by Magnesium Ions.
Bull.Environ.Contam.Toxicol. 20:93-95 (Author
Communication Used).

2743

AF, UEndp, Eff,
Con

Mizutani, A., E. Ifune, A. Zanella, and C. Eriksen. 1991.
Uptake of Lead, Cadmium and Zinc by the Fairy Shrimp,
Branchinecta longiantenna (Crustacea; Anostraca).
Hydrobiologia 212:145-149.

3681

AF, UEndp

Morgan, W.S.G.. 1976. Fishing for Toxicity: Biological
Automonitor for Continuous Water Quality Control. Effluent
Water Treat. J. 16(9):471-472, 474-475 (Author
Communication Used).

5462

UEndp, Eff, Dur,
Con

Morgan, W.S.G.. 1977. Biomonitoring with Fish: An Aid to
Industrial Effluent and Surface Water Quality Control.

Prog .Water Technol. 9(3):703-711.

5463

UEndp, Eff, Dur

259

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Morgan, W.S.G.. 1978. The Use of Fish As a Biological
Sensor for Toxic Compounds in Potable Water. Prog.Water
Technol.10(1/2):395-398 (Author Communication Used).

11127

UEndp, Eff, Dur,
Con

Morgan, W.S.G.. 1979. Fish Locomotor Behavior Patterns
as a Monitoring Tool. J.Water Pollut.Control Fed. 51(3):580-
589.

131

AF, Uendp, Eff, Dur

Mostafa, I.Y., and Z. Khalil. 1986. Uptake, Release and
Incorporation of Radioactive Cadmium and Mercury by the
Freshwater Alga Phormidium fragile. Isot.Radiat.Res.
18(1):57-62.

125

Plant, AF, UEndp

Mount, D.I., and C.E. Stephan. 1967. A Method for
Detecting Cadmium Poisoning in Fish. J.Wildl.Manage.
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8087

AF, UEndp, Con

Mowbray, D.L.. 1988. Assessment of the Biological Impact
of Ok Tedi Mine Tailings, Cyanide and Heavy Metals. In:
J.C.Pernetta (Ed.), Potential Impacts of Mining on the Fly
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17356

Moza, U., S.S. DeSilva, and B.M. Mitchell. 1995. Effect of
Sub-Lethal Concentrations of Cadmium on Food Intake,
Growth and Digestibility in the Gold Fish, Carassius auratus
L. J.Environ.Biol. 16(3):253-264.

16668

UEndp, Eff

Muino, C.V., L. Ferrari, and A. Salibian. 1990. Protective
Action of Ions Against Cadmium Toxicity to Young Bufo
arenarum Tadpoles. Bull.Environ.Contam.Toxicol.
45(3):313-319.

14973

Muller, K.W., and H.D. Payer. 1979. The Influence of pH on
the Cadmium-Repressed Growth of the Algae Coelastrum
proboscideum. Physiol.Plant 45:415-418.

14389

Plant, AF, UEndp,
Dur

Muller, K.W., and H.D. Payer. 1980. The Influence of Zinc
and Light Conditions on the Cadmium-Repressed Growth of
the Green Alga Coelastrum proboscideum. Physiol.Plant
50:265-268.

14390

Plant, AF, UEndp,
Dur

260

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Munger, C., L. Hare, A. Craig, and P.M. Charest. 1999.
Influence of Exposure Time on the Distribution of Cadmium
Within the Cladoceran Ceriodaphnia dubia. Aquat.Toxicol.
44(3) :195-200.

20084

UEndp

Muramoto, S.. 1980. Effect of Complexans (EDTA, NTAand
DTPA) on the Exposure to High Concentrations of
Cadmium, Copper, Zinc and Lead.
Bull.Environ.Contam.Toxicol. 25(6):941-946.

6698

AF, UEndp, Dur,
Con

Muramoto, S.. 1981. Vertebral Column Damage and
Decrease of Calcium Concentration in Fish Exposed
Experimentally to Cadmium. Environ.Pollut.Ser.A Ecol.Biol.
24:125-133.

2590

AF, UEndp, Con

Muramoto, S.. 1981. Influence of Complexans (EDTA,
DTPA) on the Toxcity of Cadmium to Fish at Chronic
Levels. Bull.Environ.Contam.Toxicol. 26(5):641-646.

15167

AF, UEndp

Muramoto, S.. 1981. Variations of Some Elements in

Cadmium-Induced, Malformed Fish.

Bull.Environ.Contam.Toxicol. 27(2):193-200.

15402

AF, UEndp, Con

Murti, R., and G.S. Shukla. 1984. Acute Toxicity of Mercuric
Chloride and Cadmium Chloride to Freshwater Prawn,
Macrobrachium lamarrei (H. Milne Edwards). Acta
Hydrochim. Hydrobiol. 12(6):689-692.

11443

AF, Dur, Con

Musko, I.B., W. Meinel, R. Krause, and M. Barlas. 1990.
The Impact of Cd and Different pH on the Amphipod
Gammarus fossarum Koch (Crustacea: Amphipoda).
Comp.Biochem.Physiol.C 96(1): 11 -16.

3445

Con

Mwangi, S.M., and M.A. Alikhan. 1993. Cadmium and
Nickel Uptake by Tissues of Cambarus bartoni (Astacidae,
Decapoda, Crustacea): Effects on Copper and Zinc Stores.
Water Res. 27(5):921-927.

6986

UEndp, Dur

261

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Mysing-Gubala, M., and M.A. Poirrier. 1981. The Effects of
Cadmium and Mercury on Gemmule Formation and
Gemmosclere Morphology in Ephydatia fluviatilis (Porifera:
Spongillidae). Hydrobiologia 76(1/2): 145-148 (Author
Communication Used).

9487

AF, UEndp, Eff

Naimo, T.J., G.J. Atchison, and L.E. Holland-Bartels. 1992.
Sublethal Effects of Cadmium on Physiological Responses
in the Pocketbook Mussel, Lampsilis ventricosa.
Environ.Toxicol. Chem. 11 (7):1013-1021.

5925

AF, UEndp, Eff

Nakagawa, H., and S. Ishio. 1988. Aspects of Accumulation
of Cadmium Ion in the Egg of Medaka Oryzias latipes.
Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan Gakkaishi)
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3211

AF, UEndp, Dur,
Con

Nakagawa, H., and S. Ishio. 1989. Aspects of Accumulation
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3210

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Nakagawa, H., and S. Ishio. 1989. Effects of Water pH on
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Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan Gakkaishi) 55(2):327-
331.

3212

AF, UEndp, Dur,
Con

Nakagawa, H., and S. Ishio. 1989. Effects of Water
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3213

AF, UEndp, Dur

Nakanishi, H., T. Tsuda, S. Fukui, and T. Hirayama. 1987.
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12310

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262

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EcoRef#

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Comment

Nalecz-Jawecki, G., and J. Sawicki. 1998. Toxicity of
Inorganic Compounds in the Spirotox Test: A Miniaturized
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18997

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Naqvi, S.M., and R.D. Howell. 1993. Cadmium and Lead
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6843

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Naqvi, S.M., R.D. Howell, and M. Sholas. 1993. Cadmium
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9068

Plant, AF, UEndp

Nasu, Y., and M. Kugimoto. 1981. Lemna (Duckweed) As
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9489

Plant, AF, UEndp,
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Nasu, Y., K. Hirabayashi, and M. Kugimoto. 1988. The
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9057

Plant, AF, UEndp,
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Nasu, Y., M. Kugimoto, 0. Tanaka, D. Yanase, and A.
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11477

Plant, AF, UEndp

Naylor, C., E.J. Cox, M.C. Bradley, and P. Calow. 1992.
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6556

Eff, Con

263

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EcoRef#

Rejection Code(s)

Comment

Nebeker, A.V., G.S. Schuytema, and S.L. Ott. 1994. Effects
of Cadmium on Limb Regeneration in the Northwestern
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Arch.Environ.Contam.Toxicol. 27(3):318-322.

13685

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Nebeker, A.V., M.A. Cairns, S.T. Onjukka, and R.H. Titus.
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12311

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Nelson, S.M., and R.A. Roline. 1998. Evaluation of the
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18961

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Bui I. Environ. Contam. Toxicol. 62(2):230-237.

20030

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Nicola Giudici, M., L. Migliore, C. Gambardella, and A.
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12871

Nir, R., A. Gasith, and A.S. Perry. 1990. Cadmium Uptake
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2799

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Nishihara, T., T. Shimamoto, K.C. Wen, and M. Kondo.
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12185

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Norey, C.G., A. Cryer, and J. Kay. 1990. Cadmium Uptake
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3460

AF, UEndp, Con

264

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EcoRef#

Rejection Code(s)

Comment

Norey, C.G., M.W. Brown, A. Cryer, and J. Kay. 1990. A
Comparison of the Accumulation, Tissue Distribution and
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3451

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Notenboom, J., K. Cruys, J. Hoekstra, and P. Van Beelen.
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5975

Oikari, A., J. Kukkonen, and V. Virtanen. 1992. Acute
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5679

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Okamura, H., and I. Aoyama. 1994. Interactive Toxic Effect
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13501

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Olsson, P.E., and C. Hogstrand. 1987. Subcellular
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Onuoha, G.C., F.O. Nwadukwe, and E.S. Erondu. 1996.
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Ornes, W.H., and K.S. Sajwan. 1993. Cadmium
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9233

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Oronsaye, J.A.O.. 1987. The Uptake and Loss of Dissolved
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12680

AF, UEndp

265

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Comment

Oronsaye, J.A.O.. 1989. Histological Changes in the
Kidneys and Gills of the Stickleback, Gasterosteus
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729

AF, UEndp, Eff

Oronsaye, J.A.O., and A.E. Brafield. 1984. The Effect of
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10754

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5005

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Outridge, P.M., and T.C. Hutchinson. 1990. Effects of
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7779

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Overnell, J.. 1975. The Effect of Some Heavy Metal Ions on
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15663

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18552

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Palanichamy, S., and P. Baskaran. 1995. Selected
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Pandey, A.K., and A. Shrivastava. 1985. Chronic Cadmium
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12358

UEndp, Eff

266

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Rejection Code(s)

Comment

Pantani, C., P.F. Ghetti, A. Cavacini, and P. Muccioni. 1990.
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16240

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12425

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2038

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Pascoe, D., K.A. Williams, and D.W.J. Green. 1989. Chronic
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9627

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Pascoe, D., S.A. Evans, and J. Woodworth. 1986. Heavy
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11987

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Patil, H.S., and M.B. Kaliwal. 1983. Influence of Cadmium,
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1(3): 175-177.

11545

AF, UEndp, Eff,
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267

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EcoRef#

Rejection Code(s)

Comment

Patil, H.S., and M.B. Kaliwal. 1986. Relative Sensitivity of a
Freshwater Prawn Macrobrachium hendersodyanum to
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12787

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Pawlik, B., T. Skowronski, Z. Ramazanow, P. Gardestrom,
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4153

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Pelgrom, S.M.G.J., L.P.M. Lamers, A. Haaijman, P.H.M.
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18517

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Pelgrom, S.M.G.J., L.P.M. Lamers, R.A.C. Lock, P.H.M.
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16383

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17869

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Penttinen, S., A. Kostamo, and J.V.K. Kukkonen. 1998.
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15821

Det

268

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Rejection Code(s)

Comment

Penttinen, S., J. Kukkonen, and A. Oikari. 1995. The
Kinetics of Cadmium in Daphnia magna as Affected by
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14219

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Bui I. Environ. Contam. Toxicol. 56(4):663-669.

17110

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Perez-Coll, C.S., J. Herkovits, 0. Fridman, P. Daniel, and
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20345

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Peterson, R.H.. 1976. Temperature Selection of Juvenile
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5160

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Peverly, J.H.. 1988. Cadmium Movement and Accumulation
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13403

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Phipps, G.L., V.R. Mattson, and G.T. Ankley. 1995. Relative
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14907

Piccinni, E., and V. Albergoni. 1996. Cadmium
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Pickering, Q.H., and C. Henderson. 1964. The Acute
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2033

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Pittinger, C.A., D.J. Versteeg, B.A. Blatz, and E.M. Meiers.
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Aquat.Toxicol. 24(1/2):83-102.

6561

AF, UEndp

269

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ECOTOX
EcoRef#

Rejection Code(s)

Comment

Playle, R.C., D.G. Dixon, and K. Burnison. 1993. Copper
and Cadmium Binding to Fish Gills: Estimates of Metal-Gill
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Pokethitiyook, P., E.S. Upatham, and 0. Leelhaphunt. 1987.
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45061

Polar, E., and R. Kucukcezzar. 1986. Influence of Some
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11731

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Poldoski, J.E.. 1979. Cadmium Bioaccumulation Assays.
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2441

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Postma, J.F., A. Van Kleunen, and W. Admiraal. 1995.
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16129

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Postma, J.F., and C. Davids. 1995. Tolerance Induction and
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15321

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Postma, J.F., M.C. Buckert-De Jong, N. Staats, and C.
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13653

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Postma, J.F., P. Van Nugteren, and M.B. Buckert-De Jong.
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16512

AF, UEndp

270

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ECOTOX
EcoRef#

Rejection Code(s)

Comment

Pratap, H.B., and S.E. Wendelaar Bonga. 1993. Effect of
Ambient and Dietary Cadmium on Pavement Cells, Chloride
Cells, and Na+/K+ -ATPase Activity in the Gills of the
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8265

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Pratt, J.R., D. Mochan, and Z. Xu. 1997. Rapid Toxicity
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20289

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Presing, M., K.V. Balogh, and J. Salanki. 1993. Cadmium
Uptake and Depuration in Different Organs of Lymnaea
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7094

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Pundir, R., and A.B. Saxena. 1990. Seasonal Changes in
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3329

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Pundir, R., and A.B. Saxena. 1992. Chronic Toxic Exposure
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3902

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Pynnonen, K., D.A. Holwerda, and D.I. Zandee. 1987.
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12961

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Qureshi, S.A., A.B. Saksena, and V.P. Singh. 1980. Acute
Toxicity of Four Heavy Metals to Benthic Fish Food
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5288

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Rachlin, J.W., and A. Grosso. 1991. The Effects of pH on
the Growth of Chlorella vulgaris and Its Interactions with
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508.

102

Plant, AF, UEndp

271

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ECOTOX
EcoRef#

Rejection Code(s)

Comment

Rachlin, J.W., T.E. Jensen, B. Warkentine, and H.H.
Lehman. 1982. The Growth Response of the Green Alga
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14310

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Radhakrishnaiah, K.. 1988. Effect of Cadmium on the
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12903

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Rai, U.N., and P. Chandra. 1989. Removal of Heavy Metals
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3348

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Rai, U.N., R.D. Tripathi, S. Sinha, and P. Chandra. 1995.
Chromium and Cadmium Bioaccumulation and Toxicity in
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19941

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Raj, A.I.M., and P.S. Hameed. 1991. Effect of Copper,
Cadmium and Mercury on Metabolism of the Freshwater
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3776

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Ramesha, A.M., T.R.C. Gupta, C. Lingdhal, K.V.B. Kumar,
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Mercury and Cadmium to the Common Carp Cyprinus
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18079

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Ramesha, A.M., T.R.C. Guptha, R.J. Katti, G. Gowda, and
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18178

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Randi, A.S., J.M. Monserrat, E.M. Rodriguez, and L.A.
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20252

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272

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ECOTOX
EcoRef#

Rejection Code(s)

Comment

Rani, A.U., and R. Ramamurthi. 1987. Effects of Sub-lethal
Concentration of Cadmium on Oxidative Metabolism in the
Fresh Water Teleost, Tilapia mossambica. Indian
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9974

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Rani, A.U., and R. Ramamurthi. 1989. Histopathological
Alterations in the Liver of Freshwater Teleost Tilapia
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476

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Rao, I.J., and M.N. Madhyastha. 1987. Toxicities of Some
Heavy Metals to the Tadpoles of Frog, Microhyla ornata
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6357

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Rausina, G., J.W. Goode, M.L. Keplinger, and J.C.
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8424

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16334

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Reddy, S.L.N., and N.B.R. Venugopal. 1991. In Vivo Effects
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3778

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3438

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274

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19781

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18987

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Rishi, K.K., and M. Jain. 1998. Effect of Toxicity of
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18906

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8390

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Rogge, R.W., and C.D. Drewes. 1993. Assessing Sublethal
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8259

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Rossini, G.D.B., and A.E. Ronco. 1996. Acute Toxicity
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16939

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5078

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10762

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Rejection Code(s)

Comment

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10929

Tests included
sediment

Possible 48 h LC50s
available from study,
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8709

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Rejection Code(s)

Comment

Sehgal, R., and A.B. Saxena. 1987. Determination of Acute
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Sehgal, R., V. Tomar, and A.K. Pandey. 1984. Comparative
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11017

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Selby, D.A., J.M. Ihnat, and J.J. Messer. 1985. Effects of
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Sharma, A., and M.S. Sharma. 1993. Vertebral Defects in
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4144

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11738

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EcoRef#

Rejection Code(s)

Comment

Shcherban, E.P. 1977. Toxicity of Some Heavy Metals for
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5924

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Shedd, T.R., M.W. Widder, M.W. Toussaint, M.C. Sunkel,
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20487

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Sherman, R.E., S.P. Gloss, and L.W. Lion. 1987. A
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12647

Six 96 h LC50s
from approx. 6,900
to 15,200 ug/L
dissolved cadmium
normalized to 100
mg/L as CaC03
hardness. Tests
were static,
measured.

This study appears to
provide appropriate
96 h LC50s for P.
promelas, but the
paper should be
secured to ensure
acceptability. Species
is relatively
insensitive to acute
cadmium exposure

Shivaraj, K.M., and H.S. Patil. 1988. Toxicity of Cadmium
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13240

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Shivaraj, K.M., B.B. Hosetti, and H.S. Patil. 1989. Oxygen
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2625

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12743

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Shukla, J.P., and K. Pandey. 1988. Toxicity and Long Term
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56638

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281

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EcoRef#

Rejection Code(s)

Comment

Silverman, H., J.W. Mcneil, and T.H. Dietz. 1987. Interaction
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12688

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65402

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Singh, J., P.N. Viswanathan, M. Gupta, and S. Devi. 1993.
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8119

Plant, AF, UEndp

Singh, J., S. Devi, G. Chawla, M. Gupta, and P.N.
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17892

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20000

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Sinha, G.M., A.B. Kesh, K. Sengupta, and A.K. Das. 1992.
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13586

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15038

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282

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ECOTOX
EcoRef#

Rejection Code(s)

Comment

Skowronski, T., S. Szubinska, B. Pawlik, M. Jakubowski, R.
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3940

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Slabbert, J.L., and W.S.G. Morgan. 1982. A Bioassay
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11048

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16368

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17278

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Slooff, W. 1979. Detection Limits of a Biological Monitoring

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5938

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Slooff, W. 1983. Benthic Macroinvertebrates and Water
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15788

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Slooff, W., and R. Baerselman. 1980. Comparison of the
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9740

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Smith, B.P., E. Hejtmancik, and B.J. Camp. 1976. Acute
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8325

AF, UEndp, Con

283

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Rejection Code(s)

Comment

Smith, S., K.H.M. Kwan, and S. Mannings. 1992.
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18142

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Snell, T.W., and G. Persoone. 1989. Acute Toxicity
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Snell, T.W., and M.J. Carmona. 1995. Comparative
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317 (OECDG Data File).

9385

AF, Dur

Solbe, J.F.D., and V.A. Flook. 1975. Studies on the Toxicity
of Zinc Sulphate and of Cadmium Sulphate to Stone Loach
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15989

NonRes

Sosak-Swiderska, B., and D. Tyrawska. 1994. Cadmium
Accumulation Ability of Chlorella vulgaris Beij. 1890, Strain
A-8. Pol.Arch.Hydrobiol. 41(1): 149-159.

18721

Plant, AF, UEndp

Spehar, R.L., E.N. Leonard, and D.L. De Foe. 1978.
Chronic Effects of Cadmium and Zinc Mixtures on Flagfish
(Jordanella floridae). Trans.Am.Fish.Soc. 107(2):354-360.

15954

UEndp

Spehar, R.L., R.L. Anderson, and J.T. Fiandt. 1978. Toxicity
and Bioaccumulation of Cadmium and Lead in Aquatic
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2104

Eff, Con

284

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ECOTOX
EcoRef#

Rejection Code(s)

Comment

Srivastava, A., and V.S. Jaiswal. 1989. Biochemical
Changes in DuckWeed After Cadmium Treatment.
Enhancement in Senescence. Water Air Soil Pollut.
50(1/2):163-170.

3264

Plant, AF, UEndp,
Eff

Srivastava, A., and V.S. Jaiswal. 1989. Effect of Cadmium
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17764

Plant, AF, UEndp

Stackhouse, R.A., and W.H. Benson. 1989. Interaction of
Humic Acid with Selected Trace Metals: Influence on
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3556

AF, UEndp

Stallwitz, E., and D.P. Hader. 1993. Motility and Phototatic
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Heavy Metal Ions. J.Photochem.Photobiol. B:Biol-74.

7299

AF, UEndp, Con

Stary, J., and K. Kratzer. 1982. The Cumulation of Toxic
Metals on Alga. J.Environ.Anal.Chem. 12:65-71.

14286

Plant, AF, UEndp

Stary, J., B. Havlik, K. Kratzer, J. Prasilova, and J.
Hanusova. 1983. Cumulation of Zinc, Cadmium and
Mercury on the Alga Scenedesmus obliquus. Acta
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14088

Plant, AF, UEndp

Stary, J., K. Kratzer, B. Havlik, J. Prasilova, and J.
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120.

16091

AF, UEndp, RouExp

Stauber, J.L., and T.M. Florence. 1987. Mechanism of
Toxicity of Ionic Copper and Copper Complexes to Algae.
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12971

UEndp

Stephenson, M., and G.L. Mackie. 1989. A Laboratory
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776

AF, UEndp

285

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Stratton, G.W., and C.T. Corke. 1979. The Effect of
Mercuric, Cadmium, and Nickel Ion Combinations on a
Blue-Green Alga. Chemosphere 8(10):731-740.

15822

Plant, AF, UEndp

Streit, B., and S. Winter. 1993. Cadmium Uptake and
Compartmental Time Characteristics in the Freshwater
Mussel Anodonta anatina. Chemosphere 26(8): 1479-1490.

7031

UEndp, Con

Stromberg, P.C., J.G. Ferrante, and S. Carter. 1983.
Pathology of Lethal and Sublethal Exposure of Fathead
Minnows, Pimephales promelas, to Cadmium: A Model for
Aquatic Toxicity Assessment. J.Toxicol. Environ.Health
11(2):247-259.

11172

AF, UEndp, Eff, Dur

Stubblefield, W.A., B.L. Steadman, T.W. La Point, and H.L.
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20727

Det

Stuijfzand, S.C., M.J. Jonker, E. Van Ammelrooy, and W.
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Organically Enriched River Water, with Emphasis on Effects
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20353

AF, UEndp

Subramanian, V.V., V. Sivasubramanian, and K.P.
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18777

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Dur

Suedel, B.C., J.H. Rodgers Jr., and E. Deaver. 1997.
Experimental Factors that may Affect Toxicity of Cadmium
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18420

No definitive water
hardness provided

Sultana, R., V.U. Devi, and M.N. Prasad. 1991. Effect of
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4421

AF, UEndp, Eff, Dur

286

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Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Sumi, Y., T. Suzuki, M. Yamamura, S. Hatakeyama, Y.
Sugaya, and K.T. Suzuki. 1984. Histochemical Staining of
Cadmium Taken Up by the Midge Larva, Chironomus
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Comp.Biochem.Physiol.A 79(3):353-357.

11481

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Suzuki, K.. 1959. The Toxic Influence of Heavy Metal Salts
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6(14): 196-209.

2701

AF, UEndp, Eff

Suzuki, K.T., H. Sunaga, E. Kobayashi, and S.
Hatakeyama. 1987. Environmental and Injected Cadmium
Are Sequestered by Two Major Isoforms of Basal Copper,
Zinc-Metallothionein in Gibel (Carassius auratus.
Comp.Biochem.Physiol.C 87(1):87-93.

12736

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Con

Swinehart, J.H.. 1990. The Effects of Humic Substances on
the Interactions of Metal Ions wiht Organisms and
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17696

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Takamura, N., F. Kasai, and M.M. Watanabe. 1989. Effects
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3095

Plant, AF, UEndp,
Dur, Con

Tarzwell, C.M., and C. Henderson. 1960. Toxicity of Less
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2042

Con

Tatara, C.P., M.C. Newman, J.T. McCloskey, and P.L.
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18605

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Tatara, C.P., M.C. Newman, J.T. McCloskey, and P.L.
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5072

AF, Dur

287

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Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Tatem, H.E.. 1986. Bioaccumulation of Polychlorinated
Biphenyls and Metals From Contaminated Sediment by
Freshwater Prawns, Macrobrachium rosenbergii and
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12002

AF, UEndp, Dur

Taylor, G., D.J. Baird, and A.M.V.M. Soares. 1998. Surface
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18779

Plant, AF, UEndp,
Dur

Teisseire, H., M. Couderchet, and G. Vernet. 1998. Toxic
Responses and Catalase Activity of Lemna minor L.
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19278

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Tessier, C., and J.S. Blais. 1996. Determination of
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17781

AF, UEndp

Tessier, L., G. Vaillancourt, and L. Pazdernik. 1994.
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Arch.Environ.Contam.Toxicol. 26:179-184.

13597

AF, UEndp

Tessier, L., G. Vaillancourt, G., and L. Pazdernik. 1996.
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17094

AF, UEndp

Thomas, A.. 1915. Effects of Certain Metallic Salts upon
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2865

AF, UEndp, Dur

Thomas, D.G., A. Cryer, J.F.D.E. Solbe, and J. Kay. 1983.
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12383

AF, UEndp, Con

288

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Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Thompson, P.A., and P. Couture. 1990. Aspects of Carbon
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3335

Plant, AF, UEndp,
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Thompson, P.A., and P. Couture. 1993. Physiology of
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8268

Plant, AF, UEndp,
Dur

Thompson, P.A., P. Couture, C. Thellen, and J.C. Auclair.
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12916

Plant, AF, UEndp

Thorp, V.J., and P.S. Lake. 1974. Toxicity Bioassays of
Cadmium on Selected Freshwater Invertebrates and the
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8731

NonRes

Thuvander, A.. 1989. Cadmium Exposure of Rainbow Trout,
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3401

AF, UEndp, Eff

Timmermans, K.R., and P.A. Walker. 1989. The Fate of
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2729

AF, UEndp

Timmermans, K.R., E. Spijkerman, M. Tonkes, and H.
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13427

AF, UEndp

Timmermans, K.R., W. Peeters, and M. Tonkes. 1992.
Cadmium, Zinc, Lead and Copper in Chironomus riparius
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6029

AF, UEndp, Eff

289

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Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Ting, Y.P., F. Lawson, and I.G. Prince. 1989. Uptake of
Cadmium and Zinc by the Alga Chlorella vulgaris: Part 1.
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3362

Plant, AF, UEndp,
Dur, Con

Torreblanca, A., J. Del Ramo, J.A. Arnau, and J. Diaz-
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2695

AF, UEndp

Tripathi, R.D., U.N. Rai, M. Gupta, M. Yunus, and P.
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Macrophyte Ceratophyllum demersum L. in Presence of
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16157

AF, UEndp, Eff, Dur

Tsuji, S., Y. Tonogai, Y. Ito, and S. Kanoh. 1986. The
Influence of Rearing Temperatures on the Toxicity of
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12497

AF, Dur, Con

Turbak, S.C., S.B. Olson, and G.A. McFeters. 1986.
Comparison of Algal Assay Systems for Detecting
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11780

Plant, AF, Eff, Dur

Twagilimana, L., J. Bohatier, C.A. Groliere, F. Bonnemoy,
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20057

Ace, AF, Dur

Tyrawska, D., K. Grochala, Z. Kowszylo, and L.
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17331

AF, UEndp, Eff

Umezu, T.. 1991. Saponins and Surfactants Increase Water
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7136

AF, UEndp, Dur

290

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Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Van der Heever, J.A., and J.U. Grobbelaar. 1996.
Evaluation of Short-lncubation-Time Small-Volume
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18763

Plant, AF, Eff, Dur

Van der Heever, J.A., and J.U. Grobbelaar. 1997. The Use
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19854

Plant, AF, UEndp,
Eff, Dur

Van der Werff, M., and M.J. Pruyt. 1982. Long-Term Effects
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14480

Plant, AF, UEndp

Van Ginneken, L., M.J. Chowdhury, and R. Blust. 1999.
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20483

AF, UEndp, Dur,
Form

Van Haaften, M., and D.C. Lasenby. 1994. Changes in the
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13705

AF, UEndp, Dur,
RouExp

Van Hattum, B.P.D., L. Van den Bosch, N.M. Van Straalen,
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Cadmium by the Freshwater lospod Asellus aquaticus (L.)
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881

AF, UEndp

Van Kessel, W.H.M., R.W. Brocades Zaalberg, and W.
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20202

AF, UEndp

Van Leeuwen, C.J., P.S. Griffioen, W.H.A. Vergouw, and
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11519

AF, Con

291

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Van Leeuwen, C.J., W.J. Luttmer, and P.S. Griffioen. 1988.
The Use of Cohorts and Populations in Chronic Toxicity
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10589

Van Puymbroeck, S.L.C., W.J.J. Stips, and O.L.J.
Vanderborght. 1982. The Antagonism between Selenium
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Arch.Environ.Contam.Toxicol. 11(1): 103-106.

12986

Vardia, H.K., P.S. Rao, and V.S. Durve. 1988. Effect of
Copper, Cadmium and Zinc on Fish-Food Organisms,
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Acad. Sci.Anim. Sci. 97(2): 175-180.

12365

AF, Dur, Con

Vasseur, P., P. Pandard, and D. Burnel. 1988. Influence of
Some Experimental Factors on Metal Toxicity to
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752

Plant, AF, UEndp,
Con

Vazquez, M.D., J. Lopez, and A. Carballeira. 1999. Uptake
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20585

Plant, AF, UEndp,
Dur

Verma, S.R., I.P. Tonk, A.K. Gupta, and M. Saxena. 1984.
Evaluation of an Application Factor for Determining the Safe
Concentration of Agricultural and Industrial Chemicals.
Water Res. 18(1): 111-115.

10575

Con

Verma, S.R., I.P. Tonk, and R.C. Dalela. 1981.
Determination of the Maximum Acceptable Toxicant
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Certain Aquatic Pollutants. Acta Hydrochim.Hydrobiol.
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10385

Con

Viale, G., and D. Calamari. 1984. Immune Response in
Rainbow Trout Salmo gairdneri After Long-Term Treatment
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Ecol.Biol. 35(3):247-257.

10732

AF, Eff

292

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Victor, B.. 1993. Responses of Hemocytes and Gill Tissues
to Sublethal Cadmium Chloride Poisoning in the Crab
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Arch.Environ.Contam.Toxicol. 24:432-439.

6773

Dur

Victor, B.. 1993. Histopathological Progression of Hemic
Neoplasms in the Tropical Crab Paratelphusa
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Chloride. Arch.Environ.Contam.Toxicol. 25:48-54.

6785

NonRes

Victor, B., S. Mahalingam, and R. Sarojini. 1986. Toxicity of
Mercury and Cadmium on Oocyte Differentiation and
Vitellogenesis of the Teleost, Lepidocephalichtyhs thermalis
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12099

AF, UEndp, Eff

Vijayaraman, K., G. John, P. Sivakumar, and R.R.
Mohamed. 1999. Uptake and Loss of Heavy Metals by the
Freshwater Prawn, Macrobrachium malcolmsonii.
J.Environ.Biol. 20(3):217-222.

55226

UEndp

Vijayram, K., and P. Geraldine. 1996. Are the Heavy Metals
Cadmium and Zinc Regulated in Freshwater Prawns?.
Ecotoxicol.Environ.Saf. 34(2):180-183 (Publ in Part As
16442).

17782

UEndp

Vijayram, K., P. Geraldine, T.S. Varadarajan, L. James, K.
Periaswamy, G. John, and P. Loganathan. 1990. Vertebral
Deformities and Decrease of Mineral Content in Anabas
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674.

3441

UEndp, Eff

Vincent, S., and T. Ambrose. 1994. Uptake of Heavy Metals
Cadmium and Chromium in Tissues of the Indian Major
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19450

UEndp

Vitale, A.M., J.M. Monserrat, P. Castilho, and E.M.
Rodriguez. 1999. Inhibitory Effects of Cadmium on Carbonic
Anhydrase Activity and Ionic Regulation of the Estuarine
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Comp. Biochem. Physiol. C 122(1 ):121 -129.

19662

293

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Vocke, R.W., K.L. Sears, J.J. O'Toole, and R.B. Wildman.
1980. Growth Responses of Selected Freshwater Algae to
Trace Elements and Scrubber Ash Slurry Generated by
Coal-Fired Power Plants. Water Res. 14(2): 141-150.

5342

Plant

Vykusova, B., and Z. Svobodova. 1987. Comparison of the
Sensitivity of Male and Female Guppies (Poecilia reticulata
Peters) to Toxic Substances. Bul.Vyzk.Ustav
Ryb.Hydrobiol.Vodnany 23(3):20-23 (CZE) (ENG ABS).

312

AF, Dur, Con

Vymazal, J.. 1990. Uptake of Lead, Chromium, Cadmium

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Bui I. Environ. Contam. Toxicol. 44(2):468-472.

2191

Plant, AF, Uendp,
Dur

Vymazal, J.. 1990. Uptake of Heavy Metals by Cladophora
glomerata. Acta Hydrochim.Hydrobiol. 18(6):657-665.

45131

Plant, AF, Uendp,
Dur

Vymazal, J.. 1995. Influence of pH on Heavy Metals Uptake
by Cladophora glomerata. Pol.Arch.Hydrobiol. 42(3):231-
237.

45130

Plant, AF, Uendp,
Dur

Wagh, S.B., K. Shareef, and S. Shaikh. 1985. Acute Toxicity
of Cadmium Sulphate, Zinc Sulphate and Copper Sulphate
to Barbus ticto (Ham.): Effect on Oxygen Consumption and
Gill Histology. J.Environ.Biol. 6(4):287-293.

11483

Dur, Con

Wang, T.C., J.C. Weissman, G. Ramesh, R. Varadarajan,
and J.R. Benemann. 1996. Parameters for Removal of
Toxic Heavy Metals by Water Milfoil (Myriophyllum
spicatum). Bull.Environ.Contam.Toxicol. 57(5):779-786.

20408

Plant, AF, UEndp,
Dur

Wang, W.. 1994. Rice Seed Toxicity Tests for Organic and
Inorganic Substances. Environ.Monit.Assess. 29:101-107.

45060

Plant, AF

Wani, G.P., and A.N. Latey. 1983. Toxic Effects of
Cadmium on the Liver of a Freshwater Teleost Garra mullya
(Sykes). Curr.Sci. 52(21): 1034-1035.

11016

294

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Water Pollution Research Board. 1968. Effects of Pollution
on Fish: Chronic Toxicity of Ammonia to Rainbow Trout. In:
Water Pollution Research 1967, Water Pollution Research
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10185

AF, UEndp, Con

Watson, C.F.. 1988. Sublethal Effects of Cadmium
Exposure on Freshwater Teleosts. Diss.Abstr.lnt.B
Sci.Eng.50(3):830 / Ph.D.Thesis, Northeast Louisiana
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2707

AF, UEndp, Eff,
Con

Watson, C.F., and W.H. Benson. 1987. Comparative Activity
of Gill Atpase in Three Freshwater Teleosts Exposed to
Cadmium. Ecotoxicol.Environ.Saf. 14:252-259.

12806

AF, UEndp, Dur

Wehrheim, B., and M. Wettern. 1994. Comparative Studies
of the Heavy Metal Uptake of Whole Cells and Different
Types of Cell Walls from Chlorella fusca. Biotechnol.Tech.
8(4):227-232.

16139

Plant, AF, UEndp,
Dur

Wehrheim, B., and M. Wettern. 1994. Influence of the
External REDOX State on Heavy Metal Adsorption by
Whole Cells and Isolated Cell Walls of Chlorella fusca.
Biotechnol.Tech. 8:221-226.

45132

Plant, AF, UEndp,
Dur

Weis, J.S., and P. Weis. 1977. Effects of Heavy Metals on
Development of the Killifish, Fundulus heterclitus. J. Fish
Biol. 11 (1):49-54.

45298

AF, UEndp, Eff, Dur

Welsh, P.G.. 1996. Influence of Dissolved Organic Carbon
on the Speciation, Bioavailability and Toxicity of Metals to
Aquatic Biota in Soft Water Lakes. Ph.D.Thesis, University
ofWaterloo, Ontario, Canada : 181 p..

45189

Wentsel, R.S.. 1977. Distributional and Sublethal Effects of
Heavy Metals on Benthic Macroinvertebrates. Ph.D.Thesis,
Purdue University, West Lafayette, I N:108.

6175

UEndp

295

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Wicklum, D., and R.W. Davies. 1996. The Effects of Chronic
Cadmium Stress on Energy Acquisition and Allocation in a
Freshwater Benthic Invertebrate Predator. Aquat.Toxicol.
35(3/4):237-252.

19521

AF, UEndp

Wicklum, D., D.E.C. Smith, and R.W. Davies. 1997.

Mortality, Preference, Avoidance, and Activity of a Predatory
Leech Exposed to Cadmium. Arch.Environ.Contam.Toxicol.
32(2):178-183.

17876

Wicklund Glynn, A.. 1996. The Concentration Dependency
of Branchial Intracellular Cadmium Distribution and Influx in
the Zebrafish (Brachydanio rerio). Aquat.Toxicol. 35(1 ):47-
58.

17192

AF, UEndp, Dur

Wicklund, A., and P. Runn. 1988. Calcium Effects on
Cadmium Uptake, Redistribution, and Elimination in
Minnows, Phoxinus phoxinus, Acclimated to Different
Calcium Concentrations. Aquat.Toxicol. 13(2):109-122.

13182

AF, UEndp, Dur

Wicklund, A., L. Norrgren, and P. Runn. 1990. The Influence
of Cadmium and Zinc on Cadmium Turnover in the
Zebrafish, Brachydanio rerio. Arch.Environ.Contam.Toxicol.
19(3):348-353.

3171

AF, UEndp, Dur,
Con

Wicklund, A., P. Runn, and L. Norrgren. 1988. Cadmium
and Zinc Interactions in Fish: Effects of Zinc on the Uptake,
Organ Distribution, and Elimination of 109Cd in the
Zebrafish, Brachydanio rerio. Arch.Environ.Contam.Toxicol.
17(3):345-354.

2428

AF, UEndp, Con

Wikfors, G.H., A. Neeman, and P.J. Jackson. 1991.
Cadmium-Binding Polypeptides in Microalgal Strains with
Laboratory-Induced Cadmium Tolerance.
Mar.Ecol.Prog.Ser. 79(1/2):163-190.

6385

Plant, AF, UEndp

Wilczok, A., U. Mazurek, D. Tyrawska, and B. Sosak-
Swiderska. 1994. Effect of Cadmium on the Cell Division of
Chlorella vulgaris Beij. 1890, Strain A-8. Pol.Arch.Hydrobiol.
41 (1 ):123-131.

18720

Plant, AF, UEndp,
Dur

296

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Williams, D.R.Jr.. 1978. Relative Importance of Food and
Water Sources to Cadmium Uptake by Gambusia affinis
(Poeciliidae). Environ.Res. 16(1-3):326-332.

15673

UEndp, RouExp

Williams, K.A., D.W.J. Green, D. Pascoe, and D.E. Gower.
1986. The Acute Toxicity of Cadmium to Different Larval
Stages of Chironomus riparius (Diptera: Chironomidae) and
its Ecological Significance for Pollutio. Oecologia 70(3):362-
366.

12042

Williams, K.A., D.W.J. Green, D. Pascoe, and D.E. Gower.
1987. Effect of Cadmium on Oviposition and Egg Viability in
Chironomus riparius (Diptera: Chironomidae).

Bui I. Environ. Contam. Toxicol. 38(1):86-90.

12395

AF, UEndp, Dur

Williams, P.L., and D.B. Dusenbery. 1990. Aquatic Toxicity
Testing Using the Nematode, Caenorhabditis elegans.
Environ.Toxicol.Chem. 9(10):1285-1290.

3437

Willuhn, J., A. Otto, H. Koewius, and F. Wunderlich. 1996.
Subtoxic Cadmium-Concentrations Reduce Copper-Toxicity
in the Earthworm Enchytraeus buchholzi. Chemosphere
32(11):2205-2210.

20269

AF, Dur

Winner, R.W.. 1984. The Toxicity and Bioaccumulation of
Cadmium and Copper as Affected by Humic Acid.
Aquat.Toxicol. 5(3):267-274.

11355

AF, Con

Wong, C.K., and P.K. Wong. 1990. Life Table Evaluation of
the Effects of Cadmium Exposure on the Freshwater
Cladoceran, Moina macrocarpa.
Bull.Environ.Contam.Toxicol. 44(1): 135-141.

2800

AF, Dur

Woo, P.T.K., Y.M. Sin, and M.K. Wong. 1993. The Effects of
Short-Term Acute Cadmium Exposure on Blue Tilapia,
Oreochromis aureus. Environ.Biol.Fish. 37(1):67-74.

9911

AF, UEndp

Woodall, C., N. MacLean, and F. Crossley. 1988.
Responses of Trout Fry (Salmo gairdneri) and Xenopus
laevis Tadpoles to Cadmium and Zinc.
Comp.Biochem.Physiol.C 89(1):93-99.

6074

Dur

297

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Woodworth, J., and D. Pascoe. 1983. Cadmium Uptake and
Distribution in Sticklebacks Related to the Concentration
and Method of Exposure. Ecotoxicol.Environ.Saf. 7(6):525-
530 (Used Ref 10578).

10549

UEndp

Wooldridge, C.R., and D.P. Wooldridge. 1969. Internal
Damage in an Aquatic Beetle Exposed to Sublethal
Concentrations of Inorganic Ions. Ann.Entomol.Soc.Am.
62(4):921-933.

2868

AF, UEndp, Eff

Wren, M.J., and D. McCarroll. 1990. A Simple and Sensitive
Bioassay for the Detection of Toxic Materials Using a
Unicellular Green Alga. Environ.Pollut. 64(1):87-91.

3265

Plant, AF, Con

Wright, D.A.. 1988. Dose-Related Toxicity of Copper and
Cadmium in Striped Bass Larvae from the Chesapeake
Bay: Field Considerations. Water Sci.Technol. 20(6-7):39-
48.

910

Wright, D.A.,andJ.W. Frain. 1981. The Effect of Calcium
on Cadmium Toxicity in the Freshwater Amphipod,
Gammarus pulex (L.). Arch.Environ.Contam.Toxicol.
10(3):321-328.

9509

AF, Dur

Wright, D.A., M.J. Meteyer, and F.D. Martin. 1985. Effect of
Calcium on Cadmium Uptake and Toxicity in Larvae and
Juveniles of Striped Bass (Morone saxatilis).

Bui I. Environ. Contam. Toxicol. 34(2): 196-204.

10625

UEndp, Dur

Xiaorong, W., J. Mei, S. Hao, and X. Ouyong. 1997. Effects
of Chelation on the Bioconcentration of Cadmium and
Copper by Carp (Cyprinus carpio L.).
Bull.Environ.Contam.Toxicol. 59(1): 120-124.

18423

UEndp

Yager, C.M., and H.W. Harry. 1964. The Uptake of
Radioactive Zinc, Cadmium and Copper by the Freshwater
Snail, Taphius glabratus. Malacologia 1(3):339-353.

14058

AF, UEndp, Dur

298

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Yamamoto, Y., and M. Inoue. 1985. Lethal Tolerance of
Acute Cadmium Toxicity in Rainbow Trout Previously
Exposed to Cadmium. Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan
Gakkaishi) 51 (10): 1733-1735 (JPN) (ENG ABS).

12102

AF, UEndp, Con

Yang, H.N., and H.C. Chen. 1996. Uptake and Elimination
of Cadmium by Japanese Eel, Anguilla japonica, at Various
Temperatures. Bull.Environ.Contam.Toxicol. 56(4):670-676.

17926

AF, Uendp, NonRes

Yang, H.N., and H.C. Chen. 1996. The Influence of
Temperature on the Acute Toxicity and Sublethal Effects of
Copper, Cadmium and Zinc to Japanese Eel, Anguilla
japonica. Acta Zool.Taiwan. 7(1):29-38.

18914

NonRes

Yoshitomi, T., J. Koyama, A. Lida, N. Okamoto, and Y.
Ikeda. 1998. Cadmium-Induced Scale Deformation in Carp
(Cyprinus carpio). Bull.Environ.Contam.Toxicol. 60:639-644.

18754

AF, UEndp, RouExp

Zettergren, L.D., B.W. Boldt, D.H. Petering, M.S. Goodrich,
D.N. Weber, and J.G. Zettergren. 1991. Effects of
Prolonged Low-Level Cadmium Exposure on the Tadpole
Immune System. Toxicol.Lett.(Amst.) 55(1 ):11 -19.

7384

AF, UEndp

Zhang, F., Y. Zhou, and R. Zhou. 1988. Toxicities of Two
Metals and Two Pesticides to Grass Carps at Different
Development Stages. Acta Sci.Circumstant.(Huanjing
Kexue Xuebao) 8(1):67-71 (CHI) (ENG ABS).

3477

AF, Dur, Con

Zia, S., and D.G. McDonald. 1994. Role of the Gills and Gill
Chloride Cells in Metal Uptake in the Freshwater-Adapted
Rainbow Trout, Oncorhynchus mykiss.
Can.J.Fish.Aquat.Sci. 51 (11 ):2482-2492.

17464

AF, UEndp, Eff, Dur

Zitko, V., and W.G. Carson. 1976. A Mechanism of the
Effects of Water Hardness on the Lethality of Heavy Metals
to Fish. Chemosphere 5(5):299-303.

8483

UEndp, Dur

299

-------
Article Number and Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Zou, E., and S. Bu. 1994. Acute Toxicity of Copper,
Cadmium, and Zinc to the Water Flea, Moina irrasa
(Cladocera). Bull.Environ.Contam.Toxicol. 52(5):742-748.

13762

NonRes

Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A. For specific study
determinations, see Appendix C.

1) For the studies that were not utilized, but the most representative value fell below the criterion, or, if the studies were for a
species associated with one of the four most sensitive genera used to calculate the FAV in the most recent national ambient

water quality criteria dataset used to derive the CMC , EPA is providing a transparent rationale as to why they were not
utilized (see below).

2) For the studies that were not utilized because they were not found to be pertinent to this determination (including failing
the QA/QC procedures listed in Appendix A) upon initial review of the download from ECOTOX, EPA is providing the
code that identifies why EPA determined that the results of the study were not reliable.

General QA/QC failure because non-resident species in Oregon

All data considered in this CWA review and approval/disapproval action of OR WQS for cadmium below the chronic criterion or
related to the four most sensitive genera were from species that are known or expected to have a breeding wild population in Oregon's
waters.

Other Acute tests failing QA/QC by species
Salvelinus fontinalis - brook trout

Holcombe, G.W., G.L. Phipps and J.T. Fiandt. 1983. Toxicity of selected priority pollutants to various aquatic organisms.
Ecotoxicol. Environ. Safety 7: 400-409.

81 U.S. EPA. 2001. 2001 Update of Ambient Water Quality Criteria for Cadmium. EPA-822-R-01-001.

300

-------
Data was significantly different than other data for species in the same genus, so it was considered an outlier and not included.
Oncorhynchus mykiss — rainbow trout

The following tests were included in EPA's BE of the OR WQS for cadmium in freshwater, but were not used in this CWA review
and approval/disapproval action of these standards because a more sensitive lifestage was available which provides greater protection
for the species.

Chapman, G.A. 1978. Toxicities of cadmium, copper, and zinc to four juvenile stages of chinook salmon and steelhead. Trans.
Am. Fish. Soc. 107: 841.

Other data from this study used for this species.

Chapman, G.A. 1975. Toxicity of copper, cadmium and zinc to Pacific Northwest salmonids. U.S. EPA, Corvallis, Oregon.

Other data from this study used for this species.

The following tests were not used in this CWA review and approval/disapproval action of these standards because the tests were not
based on the preferred flow-through measured test conditions; however, other flow-through measured test concentrations were
available for this species that was included.

Hollis, L., J.C. McGeer, D.G. McDonald and C.M. Wood. 1999. Cadmium Accumulation, Gill Cd Binding, Acclimation, and
Physiological Effects During Long Term Sublethal Cd Exposure in Rainbow Trout. Aquat. Toxicol. 46(2): 101-119.

Two LC50 values from F,U tests ranging from 14.75 to 167.63 |ig/L.

Buhl, K.J. and S.J. Hamilton. 1991. Relative sensitivity of early life stages of arctic grayling, coho salmon, and rainbow trout
to nine inorganics. Ecotoxicol. Environ. Safety. 22: 184-197.

One LC50 value from S,U test of 3.51 |ig/L.

Spehar, R.L. and A.R. Carlson. 1984a. Derivation of site-specific water quality criteria for cadmium and the St. Louis River
Basin, Duluth, Minnesota. PB84-153196. National Technical Information Service, Springfield, VA.

One LC50 value from S,M test of 5.06 |ig/L.

Spehar, R.L. and A.R. Carlson. 1984b. Derivation of site-specific water quality criteria for cadmium and the St. Louis River
Basin, Duluth, Minnesota. Environ. Toxicol. Chem. 3: 651.

301

-------
One LC50 value from S,M test of 5.06 |ig/L.

Kumada H., S. Kimura and M. Yokote. 1980. Accumulation and biological effects of cadmium in rainbow trout. Bull. Jap. Soc.
Sci. Fish. 46: 97-103.

Two LC50 values from S,U tests ranging from 6.00 to 7.00 |ig/L, with no hardness adjustment; water hardness level was not available
for this test.

Kumada, H., S. Kimura, M. Yokote and Y. Matida. 1973. Acute and chronic toxicity, uptake and retention of cadmium in
freshwater organisms. Bull. Freshwater Fish. Res. Lab. 22: 157-165.

One LC50 value from S,U test of 6.00 |ig/L, with no hardness adjustment; water hardness level was not available for this test.

The following test was not used in this CWA review and approval/disapproval action of these standards because no water hardness
level was available for the test.

Hale, J.G. 1977. Toxicity of metal mining wastes. Bull. Environ. Contam. Toxicol. 17: 66.

Oncorhynchus tshawytscha— Chinook salmon

The following tests were included in EPA's BE of the OR WQS for cadmium in freshwater, but were not used for determining the
most representative SMAV in this CWA review and approval/disapproval action of these standards because a more sensitive lifestage
was available.

Chapman, G.A. 1978. Toxicities of cadmium, copper, and zinc to four juvenile stages of chinook salmon and steelhead. Trans.
Am. Fish. Soc. 107: 841.

Other data from this study used for this species.

Chapman, G.A. 1975. Toxicity of copper, cadmium and zinc to Pacific Northwest salmonids. U.S. EPA, Corvallis, OR.

Other data from this study used for this species.

302

-------
Hamilton, S.J. and K.J. Buhl. 1990. Safety assessment of selected inorganic elements to fry of chinook salmon (Oncorhynchus
tshawytscha). Ecotoxicol. Environ. Safety. 20: 307-324.

Two LC50 values from S,U tests ranging from 11.49 to 15.37 |ig/L.

Oncorhynchus kisutch— Coho salmon

Chapman, G.A. 1975. Toxicity of copper, cadmium and zinc to Pacific Northwest salmonids. U.S. EPA, Corvallis, OR.

Other data from this study used for this species.

Buhl, K.J. and S.J. Hamilton. 1991. Relative sensitivity of early life stages of arctic grayling, coho salmon, and rainbow trout
to nine inorganics. Ecotoxicol. Environ. Safety. 22: 184-197.

Two LC50 values from S,U tests ranging from 7.95 to 14.02 |ig/L.

Lorz, H.W., R.H. Williams and C.A. Fustish. 1978. Effects of several metals on smolting of coho salmon. EPA-600/3-78-090.
National Technical Information Service, Springfield, VA.

One LC50 value from S,U test of 10.93 |ig/L.

Oncorhynchus nerka— Sockeye salmon

Servizi, J.A. and D.W. Martens. 1978. Effects of Selected Heavy Metals on Early Life of Sockeye and Pink Salmon. Rep. No.
39, Int. Pacific Salmon Fish. Comm. (Br. Col.): 26.

7-day acute fish test.

303

-------
Oncorhynchus gorbuscha— Pink salmon

Servizi, J.A. and D.W. Martens. 1978. Effects of Selected Heavy Metals on Early Life of Sockeye and Pink Salmon. Rep. No.
39, Int. Pacific Salmon Fish. Comm. (Br. Col.): 26.

7-day acute fish test.

Morone saxatilis — striped bass

The following tests were not used in this CWA review and approval/disapproval action of these standards due to questionable
treatment of organisms or inappropriate test conditions or methodology, according to ASTM standards for toxicity testing
methodologies.

Rehwoldt, R., L.W. Menapace, B. Nerrie and D. Allessandrello. 1972. The effect of increased temperature upon the acute
toxicity of some heavy metal ions. Bull. Environ. Contam. Toxicol. 8(2): 91-96.

Hughes, J.S. 1973. Acute Toxicity to Thirty Chemicals to Striped Bass (Morone saxatilis). Western Assoc. State Game Fish
Comm., Salt Lake City, UT.

72-hr acute fish test.

Morone americana — white perch

304

-------
Rehwoldt, R., L.W. Menapace, B. Nerrie and D. Allessandrello. 1972. The effect of increased temperature upon the acute
toxicity of some heavy metal ions. Bull. Environ. Contam. Toxicol. 8(2): 91-96.

This species is also an Oregon nonresident species.

Chironomus tetans — midge

The following tests were included in EPA's BE of the OR WQS for cadmium in freshwater, but were not used in this CWA review
and approval/disapproval action of these standards because because the dilution water for the test was from an uncharacterized natural
water source. Note: this data was relegated to Table 6 in the 2001 criteria document for the same reason.

Khangarot, B.S. and P.K. Ray. 1989b. Sensitivity of midge larvae of Chironomus tentans Fabricius (Diptera: Chironomidea) to
heavy metals. Bull. Environ. Contam. Toxicol. 1989. 42: 325-330.

Chironomus riparius— midge

The following tests were not used in this CWA review and approval/disapproval action of these standards because the tests were not
based on the preferred flow-through measured test conditions; however other flow-through measured test concentrations were
available for this species.

Pascoe, D., A.F. Brown, B.M.J. Evans and C. McKavanagh. 1990. Effects and fate of cadmium during toxicity tests with
Chironomus riparius - the influence of food and artificial sediment. Arch. Environ. Contam. Toxicol. 19: 872-877.

One LC50 value from R,U test of 106,201 |ig/L.

Chironomus sp. — midge

Rehwoldt, R., L. Lasko, C. Shaw and E. Wirhowski. 1973. The acute toxicity of some heavy metal ions toward benthic
organisms. Bull. Environ. Contam. Toxicol. 10(5): 291-294.

305

-------
Hyalella azteca - amphipod

The following tests were included in EPA's BE of the OR WQS for cadmium in freshwater, but were not in this CWA review and
approval/disapproval action of these standards because H. azteca is sensitive to chloride concentration (see EPA (2009) for more
details). EPA has decided to not use data for this species until additional tests are conducted.

Collyard, S.A., G.T. Ankley, R.A. Hoke and T. Goldenstein. 1994. Influence of age on the relative sensitivity of Hyalella azteca
to diazinon, alkylphenol ethoxylates, copper, cadmium, and zinc. Arch. Environ. Contam. Toxicol. 26: 110-113.

McNulty, E.W., F.J. Dwyer, M.R. Ellersieck, E.I. Greer, C.G. Ingersoll and C.F. Rabeni. 1999. Evaluation of ability of
reference toxicity tests to identify stress in laboratory populations of the amphipod Hyalella azteca. Environ. Toxicol. Chem.
18(3): 544-548.

Daphttia magna - cladoceratt

Stuhlbacher, A., M.C. Bradley, C. Naylor and P. Calow. 1993. Variation in the development of cadmium resistance in Daphnia
magna Straus; effect of temperature, nutrition, age and genotype. Environ. Pollut. 80(2): 153-158.

Data for a more sensitive lifestage was available for this species.

Anderson, B.G. 1948. The apparent thresholds of toxicity to Daphnia magna for chlorides of various metals when added to
Lake Erie water. Trans. Am. Fish. Soc. 78: 96.

This less than value was not used because more definitive data was available.

The following tests were included in EPA's BE of the OR WQS for cadmium in freshwater, but were not in this CWA review and
approval/disapproval action of these standards because the dilution water for the test was from an uncharacterized natural water
source. Note: this data was relegated to Table 6 in the 2001 criteria document for the same reason.

Hickey, C.W. and M.L. Vickers. 1992. Comparison of the sensitivity to heavy metals and pentachlorophenol of the mayflies
Deleatidium spp. and the cladoceran Daphnia magna. N. Z. J. Mar. Freshwater Res. 26(1): 87-93.

Khangarot, B.S. and P.K. Ray. 1989a. Investigation of correlation between physicochemical properties of metals and their
toxicity to the water flea Daphnia magna Straus. Ecotoxicol. Environ. Saf. 18(2): 109-120.

306

-------
The following test was not used in this CWA review and approval/disapproval action of these standards because the water hardness
the test was performed at was not provided.

Canton, J.H. and D.M.M. Adema. 1978. Reproducibility of short-term and reproduction toxicity experiments with Daphnia
magna and comparison of the sensitivity of Daphnia magna with Daphnia pulex and Daphnia cucullata in short-term
experiments. Hydrobiol. 59: 135.

The following test was not used in this CWA review and approval/disapproval action of these standards because the test organisms
were fed.

Mount, D.I. and T.J. Norberg. 1984. A seven-day life-cycle cladoceran toxicity test. Environ. Toxicol. Chem. 3(3): 425-434
(Author Communication Used).

Daphnia pulex - cladoceran

The following test was not used in this CWA review and approval/disapproval action of these standards because the water hardness
the test was performed at was not provided.

The following test was not used in this CWA review and approval/disapproval action of these standards because the test organisms
were fed.

Mount, D.I. and T.J. Norberg. 1984. A seven-day life-cycle cladoceran toxicity test. Environ. Toxicol. Chem. 3(3): 425-434
(Author Communication Used).

Other Chronic tests failing QA/QC by species
Salmo trutta — brown trout

307

-------
Eaton, J. G., J.M. McKim and G.W. Holcombe. 1978. Metal toxicity to embryos and larvae of seven freshwater fish species - I.
cadmium. Bull. Environ. Contam. Toxicol. 19: 95-103.

CV from this study was not used to calculate the SMCV in the 2001 ALC, because it is from an ELS test as opposed to the life-cycle
test conducted by Brown et al. (1994).

Salmo salar — Atlantic salmon

Peterson, R.H., J.L. Metcalfe and S. Ray. 1985. Uptake of cadmium by eggs and alevins of Atlantic salmon (Salmo salar) as
influenced by acidic conditions. Bull. Environ. Contam. Toxicol. 34: 359-368.

This test is listed in Table 6 of the ALC document as Peterson et al. 1983, because of unspecified test methods (which ECOTOX
specifies as R,M).

Rombough, P.J. and E.T. Garside. 1982. Cadmium toxicity and accumulation in eggs and alevins of Atlantic salmon Salmo
salar. Can. J. Zool. 60: 2006.

Results from this test were included in Table 2 of the 2001 ALC document, but the value includes footnotes stating that it was not
used to calculate the SMCV for S. salar, and to see the text for an explanation. The text in the ALC document, however, does not
mention this specific test or study.

The mean measured NOEC for S. salar in the BE included three values; two of which were values from this same study: a 45-day
LC50 of 7.34 ug/L and a concentration associated with no effect on growth at 1.38 ug/L after 46 days of exposure. Both of these
values were used as reported in ECOTOX, but the test fails QA/QC for ALC development because: 1) it was too short to qualify as an
acceptable ELS test for a salmonid species, and 2) the exposure was based on the renewal of test solutions instead of the required
flow-through test conditions..

Salvelinus fontinalis - brook trout

Eaton, J. G., J.M. McKim and G.W. Holcombe. 1978. Metal toxicity to embryos and larvae of seven freshwater fish species -1,
cadmium. Bull. Environ. Contam. Toxicol. 19: 95-103.

CV from this study was not used to calculate the SMCV in the 2001 ALC, because it is from an ELS test as opposed to the life-cycle
test conducted by Brown et al. (1994).

308

-------
Sauter, S., K. S. Buxton, K.J. Macek and S.R. Petrocelli. 1976. Effects of exposure to heavy metals on selected freshwater fish.
Toxicity of copper, cadmium, chromium and lead to eggs and fry of seven fish species. EPA-600/3-76-105. National Technical
Information Service, Springfield, Virginia.

CV from this study was not used to calculate the SMCV in the 2001 ALC, because it is from an ELS test as opposed to the life-cycle
test conducted by Brown et al. (1994).

Jop, K.M., A.M. Askew and R.B. Foster. 1995. Development of a water-effect ratio for copper, cadmium, and lead for the
Great Works River in Maine using Ceriodaphttia dubia and Salvelinus fontinalis. Bull. Environ. Contam. Toxicol. 54(1): 29-35.

10-day chronic fish test.

Oncorhynchus mykiss — rainbow trout

The following tests were included in EPA's BE of the OR WQS for cadmium in freshwater, but were not used in this CWA review
and approval/disapproval action of these standards because they were non-qualifying ELS tests for salmonids according to the 1985
guidelines.

Davies, P.H. and W.C. Gorman. 1987. Effects of chemical equilibria and kinetics on the bioavailability and toxicity of
cadmium to rainbow trout. Am. Chem. Soc. Natl. Meeting. 194: 646-650.

Davies, P.H., W.C. Gorman, C.A. Carlson and S.F. Brinkman. 1993. Effect of hardness on bioavailability and toxicity of
cadmium to rainbow trout. Chem. Spec. Bioavail. 5(2): 67-77.

Hyalella azteca - amphipod

The following tests were included in EPA's BE of the OR WQS for cadmium in freshwater, but were not used in this CWA review
and approval of these standards because H. azteca is sensitive to chloride concentration (U.S. EPA (2009) for more details). Further,
EPA is currently involved with testing and will be developing interim draft guidance regarding best husbandry practices, including
feeding regimes and water quality characteristics, for Hyalella tests to ensure that tests used in criteria development are of sufficient
quality and are reproducible. This guidance will be applied prospectively to Hyallela tests in future criteria development. EPA has
decided not to use data for this species until these analyses are conducted to ensure that the analyses are based on studies of assured
quality and reproducibility.

309

-------
Ingersoll, C.G. and N. Kemble. 2000. Unpublished. Methods development for long-term sediment toxicity tests with the
amphipod Hyalella azteca and the midge Chironomus tentans.

Daphttia pulex - cladoceratt

Ingersoll, C.G. and R.W. Winner. 1982. Effect on Daphniapulex (De Geer) of daily pulse exposures to copper or cadmium.
Environ. Toxicol. Chem. 1: 321.

The data from this test was relegated to Table 6 in the ALC document, because test methods (whether renewal or measured or non-
measured) were not provided.

Winner, R.W. 1986. Interactive effects of water hardness and humic acid on the chronic toxicity of cadmium to Daphnia pulex.
Aquat. Toxicol. 8: 281-293.

Unmeasured chronic tests. Note: these data were entered into the BE core data as test data for Ceriodaphnia dubia, instead of
Daphnia magna.

310

-------
Appendix D Chromium III (freshwater)
Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Abbasi, S.A., P.C. Nipaney and R. Soni. 1988. Studies
on environmental management of mercury (II), chromium
(VI) and zinc (II) with respect to the impact on some
arthropods and protozoans Int. J. Environ. Stud. 32:
181-187.

13255

AF, Tox, Dur

Al Akel, A.S. and M.J.K. Shamsi. 1996. Hexavalent
chromium: Toxicity and impact on carbohydrate
metabolism and haematological parameters of carp
(Cyprinus carpio L.) from Saudi Arabia. Aquat. Sci. 58(1):
24-30.

19485

AF, Tox

Al-Sabti, K., M. Franko, B. Andrijanic, S. Knez and P.
Stegnar. 1994. Chromium-induced micronuclei in fish. J.
Appl. Toxicol. 14(5): 333-336.

14448

AF, UEndp, Dur

Anderson, B.G. 1948. The apparent thresholds of toxicity
to Daphnia magna for chlorides of various metals when
added to Lake Erie water. Trans. Am. Fish. Soc. 78: 96-
113.

2054

AF, Dur

Anusuya, D. and I. Christy. 1999. Effects of chromium
toxicity on hatching and development of tadpoles of Bufo
melanostictus. J. Environ. Biol. 20(4): 321-323.

47043

AF, Tox

Baekken, T. and K.J. Aanes. 1994. Sublethal effects of
the insecticide fimethoate on invertebrates in
experimental streams. Norw. J. Agric. Sci. Suppl. 13:
167-177.

16081

AF, UEndp, Dur

Banerjee, V. and M. Banerjee. 1988. Effect of heavy
metal poisoning on peripheral haemogram in
Heteropneustes fossilis (Bloch) mercury, chromium and
zinc chlorides (LC50). Comp. Physiol. Ecol. 13(2): 128-
134.

3131

AF, NonRes, UEndp, Dur

Baudouin, M.F. and P. Scoppa. 1974. Accumulation and
retention of chromium-51 by freshwater zooplankton.
Comm.of the European Communities, Joint Nuclear Res.
Center, Ispra, Italy: 23.

14542

AF, UEndp, Dur

311

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Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Biesinger, K.E., and G.M. Christensen. 1972. Effects of
Various Metals on Survival, Growth, Reproduction and
Metabolism of Daphnia magna. J.Fish Res.Board Can.
29:1691-1700.

2022

UEndp

Billard, R. and P. Roubaud. 1985. The effect of metals
and cyanide on fertilization in rainbow trout (Salmo
gairdneri). Water Res. 19(2): 209-214.

10552

AF, UEndp, Dur

Birge, W.J., J.A. Black and A.G. Westerman. 1979.
Evaluation of aquatic pollutants using fish and amphibian
eggs as bioassay organisms. In: S.W. Nielsen, G.

Migaki, and D.G. Scarpelli (Eds.), Symp. Animals
Monitors Environ. Pollut., 1977, Storrs, CT 12: 108-118.

4943

AF, Tox

Boutet, C. and C. Chaisemartin. 1973. Specific toxic
properties of metallic salts in Austropotamobius pallipes
pallipes and Orconectes limosus. C. R. Soc. Biol. (Paris)
167(12): 1933-1938 (FRE) (ENG TRANSL).

5421

Brady, D., B. Letebele, J.R. Duncan and P.D. Rose.
1994. Bioaccumulation of metals by Scenedesmus,
Selenastrum and Chlorella Algae. Water S.A. 20(3): 213-
218.

45157

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Bringmann, G. and R. Kuhn. 1959. The toxic effects of
waste water on aquatic bacteria, algae, and small
crustaceans. Tr-Ts-0002; Gesund. Ing. 80: 115-120 53:
17390G-(GER)(ENG TRANSL).

607

AF, UEndp

Bringmann, G. and R. Kuhn. 1959. Water toxicological
studies with protozoa as test organisms. TR-80-0058,
Literature Research Company: 13 p.; Gesund.-Ing. 80:
239-242 (GER); Chem. Abstr. 53: 22630D-(GER)(ENG
TRANSL).

2394

AF, UEndp, Ace, Dur

Bringmann, G. and R. Kuhn. 1959. Comparative water-
toxicological investigations on bacteria, algae, and
Daphnia. Gesundheitsingenieur 80(4): 115-120.

61194

AF, UEndp

Bringmann, G. and R. Kuhn. 1960. The water-
toxicological detection of insecticides (Zum wasser-
toxikologischen nachweis von insektiziden). Gesund. Ing.
8: 243-244 (GER).

58990

AF, RouExp, Tox

Calevro, F., C. Filippi, P. Deri, C. Albertosi and R.
Batistoni. 1998. Toxic effects of aluminium, chromium
and cadmium in intact and regenerating freshwater
planarians. Chemosphere 37(4): 651-659.

19264

AF, UEndp, Dur

312

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Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Calevro, F., S. Campani, M. Ragghianti, S. Bucci and G.
Mancino. 1998. Tests of toxicity in biphasic vertebrates
treated with heavy metals (Cr3+, AI3+, Cd2+).
Chemosphere 37(14/15): 3011-3017.

20095

NonRes

Call, D.J., L.T. Brooke and N. Ahmad. 1981. Estimates of
"No Effect" Concentrations of Selected Pesticides in
Freshwater Organisms. Fourth Quarterly Progress
Report to EPA, EPA Cooperative Agreement No. CR
806864030, University of Wisconsin, Superior, Wl : 84.

4154

AF, UEndp, Dur

Chin, H.C. and F.F. Chou. 1978. Acute chromium toxicity
of the freshwater mussel, Hyriopsis cumingii Lea. Nan-
Ching Ta Hsueh Hsueh Pao, Tzu Jan K'O Hsueh 4: 96-
101 (CHI).

8328

NonRes

Den Dooren de Jong, L.E. 1965. Tolerance of Chlorella
vulgaris for metallic and non-metallic Ions. Antonie
Leeuwenhoek J. Microbiol. Serol. 31: 301-313.

2849

AF, UEndp, Dur

Dive, D., P. Vasseur, O. Hanssen and P.J. Gravil. 1988.
Studies on interactions between components of
electroplating wastes. Can. Tech. Rep. Fish. Aquat. Sci.
No. 1607: 23-33.

4928

Ace, AF, Dur

Dorn, P.B., J.P. Salanitro, S.H. Evans and L. Kravetz.
1993. Assessing the aquatic hazard of some branched
and linear nonionic surfactants by biodegradation and
toxicity. Environ. Toxicol. Chem. 12(10): 1751-1762.

20415

Tox / AF, Tox / AF, Tox,
UEndp

Dowden, B.F. 1961. Cumulative toxicities of some
inorganic salts to Daphnia magna as determined by
median tolerance limits. Proc. La. Acad. Sci. 23: 77-85.

2465

Dowden, B.F. and H.J. Bennett. 1965. Toxicity of
selected chemicals to certain animals. J. Water Pollut.
Control Fed. 37(9): 1308-1316.

915

Draggan, S. 1977. Interactive effect of chromium
compounds and a fungal parasite on carp eggs. Bull.
Environ. Contam. Toxicol. 17(6): 653-659.

14240

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Falk, M.R. and M.J. Lawrence. 1973. Acute Toxicity of
Petrochemical Drilling Fluids Components and Wastes to
Fish. Tech. Rep. Ser. No. CEN T-73-1, Canada Dep. of
the Environ., Fisheries and Marine Service Resour.
Manag. Branch, Winnipeg, Manitoba, Canada: 112.

6215

AF, Tox

313

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ECOTOX
EcoRef#

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Comment

Fargasova, A. 1994. Comparative toxicity of five metals
on various biological subjects. Bull. Environ. Contam.
Toxicol. 53(2): 317-324.

13707

Plant, Tox

Plants do not drive
criteria, and therefore,
are not included in
CWA review and
approval of OR WQS

Fromm, P.O. and R.M. Stokes. 1962. Assimilation and
metabolism of chromium by trout. J. Water Pollut. Control
Fed. 34(11): 1151-1155.

10362

AF, UEndp, Tox

Gendusa, A.C. 1990. Toxicity of chromium and
fluoranthene from aqueous and sediment sources to
selected freshwater fish. Ph.D. Thesis, University of
North Texas: 138 p. (Publ in Part As 9393, 5091).

4087

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Gendusa, T.C. and T.L. Beitinger. 1992. External
biomarkers to assess chromium toxicity in adult Lepomis
macrochirus. Bull. Environ. Contam. Toxicol. 48(2): 237-
242.

5091

AF, UEndp

Godet, F., M. Babut, D. Burnel, A.M. Veberand P.
Vasseur. 1996. The genotoxicity of iron and chromium in
electroplating effluents. Mutat. Res. 370(1): 19-28.

20537

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Gorbi, G., M.G. Corradi, A. Torelli and M. Bassi. 1996.
Comparison between a normal and a Cr-tolerant strain of
Scenedesmus acutus as a food source to Daphnia
magna. Ecotoxicol. Environ. Saf. 35(2): 109-111.

18532

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RouExp

Guilhermino, L., T. Diamantino, M.C. Silva and A.M.V.M.
Soares. 2000. Acute toxicity test with Daphnia magna:
An alternative to mammals in the prescreening of
chemical toxicity? Ecotoxicol. Environ. Saf. 46(3): 357-
362.

49794

Hale, J.G. 1977. Toxicity of metal mining wastes. Bull.
Environ. Contam. Toxicol. 17(1): 66-73.

861

Holland, G.A., J.E. Lasater, E.D. Neumann and W.E.
Eldridge. 1960. Toxic Effects of Organic and Inorganic
Pollutants on Young Salmon and Trout. Res. Bull. No. 5,
State ofWashington Dept. Fish., Seattle, WA: 263.

14397

AF, UEndp, Dur

Jaworska, M., J. Sepiol and P. Tomasik. 1996. Effect of
metal ions under laboratory conditions on the
entomopathogenic Steinernema carpocapsae
(Rhabditida: Steinernematidae). Water Air Soil Pollut.
88(3/4): 331-341.

17002

AF, UEndp

314

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Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Jones, J.R.E. 1939. The relation between the electrolytic
solution pressures of the metals and their toxicity to the
stickleback (Gasterosteus aculeatus L.). J. Exp. Biol.
16(4): 425-437.

2851

AF, UEndp, Dur

Jones, J.R.E. 1940. A further study of the relation
between toxicity and solution pressure, with Polycelis
nigra as test animal. J. Exp. Biol. 17:408-415.

10012

AF, UEndp, Dur

Kapu, M.M. and D.J. Schaeffer. 1991. Planarians in
toxicology. Responses of asexual Dugesia
dorotocephala to selected metals. Bull. Environ. Contam.
Toxicol. 47(2): 302-307.

10581

AF, UEndp, Tox, Dur

Keller, A.E. and S.G. Zam. 1991. The acute toxicity of
selected metals to the freshwater mussel, Anodonta
imbecilis. Environ. Toxicol. Chem. 10(4) :539-546.

108

AF, Tox, Dur

Kuhnert, P.M. and B.R. Kuhnert. 1976. The effect of in
vivo chromium exposure on Na/K- and Mg-ATPase
activity in several tissues of the rainbow trout (Salmo
gairdneri). Bull. Environ. Contam. Toxicol. 15(4): 383-
390.

14243

AF, UEndp, Biom, Dur

Lenzi, E., E.B. Luchese and S.B. De Lima. 1994.
Improvement of the Eichhornia crassipes - water
hyacinth - use in the decontamination of chrominum
contaminated solution. Arq. Biol. Tecnol. (Curitiba) 37(3):
603-609 (POR) (ENG ABS).

14325

AF, UEndp, Dur

Lewis, J.W., A.N. Kay and N.S. Hanna. 1994.
Responses of electric fish (Family Mormyridae) to
chemical changes in water quality: III. Heavy metals.
Environ. Technol. 15(10): 969-978.

17039

AF, UEndp, Dur

Mao, S. and C. Wang. 1990. The effect of some
pollutants on SCE of grass carp (Ctenopharyngodon
idellus) cells. Oceanol. Limnol. Sin./Haiyang Yu Huzhao
21(3): 205-211 (CHI) (ENG ABS).

9540

AF, UEndp, Tox, Dur

Mayer, F.L.J, and M.R. Ellersieck. 1986. Manual of Acute
Toxicity: Interpretation and Data Base for 410 Chemicals
and 66 Species of Freshwater Animals. Resour. Publ.
No. 160, U.S. Dep. Interior, Fish Wildl. Serv.,

Washington, DC: 505 p. (USGS Data File).

6797

AF, Tox

315

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Mount, D.I. and T.J. Norberg. 1984. Aseven-day life-
cycle cladoceran toxicity test. Environ. Toxicol. Chem.
3(3): 425-434 (Author Communication Used).

11181

Tox/AF, Tox

Mukai, H. 1977. Effects of chemical pretreatment on the
germination of statoblasts of the freshwater bryozoan,
Pectinatella gelatinosa. Biol. Zentralbl. 96: 19-31.

705

AF, UEndp, Dur

Munzinger, A. and F. Monicelli. 1991. A comparison of
the sensitivity of three Daphnia magna populations under
chronic heavy metal stress. Ecotoxicol. Environ. Saf. 22:
24-31.

3950

AF, UEndp, Tox

Munzinger, A. and F. Monicelli. 1992. Heavy metal co-
tolerance in a chromium tolerant strain of Daphnia
magna. Aquat. Toxicol. 23(3/4): 203-216.

6162

AF, UEndp, Tox

Muramoto, S. 1981. Influence of complexans (NTA,
EDTA) on the toxicity of trivalent chromium (chromium
chloride, sulfate) at levels lethal to fish. J. Environ. Sci.
Health A16(6): 605-610.

15431

AF, UEndp, Dur

Nalecz-Jawecki, G. and J. Sawicki. 1998. Toxicity of
inorganic compounds in the spirotox test: A miniaturized
version of the Spirostomum ambiguum test. Arch.
Environ. Contam. Toxicol. 34(1): 1-5.

18997

AF, Ace

Nath, K. and N. Kumar. 1987. Effect of hexavalent
chromium on the carbohydrate metabolism of a
freshwater tropical teleost Colisa fasciatus. C. A. Sel.-
Environ. Pollut.25: 107-213161T / Bull. Inst. Zool. Acad.
Sin.(Taipei) 26(3): 245-248.

12719

AF, UEndp, Tox, Dur

Nath, K. and N. Kumar. 1987. Toxic impact of hexavalent
chromium on the blood pyruvate of Colisa fasciatus. Acta
Hydrochim. Hydrobiol. 15(5): 531-534.

12803

AF, UEndp, Tox, Dur

Pardue, W.J. and T.S. Wood. 1980. Baseline toxicity
data for freshwater bryozoa exposed to copper,
cadmium, chromium, and zinc. J. Tenn. Acad. Sci. 55(1):
27-31.

6703

AF, Tox

Patrick, F.M. and M.W. Loutit. 1978. Passage of metals
to freshwater fish from their food. Water Res. 12: 395-
398 (Used Ref 15021).

2709

AF, RouExp, Tox, UEndp

316

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ECOTOX
EcoRef#

Rejection Code(s)

Comment

Patrick, R., T. Bott and R. Larson. 1975. The Role of
Trace Elements in Management of Nuisance Growths.
EPA 600/2-75-008, U.S. EPA, Corvallis, OR: 250 p.
(U.S. NTIS PB-241985).

14692

AF, Plant, NoOrg, Tox,
UEndp, Dur

Plants do not drive
criteria, and therefore,
are not included in
CWA review and
approval of OR WQS

Pickering, Q.H. 1988. Evaluation and comparison of two
short-term fathead minnow tests for estimating chronic
toxicity. Water Res. 22(7): 883-893.

13227

Tox/AF, Tox

Rai, U.N. and P. Chandra. 1989. Removal of heavy
metals from polluted waters by Hydrodictyon reticulatum
(Linn.) Lagerheim. Sci. Total Environ. 87/88: 509-515.

3348

AF, Plant, Tox, UEndp, Dur

Plants do not drive
criteria, and therefore,
are not included in
CWA review and
approval of OR WQS

Rehwoldt, R., L. Lasko, C. Shaw and E. Wirhowski.
1973. The acute toxicity of some heavy metal ions
toward benthic organisms. Bull. Environ. Contam.
Toxicol. 10(5): 291-294.

2020

AF, Plant, NoOrg

Plants do not drive
criteria, and therefore,
are not included in
CWA review and
approval of OR WQS

Richter, J.E. 1982. Memo to C.E. Stephan, U.S. EPA,
Duluth, MN. Results of Algal Toxicity Tests with Priority
Pollutants. Center for Lake Superior Environmental
Stud., Univ. of Wisconsin-Superior, Superior, Wl: 12 p.

14312

AF, Plant

Plants do not drive
criteria, and therefore,
are not included in
CWA review and
approval of OR WQS

Ruesink, R.G. and L.L. Smith Jr. 1975. The relationship
of the 96-hr LC50 to the lethal threshold concentration of
hexavalent chromium, phenol, and sodium
pentachlorophenate for fathead minnows (Pimephales
promelas Rafinesque). Trans. Am. Fish. Soc. 104(3):
567-570 (Personal Communication Used as Reference).

837

AF, Tox

Saltabas, O. and G. Akcin. 1994. Removal of chromium,
copper and nickel by water hyacinth (Eichhornia
crassipes). Toxicol. Environ. Chem. 41: 131-134.

14541

AF, Plant, Tox, Uendp

Plants do not drive
criteria, and therefore,
are not included in
CWA review and
approval of OR WQS

Santojanni, A., G. Gorbi and F. Sartore. 1998. Prediction
of fecundity in chronic toxicity tests on Daphnia magna.
Water Res. 32(10): 3146-3156.

19658

AF, UEndp, Tox, Dur

Sarkar, S.K. 1989. Evaluation of two heavy metals on the
oxygen consumption of Tilapia mossambica (Peters).
Geobios 16(2/3): 108-110.

13389

AF, UEndp, Dur

Sastry, K.V. and K.M. Sunita. 1982. Effect of cadmium
and chromium on the intestinal absorption of glucose in
the snakehead fish, Channa punctatus. Toxicol. Lett.
10(2/3): 293-296.

15667

AF, UEndp, Tox, Dur,
RouExp, NonRes

317

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Sauvant, M.P., D. Pepin, C.A. Groliere and J. Bohatier.
1995. Effects of organic and inorganic substances on the
cell proliferation of L-929 fibroblasts and Tetrahymena
pyriformis GL protozoa used for toxicological bioassays.
Bull. Environ. Contam. Toxicol. 55(2): 171-178.

14980

AF, Ace, Dur

Sauvant, M.P., D. Pepin, J. Bohatier and C.A. Groliere.
1995. Microplate technique for screening and assessing
cytotoxicity of xenobiotics with Tetrahymena pyriformis.
Ecotoxicol. Environ. Saf. 32(2): 159-165.

16142

AF, Ace, Dur

Schiffman, R.H. and P.O. Fromm. 1959. Chromium-
induced changes in the blood of rainbow trout, Salmo
qairdnerii. Sewage Ind. Wastes 31: 205-211.

10294

AF, Dur, Tox / UEndp, Dur,
Tox

See, C.L., A.L. Buikema, Jr. and J. Cairns, Jr. 1974. The
effects of selected toxicants on survival of Dugesia
tigrina (Turbellaria). ASB (Assoc. Southeast. Biol.) Bull.
21(2): 82.

8709

AF, Tox

Shabana, E.F., A.F. Dowidar, I .A. Kobbia and S.A. El
Attar. 1986. Studies on the effects of some heavy metals
on the biological activities of some phytoplankton
species. II. The effects of some metallic ions on the
growth criteria and morphology of Anabaena oryzae and
Aulosira fertilissima. Egypt. J. Physiol. Sci. 13(1/2): 55-
71.

3385

AF, Plant, UEndp

Plants do not drive
criteria, and therefore,
are not included in
CWA review and
approval of OR WQS

Shabana, E.F., I .A. Kobbia, A.E. Dowidar and S.A. El
Attar. 1986. Studies on the effects of some heavy metals
on the biological activities of some phytoplankton
species. III. Effects ofAI3+, Cr3+, Pb2+and Zn2+on
heterocyst frequency, nitrogen and phosphorus
metabolism of Anabaena. Egypt. J. Physiol. Sci. 13(1/2):
73-94.

3406

AF, Plant, UEndp, Tox

Plants do not drive
criteria, and therefore,
are not included in
CWA review and
approval of OR WQS

Shandilya, S. and V. Banerjee. 1989. Effect of sublethal
toxicity of zinc and chromium on peripheral hemogram in
the fish Heteropneustes fossilis. Environ. Ecol. 7(1 ):16-
23.

2388

AF, UEndp, NonRes, Dur

Sinha, S., U.N. Rai, R.D. Tripathi and P. Chandra. 1993.
Chromium and manganese uptake by Hydrilla verticillata
(l.f.) Royle: Amelioration of chromium toxicity by
manganese. J. Environ. Sci. Health A28(7): 1545-1552.

13288

AF, Plant, UEndp, Tox

Plants do not drive
criteria, and therefore,
are not included in
CWA review and
approval of OR WQS

Slabbert, J.L. and J.P. Maree. 1986. Evaluation of
interactive toxic effects of chemicals in water using a
Tetrahymena pyriformis toxicity screening test. Water
S.A. 12(2): 57-62.

12836

AF, Ace, UEndp, Dur

318

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ECOTOX
EcoRef#

Rejection Code(s)

Comment

Smissaert, H.R., D.A. Van Bruggen and A.M. Thiadens.
1975. Pitfalls in experiment on a possible toxic effect of
chromium III, with special reference to the
acetylcholinesterase of the gill of the rainbow. In: J.H.
Koeman and J.J.T.W.A. Strik (Eds.), Sublethal Effects of
Toxic Chemicals on Aquatic Animals, Elsevier Sci. Publ.,
Amsterdam, NY: 93-102.

15543

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Snell, T.W. 1991. New Rotifer Bioassays for Aquatic
Toxicology. Final Report, U.S. Army Medical Research
and Development Command, Ft. Detrick, Frederick, MD:
29 p. (U.S. NTIS AD-A258002).

17689

AF, UEndp, Tox

Snell, T.W. and B.D. Moffat. 1992. A 2-d life cycle test
with the rotifer Brachionus calyciflorus. Environ. Toxicol.
Chem. 11(9): 1249-1257.

3963

AF, Dur, Tox

Sornaraj, R., P. Baskaran and S. Thanalakshmi. 1995.
Effects of heavy metals on some physiological
responses of air-breathing fish Channa punctatus
(Bloch). Environ. Ecol. 13(1): 202-207.

17380

AF, Tox

Sornaraj, R., S. Thanalashmi and P. Baskaran. 1995.
Influence of heavy metals on biochemical responses of
the freshwater air-breathing fish Channa punctatus
(Bloch). J. Ecotoxicol. Environ. Monit. 5(1): 19-27.

14012

AF, NonRes, UEndp, Dur

Sprague, J.B. and W.J. Logan. 1979. Separate and joint
toxicity to rainbow trout of substances used in drilling
fluids for oil exploration. Environ. Pollut. 19(4): 269-281
(Author Communication Used).

869

AF, Tox

Sridevi, B„ K.V. Reddy and S.L.N. Reddy. 1998. Effect
of trivalent and hexavalent chromium on antioxidant
enzyme activities and lipid peroxidation in a freshwater
field crab, Barytelphusa guerini. Bull. Environ. Contam.
Toxicol. 61(3): 384-390.

19810

AF, Dur

Stanley, R.A. 1974. Toxicity of heavy metals and salts to
Eurasian watermilfoil (Myriophyllum spicatum L.). Arch.
Environ. Contam. Toxicol. 2(4): 331-341.

2262

AF, Plant, Tox

Plants do not drive
criteria, and therefore,
are not included in
CWA review and
approval of OR WQS

Stary, J. and K. Kratzer. 1982. The cumulation of toxic
metals on alga. J. Environ. Anal. Chem. 12: 65-71.

14286

AF, Plant, UEndp, Dur

Plants do not drive
criteria, and therefore,
are not included in
CWA review and
approval of OR WQS

Stary, J., B. Havlik, K. Kratzer, J. Prasilova and J.
Hanusova. 1983. Cumulation of zinc, cadmium and
mercury on the alga Scenedesmus obliquus. Acta
Hydrochim. Hydrobiol. 11(4): 401-409.

14088

AF, Plant, UEndp, Dur

Plants do not drive
criteria, and therefore,
are not included in
CWA review and
approval of OR WQS

319

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Stary, J., K. Kratzer, J. Prasilova and T. Vrbska. 1982.
The cumulation of chromium and arsenic species in fish
(Poecilia reticulata). Int. J. Environ. Anal. Chem. 12: 253-
257.

14539

AF, Plant, UEndp, Dur

Plants do not drive
criteria, and therefore,
are not included in
CWA review and
approval of OR WQS

Tatara, C.P., M.C. Newman, J.T. McCloskey and P.L.
Williams. 1998. Use of ion characteristics to predict
relative toxicity of mono-, di- and trivalent metal ions:
Caenorhabditis elegans. Aquat. Toxicol. 42: 255-269.

5072

AF, Dur

Tomasik, P., C.H.D. Magadza, S. Mhizha and A.
Chirume. 1995. The metal-metal interactions in biological
systems. Part III. Daphnia magna. Water Air Soil Pollut.
82: 695-711.

45194

AF, UEndp, RouExp, Dur

Tomasik, P., C.M. Magadza, S. Mhizha, A. Chirume,
M.F. Zaranyika and S. Muchiriri. 1995. Metal-metal
interactions in biological systems. Part IV. Freshwater
snail Bulinus globosus. Water Air Soil Pollut. 83(1/2):
123-145.

16369

AF, UEndp, NoConc

Vareille-Morel, C. and C. Chaisemartin. 1982. Natural
tolerance and acclimation of different populations of
Austropotamobius pallipes (Le.) to heavy metals
(chromium and lead). Acta Oecol.Oecol.Appl. 3(1): 105-
122 (FRE) (ENGABS).

15732

NonRes

Venugopal, N.B.R.K. and S.L.N. Reddy. 1992.
Nephrotoxic and hepatotoxic effects of trivalent and
hexavalent chromium in a teleost fish Anabas scandens:
Enzymological and biochemical changes. Ecotoxicol.
Environ. Saf. 24(3): 287-293.

6572

AF, UEndp, Dur

Venugopal, N.B.R.K. and S.L.N. Reddy. 1992. Effect of
trivalent and hexavalent chromium on renal and hepatic
tissue glycogen metabolism of a fresh water teleost
Anabas scandens. Environ. Monit. Assess. 21(2): 133-
140.

7399

AF, UEndp, Dur

Venugopal, N.B.R.K. and S.L.N. Reddy. 1993. In vivo
effects of trivalent and hexavalent chromium on renal
and hepatic ATPases of a freshwater teleost Anabas
scandens. Environ. Monit. Assess. 28(2): 131-136.

10731

AF, Dur

Verma, N., S. Batta and R. Rehal. 1995. Studies on
some cyanobacteria for the selection of bioindicators and
bioscavengers of chromium metal ions for industrial
waste waters. Int. J. Environ. Stud. 47(3/4): 211-215.

19599

AF, UEndp, Tox, Bact, Dur

320

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Verma, S.R., M. Jain and R.C. Dalela. 1982. A laboratory
study to assess separate and in-combination effects of
zinc, chromium and nickel to the gish Mystus vittatus.
Acta Hydrochim. Hydrobiol. 10(1): 23-29.

15793

AF, Tox

Vijayram, K. and P. Geraldine. 1996. Regulation of
essential heavy metals (Cu, Cr, and Zn) by the
freshwater prawn Macrobrachium malcolmsonii (Milne
Edwards). Bull. Environ. Contam. Toxicol. 56(2): 335-
342.

16442

AF, UEndp, Tox, Dur

Vincent, S. and T. Ambrose. 1994. Uptake of heavy
metals cadmium and chromium in tissues of the Indian
major carp, Catla catla (Ham.). Indian J. Environ. Health
36(3): 200-204.

19450

AF, UEndp, Tox, Dur

Vymazal, J. 1990. Uptake of lead, chromium, cadmium
and cobalt by Cladophora glomerata. Bull. Environ.
Contam. Toxicol. 44(2): 468-472.

2191

AF, Plant, UEndp, Dur

Plants do not drive
criteria, and therefore,
are not included in
CWA review and
approval of OR WQS

Vymazal, J. 1990. Uptake of heavy metals by
Cladophora glomerata. Acta Hydrochim. Hydrobiol.
18(6): 657-665.

45131

AF, Plant, UEndp, Dur

Plants do not drive
criteria, and therefore,
are not included in
CWA review and
approval of OR WQS

Vymazal, J. 1995. Influence of pH on heavy metals
uptake by Cladophora glomerata. Pol. Arch. Hydrobiol.
42(3): 231-237.

45130

AF, Plant, UEndp, Dur

Plants do not drive
criteria, and therefore,
are not included in
CWA review and
approval of OR WQS

Wang, W. 1986. Toxicity tests of aquatic pollutants by
using common duckweed. Environ. Pollut. Ser. B Chem.
Phys. 11(1): 1-14.

11789

AF, Plant, Tox

Plants do not drive
criteria, and therefore,
are not included in
CWA review and
approval of OR WQS

Winner, R.W. 1976. Toxicity of Copper to Daphnids in
Reconstituted and Natural Waters. EPA-600/3-76-051,
U.S. EPA, Duluth, MN: 68 p.(U.S. NTIS PB-252915)
(Publ in Part As 8477 and 8478).

8476

AF, Tox

Wolmarans, C.T., E. Yssel and V.L. Hamilton-Attwell.
1988. Toxic effects of chromium on Schistosoma
haematobium miracidia. Bull. Environ. Contam. Toxicol.
41(6): 928-935.

8767

AF, UEndp, Dur

Wooldridge, C.R. and D.P. Wooldridge. 1969. Internal
damage in an aquatic beetle exposed to sublethal
concentrations of inorganic ions. Ann. Entomol. Soc. Am.
62(4): 921-933.

2868

AF, UEndp, Dur

321

-------
Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated the studies and determined that the results were not reliable for use in this determination, either because they were
not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

FAV in the most recent national ambient water quality criteria dataset used to derive the CMC , EPA is providing a
transparent rationale as to why they were not utilized (see below).

4) For the studies that were not utilized because they were not found to be pertinent to this determination (including
failing the QA/QC procedures listed in Appendix A) upon initial review of the download from ECOTOX, EPA is
providing the code that identifies why EPA determined that the results of the study were not reliable.

General QA/QC failure because non-resident species in Oregon

Tests with the following several species were used in the EPA BE of OR WQS for chromium III in freshwater, but were not
considered in the CWA review and approval/disapproval action of the standards because these species do not have a breeding wild
population in Oregon's waters:

Ephemerella

subvaria

Mayfly

Warnick and Bell 1969

Poecilia

reticulata

Guppy

Pickering and Henderson 1964

Other Acute tests failins QA/QC by species

Daphnia pulex - Cladoceran

The following test was included in EPA's BE of the OR WQS for chromium III in freshwater, but was not used in this CWA review
and approval/disapproval action of these standards because it is a 96-hr test, and the 48-hr test for the same species is the preferred
data according to the 1985 Guidelines. Also, note that the 96-h LC50 from this test, when normalized to a hardness of 100 mg/L as
CaC03 and expressed on a dissolved basis, was over an order of magnitude lower than the acute values for all other species, including
other cladocerans. Data from the 48-hr test in this study was used.

82 U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient Water. EPA-820-B-96-001.

322

-------
Stackhouse, R.A. and W.H. Benson. 1989. The effect of humic acid on the toxicity and bioavailability of trivalent chromium.
Ecotoxicol. Environ. Saf. 17(1): 105-111.

Other Chronic tests failing QA/QC by species

Daphnia magna - Cladoceran

Kuhn, R., M. Pattard, K.-D. Pernak and A. Winter. 1989. Results of the harmful effects of water pollutants to Daphnia magna
in the 21 day reproduction test. Wat. Res. 23(4): 501-510.

323

-------
Appendix E Chromium VI (freshwater)
Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Anderson, 1946.

2130

UEndp, Dur

No Info

Bringmann, G. and R. Kuhn. 1960. The Water-Toxicological
Detection of Insecticides (Zum Wasser-Toxikologischen
Nachweis von Insektiziden). Gesund.lng. 8:243-244 (GER).

58990

Det

Khangarot, B.S., P.K. Ray and H. Chandra. 1987. Daphnia
magna as a Model to Assess Heavy Metal Toxicity:
Comparative Assessment with Mouse System. Acta
Hydrochim. Hydrobiol. 15(4):427-432.

12575

Det

Merlin, G., P. Eulaffroy and G. Blake. 1993. Use of
Fluorescence Induction Kinetics of Lemna minor as a Tool for
Chemical Stress Evaluation. Sci.Total Environ.(Suppl.) :761-
772.

4334

Plant

Plants do not drive
criteria, and
therefore, are not
included in CWA
review and approval
of OR WQS

Wang, W. 1986. Toxicity Tests of Aquatic Pollutants by Using
Common Duckweed. Environ.Pollut.Ser.B Chem.Phys.
11 (1 ):1 -14.

11789

Plant

Plants do not drive
criteria, and
therefore, are not
included in CWA
review and approval
of OR WQS

Wang, W. 1987. Chromate Ion As a Reference Toxicant for
Aquatic Phytotoxicity Tests. Environ.Toxicol.Chem. 6(12):953-
960.

12693

Plant

Plants do not drive
criteria, and
therefore, are not
included in CWA
review and approval
of OR WQS

Note: Also see Chromium III

Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

324

-------
3) For the studies that were not utilized, but the most representative GMAV/2 or most representative SMCV fell below the
criterion, or, if the studies were for a species associated with one of the four most sensitive genera used to calculate the
FAV in the most recent national ambient water quality criteria dataset used to derive the CMC, EPA is providing a
transparent rationale as to why they were not utilized (see below).

General QA/QC failure because non-resident species in Oregon

Tests with the following several species were used in the EPA BE of OR WQS for chromium VI in freshwater, but were not
considered in the CWA review and approval/disapproval action of the standards because these species do not have a breeding wild
population in Oregon's waters:

Gammarus

pseudolimnaeus

Amphipod

Call etal. 1983

Daphnia

obtusa

Cladoceran

Rossini and Ronco 1996; Coniglio and Baudo 1989

Other Acute tests failins QA/QC by species

Daphnia pulex - Cladoceran

The following tests were included in EPA's BE of the OR WQS for chromium VI in freshwater, but were not used in this CWA
review and approval/disapproval action of these standards because the tests were not based on the preferred flow-through measured
test conditions; however, other flow-through measured test concentrations were available for these species.

Mount, D.I. and T.J. Norberg. 1984. A seven-day life-cycle cladoceran toxicity test. Environ. Toxicol. Chem. 3: 425.

One LC50 value from S,U test of 47.14 |ig/L.

Cairns, J. Jr., A.L. Buikema, A.G. Heath and B.C. Parker. 1978. Effects of Temperature on Aquatic Organism Sensitivity to
Selected Chemicals. Va. Water Resour. Res. Center Bull. 106, OWRT Proj. B-084-VA, Va. Polytechnic Inst. State Univ.,
Blacksburg, VA: 88 p.

One LC50 value from S,U test of 392.80 |ig/L.

325

-------
Dorn, P.B., J.H. Rodgers Jr., K.M. Jop, J.C. Raia and K.L. Dickson. 1987. Hexavalent chromium as a reference toxicant in
effluent toxicity tests. Environ. Toxicol. Chem. 6(6): 435-444.

Eighteen LC50 values from static tests ranging from 19.64 to 166.94 |ig/L.

Elnabarawy, M.T., A.N. Welter and R.R. Robideau. 1986. Relative sensitivity of three daphnid species to selected organic and
inorganic chemicals. Environ. Toxicol. Chem. 5(4): 393-398.

One LC50 value from S,U test of 119.80 |ig/L.

Jop, K.M., A.M. Askew, D.J. Texeira and J. MacGregor. 1993. Quality Control in Aquatic Toxicity Testing Programs:
Evaluation of Copper and Hexavalent Chromium as Reference Toxicants. Environ. Toxicol. Risk Assess., ASTM STP 1179,
W.G. Landis, J.S. Hughes and M.A. Lewis (Eds.), Amer. Soc. for Testing and Materials, Philadelphia, pp. 397-404.

One LC50 value from S,M test of 183.63 |ig/L.

Jop, K.M., J.H. Rodgers Jr., E.E. Price and K.L. Dickson. 1986. Renewal device for test solutions in daphnia toxicity tests.
Bull. Environ. Contam. Toxicol. 36: 95-100.

Two LC50 values from static and renewal tests, both with values of 216.04 |ig/L.

Jop, K.M., J.H. Rodgers Jr., P.B. Dorn and K.L. Dickson. 1986. Use of hexavalent chromium as a reference toxicant in
aquatic toxicity tests. In: T.M. Poston and R. Purdy (Eds.), Aquatic Toxicology and Environmental Fate, 9th Volume, ASTM
STP 921, Philadelphia, PA: 390-403.

One LC50 value from a static test of 108.02 |ig/L.

Jop, K.M., T.F. Parkerton, J.H. Rodgers Jr., K.L. Dickson and P.B. Dorn. 1987. Comparative toxicity and speciation of two
hexavalent chromium salts in acute toxicity tests. Environ. Toxicol. Chem. 6(9): 697-703.

Two LC50 values from static tests, both with values of 216.04 |ig/L.

Jop, K.M., R.B. Foster and A.M. Askew. 1991. Factors affecting toxicity identification evaluation: The role of source water
used in industrial processes. In: M.A. Mayes and M.G. Barron (Eds.), Aquatic Toxicology and Risk Assessment, 14th Volume,
ASTM STP 1124, Philadelphia, PA: 84-93.

One LC50 value from a static test of 216.04 |ig/L.

Stackhouse, R.A. and W.H. Benson. 1988. The influence of humic acid on the toxicity and bioavailability of selected trace
metals. Aquat. Toxicol. 13(2): 99-108.

326

-------
One LC50 value from a static test of 356.07 |ig/L.

Daphttia magna - Cladoceran

Anderson, B.G. 1946. The toxicity thresholds of various substances found in industrial wastes as determined by the use of
Daphttia magna. Sew. Works J. 16: 1156.

Two LC50 values from S,U tests ranging from <103 to <123 |ig/L.

Baird, D.J., I. Barber, M. Bradley, A.M.V.M. Soares and P. Calow. 1991. A comparative study of genotype sensitivity to acute
toxic stress using clones of Daphnia magna Straus. Ecotoxicol. Environ. Saf. 21(3): 257-265.

Six LC50 values from static tests ranging from 98.56 to 283.11 |ig/L.

Berglind, R. and G. Dave. 1984. Acute toxicity of chromate, DDT, PCP, TPBS, and zinc to Daphnia magna cultured in hard
and soft water. Bull. Environ. Contam. Toxicol. 33(1): 63-68.

Two LC50 values from static tests ranging from 265.14 to 314.24 |ig/L.

Two LC50 values from static tests ranging from 549.92 to 883.80 |ig/L.

Call, D.J., L.T. Brooke, N. Ahmad and D.D. Vaishnav. 1981. Aquatic Pollutant Hazard Assessments and Development of a
Hazard Prediction Technology by Quantitative Structure-activity Relationships. Second Quarterly Report to EPA. Center
for Lake Superior Environmental Studies, University of Wisconsin-Superior, Superior, WI: 74 p.

Twelve LC50 values from S,M tests ranging from 15.02 to 208.18 |ig/L.

Cerejeira, M.J., T. Pereira and A. Silva-Fernandes. 1998. Use of new microbiotests with Daphnia magna and Selenstrum
capricornutum immobilized forms. Chemosphere 37(14/15): 2949-2955.

One LC50 value from an unknown test of 638.30 |ig/L.

327

-------
Crisinel, A., L. Delaunay, D. Rossel, J. Tarradellas, H. Meyer, H. Saiah, P. Vogel, C. Delisle and C. Blaise. 1994. Cyst-based
ecotoxicological tests using anostracans: Comparison of two species of Streptocephalus. Environ. Toxicol. Water Qual. 9(4):
317-326.

One LC50 value from an unknown test of 1031.10 |ig/L.

Diamantino, R.C., L. Gilhermino, E. Almeida and A.M.V.M. Soares. 2000. Toxicity of sodium molybdate and sodium
dichromate to Daphnia magna Straus evaluated in acute, chronic, and acetylcholinesterase inhibition tests. Ecotoxicol.
Environ. Saf. 45: 253-259.

One LC50 value from a S,U test of 284.78 |ig/L.

Dowden, B.F. and H.J. Bennett. 1965. Toxicity of selected chemicals to certain animals. J. Water Pollut. Control Fed. 37:
1308-1316.

One LC50 value from a S,U test of 138.46 |ig/L.

Elnabarawy, M.T., A.N. Welter and R.R. Robideau. 1986. Relative sensitivity of three daphnid species to selected organic and
inorganic chemicals. Environ. Toxicol. Chem. 5(4): 393-358.

One LC50 value from a static test of 109.98 |ig/L.

Enserink, L., W. Luttmer and H. Maas-Diepeveen. 1990. Reproductive Strategy of Daphnia magna Affects the Sensitivity of
Its Progeny in Acute Toxicity Tests. Aquat. Toxicol. 17(1): 15-26.

One LC50 value from a static test of 1276.60 |ig/L.

Fargasova, A. 1994. Comparative toxicity of five metals on various biological subjects. Bull. Environ. Contam. Toxicol.
53(2): 317-324.

Two LC50 values from static tests ranging from 157.12 to 353.52 |ig/L.

Fargasova, A. 1994. Toxicity of metals on Daphnia magna and Tubifex tubifex. Ecotoxicol. Environ. Saf. 27(2): 210-213.

Two LC50 values from unknown tests ranging from 159.08 to 357.45 |ig/L.

Guilhermino, L., T. Diamantino, M.C. Silva and A.M.V.M. Soares. 2000. Acute toxicity test with Daphnia magna: An
alternative to mammals in the prescreening of chemical toxicity? Ecotoxicol. Environ. Saf. 46(3): 357-362.

One LC50 value from an unknown test of 764.00 |ig/L.

328

-------
Guilhermino, L., T.C. Diamantino, R. Ribeiro, F. Goncalves and A.M.V.M. Soares. 1997. Suitability of test media containing
EDTA for the evaluation of acute metal toxicity to Daphttia magna Straus. Ecotoxicol. Environ. Saf. 38(3): 292-295.

Two LC50 values from static tests ranging from 183.63 to 224.98 |ig/L.

Hermens, J., H. Canton, N. Steyger and R. Wegman. 1984. Joint effects of a mixture of 14 chemicals on mortality and
inhibition of reproduction of Daphttia magna. Aquat. Toxicol. 5(4): 315-322.

One LC50 value from a static test of 451.72 |ig/L.

Janssen, C.R. and G. Persoone. 1993. Rapid toxicity screening tests for aquatic biota. 1. Methodology and experiments with
Daphnia magna. Environ. Toxicol. Chem. 12: 711-717.

One LC50 value from a static test of 157.12 |ig/L.

Kazlauskiene, N., A. Burba and G. Svecevicius. 1994. Acute toxicity of five galvanic heavy metals to hydrobionts. Ekologija
1: 33-36.

One LC50 value from a renewal test of 147.30 |ig/L.

Kim, S.D., K.S. Park and M.B. Gu. 2002. Toxicity of hexavalent chromium to Daphnia magna: Influence of reduction reaction
by ferrous iron. J. Hazard. Mat. A93(2): 155-164.

One LC50 value from a S,U test of 5361.32 |ig/L.

Office of Pesticide Programs. 2000. Pesticide Ecotoxicity Database (Formerly: Environmental Effects Database (EEDB)).
Environmental Fate and Effects Division, U.S. EPA, Washington, D.C.

One LC50 value from a static test of 746.32 |ig/L.

Oikari, A., J. Kukkonen and V. Virtanen. 1992. Acute toxicity of chemicals to Daphnia magna in humic waters. Sci. Total
Environ. 117/118: 367-377.

One LC50 value from a static test of 19.64 |ig/L.

Stephenson, R.R. and S.A. Watts. 1984. Chronic toxicity tests with Daphnia magna: The effects of different food and
temperature regimes on survival, reproduction and growth. Environ. Pollut. Ser. A Ecol. Biol. 36(2): 95-107.

Ten LC50 values from static tests ranging from 34.37 to 117.84 |ig/L.

329

-------
Trabalka, J.R. and C.W. Gehrs. 1977. An observation on the toxicity of hexavalent chromium to Daphnia magna. Toxicol.
Letters 1: 131.

One LC50 value from a S,M test of 49.10 |ig/L.

White, B. 1979. Report of two toxicity evaluations conducted using hexavalent chromium. Michigan Department of Natural
Resources.

Two LC50 values from S,M tests ranging from 154.17 to 171.85 |ig/L.

Ceriodaphnia reticulata - Cladoceran

Elnabarawy, M.T., A.N. Welter and R.R. Robideau. 1986. Relative sensitivity of three daphnid species to selected organic and
inorganic chemicals. Environ. Toxicol. Chem. 5(4): 393-358.

One LC50 value from a S,U test of 191.49 |ig/L.

Simocephalus vetulus - Cladoceran

Mount, D.I. and T.J. Norberg. 1984. A seven-day life-cycle cladoceran toxicity test. Environ. Toxicol. Chem. 3: 425.

One LC50 value from a S,U test of 49.10 |ig/L.

Gammarus pseudolimnaeus - Cladoceran

330

-------
Call, D.J., L.T. Brooke, N. Ahmad and D.D. Vaishnav. 1981. Aquatic Pollutant Hazard Assessments and Development of a
Hazard Prediction Technology by Quantitative Structure-activity Relationships. Second Quarterly Report to EPA. Center
for Lake Superior Environmental Studies, University of Wisconsin-Superior, Superior, WI: 74 p.

One LC50 value from a S,M test of 99.18 |ig/L. Some data from this study was used for this species.

Call, D.J., L.T. Brooke, N. Ahmad and J.E. Richter. 1983. Toxicity and metabolism studies with EPA priority pollutants and
related chemicals in freshwater organisms. PB83-263665. National Technical Information Service, Springfield, VA.

One LC50 value from a S,U test of 92.41 |ig/L. Some data from this study was used for this species.

Other Chronic tests failing QA/QC by species
Daphnia magna - Cladoceran

Gorbi, G., M.G. Corradi, M. Invidia, L. Rivara and M. Bassi. 2002. Is Cr(VI) toxicity to Daphnia magna modified by food
availability or algal exudate? The hypothesis of a specific chromium/algae/exudates interaction. Water Res. 36(8): 1917-1926.

The concentrations in this chronic test were unmeasured. Unmeasured chronic tests are considered "other" data and relegated to Table
6 per the 1985 Guidelines.

Kuhn, R., M. Pattard, K. Pernak and A. Winter. 1989. Results of the harmful effects of water pollutants to Daphnia magna in
the 21 day reproduction test. Water Res. 23(4): 501-510 (OECDG Data File).

This test did not report a corresponding LOEC with the NOEC. Furthermore, many details were missing in this report.

Munzinger, A. and F. Monicelli. 1991. A comparison of the sensitivity of three Daphnia magna populations under chronic
heavy metal stress. Ecotoxicol. Environ. Saf. 22: 24-31.

Effects occurred at all concentrations tested. The value used in the BE is an LOEC indicated with an effect occurring less than "<"
4.81 |ig/L. Other tests were available and provided definitive chronic values for the species. Interestingly, this value corresponds with
the SMCV calculated for Daphnia magna from those definitive tests.

Ceriodaphnia dubia - Cladoceran

DeGraeve, G.M., J.D. Cooney, B.H. Marsh, T.L. Pollock and N.G. Reichenbach. 1992. Variability in the performance of the
7-d Ceriodaphnia dubia survival and reproduction test: An intra- and interlaboratory study. Environ. Toxicol. Chem. 11(6):
851-866.

331

-------
This study was rejected because a corresponding LOEC cannot be determined from the article as published.

332

-------
Appendix F Dieldrin (freshwater)
Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Adema, D.M.M. 1978. Daphnia magna as a
Test Animal in Acute and Chronic Toxicity
Tests. Hydrobiologia 59(2):125-134.

2018

See comment

LC50 value is a greater than
highest concentration tested,
i.e., > 200 ug/L; other more
appropriate data used for the
species.

Allan, J.D., and R.E. Daniels. 1980. Sublethal
Effects of Pollutants: Test of the Usefulness of
Life Table for Evaluating the Impact of Chronic
Toxicity. Tech.Rep.No.57, Water
Resour.Res.Cen., University of Maryland,
College Park, MD:69 p.(U.S.NTIS PB80-
216674).

5582

Con

Argyle, MR.., G.C. Williams, and C.B. Daniel.
1975. Dieldrin in the Diet of Channel Catfish
(Ictalurus punctatus): Uptake and Effect on
Growth. J.Fish.Res.Board Can. 32(11):2197-
2204.

15795

UEndp, Dur, RouExp

Batterton, J.C., G.M. Boush, and F. Matsumura.
1971. Growth Response of Blue-Green Algae
to Aldrin, Dieldrin Endrin and Their Metabolites.
Bull.Environ.Contam.Toxicol. 6(6):589-594.

9282

Plant, UEndp, Dur,

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS

Bedford, J.W., and M.J. Zabik. 1973. Bioactive
Compounds in the Aquatic Environment:
Uptake and Loss of DDT and Dieldrin by
Freshwater Mussels.

Arch.Environ.Contam.Toxicol. 1 (2):97-111.

2073

UEndp

Benson, B., and G.M. Boush. 1983. Effect of
Pesticides and PCBs on Budding Rates of
Green Hydra. Bull.Environ.Contam.Toxicol.
30(3):344-350.

15737

Plant, UEndp

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS

Bhatnagar, P., S. Kumar, and R. Lai. 1988.
Uptake and Bioconcentration of Dieldrin,
Dimethoate, and Permethrin by Tetrahymena
pyriformis. Water Air Soil Pollut. 40(3/4):345-
349.

4707

UEndp, Dur

333

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Boryslawskyj, M., A.C. Garrood, J.T. Pearson,
and D. Woodhead. 1987. Rates of
Accumulation of Dieldrin by a Freshwater Filter
Feeder: Sphaerium corneum. Environ.Pollut.
43(1):3-13.

12248

UEndp, Dur

Boryslawskyj, M., T. Garrood, M. Stanger, T.
Pearson, and D. Woodhead. 1988. Role of
Lipid/Water Partitioning and Membrane
Composition in the Uptake of Organochlorine
Pesticides Into a Freshwater Mussel.
Mar.Environ.Res. 24(1-4):57-61.

13095

UEndp, Dur

Bowman, M.C., W.L. Oiler, T. Cairns, A.B.
Gosnell, and K.H. Oliver. 1981. Stressed
Bioassay Systems for Rapid Screening of
Pesticide Residues. Part I: Evaluation of
Bioassay Systems.

Arch. Envi ron. Contam .Toxicol. 10:9-24.

2192

Dur

Boyd, J.E.. 1957. The Use of Daphnia magna in
the Microbioassay of Insecticides. Ph.D.Thesis,
Penn.State University, University Park, PA
:194.

14647

UEndp, Dur

Brockway, D.L.. 1972. The Uptake, Storage,
and Release of Dieldrin and Some Effects of its
Release in the Fish, Cichlasoma bimaculatum
(Linnaeus). Ph.D.Thesis, University of
Michigan, Ann Arbor, Ml:104 p; Diss.Abstr.lnt.B
Sci.Eng.33(9):4323-4324 (1973).

9050

UEndp, Con

Bulkley, R.V., L.R. Shannon, and R.L. Kellogg.
1974. Contamination of Channel Catfish with
Dieldrin from Agricultural Runoff. Proj.No.A-
042-IA, Iowa State Water Res.Inst., Iowa State
University, Ames, IA :144 p..

16211

UEndp, Dur

Burchfield, H.P., and E.E. Storrs. 1954. Kinetics
of Insecticidal Action Based on the
Photomigration of Larvae of Aedes aegypti (L.).
Contrib.Boyce Thompson Inst. 17:439-452.

2929

UEndp, Dur, Con

Burnett, K.M., and W.J. Liss. 1990. Multi-
Steady-State Toxicant Fate and Effect in
Laboratory Aquatic Ecosystems.
Environ.Toxicol.Chem. 9(3):637-647.

3135

UEndp, Con

Cairns, J.Jr.. 1968. The Effects of Dieldrin on
Diatoms. Mosq.News 28:177-179.

14723

Plant, Dur

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS

Cairns, J.Jr., and J.J. Loos. 1966. Changes in
Guppy Populations Resulting From Exposure to

2429

UEndp, Con

334

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Dieldrin. Prog.Fish-Cult. 28(4):220-226.

Cairns, J.Jr., N.R. Foster, and J.J. Loos. 1967.
Effects of Sublethal Concentrations of Dieldrin
on Laboratory Populations of Guppies, Poecilia
reticulata Peters.

Proc.Acad.Nat.Sci.Philadelphia 119:75-91.

7386

UEndp, Con

Christoffers, D., and D.E.W. Ernst. 1983. The
In-Vivo Fluorescence of Chlorella fusca as a
Biological Test for the Inhibition of
Photosynthesis. Toxicol.Environ.Chem. 7:61-
71.

45160

Plant, UEndp, Dur,

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS

Clegg, T.J., and J.L. Koevenig. 1974. The
Effect of Four Chlorinated Hydrocarbon
Pesticides and One Organophosphate
Pesticide on ATP Levels in Three Species of
Photosynthesizing Freshwater Algae. Bot.Gaz.
135(4):368-372.

17261

Plant, UEndp, Dur,

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS

Clemens, H.P., and K.E. Sneed. 1959. Lethal
Doses of Several Commercial Chemicals for
Fingerling Channel Catfish. U.S.Fish
Wildl.Serv.Sci.Rep.Fish.No.316, U.S.D.I.,
Washington, D.C. :10p..

934

Pur, Con

Crosby, D.G., R.K. Tucker, and N. Aharonson.
1966. The Detection of Acute Toxicity with
Daphnia magna. Food Cosmet.Toxicol. 4:503-
514.

7984

Dur, Con

Dhanaraj, P.S., S. Kumar, and R. Lai. 1989.
Bioconcentration and Metabolism of Aldrin and
Phorate by the Blue-Green Algae Anabaena
(ARM 310) and Aulosira fertilissima (ARM 68).
Ag ric. Ecosyst. Environ. 25(2-3): 187-193.

9990

Plant, UEndp, Dur, Con

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS

Diamond, J.M., M.J. Parson, and D. Gruber.
1990. Rapid Detection of Sublethal Toxicity
Using Fish Ventilatory Behavior.
Environ.Toxicol.Chem. 9(1 ):3-11.

3190

UEndp, Dur

Douglas, M.T., D.O. Chanter, I.B. Pell, and
G.M. Burney. 1986. A Proposal for the
Reduction of Animal Numbers Required for the
Acute Toxicityto Fish Test (LC50
Determination). Aquat.Toxicol. 8(4):243-249.

12210

Con

335

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Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Estenik, J.F., and W.J. Collins. 1979. In Vivo
and In Vitro Studies of Mixed-Function Oxidase
in an Aquatic Insect, Chironomus riparius. In:
M.A.Q.Khan, J.J.Lech, and J.J.Menn (Eds.),
Pesticide and Xenobiotic Metabolism in Aquatic
Organisms, ACS (Am.Chem.Soc.) Symp.Ser.99
:349-370 (Author Communication Used).

6830

UEndp, Dur, Con

Ferguson, D.E., D.D. Culley, and W.D. Cotton.
1965. Tolerances of Two Populations of Fresh
Water Shrimp to Five Chlorinated Hydrocarbon
Insecticides. J.Miss.Acad.Sci. 11:235-237.

8063

Dur

Frear, D.E.H., and J.E. Boyd. 1967. Use of
Daphnia magna for the Microbioassay of
Pesticides. I. Development of Standardized
Techniques for Rearing Daphnia and
Preparation of Dosage-M. J.Econ.Entomol.
60(5): 1228-1236.

2820

Dur, Con

Frederick, L.L.. 1975. Comparative Uptake of a
Polychlorinated Biphenyl and Dieldrin by the
White Sucker (Catostomus commersoni).
J.Fish.Res.Board Can. 32(10):1705-1709.

2294

UEndp, Con

Gauna, L., A. Caballero de Castro, M. Chifflet
de Llamas, and A.M. Pechen de D'Angelo.
1991. Effects of Dieldrin Treatment on
Physiological and Biochemical Aspects of the
Toad Embryonic Development.
Bull.Environ.Contam.Toxicol. 46:633-640.

2638

UEndp, Con

Georgacakis, E., and M.A.Q. Khan. 1971.
Toxicity of the Photoisomers of Cyclodiene
Insecticides to Freshwater Animals.
C.R.Hebd.Seances Acad.Sci.Ser.D
233(5315):120-121.

9334

Dur, Con

Gilroy, D.J., H.M. Carpenter, L.K. Siddens, and
L.R. Curtis. 1993. Chronic Dieldrin Exposure
Increases Hepatic Disposition and Biliary
Excretion of [14C]Dieldrin in Rainbow Trout.
Fundam.Appl.Toxicol. 20(3):295-301.

13609

UEndp, RouExp

Glooschenko, W.A.. 1971. The Effect of DDT
and Dieldrin upon 14C Uptake by In Situ
Phytoplankton in Lakes Erie and Ontario. In:
Proc.14th Conf.Int.Assoc.Great Lakes Res.,
Ann Arbor, Ml :219-223.

9337

Plant, UEndp, Dur, Con

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS

Golow, A.A., and K.S. Aborah. 1992. Acute
Toxicity of Wood Tar and Dieldrin to Lebistes
reticulatus (PL). Bull.Environ.Contam.Toxicol.
48(3):463-466.

5007

Dur, Con

336

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Golow, A.A., and T.A. Godzi. 1994. Acute
Toxicity of Deltamethrin and Dieldrin to
Oreochromis niloticus (LIN).
Bull.Environ.Contam.Toxicol. 52(3):351 -354.

13799

Pur

Grant, B.F., and P.M. Mehrle. 1970. Pesticide
Effects on Fish Endocrine Function. In:
Resour.Publ.No.88, Prog.Sport Fish.Res. 1969,
Div.Fish.Res., Bur.Sport Fish.Wildl., U.S.D.I.,
Washington, D.C. :13-15.

17208

UEndp, RouExp

Grzenda, A.R., W.J. Taylor, and D.F. Paris.
1971. The Uptake and Distribution of
Chlorinated Residues by Goldfish (Carassius
auratus) Fed a 14C-Dieldrin Contaminated Diet.
Trans.Am. Fish.Soc. 100(2):215-221.

9341

UEndp, Dur, RouExp,
Con

Grzenda, A.R., W.J. Taylor, and D.F. Paris.
1972. The Elimination and Turnover of 14C-
Dieldrin by Different Goldfish Tissues.

T rans. Am. Fish. Soc. 101 (4):686-690.

9093

UEndp, Dur,Con, RouExp

Hashimoto, Y., and J. Fukami. 1969. Toxicity of
Orally and Topically Applied Pesticide
Ingredients to Carp, Cyprinus carpio Linne.
Sci.Pest Control /Botyu-Kagaku 34(2):63-66.

9038

Dur,Con, RouExp

Hendricks, J.D., T.P. Putnam, and R.O.
Sinnhuber. 1979. Effect of Dietary Dieldrin on
Aflatoxin B1 Carcinogenesis in Rainbow Trout
(Salmo gairdneri). J.Environ.Pathol.Toxicol.
2(3):719-728.

15774

UEndp, RouExp

Hogan, R.L., and E.W. Roelofs. 1971.
Concentrations of Dieldrin in the Blood and
Brain of the Green Sunfish, Lepomis cyanellus,
at Death. J.Fish.Res.Board Can. 28(4):610-
612.

9354

UEndp, Dur, Con

Hoke, R.A., P.A. Kosian, G.T. Ankley, A.M.
Cotter, F.M. Vandermeiden, G.L. Phipps, and
E.J. Durhan. 1995. Check Studies with Hyalella
azteca and Chironomus tentans in Support of
the Development of Sediment Quality Criterion
for Dieldrin. Environ.Toxicol.Chem. 14(3):435-
443.

14207

UEndp, Dur

Holden, A.V.. 1966. Organochlorine Insecticide
Residues in Salmonid Fish. J.AppI.Ecol. 3:45-
53.

4977

UEndp, Dur

Javaid, M.Y., and A. Waiz. 1972. Acute Toxicity
of Five Chlorinated Hydrocarbon Insecticides to
the Fish, Channa punctatuts.

Pak.J.Sci.lnd.Res. 15(4-5):291-293.

8371

Con

337

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Jensen, L.D., and A.R. Gaufin. 1966. Acute and
Long-Term Effects of Organic Insecticides on
Two Species of Stonefly Naiads. J.Water
Pollut.Control.Fed. 38(8): 1273-1286.

604

Dur

Jeyasingam, D.N.T., B. Thayumanavan, and S.
Krishnaswamy. 1978. The Relative Toxicities of
Insecticides on Aquatic Insect Eretes sticticus
(Linn.) (Coleoptera: Dytiscidae). J.Madurai
Univ. 7(1):85-87.

5182

Dur

Kader, H.A., B. Thayumanavan, and S.
Krishnaswamy. 1976. The Relative Toxicities of
Ten Biocides on Spicodiaptomus chelospinus
Rajendran (1973) [Copepoda: Calanoida],
Comp.Physiol.Ecol. 1(3):78-82.

5264

Dur

Kanazawa, J.. 1980. Prediction of Biological
Concentration Potential of Pesticides in Aquatic
Organisms. Rev.Plant Prot.Res. 13:27-36.

59925

UEndp, Dur

Kanazawa, J.. 1981. Measurement of the
Bioconcentration Factors of Pesticides by
Freshwater Fish and Their Correlation with
Physicochemical Properties or Acute Toxicities.
Pestic.Sci. 12(4):417-424.

15599

UEndp, Dur

Kanazawa, J.. 1981. Bioconcentration Potential
of Pesticides by Aquatic Organisms.
Jpn.Pestic.lnf. 39:12-16.

12534

UEndp, Dur

Kanazawa, J.. 1983. A Method of Predicting the
Bioconcentration Potential of Pesticides by
Using Fish. Jarq (Jpn.Agric.Res.Q.) 17(3):173-
179.

10750

UEndp, Dur, Con

Karnak, R.E., and W.J. Collins. 1974. The
Susceptibility to Selected Insecticides and
Acetylcholinesterase Activity in a Laboratory
Colony of Midge Larvae, Chironomus tentans.
Bull.Environ.Contam.Toxicol. 12(1):62-69.

6267

Dur

Kawatski, J.A., and J.C. Schmulbach. 1971.
Toxicities of Aldrin and Dieldrin to the
Freshwater Ostracod Chlamydotheca arcuata.
J.Econ.Entomol. 64(5): 1082-1085.

9366

Dur

Kimura, T., and H.L. Keegan. 1966. Toxicity of
Some Insecticides and Molluscicides for the
Asian Blood Sucking Leech, Hirudo nipponia
Whitman. Am.J.Trop.Med.Hyg. 15(1): 113-115.

2890

Dur, Con

Kuwabara, K., A. Nakamura, and T. Kashimoto.
1980. Effect of Petroleum Oil, Pesticides, PCBs
and Other Environmental Contaminants on the
Hatchability of Artemia salina Dry Eggs.
Bull.Environ.Contam.Toxicol. 25(1):69-74.

6548

UEndp, Dur

338

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

LaBrecque, G.C., J.R. Noe, and J.B. Gahan.
1956. Effectiveness of Insecticides on Granular
Clay Carriers Against Mosquito Larvae.
Mosq.News 16:1-3.

2808

UEndp, Dur, Pur

1 % solution

Lamai, S.L., G.F. Warner, and C.H. Walker.
1999. Effects of Dieldrin on Life Stages of the
African Catfish, Clarias gariepinus (Burchell).
Ecotoxicol. Environ. Saf. 42(1):22-29.

20063

NonRes / NonRes,
UEndp

Lichtenstein, E.P., K.R. Schulz, R.F. Skrentny,
and Y. Tsukano. 1966. Toxicity and Fate of
Insecticide Residues in Water.

Arch. Environ. Health 12:199-212.

8020

UEndp, Dur

Liong, P.C., W.P. Hamzah, and V. Murugan.
1988. Toxicity of Some Pesticides Towards
Freshwater Fishes.

Fish.Bull.Dep.Fish.(Malays.) No .57:13.

3296

Pur

Lohner, T.W., and W.J. Collins. 1987.
Determination of Uptake Rate Constants for Six
Organochlorines in Midge Larvae.
Environ.Toxicol.Chem. 6(2):137-146.

12298

UEndp, Dur, Con

Lorio, W.J., J.H. Jenkins, and M.T. Huish. 1976.
Deposition of Dieldrin in Four Components of
Two Artificial Aquatic Systems and a Farm
Pond. Trans.Am.Fish.Soc. 105(6):695-699.

9009

Plant UEndp, Dur/
UEndp, Dur

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS

Lunn, C.R., D.P. Toews, and D.J. Pree. 1976.
Effects of Three Pesticides on Respiration,
Coughing, and Heart Rates of Rainbow Trout
(Salmo gairdneri Richardson). Can.J.Zool.
54(2):214-219.

7846

UEndp, Dur / UEndp, Dur,
Con

Lydy, M.J., K.A. Bruner, D.M. Fry, and S.W.
Fisher. 1990. Effects of Sediment and the
Route of Exposure on the Toxicity and
Accumulation of Neutral Lipophilic and
Moderately Water-Soluble Metabolizable
Compounds in the Midge, Chironomus riparius.
In: W.G.Landis and W.H.Van der Schalie
(Eds.), Aquatic Toxicology and Risk
Assessment, 13th Volume, ASTM STP 1096,
Philadelphia, PA :140-164.

18935

Dur

Macek, K.J., C.R. Rodgers, D.L. Stalling, and
S. Korn. 1970. The Uptake, Distribution and
Elimination of Dietary 14C-DDT and 14C-
Dieldrin in Rainbow Trout. Trans.Am.Fish.Soc.
99(4):689-695.

9623

UEndp, RouExp

339

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

MacPhee, C., and R. Ruelle. 1969. Lethal
Effects of 1888 Chemicals upon Four Species
of Fish From Western North America. Univ.of
Idaho Forest, Wildl.Range Exp.Station
Bull.No.3, Moscow, ID :112 p..

15148

UEndp, Dur, Con

Malone, C.R., and B.G. Blaylock. 1970. Toxicity
of Insecticide Formulations to Carp Embryos
Reared In Vitro. J.Wildl.Manage. 34(2):460-
463.

9629

UEndp

Matsuo, K., and T. Tamura. 1970. Laboratory
Experiments on the Effect of Insecticides
Against Blackfly Larvae (Diptera: Simuliidae)
and Fishes. Sci.Pest Control/Botyu-Kagaku
35(4): 125-130.

9634

UEndp, Dur, Pur

Mayhew, J.. 1955. Toxicity of Seven Different
Insecticides to Rainbow Trout Salmo gairdnerii
(Richardson). Proc.lowa J.Acad.Sci. 62:599-
606.

6461

UEndp, Dur, Pur

Mehrle, P.M., and M.E. Declue. 1972.
Phenylalanine Metabolism Altered by Dietary
Dieldrin. Nature (London) 238(5365):462-463.

9140

UEndp, RouExp, Con

Mehrle, P.M., F.L. Mayer, and W.W. Johnson.
1977. Diet Quality in Fish Toxicology: Effects
on Acute and Chronic Toxicity. In: F.L.Mayer
and J.L.Hamelink (Eds.), Aquatic Toxicology
and Hazard Evaluation, 1st Symposium, ASTM
STP 634, Philadelphia, PA :269-280 (Publ in
Part As 6797).

7574

UEndp, RouExp

Metcalf, R.L., I.P. Kapoor, P.Y. Lu, C.K. Schuth,
and P. Sherman. 1973. Model Ecosystem
Studies of the Environmental Fate of Six
Organochlorine Pesticides. Environ.Health
Perspect. 4:35-44.

740

UEndp, Con

Mitsuhashi, J., T.D.C. Grace, and D.F.
Waterhouse. 1970. Effects of Insecticides on
Cultures of Insect Cells. Entomol.Exp.Appl.
13:327-341.

2797

UEndp, Dur, Con

Morgan, W.S.G.. 1975. Monitoring Pesticides
by Means of Changes in Electric Potential
Caused by Fish Opercular Rhythms.
Prog.Water Technol.7(2):33-40 (Author
Communication Used).

8151

UEndp, Dur, Con

Mulla, M.S., R.L. Metcalf, and G. Kats. 1964.
Evaluation of New Mosquito Larvicides, with
Notes on Resistant Strains. Mosq.News
24(3):312-319.

4431

Dur

340

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Naqvi, S.M., and D.E. Ferguson. 1968.
Pesticide Tolerances of Selected Freshwater
Invertebrates. J.Miss.Acad.Sci. 14:121-127.

2093

UEndp, Dur, Con

Naqvi, S.M.Z.. 1973. Toxicity of Twenty-Three
Insecticides to a Tubificid Worm Branchiura
sowerbyi From the Mississippi Delta.
J.Econ.Entomol. 66(1):70-74.

2798

UEndp, Dur, Con

Nebeker, A.V., and A.R. Gaufin. 1964.
Bioassays to Determine Pesticide Toxicity to
the Amphipod Crustacean, Gammarus
lacustris. Proc.Utah Acad.Sci. 4(1):64-67.

2094

Con

Novak, A., B.S. Walters, and D.R.M. Passino.
1980. Toxicity of Contaminants to Invertebrate
Food Organisms. Prog.Fish.Res.1980, Great
Lakes Fish.Lab., U.S.Fish Wildl.Serv., Ann
Arbor, M 1:2.

2210

Con

Office of Pesticide Programs. 2000. Pesticide
Ecotoxicity Database (Formerly: Environmental
Effects Database (EEDB)). Environmental Fate
and Effects Division, U.S.EPA, Washington,
D.C..

344

Dur / UEndp, Dur Con

Perschbacher, P.W., and J. Sarkar. 1989.
Toxicity of Selected Pesticides to the
Snakehead, Channa punctata. Asian Fish.Sci.
2(2):249-254.

158

UEndp, Dur, Con

Phipps, G.L., V.R. Mattson, and G.T. Ankley.
1995. Relative Sensitivity of Three Freshwater
Benthic Macroinvertebrates to Ten
Contaminants. Arch.Environ.Contam.Toxicol.
28(3):281-286.

14907

Dur

Rao, T.S., M.S. Rao, and S.B.S. Prasad. 1975.
Median Tolerance Limits of Some Chemicals to
the FreshWater Fish "Cyprinus carpio". Indian
J. Environ. Health 17(2):140-146.

2077

Pur

Reinert, R.E., L.J. Stone, and H.L. Bergman.
1974. Dieldrin and DDT: Accumulation From
Water and Food by Lake Trout (Salvelinus
namaycush) in the Laboratory. Proc. 17th
Conf.Great Lakes Res ,:52-58.

2049

UEndp

Rettich, F.. 1977. The Susceptibility of Mosquito
Larvae to Eighteen Insecticides in
Czechoslovakia. Mosq.News 37(2):252-257.

2914

Dur, Con

Rongsriyam, Y., S. Prownebon, and S.
Hirakoso. 1968. Effects of Insecticides on the
Feeding Activity of the Guppy, a Mosquito-
Eating Fish, in Thailand. Bull.W.H.O. 39:977-
980.

3663

Dur, Con

341

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Sanders, H.O., and O.B. Cope. 1968. The
Relative Toxicities of Several Pesticides to
Naiads of Three Species of Stoneflies.
Limnol.Oceanogr. 13(1): 112-117 (Author
Communication Used) (Publ in Part As 6797).

889

Dur, Con

Santerre, C.R., V.S. Blazer, N. Khanna, R.E.
Reinert, and F.T. Barrows. 1997. Absorption of
Dietary Dieldrin by Striped Bass.
Bull.Environ.Contam.Toxicol. 58(2):334-340.

17906

UEndp, RouExp

Schmulbach, J.C.. 1969. Effects of Chlorinated
Hydrocarbon Insecticides on the Freshwater
Seed Shrimp. South Dakota University,
Vermillion, SD:60 p.(U.S.NTIS PB-188796).

6049

UEndp, Dur, Con

Schoettger, R.A.. 1970. Fish-Pesticide
Research Laboratory: Progress in Sport
Fishery Research. U.S.Dep.Interior, Bur.Sport
Fish.Wildl.Res., Publ. 106:2-40 (Publ in Part As
6797).

6615

NonRes; Form

Acute data for Korean shrimp
was used in Table 1 of the ALC
document, but no mention was
made of the acute data
provided for Oncorhynchus
tshawyscha

Shannon, L.R.. 1977. Accumulation and
Elimination of Dieldrin in Muscle Tissue of
Channel Catfish. Bull.Environ.Contam.Toxicol.
17(6):637-644.

16450

UEndp, Dur, RouExp

Shannon, L.R.. 1977. Equilibrium Between
Uptake and Elimination of Dieldrin by Channel
Catfish, Ictalurus punctatus.

Bull. Environ.Contam .Toxicol. 17(3):278-284.

16451

UEndp, Dur

Shim, J.C., and L.S. Self. 1973. Toxicity of
Agricultural Chemicals to Larvivorous Fish in
Korean Rice Fields. Trop.Med. 15(3):123-130.

8977

Dur, Con

Silbergeld, E.K. 1973. Dieldrin. Effects of
Chronic Sublethal Exposure on Adaptation to
Thermal Stress in Freshwater Fish.

Envi ron. Sci .Technol. 7(9):846-849.

8983

UEndp, Dur, Con

Statham, C.N., and J.J. Lech. 1975.
Potentiation of the Acute Toxicity of Several
Pesticides and Herbicides in Trout by Carbaryl.
Toxicol.Appl.Pharmacol. 34(1):83-87.

5550

UEndp, Dur, Con

Tsuji, S., Y. Tonogai, Y. Ito, and S. Kanoh.
1986. The Influence of Rearing Temperatures
on the Toxicity of Various Environmental
Pollutants for Killifish (Oryzias latipes).
J.Hyg.Chem./Eisei Kagaku 32(1):46-53 (JPN)
(ENG ABS).

12497

Dur, Con

342

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Van Jaarsveld, J.H.. 1970. Laboratory Study on
the Toxicity of Dieldrin to Fresh Water
Invertebrates. Phytophylactica 2:269-274.

9712

Dur, Con, Pur

Vance, B.D., and W. Drummond. 1969.
Biological Concentration of Pesticides by Algae.
J.Am.Water Words Assoc. 61:360-362.

4967

Plant, UEndp

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS

Wade, R.A. 1969. Ecology of Juvenile Tarpon
and Effects of Dieldrin on Two Associated
Species. Tech.Pap.No.41, Sport Fish Wildl.,
Fish Wildl.Serv., U.S.D.I., Washington, D.C
,:85.

16215

Dur

Warren, C.E. 1972. Effects of Dieldrin on the
Longevity, Reproduction and Growth of Aquatic
Animals in Laboratory Ecosystems. Oregon
State Univ.Environ.Health Sci.Cen .: 181 -185.

9270

UEndp, RouExp, Con

Whitten, B.K., and C.J. Goodnight. 1966.
Toxicity of Some Common Insecticides to
Tubificids. J.Water Pollut.Control Fed.
38(2):227-235.

8046

Con, Pur

Woltering, D.M. 1983. Environmental Influence
on the Response of Aquatic Laboratory
Ecosystems to a Toxicant. In: W.E.Bishop,
R.D.Cardwell, and B.B.Heidolph (Eds.), Aquatic
Toxicology and Hazard Assessment, 6th
Symposium, ASTM STP 802, Philadelphia, PA
:153-170.

10186

UEndp

343

-------
Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

FAV in the most recent national ambient water quality criteria dataset used to derive the CMC , EPA is providing a
transparent rationale as to why they were not utilized (see below).

General QA/QC failure because non-resident species in Oregon

The test with the following species was used in the EPA BE of OR WQS for dieldrin in freshwater, but was not considered in the
CWA review and approval/disapproval action of the standards because this species does not have a breeding wild population in
Oregon's waters:

Claassenia

sabulosa

Stonefly

Mayer and Ellersieck 1986

Other Acute tests failins QA/QC by species

Oncorhynchus mykiss — Rainbow Trout

The following tests were included in EPA's BE of the OR WQS for dieldrin in freshwater, but were not used for determining the most
representative SMAV in this CWA review and approval/disapproval action of these standards because the tests were not based on the
preferred flow-through measured test conditions; however, other flow-through measured test concentrations were available for these
species which was utilized.

Mayer, F.L.J., and M.R. Ellersieck. 1986. Manual of Acute Toxicity: Interpretation and Data Base for 410 Chemicals and 66
Species of Freshwater Animals. Resour. Publ. No. 160, U.S. Dep. Interior, Fish Wildl. Serv., Washington, DC: 505 p. (USGS
Data File).

83 U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient Water. EPA-820-B-96-001.

344

-------
Three LC50 values from static tests ranging from 1.2 ug/L to 2.3 ug/L.

Van Leeuwen, C.J., P.S. Griffioen, W.H.A. Vergouw and J.L. Maas-Diepeveen. 1985. Differences in susceptibility of early life
stages of rainbow trout (Salmo gairdneri) to environmental pollutants. Aq. Toxicol. 7: 59-78.

One LC50 value from a static or renewal test of 3 |ig/L.

Katz, M. 1961. Acute toxicity of some organic insecticides to three species of salmonids and to the threespine stickleback.
Trans. Am. Fish. Soc. 90(3): 264-268.

One LC50 value from S,U test of 9.9 |ig/L.

Macek, K.J., C. Hutchinson and O.B. Cope. 1969. The effects of temperature on the susceptibility of bluegills and rainbow
trout to selected pesticides. Bull. Environ. Contam. Toxicol. 4: 175-183.

Three LC50 values from S,U tests ranging from 1.1 |ig/L to 2.4 |ig/L.

Pteronarcys califortticus — Stonefly

The following test was included in EPA's BE of the OR WQS for dieldrin in freshwater, but was not used for determining the most
representative SMAV in this CWA review and approval of these standards because the value was deemed an outlier and unacceptable
to use for calculating the SMAV for the species as per 1995 GLI method:

Jensen, L.D. and A.R. Gaufin. 1964. Effects of ten organic insecticides on two species of stonefly naiads. Trans. Am. Fish. Soc.
93(1): 27-34.

P. californicus test was a S,U test using 100% dieldrin which resulted in an LC50 of 39 ug/L.

345

-------
Appendix G Endrin (freshwater)
Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Argyle, R.L., G.C. Williams, and H.K. Dupree. 1973. Endrin Uptake and
Release by Fingerling Channel Catfish (Ictalurus punctatus).
J.Fish.Res.Board Can. 30(11):1743-1744.

8291

Insuff. Control, Endpoint (ACC)

Batterton, et al. 1971.

Non-NA, Details, Endpoint
(ICxx)

Bennett, R.O., and R.E. Wolke. 1987. The Effect of Sublethal Endrin
Exposure on Rainbow Trout, Salmo gairdneri Richardson. II. The Effect of
Altering Serum Cortisol Concentrations on the. J.Fish Biol. 31(3):387-394.

235

Insuff. Control, Endpoint (PHY)

Bennett, R.O., and R.E. Wolke. 1987. The Effect of Sublethal Endrin
Exposure on Rainbow Trout, Salmo gairdneri Richardson. I. Evaluation of
Serum Cortisol Concentrations and Immune. J.Fish Biol. 31(3):375-385.

562

Insuff. Control, Endpoint (PHY)

Bennett, R.O., and R.E. Wolke. 1988. The Effect of Sublethal Endrin
Exposure on the Immune Response of Rainbow Trout, Salmo gairdneri.
Mar. Environ. Res.24(1-4):351 (ABS).

13092

Endpoint (ACC)

Bennett, W.N., and J.W. Day Jr.. 1970. Absorption of Endrin by the Bluegill
Sunfish, Lepomis macrochirus. Pestic.Monit.J. 3(4):201-203.

9495

Dur, Insuff. Control

Bonner, J.C., and J.D. Yarbrough. 1988. Vertebrate Cyclodiene Insecticide
Resistance: Role of gamma-Aminobutyric Acid and Diazepam Binding Sites.
Arch.Toxicol. 62(4):311-315.

5121

Dur, Insuff. Control

Boyd, C.E., and D.E. Ferguson. 1964. Susceptibility and Resistance of
Mosquito Fish to Several Insecticides. J.Econ.Entomol. 57(4):430-431.

10332

Dur

Boyd, J.E.. 1957. The Use of Daphnia magna in the Microbioassay of
Insecticides. Ph.D.Thesis, Penn.State University, University Park, PA :194.

14647

Dur

346

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Crosby, D.G., R.K. Tucker, and N. Aharonson. 1966. The Detection of Acute
Toxicity with Daphnia magna. Food Cosmet.Toxicol. 4:503-514.

7984

Dur, Insuff. Control

Dalela, R.C., S.R. Verma, and M.C. Bhatnagar. 1978. Biocides in Relation to
Water Pollution. Part I: Bioassay Studies on the Effects of a Few Biocides on
FreshWater Fish, Channa gachua. Acta Hydrochim.Hydrobiol. 6(1):15-25
(Author Communication Used).

5736

Non-NA, Dur, Purity

20 Emulsified Concentration

Denison, M.S., J.E. Chambers, and J.D. Yarbrough. 1985. Short-Term
Interactions between DDT and Endrin Accumulation and Elimination in
Mosquitofish (Gambusia affinis). Arch.Environ.Contam.Toxicol. 14(3):315-
320.

10811

Dur, Insuff. Control, Endpoint
(ACC)

Devillers, J., T. Meunier, and P. Chambon. 1985. Advantage of the Dosage-
Action-Time Relation in Ecotoxicology for the Test of the Various Chemical
Species of Toxics. Tech.Sci.Munic. 80:329-334 (FRE) (ENG ABS).

17456

Dur

El Refai, A., F.A. Fahmy, M.F.A. Abdel-Lateef, and A.K.E. Imam. 1976.
Toxicity of Three Insecticides to Two Species of Fish. Int. Pest Control
18(6): 4-8.

6090

Dur, Purity

19.5% Emulsified Concentration

Eller, L.L.. 1971. Histopathologic Lesions in Cutthroat Trout (Salmo clarki)
Exposed Chronically to the Insecticide Endrin. Am.J.Pathol. 64(2):321-336.

9317

Dur, Insuff. Control, Endpoint
(HIS)

Fabacher, D.L.. 1976. Toxicity of Endrin and an Endrin-Methyl Parathion
Formulation to Largemouth Bass Fingerlings. Bull.Environ.Contam.Toxicol.
16(3):376-378.

6207

Dur, Insuff. Control, Unknown
Endpoint

Fabacher, D.L., and H. Chambers. 1971. A Possible Mechanism of
Insecticide Resistance in Mosquitofish. Bull.Environ.Contam.Toxicol.
6(4):372-376.

15104

Dur, Insuff. Control, Endpoint
(PHY)

Ferguson, D.E., and C.R. Bingham. 1966. Endrin Resistance in the Yellow
Bullhead, Ictalurus natalis. Trans.Am.Fish.Soc. 95(3):325-326.

4388

Dur, Insuff. Control

Ferguson, D.E., and C.R. Bingham. 1966. The Effects of Combinations of
Insecticides on Susceptible and Resistant Mosquito Fish.
Bull.Environ.Contam.Toxicol. 1(3):97-103.

10340

Dur, Insuff. Control, Unknown
Endpoint

347

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Ferguson, D.E., D.D. Culley, and W.D. Cotton. 1965. Tolerances of Two
Populations of Fresh Water Shrimp to Five Chlorinated Hydrocarbon
Insecticides. J.Miss.Acad.Sci. 11:235-237.

8063

Dur

Ferguson, D.E., D.D. Culley, W.D. Cotton, and R.P. Dodds. 1964.
Resistance to Chlorinated Hydrocarbon Insecticides in Three Species of
Freshwater Fish. Bioscience 14(1):43-44.

10341

Dur

Ferguson, D.E., J.L. Ludke, and G.G. Murphy. 1966. Dynamics of Endrin
Uptake and Release by Resistant and Susceptible Strains of Mosquitofish.
Trans.Am.Fish.Soc. 95(4):335-344.

4389

Dur, Insuff. Control, Endpoint
(ACC, Lethal, Unknown)

Finley, M.T., D.E. Ferguson, and J.L. Ludke. 1970. Possible Selective
Mechanisms in the Development of Insecticide-Resistant Fish.
Pestic.Monit.J. 3(4):212-218.

9556

Species, Dur, Endpoint (Lethal,
No Effect), Dietary Exp

Frear, D.E.H., and J.E. Boyd. 1967. Use of Daphnia magna for the
Microbioassay of Pesticides. I. Development of Standardized Techniques for
Rearing Daphnia and Preparation of Dosage-M. J.Econ.Entomol.
60(5): 1228-1236.

2820

Dur, Insuff. Control

Georgacakis, E., and M.A.Q. Khan. 1971. Toxicity of the Photoisomers of
Cyclodiene Insecticides to Freshwater Animals. C.R.Hebd.Seances
Acad.Sci.Ser.D 233(5315):120-121.

9334

Dur, Insuff. Control

Ghazaly, K.S. 1991. Physiological Alterations in Claria lazera Induced by
Two Different Pollutants.'Water Air Soil Pollut. 60(1 /2):181 -187.

3997

Non-NA

Grant, B.F., and P.M. Mehrle. 1970. Pesticide Effects on Fish Endocrine
Function. In: Resour.Publ.No.88, Prog.Sport Fish.Res.1969, Div.Fish.Res.,
Bur.Sport Fish.Wildl., U.S.D.I., Washington, D.C. :13-15.

17208

Dur, Endpoint (Lethal)

Hansen, D.J., E. Matthews, S.L. Nail, and D.P. Dumas. 1972. Avoidance of
Pesticides by Untrained Mosquitofish, Gambusia affinis.
Bull.Environ.Contam.Toxicol. 8(1):46-51.

5147

Dur, Insuff. Control

Hashimoto, Y., and J. Fukami. 1969. Toxicity of Orally and Topically Applied
Pesticide Ingredients to Carp, Cyprinus carpio Linne. Sci.Pest Control
/Botyu-Kagaku 34(2):63-66.

9038

Dur, Insuff. Control, Endpoint
(LD50), Dietary Exp

348

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Henderson, C., Q.H. Pickering, and C.M. Tarzwell. 1960. The Toxicity of
Organic Phosphorus and Chlorinated Hydrocarbon Insecticides to Fish. In:
C.M.Tarzwell (Ed.), Biological Problems in WAter Pollution, Trans.2nd
Seminar, April 20-24, 1959, Tech.Rep.W60-3, U.S.Public Health Service,
R.A.Taft Sanitary Engineering Center, Cincinnati, OH :76-88.

936

Insuff. Control

Hermanutz, R.O., J.G. Eaton, and L.H. Mueller. 1985. Toxicity ofEndrinand
Malathion Mixtures to Flagfish (Jordanella floridae).

Arch. Environ.Contam.Toxicol. 14:307-314.

10687

96 h LC50 = 0.85 ug/L

This study appears to provide an appropriate
96 h LC50 for J. floridae, but the paper should
be secured to ensure acceptability. Species is
relatively insensitive to acute endrin exposure.

Javaid, M.Y., and A. Waiz. 1972. Acute Toxicity of Five Chlorinated
Hydrocarbon Insecticides to the Fish, Channa punctatuts.'
Pak.J.Sci.lnd.Res. 15(4-5):291-293.

8371

Non-NA

Joshi, H.C., D. Kapoor, R.S. Panwar, and R.A. Gupta. 1975. Toxicity of
Some Insecticides to Chironomid Larvae. Indian J.Environ.Health 17(3):238-
241.

7954

Species, Dur, Purity

20 Emulsified Concentration

Khangarot, B.S., A. Sehgal, and M.K. Bhasin. 1985. Man and Biosphere-
Studies on the Sikkim Himalayas. Part 6: Toxicity of Selected Pesticides to
Frog Tadpole Rana hexadactyla (Lesson). Acta Hydrochim.Hydrobiol.
13(3):391-394.

11521

Dur, Purity

20 Emulsified Concentration

Khudairi, S.Y.A.D., and E. Ruber. 1974. Survival and Reproduction of
Ostracods As Affected by Pesticides and Temperature. J.Econ.Entomol.
67(1):22-24.

8599

Dur, Insuff. Control

Kulkarni, K.M., and S.V. Kamath. 1980. The Metabolic Response of
Paratelphusa jacquemontii to Some Pollutants. Geobios (Jodhpur) 7(2):70-
73 (Author Communication Used).

5036

Dur, Endpoint (PHY)

LaBrecque, G.C., J.R. Noe, and J.B. Gahan. 1956. Effectiveness of
Insecticides on Granular Clay Carriers Against Mosquito Larvae.
Mosq.News 16:1-3.

2808

Dur, Purity, Unknown Endpoint

Lincer, J.L., J.M. Solon, and J.H. Nair lii. 1970. DDT and Endrin Fish Toxicity
Under Static Versus Dynamic Bioassay Conditions. Trans.Am.Fish.Soc.
99(1): 13-19.

9615

Dur, Insuff. Control

349

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Ludke, J.L., D.E. Ferguson, and W.D. Burke. 1968. Some Endrin
Relationships in Resistant and Susceptible Populations of Golden Shiners,
Notemigonus crysoleucas. Trans.Am.Fish.Soc. 97:260-263.

5458

Dur, Endpoint (ACC)

Macek, K.J., C. Hutchinson, and O.B. Cope. 1969. The Effects of
Temperature on the Susceptibility of Bluegills and Rainbow Trout to
Selected Pesticides. Bull.Environ.Contam.Toxicol. 4(3):174-183 (Publ in Part
As 6797).

2085

Dur, Insuff. Control

MacPhee, C., and R. Ruelle. 1969. Lethal Effects of 1888 Chemicals upon
Four Species of Fish From Western North America. Univ.of Idaho Forest,
Wildl.Range Exp.Station Bull.No.3, Moscow, ID : 112 p.

15148

Dur, Insuff. Control, Unknown
Endpoint

Malone, C.R., and B.G. Blaylock. 1970. Toxicity of Insecticide Formulations
to Carp Embryos Reared In Vitro. J.Wildl.Manage. 34(2):460-463.

9629

Dur, Endpoint (Lethal)

Mane, U.H., M.S. Kachole, and S.S. Pawar. 1979. Effect of Pesticides and
Narcotants on Bivalve Molluscs. Malacologia 18:347-360.

8286

Dur, Endpoint (HIS)

McCorkle, F.M., J.E. Chambers, and J.D. Yarbrough. 1977. Acute Toxicities
of Selected Herbicides to Fingerling Channel Catfish, Ictalurus punctatus.
Bull. Environ.Contam .Toxicol. 18(3):267-270.

858

Insuff. Control

McKim, J.M., and H.M. Goeden. 1982. A Direct Measure of the Uptake
Efficiency of a Xenobiotic Chemical Across the Gills of Brook Trout
(Salvelinus fontinalis) Under Normoxic and. Comp.Biochem.Physiol.C
72(1):65-74.

15606

Dur, Insuff. Control, Endpoint
(PHY)

Metcalf, R.L., I.P. Kapoor, P.Y. Lu, C.K. Schuth, and P. Sherman. 1973.
Model Ecosystem Studies of the Environmental Fate of Six Organochlorine
Pesticides. Environ.Health Perspect. 4:35-44.

740

Dur, Insuff. Control, Endpoint
(ACC)

Naqvi, S.M., and D.E. Ferguson. 1970. Levels of Insecticide Resistance in
Fresh-Water Shrimp, Palaemonetes kadiakensis. Trans.Am.Fish.Soc.
99(4):696-699.

2665

Dur, Insuff. Control

Naqvi, S.M.Z.. 1973. Toxicity of Twenty-Three Insecticides to a Tubificid
Worm Branchiura sowerbyi From the Mississippi Delta. J.Econ.Entomol.
66(1):70-74.

2798

Dur, Insuff. Control, Endpoint
(Lethal, Unknown)

350

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Panwar, R.S., D. Kapoor, H.C. Joshi, and R.A. Gupta. 1976. Toxicity of
Some Insecticides to the Weed Fish, Trichogaster fasciatus (Bloch and
Schneider). J.Inl.Fish.Soc.India 8:129-130.

7881

Dur, Purity

20 Emulsified Concentration

Panwar, R.S., R.A. Gupta, H.C. Joshi, and D. Kapoor. 1982. Toxicity of
Some Chlorinated Hydrocarbon and Organophosphorus Insecticides to
Gastropod, Viviparus bengalensis Swainson. J.Environ.Biol. 3(1):31-36.

14311

Dur, Purity

20 Emulsified Concentration

Rao, T.S., S. Dutt, and K. Mangaiah. 1967. TLM Values of Some Modern
Pesticides to the Freshwater Fish - Puntius puckelli. Environ.Health
(Nagpur) 9:103-109.

6722

Dur, Purity

20 Emulsified Concentration

Rosato, P., and D.E. Ferguson. 1968. The Toxicity of Endrin-Resistant
Mosquito Fish to Eleven Species of Vertebrates. Bioscience 18(8):783-784.

18492

Dur, Endpoint (ACC, Lethal,
Unknown), Dietary Exp

Roy, D., S.A.K. Nasar, and O.P. Dandotia. 1978. Effect of Tafdrin on Colisa
fasciatus (Bloch) (Perciformes: Osphronemidae). Bangladesh J.Zool. :147-
148.

271

Dur

Sanders, H.O.. 1969. Toxicity of Pesticides to the Crustacean Gammarus
lacustris. Tech.Pap.No.25, Bur.Sports Fish.Wildl., Fish Wildl.Serv., U.S.D.I.,
Washington, D.C. :18 p. (Author Communication Used)(Used with
Reference 732) (Publ in Part As 6797).

885

Dur, Insuff. Control

Sastry, K.V., and S.K. Sharma. 1978. Endrin Toxicity on Liver of Channa
punctatus (Bloch). Indian J.Exp.Biol. 16(3):372-373.

8438

Non-NA, Insuff. Control

Sharma, S.K., L.D. Chaturvedi, and K.V. Sastry. 1979. Acute Endrin Toxicity
on Oxidases of Ophiocephalus punctatus (Bloch).
Bull.Environ.Contam.Toxicol. 23(1/2):153-157.

469

Non-NA, Insuff. Control

Singh, H., and T.P. Singh. 1980. Short-Term Effect of 2 Pesticides on the
Survival, Ovarian 32P Uptake and Gonadotrophic Potency in a Freshwater
Catfish, Heteropneustes fossilis (Bloch).' J.Endocrinol. 85:193-199.

470

Non-NA

Singh, H., and T.P. Singh. 1980. Effect of Two Pesticides on Total Lipid and
Cholesterol Contents of Ovary, Liver and Blood Serum During Different
Phases of the Annual Reproductive C. Environ.Pollut.Ser.A Ecol.Biol.
23(1):9-18.

6646

Non-NA, Purity, Endpoint (PHY)

20 Emulsified Concentration

351

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Singh, H., and T.P. Singh. 1980. Short-Term Effect of Two Pesticides on
Lipid and Cholesterol Content of Liver, Ovary and Blood Serum During the
Pre-Spawning Phase in the Freshwater. Environ.Pollut.Ser.A Ecol.Biol.
22(2):85-90.

6647

Non-NA, Endpoint (PHY)

Sudershan, P., and M.A.Q. Khan. 1980. Metabolic Fate of (14C)Endrin in
Bluegill Fish. Pestic.Biochem.Physiol. 14(1 ):5-12.

9904

Dur, Insuff. Control, Endpoint
(ACC)

Toor, H.S., K. Mehta, and S. Chhina. 1973. Toxicity of Insecticides
(Commercial Formulations) to the Exotic Fish, Common Carp Cyprinus
carpio communis Linnaeus. J.Res.Punjab.Agric.Univ. 10(3):341-345.

8737

Dur, Purity, Unsatis. Control,
Unknown Endpoint

20 Emulsified Concentration

Wells, M.R., and J.D. Yarbrough. 1972. Vertebrate Insecticide Resistance:
In Vivo and In Vitro Endrin Binding to Cellular Fractions From Brain and
Liver Tissues of Gambusia. J.Agric.Food Chem. 20(1): 14-16.

9220

Dur, Insuff. Control, Endpoint
(ACC)

Yarbrough, J.D., R.T. Roush, J.C. Bonner, and D.A. Wise. 1986. Monogenic
Inheritance of Cyclodiene Insecticide Resistance in Mosquitofish, Gambusia
affinis. Experientia (Basel) 42(7):851-853.

12987

Dur, Insuff. Control

Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

FAV in the most recent national ambient water quality criteria dataset used to derive the CMC , EPA is providing a
transparent rationale as to why they were not utilized (see below).

84 U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient Water. EPA-820-B-96-001.

352

-------
General QA/QC failure because non-resident species in Oreson

All data considered in this CWA review and approval/disapproval action of OR WQS for endrin below the chronic criterion or related
to the four most sensitive genera were from species that are known or expected to have a breeding wild population in Oregon's waters.

Other Acute tests failing QA/QC by species

Lepomis macrochirus - bluegill

Katz, M. and G.G. Chadwick. 1961. Toxicity of endrin to some Pacific Northwest fishes. Trans. Am. Fish. Soc. 90: 394-397.

This study was deemed unacceptable by the 1995 GLI

The following tests were not used for determining the most representative SMAV in this CWA review and approval/disapproval
action of these standards because the tests were not based on the preferred flow-through measured test conditions; however, other
flow-through measured test concentrations were available for these species.

Sanders, H.0.1972. Toxicity of some Insecticides to Four Species of Malacostracan Crustaceans. U.S. Dep. Inter. Bur. Sport
Fish, and Wildl. Tech. Paper 66.

One LC50 value from S,U test of 0.61 ug/L

Henderson, C., Q.H. Pickering and C.M. Tarzwell. 1959. Relative toxicity of ten chlorinated hydrocarbon insecticides to four
species of fish. Trans. Am. Fish. Sot. 88: 23-32.

One LC50 value from S,U test of 0.66 ug/L

Macek, K.J., C. Hutchinson and O.B. Cope. 1969. Effects of temperature on the susceptibility of bluegills and rainbow trout to
selected pesticides. Bull. Environ. Contam. Toxicol. 4: 174-183.

Three LC50 values from S,U tests ranging from 0.37 to 0.61 ug/L

Pteronarcys californica — stonefly

Jensen, L.D. and A.R. Gaufin. 1966. Acute and long-term effects of organic insecticides on two species of stonefly naiads. J.
Water Pollut. Control Fed. 38: 1273-1286.

This study was deemed unacceptable by the 1995 GLI

353

-------
Other Chronic tests failins QA/QC by species

Pteronarcys californica - stonefly

Anderson, R.L., and D.L. De Foe. 1980. Toxicity and Bioaccumulation of Endrin and Methoxychlor in Aquatic Invertebrates
and Fish. Environ.Pollut.Ser.A Ecol.Biol. 22(2): 111-121 (Author Communication Used for ECOTOX entries)

Anderson and DeFoe (1980) reported results of 4 and 28-day exposures of a caddisfly (Brachycentrus americanus), a stonefly
(Pteronarcys dorsatd), and the bullhead (Ictalurus melas, which is now the black bullhead, Ameiurus melas) to endrin. For the black
bullhead the 96-hr LC50 is 0.45 |ig/L and the 28-day LC50 is 0.10 |ig/L. A 96-hr LC50 is not reported for the stonefly, but the 28-day
LC50 is 0.07 |ig/L. For the caddisfly the 96-hr LC50 is 0.34 |ig/L and the 28-day LC50 is reported to be >0.034 |ig/L. The 96-h
LC50s for these tests were not acceptable for SMAV calculation because they were fed tests. The 28-d LC50s were not acceptable to
calculate the SMCV because: 1) the point estimate (50% mortality), although long term, is not considered sublethal, and 2) the test
with bullhead was not an acceptable ELS test and the tests with the caddisfly and stonefly were not the full life-cycle tests required for
invertebtrates.

Oncorhynchus clarki — cutthroat trout

Post, G., and T.R. Schroeder. 1971. Toxicity of Four Insecticides to Four Salmonid Species. Bull.Environ.Contam.Toxicol.
6(2): 144-155.

This study did not provide sufficient information concerning the concentration of dissolved oxygen (DO) in the test chambers during
the tests. The study states that the concentration of DO in the incoming water supply ranged from 5.9 to 6.0 mg/L and that
temperature ranged from 13.6 to 14.6 °C. Thus the DO was initially at 57 to 59% saturation in the incoming water supply. The test
temperature was 12.9 °C, which would mean that the DO could be no higher than 56 to 57% saturation. Section 11.2.1 of the
American Society for Testing and Materials (ASTM) Standard E729 says that the concentration of DO must be at least 60% during the
first 48 hr of a static test and must be at least 40% after 48 hr in a static test; this section also says that DO must be at least 60% at all
times during renewal and flow-through tests. Forty percent was allowed after 48 hr in static tests for practical reasons; sixty percent is
the preferred minimum. The maximum DO saturation in the test solutions of the Post and Schroeder study was 57 to 59% saturation,
based on the concentration of DO in the incoming water, which most likely dropped immediately to no higher than 56 to 57%
saturation based on the temperature of the test. In addition, the test solutions also contained fish and acetone, which could use up
some DO, so the actual DO saturation most likely continued to fall during the duration of the test. Regarding the tests on malathion,
page 147 of Post and Schroeder states "Therefore, the ten experimental fish could be held in the same jar without causing serioous
depletion of dissolved oxygen." This acknowledges depletion of DO during these tests, which is normal in toxicity tests, however

354

-------
Post and Schroeder gave no indication of what is meant by "serious depletion". Thus there is very strong evidence that the
concentration of DO during the toxicity tests was below 60% and might have been substantially below 60% due to the biological
oxygen demand of acetone and due to the uptake of oxygen by the test organisms.

In addition, Section 9.2.3 of ASTM Standard E729 says that any organic solvent used should be reagent-grade or better and its
concentration in the test solution must not exceed 0.5 mL/L. Post and Schroeder says that acetone was used, but does not give the
purity of the acetone or identify how much acetone was used. Also, Section 9.1 of ASTM Standard E729 states that the test material
should be reagent-grade or better. Post and Schroeder states that the endrin used in these tests was technical grade and consisted of
95% active ingredient and 5% inert ingredient. The study did not identify the remaining 5% inert ingredients.

355

-------
Appendix H Lead (freshwater)
Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Abbasi, S.A., and R. Soni. 1986. An Examination of Environmentally Safe Levels of Zinc (II),
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Abdelhamid, A.M., and S.A. El Ayouty. 1991. Effect on Catfish (Clarias lazera) Composition
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Adams, E.S.. 1975. Effects of Lead and Hydrocarbons From Snowmobile Exhaust on Brook
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Akcin, G., 0. Saltabas, and H. Afsar. 1994. Removal of Lead by Water Hyacinth (Eichhornia
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Al Akel, A.S. 1994. Changes in Behaviour, Tissue Glycogen and Blood Chemistry of
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Alam, M.K., and O.E. Maughan. 1992. The Effect of Malathion, Diazinon, and Various
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Alam, M.K., and O.E. Maughan. 1995. Acute Toxicity of Heavy Metals to Common Carp
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Allen, P. 1993. Effects of Acute Exposure to Cadmium (II) Chloride and Lead (II) Chloride on
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Allen, P. 1993. Changes in Tissue GSH Concentrations as Indicators of Acute Cadmium or
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Allen, P. 1994. Accumulation Profiles of Lead and the Influence of Cadmium and Mercury in
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Allen, P.. 1995. Accumulation Profiles of Lead and Cadmium in the Edible Tissues of
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16322

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Allen, P.. 1995. Changes in Tissue Glutathione Levels in the Cichlid Oreochromis aureus
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Allen, P.. 1995. Soft-Tissue Accumulation of Lead in the Blue Tilapia, Oreochromis aureus
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Anderson, B.G. 1948. The Apparent Thresholds of Toxicity to Daphnia magna for Chlorides
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Anderson, B.G. 1948.

Det

No Information - Might be same
as above

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Anderson, R.L., C.T. Walbridge, and J.T. Fiandt. 1980. Survival and Growth of Tanytarsus
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Comment

Anderson, R.V.. 1978. The Effects of Lead on Oxygen Uptake in the Crayfish, Orconectes
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Applegate, V.C., J.H. Howell, A.E. Hall Jr., and M.A. Smith. 1957. Toxicity of 4,346
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Arambasic, M.B., S. Bjelic, and G. Subakov. 1995. Acute Toxicity of Heavy Metals (Copper,
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13712

Arias, G.S., L. Martinez-Tabche, and I. Galar. 1991. Effects of Paraquat and Lead on Fish
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Ariyoshi, T., S. Shiiba, H. Hasegawa, and K. Arizono. 1990. Profile of Metal-Binding Proteins
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Arshaduddin, M., R. Yasmeen, M. Masood Hussain, and M.A. Khan. 1989. Effect of Two
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Audesirk, G., and T. Audesirk. 1984. Chronic Lead Exposure Reduces Junctional Resistance
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Ay, O., M. Kalay, L. Tamer, and M. Canli. 1999. Copper and Lead Accumulation in Tissues
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Back, H.. 1983. Interactions, Uptake and Distribution of Barium, Cadmium, Lead and Zinc in
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20568

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Bailey, H.C., and D.H.W. Liu. 1980. Lumbriculus variegatus, a Benthic Oligochaete, As a
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:205-215.

6502

96 h LC50 approx. 6590 ug/L
dissolved lead normalized to
100 mg/L as CaC03 hardness.
Test was static, unmeasured.

This study appears to provide
an appropriate 96 h LC50 for L.
variegatus, but the paper
should be secured to ensure
acceptability. Species is
relatively insensitive to acute
lead exposure. Note:

Additional LC50 does not affect
SMAV/2 because other flow-
through measured data
available for species.

Bascombe, A.D., J.B. Ellis, D.M. Revitt, and R.B.E. Shutes. 1990. The Development of
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Belabed, W., N. Kestali, S. Semsari, and A. Gaid. 1994. Toxicity Study of Some Heavy
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Bell, C.E., L.A. Baldwin, P.T. Kostecki, and E.J. Calabrese. 1993. Comparative Response of
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Bender, J.A., E.R. Archibold, V. Ibeanusi, and J.P. Gould. 1989. Lead Removal from
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Bengeri, K.V., and H.S. Patil. 1984. Acute Toxicity of Lead Nitrate and Lead Acetate to a
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11579

Bengeri, K.V., and H.S. Patil. 1986. Lead Induced Histological Changes in the Liver of
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Bengeri, K.V., and H.S. Patil. 1987. Histopathological Changes in the Gill of Puntius arulius
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Berglind, R.. 1986. Combined and Separate Effects of Cadmium, Lead and Zinc on Ala-D
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Berglind, R., G. Dave, and M.L. Sjobeck. 1985. The Effects of Lead on Delta-Aminolevulinic
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Beritic, T., J. Zibar-Sikic, D. Prpic-Majic, and M. Tudor. 1980. Some Morphological and
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Biegert, E.K., and V. Valkovic. 1980. Acute Toxicity and Accumulation of Heavy Metals in
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Biesinger, K.E., and G.M. Christensen. 1972. Effects of Various Metals on Survival, Growth,
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Birge, W.J.. 1978. Aquatic Toxicology of Trace Elements of Coal and Fly Ash. In: J.H.Thorp
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Birge, W.J., J.A. Black, A.G. Westerman, and J.E. Hudson. 1980. Aquatic Toxicity Tests on
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Birge, W.J., J.A. Black, and A.G. Westerman. 1979. Evaluation of Aquatic Pollutants Using
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Birge, W.J., J.E. Hudson, J.A. Black, and A.G. Westerman. 1978. Embryo-Larval Bioassays
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Bleeker, E.A.J., M.H.S. Kraak, and C. Davids. 1992. Ecotoxicity of Lead to the Zebra Mussel
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Bogaerts, P., J. Senaud, and J. Bohatier. 1998. Bioassay Technique Using Nonspecific
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Borgmann, U., R. Cove, and C. Loveridge. 1980. Effects of Metals on the Biomass
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Boutet, C., and C. Chaisemartin. 1973. Specific Toxic Properties of Metallic Salts in
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Comment

Bringmann, G., and R. Kuhn. 1959. Water Toxicological Studies with Protozoa as Test
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Bringmann, G., and R. Kuhn. 1977. The Effects of Water Pollutants on Daphnia magna.
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Bringmann, G., and R. Kuhn. 1978. Investigation of Biological Harmful Effects of Chemical
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Bringmann, G., and R. Kuhn. 1978. Limiting Values for the Noxious Effects of Water
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Bringmann, G., and R. Kuhn. 1979. Comparison of Toxic Limiting Concentrations of Water
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Bringmann, G., and R. Kuhn. 1980. Determination of the Harmful Biological Effect of Water
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Bringmann, G., and R. Kuhn. 1981. Comparison of the Effect of Toxic Substances on the
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720

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Brown, B.E.. 1976. Observations on the Tolerance of the Isopod Asellus meridianus Rac. to
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EcoRef #

Rejection Code(s)

Comment

Brown, B.T., and B.M. Rattigan. 1979. Toxicity of Soluble Copper and Other Metal Ions to
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Brown, P.L., R.A. Jeffree, and S.J. Markich. 1996. Kinetics of 45Ca, 60Co, 210Pb, 54Mn and
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Buikema, A.L.J., J. Cairns Jr., and G.W. Sullivan. 1974. Evaluation of Philodina acuticornis
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Res. Assoc. 10(4):648-661.

2019

96 h LC50 approx. 188,500
ug/L dissolved lead normalized
to 100 mg/L as CaC03
hardness

This study appears to provide
an appropriate 96 h LC50 for P.
acuticornis, but the paper
should be secured to ensure
acceptability. Species is
relatively insensitive to acute
endrin exposure.

Buikema, A.L.Jr, J. Jr. Cairns, and G.W. Sullivan. 1974. Rotifers as Monitors of Heavy Metal
Pollution in Water. Bull.71, Center for Environmental Studies, Project #A-047-VA, Virginia
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Burden, V.M., M.B. Sandheinrich, and C.A. Caldwell. 1998. Effects of Lead on the Growth
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Busch, D., T. Lucker, M. Schirmer, and W. Wosniok. 1992. The Application of the Bivalve
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Calderon Llanten, C.E., and H. Greppin. 1993. Toxicity Tests of Zn, Cu, and Pb with
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Camusso, M., R. Balestrini, F. Muriano, and M. Mariani. 1994. Use of Freshwater Mussel
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Comment

Capelo, S., M.F. Vilhena, M.L.S. Simoes Goncalves, and M.A. Sampayo. 1993. Effect of
Lead on the Uptake of Nutrients by Unicellular Algae. Water Res. 27(10): 1563-1568.

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Cardwell, R.D., D.G. Foreman, T.R. Payne, and D.J. Wilbur. 1976. Acute Toxicity of
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Carter, J.W., and I.L. Cameron. 1973. Toxicity Bioassay of Heavy Metals in Water using
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15419

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Chandravathy, V.M., and S.L.N. Reddy. 1995. In Vivo Alterations in the Activities of Ion-
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Chaurasia, S.S., P. Gupta, A. Kar, and P.K. Maiti. 1996. Lead Induced Thyroid Dysfuntion
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Chen, Q., K. Zhang, and G. Xu. 1988. A Comprehensive Investigation of the Toxic Effects of
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Davies, P.H., and W.H. Everhart. 1973. Effects of Chemical Variations in Aquatic
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Comment

Fawade, M.M., P.R. Machale, U.H. Mane, and R. Nagabhushanam. 1983. DDT Toxicity and
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Fernandez-Leborans, G., and M.T. Antonio-Garcia. 1988. Effects of Lead and Cadmium in a
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Franchini, A., E. Barbanti, and A.M.B. Fantin. 1991. Effects of Lead on Hepatocyte
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Freedman, M.L., P.M. Cunningham, J.E. Schindler, and M.J. Zimmerman. 1980. Effect of
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Gadkari, A.S., and V.B. Marathe. 1983. Toxicity of Cadmium and Lead to a Fish and a Snail
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14666

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Three 96 hr LC50s available for
the guppy, Poecilia reticulata,
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15354

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Comment

Gaur, J.P., N. Noraho, and Y.S. Chauhan. 1994. Relationship Between Heavy Metal
Accumulation and Toxicity in Spirodela polyrhiza (L.) Schleid. and Azolla pinnata R. Br.
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16793

Gavrilenko, Y.Y., and Y.Y. Zolotukhina. 1989. Accumulation and Interaction of Copper, Zinc,
Manganese, Cadmium, Nickel and Lead Ions Absorbed by Aquatic Macrophytes.
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Gerhardt, A.. 1994. Short Term Toxicity of Iron (Fe) and Lead (Pb) to the Mayfly
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German-Faz, E.Sanchez-Hidalgo, B. Ramirez Mora, and L. Martinez-Tabche. 1993. Toxic
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Discovery to Commercialization, European Aquaculture Soc., April 1993, Oostende,
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Ghazaly, K.S.. 1991. Influences of Thiamin on Lead Intoxication, Lead Deposition in Tissues
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Rejection Code(s)

Comment

Gill, T.S., H. Tewari, and J. Pande. 1991. Effects of Water-Borne Copper and Lead on the
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2488

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Gill, T.S., H. Tewari, J. Pande, and S. Lai. 1991. In Vivo Tissue Enzyme Activities in the
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5114

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Glaven, J., M. Akkerman, and B.A. Fowler. 1993. 2-D Gel Analysis of Protein Synthesis in
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16165

UEndp, AF

Goettl et al. 1972.

Det

No Information - Might be same
as below

Goettl, J.P.J., and P.H. Davies. 1975. Water Pollution Studies. Job Progress Rep., Federal
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Goettl, J.P.J., and P.H. Davies. 1976. Water Pollution Studies. Job Progress Report, Federal
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10208

UEndp, AF

Goettl, J.P.J., J.R. Sinley, and P.H. Davies. 1972. Laboratory Studies: Water Pollution
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Goettl, J.P.J., J.R. Sinley, and P.H. Davies. 1974. Water Pollution Studies. Job Progress
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285

Secondary

Same data used from a
different study reported by the
authors in a subsequent peer-
reviewed article

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9927

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Rejection Code(s)

Comment

Gopal, V., S. Parvathy, and P.R. Balasubramanian. 1997. Effect of Heavy Metals on the
Blood Protein Biochemistry of the Fish Cyprinus carpio and Its Use as a Bio-Indicator of
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Grande, M., and S. Andersen. 1983. Lethal Effects of Hexavalent Chromium, Lead and
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Gupta, S., and P.P. Bakre. 1996. Influence of Lead in Various Organs of Lemnaea
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9822

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Hale, J.G.. 1977. Toxicity of Metal Mining Wastes. Bull.Environ.Contam.Toxicol. 17(1):66-73.

861

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Herkovits, J., and C.S. Perez-Coll. 1991. Antagonism and Synergism Between Lead and
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ECOTOX
EcoRef #

Rejection Code(s)

Comment

Hodson, P.V.. 1976. Delta-Amino Levulinic Acid Dehydratase Activity of Fish Blood As an
Indicator of a Harmful Exposure to Lead. J.Fish. Res.Board Can. 33(2):268-271.

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Hodson, P.V., B.R. Blunt, and D.J. Spry. 1978. Chronic Toxicity of Water-Borne and Dietary
Lead to Rainbow Trout (Salmo gairdneri) in Lake Ontario Water. Water Res. 12(10):869-878.

8365

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Hodson, P.V., B.R. Blunt, and D.J. Spry. 1978. pH-lnduced Changes in Blood Lead of Lead-
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15719

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Hodson, P.V., B.R. Blunt, D. Jensen, and S. Morgan. 1979. Effect of Fish Age on Predicted
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15566

UEndp

Hodson, P.V., B.R. Blunt, D.J. Spry, and K. Austen. 1977. Evaluation of Erythrocyte Delta-
Amino Levulinic Acid Dehydratase Activity As a Short-Term Indicator in Fish of a Harmful
Exposure to Lead. J.Fish.Res.Board Can. 34(4):501-508.

15460

UEndp, Con

Hodson, P.V., B.R. Blunt, U. Borgmann, C.K. Minns, and S. Mcgaw. 1983. Effect of
Fluctuating Lead Exposures on Lead Accumulation by Rainbow Trout (Salmo gairdneri).
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10840

UEndp, Eff

Hodson, P.V., D.G. Dixon, D.J. Spry, D.M. Whittle, and J.B. Sprague. 1982. Effect of Growth
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Home, M.T., and W.A. Dunson. 1995. Effects of Low pH, Metals, and Water Hardness on
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Home, M.T., and W.A. Dunson. 1995. Toxicity of Metals and Low pH to Embryos and Larvae
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374

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Comment

Iger, Y., and M. Abraham. 1989. Effects of Lead Pollution on Carp Skin. In: R.Billard, and
N.De Pauw (Eds.), Int.Aquacult.Conf., Bordeaux, France, Oct.2-4, 1989, Special Publ.No.10,
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13324

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Jain, S.K.. 1999. Protective Role of Zeolite on Short- and Long-Term Lead Toxicity in the
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20354

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Jain, S.K., P. Vasudevan, and N.K. Jha. 1990. Azolla pinnata R.Br, and Lemna minor L. for
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45092

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James, R., K. Sampath, and S. Alagurathinam. 1994. Accumulation and Prediction of Lead
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16828

James, R., K. Sampath, and S. Alagurathinam. 1996. Effects of Lead on Respiratory
Enzyme Activity, Glycogen and Blood Sugar Levels of the Teleost Oreochromis
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19442

UEndp, AF

Jampani, C.S.R.. 1988. Lead Toxicity of Alga Synechococcus aeruginosus and Its Recovery
by Nutrients. J.Environ.Biol. 9(3):261-269.

45070

UEndp, AF

Jana, S., and K. Ghosh. 1987. Effect of Heavy Metals on Population Growth of a Fish
Nematode Spinicauda spinicauda in Aquatic Environment. Environ.Ecol. 5(4):811-813.

17622

UEndp, AF

Jana, S., and M.A. Choudhuri. 1982. Senescence in Submerged Aquatic Angiosperms:
Effects of Heavy Metals. New Phytol. 90:477-484.

6024

UEndp, Dur, AF

Jana, S., and S.S. Sahana. 1989. Sensitivity of the Freshwater Fishes Clarias batrachus and
Anabas testudineus to Heavy Metals. Environ.Ecol. 7(2):265-270.

2618

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Jana, S., S.S. Sahana, M.A. Choudhuri, and D.K. Choudhuri. 1986. Heavy Metal Pollutant
Induced Changes in Some Biochemical Parameters in the Freshwater Fish Clarias
batrachus L. Acta Physiol.Hung. 68(1):39-43.

12274

UEndp

375

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Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Janssen, C. Oosterhoff, G.J.S.M. Heijmans, and H. Van der Voet. 1995. The
Toxicity of Metal Salts and the Population Growth of the Ciliate Colpoda cucculus.
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20277

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Janssens de Bisthoven, L., A. Vermeulen, and F. Ollevier. 1998. Experimental Induction of
Morphological Deformities in Chironomus riparius Larvae by Chronic Exposure to Copper
and Lead. Arch.Environ.Contam.Toxicol. 35:249-256.

19799

UEndp

Jaworska, M., A. Gorczyca, J. Sepiol, and P. Tomasik. 1997. Effect of Metal Ions on the
Entomopathogenic Nematode Heterorhabditis bacteriophora Poinar (Nematode:
Heterohabditidae) Under Laboratory Conditions. Water Air Soil Pollut. 93:157-166.

40155

UEndp, AF

Jaworska, M., J. Sepiol, and P. Tomasik. 1996. Effect of Metal Ions Under Laboratory
Conditions on the Entomopathogenic Steinernema carpocapsae (Rhabditida:
Steinernematidae). Water Air Soil Pollut. 88(3/4):331-341.

17002

UEndp, AF

Jayaraj, Y.M., M. Mandakini, and P.M. Nimbargi. 1992. Effect of Mercury and Lead on
Primary Productivity of Two Water Bodies. Environ.Ecol. 10(3):653-658.

8013

No Org, AF

Jeffree, R.A., and P.L. Brown. 1992. A Mechanistic and Predictive Model of Metal
Accumulation by the Tissue of the Australian Freshwater Mussel Velesunio angasi. Sci.Total
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4131

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Jennett, J.C., J.E. Smith, and J.M. Hassett. 1982. Factors Influencing Metal Accumulation by
Algae. EPA 600/2-82-100, U.S.EPA, Cincinnati, OH :133 p..

14512

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Jensen, T.E., M. Baxter, J.W. Rachlin, and V. Jani. 1982. Uptake of Heavy Metals by
Plectonema boryanum (Cyanophyceae) Into Cellular Components, Especially
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27(2): 119-127.

15390

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Jha, B.S.. 1991. Alterations in the Protein and Lipid Contents of Intestine, Liver and Gonads
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7533

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376

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ECOTOX
EcoRef #

Rejection Code(s)

Comment

Jha, B.S., and S. Pandey. 1989. Histopathological Lesions Induced by Lead Nitrate in the
Stomach of the Air-Breathing Teleost Channa punctatus. Environ.Ecol. 7(3):721-723.

3051

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Jones, J.R.E.. 1938. The Relative Toxicity of Salts of Lead, Zinc and Copper to the
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2657

AF, LT, UEndp

Jones, J.R.E.. 1940. A Further Study of the Relation Between Toxicity and Solution
Pressure, with Polycelis nigra As Test Animal. J.Exp.Biol. 17:408-415.

10012

UEndp, Con, AF

Jones, J.R.E.. 1948. A Further Study of the Reactions of Fish to Toxic Solutions. J.Exp.Biol.
25:22-34.

8011

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Jouany, J.M., J.F. Ferard, P. Vasseur, J. Gea, R. Truhaut, and C. Rast. 1983. Interest of
Dynamic Tests in Acute Ecotoxicity Assessment in Algae. Ecotoxicol.Environ.Saf. 7:216-228.

11896

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Kabila, V., A. Yamuna, and P. Geraldine. 1996. Water Hardness as a Determinant of the
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45145

NonRes

Kamimura, M., and T. Tanimura. 1985. The Xenopus laevis Embryo System for Evaluation of
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18818

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Kapu, M.M., and D.J. Schaeffer. 1991. Planarians in Toxicology. Responses of Asexual
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10581

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Kapur, K., and N.A. Yadav. 1982. The Effects of Certain Heavy Metal Salts on the
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45296

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Kariya, T., H. Haga, Y. Haga, and K. Kimura. 1969. Studies on the Post-Mortem
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8372

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377

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ECOTOX
EcoRef #

Rejection Code(s)

Comment

Katti, S.R., and A.G. Sathyanesan. 1983. Lead Nitrate Induced Changes in Lipid and
Cholesterol Levels in the Freshwater Fish Clarias batrachus. Toxicol.Lett. 19:93-96.

11373

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Katti, S.R., and A.G. Sathyanesan. 1985. Chronic Effects of Lead and Cadmium on the
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350

UEndp, AF

Katti, S.R., and A.G. Sathyanesan. 1986. Changes in the Hypothalamo-Neurohypophysial
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4355

UEndp, AF

Katti, S.R., and A.G. Sathyanesan. 1986. Lead Nitrate Induced Changes in the Brain
Constituents of the Freshwater Fish Clarias batrachus (L). Neurotoxicology 7(3):47-51.

12696

UEndp, AF

Katti, S.R., and A.G. Sathyanesan. 1987. Lead Nitrate Induced Changes in the Thyroid
Physiology of the Catfish Clarias batrachus (L). Ecotoxicol. Environ.Saf. 13(1): 1-6.

12336

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Katti, S.R., and A.G. Sathyanesan. 1987. Lead Nitrate-Induced Nuclear Inclusions in the
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12798

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Kaur, K., and A. Dhawan. 1994. Metal Toxicity to Different Life Stages of Cyprinus carpio
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45108

Three 96 h LC50s ranging from
approx. 5350 to 12,180 ug/L
dissolved lead normalized to
100 mg/L as CaC03 hardness.
Test s were static, unmeasured.

This study appears to provide
appropriate 96 h LC50s for C.
carpio, but the paper should be
secured to ensure
acceptability. Species is
relatively insensitive to acute
lead exposure.

Kesh, A.B., K. Sengupta, A.K. Das, and G.M. Sinha. 1993. Lead Intoxication and the Effects
of Chelating Agents on the Stomach and Intestine of the Fish Heteropneustes fossilis
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9422

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Khangarot, B.S.. 1991. Toxicity of Metals to a Freshwater Tubificid Worm, Tubifex tubifex
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2918

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378

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ECOTOX
EcoRef #

Rejection Code(s)

Comment

Khangarot, B.S., A. Sehgal, and M.K. Bhasin. 1985. Man and Biosphere-Studies on the
Sikkim Himalayas. Part 5: Acute Toxicity of Selected Heavy Metals on the Tadpoles of Rana
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11438

Con, Dur

Khangarot, B.S., and P.K. Ray. 1989. Sensitivity of Midge Larvae of Chironomus tentans
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4553

Dur

Khangarot, B.S., and P.K. Ray. 1989. Investigation of Correlation Between Physicochemical
Properties of Metals and Their Toxicity to the Water Flea Daphnia magna Straus.

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6631

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Khangarot, B.S., P.K. Ray, and H. Chandra. 1987. Daphnia magna as a Model to Assess
Heavy Metal Toxicity: Comparative Assessment with Mouse System. Acta
Hydrochim.Hydrobiol. 15(4):427-432.

12575

Inappropriate metal salt tested:
Lead Acetate

Kiewiet, A.T., and W.C. Ma. 1991. Effect of pH and Calcium on Lead and Cadmium Uptake
by Earthworms in Water. Ecotoxicol.Environ.Saf. 21(1):32-37.

20272

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Knowlton, M.F., T.P. Boyle, and J.R. Jones. 1983. Uptake of Lead From Aquatic Sediment
by Submersed Macrophytes and Crayfish. Arch.Environ.Contam.Toxicol. 12:535-541.

10267

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Kocjan, G., S. Samardakiewicz, and A. Wozny. 1996. Regions of Lead Uptake in Lemna
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45113

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Kralj-Klobucar, N.. 1993. Lead Intake in the Juvenile and Adult Carp (Cyprinus carpio L.).
Vet.Arh. 63(2):95-105.

45110

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Kralj-Klobucar, N., and S. Spasojevic. 1989. Lead Accumulations in Some Tissues of the
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45109

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Kramer, K.J.M., H.A. Jenner, and D. De Zwart. 1989. The Valve Movement Response of
Mussels: A Tool in Biological Monitoring. Hydrobiologia 188/189:433-443.

17755

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379

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Rejection Code(s)

Comment

Kulkarni, K.M., and S.V. Kamath. 1980. The Metabolic Response of Paratelphusa
jacquemontii to Some Pollutants. Geobios (Jodhpur) 7(2):70-73 (Author Communication
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5036

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Kumar, A., and R.P. Mathur. 1991. Bioaccumulation Kinetics and Organ Distribution of Lead
in a Fresh Water Teleost, Colisa fasciatus. Environ.Technol. 12(8):731-735.

3784

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Labat, R., C. Roqueplo, J.M. Ricard, P. Lim, and M. Burgat. 1977. The Ecotoxicological
Action of Some Metals (Cu,Zn,Pb,Cd) on Freshwater Fish in the River Lot (Actions
Ecotoxicologiques de Certains Metaux (Cu- Zn- Pb- Cd) chez les Poissons Dulcaquicoles de
la Riviere Lot). Ann.Limnol. 13(2):191-207 (FRE) (ENG ABS).

65413

No Org, Field, Eff, AF

Labrot, F., D. Ribera, M. Saint Denis, and J.F. Narbonne. 1996. In Vitro and In Vivo Studies
of Potential Biomarkers of Lead and Uranium Contamination: Lipid Peroxidation,
Acetylcholinesterase, Catalase and Glutathione Peroxidase Activities in Three Non-
Mammalian Species. Biomarkers 1(1):23-30.

45116

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Labus, B., H. Schuster, W. Nobel, and A. Kohler. 1977. The Effects of Toxic Water Pollutants
on Submerged Macrophytes. (Wirkung von Toxischen Abwasserkomponenten auf Submerse
Makrophyten). Angew.Bot. 51 (1/2): 17-36 (GER) (ENG ABS).

7552

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Lantataeme, S., M. Kruatruchue, S. Kaewsawangsap, Y. Chitramvong, P. Sretarugsa, and
E.S. Upatham. 1996. Acute Toxicity and Bioaccumulation of Lead in the Snail, Eilopaludina
(Siamopaludina) Martensi martensi (Frauenfeldt). J.Sci.Soc.Thailand 22:237-247.

45107

Larsen, J., and B. Svensmark. 1991. Labile Species of Pb, Zn and Cd Determined by Anodic
Stripping Staircase Voltammetry and Their Toxicity to Tetrahymena. Talanta 38(9):981-988.

3716

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Laskowski, R., and S.P. Hopkin. 1996. Effect of Zn, Cu, Pb and Cd on Fitness in Snails
(Helix aspersa). Ecotoxicol.Environ.Saf. 34(1):59-69.

45063

380

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ECOTOX
EcoRef #

Rejection Code(s)

Comment

Laube, V.M., C.N. McKenzie, and D.J. Kushner. 1980. Strategies of Response to Copper,
Cadmium, and Lead by Blue-Green and a Green Alga. Can.J.Microbiol. 26(11): 1300-1311.

9477

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Lautenbacher, H.W.. 1975. Development and Application of Analytical Methods for the Study
of Biological Changes in Goldfish Exposed to Sub-Lethal Concentrations of Nitrilotria.
Ph.D.Thesis, Temple University: 174 p.; Diss.Abstr.lnt.B Sci.Eng.36(6):2693.

8122

AF, Dur

LeBlanc, G.A.. 1982. Laboratory Investigation Into the Development of Resistance of
Daphnia magna (Straus) to Environmental Pollutants. Environ.Pollut.Ser.A Ecol.Biol.
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11065

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Lee, C.L., T.C. Wang, C.H. Hsu, and A.A. Choiu. 1998. Heavy Metals Sorption by Aquatic
Plants in Taiwan. Bull.Environ.Contam.Toxicol. 61:497-504.

19419

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Lee, D.R.. 1976. Development of an Invertebrate Bioassay to Screen Petroleum Refinery
Effluents Discharged into Freshwater. Ph.D.Thesis, Virginia Polytechnic Inst.and State
University, Blacksburg, V A:108.

3402

Eff

Lee, L.H., B. Lustigman, I.Y. Chu, and S. Hsu. 1992. Effect of Lead and Cobalt on the
Growth of Anacystis nidulans. Bull.Environ.Contam.Toxicol. 48(2):230-236.

5088

NonRes

Lefcort, H., R.A. Meguire, L.H. Wilson, and W.F. Ettinger. 1998. Heavy Metals Alter the
Survival, Growth, Metamorphosis, and Antipredatory Behavior of Columbia Spotted Frog
(Rana luteiventris) Tadpoles. Arch.Environ.Contam.Toxicol. 35(3):447-456.

20181

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Lewander, M., M. Greger, L. Kautsky, and E. Szarek. 1996. Macrophytes as Indicators of
Bioavailable Cd, Pb and Zn Flow in the River Przemsza, Katowice Region. Appl.Geochem.
11 (1/2): 169-173.

19971

UEndp, AF

Lewis, T.E., and A.W. Mcintosh. 1986. Uptake of Sediment-Bound Lead and Zinc by the
Freshwater Isopod Asellus communis at Three Different pH Levels.
Arch.Environ.Contam.Toxicol. 15(5):495-504.

12027

UEndp, Con, AF

381

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ECOTOX
EcoRef #

Rejection Code(s)

Comment

Leynen, M., T. Van den Berckt, J.M. Aerts, B. Castelein, D. Berckmans, and F. Ollevier.
1999. The Use of Tubificidae in a Biological Early Warning System. Environ.Pollut.
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19906

UEndp, Dur, AF

Lithner, G., K. Holm, and H. Borg. 1995. Bioconcentration Factors for Metals in Humic
Waters at Different pH in the Ronnskar Area (N. Sweden). Water Air Soil Pollut. 85(2):785-
790.

19851

Eff, Field

Lopez, J., M.D. Vazquez, and A. Carballeira. 1994. Stress Responses and Metal Exchange
Kinetics Following Transplant of the Aquatic Moss Fontinalis antipyretica. Freshw.Biol.
32:185-198.

45134

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Lucan-Bouche, M.L., S. Biagianti-Risbourg, F. Arsac, and G. Vernet. 1999. An Original
Decontamination Process Developed by the Aquatic Oligochaete Tubifex tubifex Exposed to
Copper and Lead. Aquat.Toxicol. 45(1):9-17.

20080

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MacPhee, C., and R. Ruelle. 1969. Lethal Effects of 1888 Chemicals upon Four Species of
Fish From Western North America. Univ.of Idaho Forest, Wildl.Range Exp.Station Bull.No.3,
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15148

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Madoni, P., D. Davoli, and G. Gorbi. 1994. Acute Toxicity of Lead, Chromium, and Other
Heavy Metals to Ciliatesfrom Activated Sludge Plants. Bull.Environ.Contam.Toxicol.
53(3):420-425.

13671

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Madoni, P., D. Davoli, G. Gorbi, and L. Vescovi. 1996. Toxic Effect of Heavy Metals on the
Activated Sludge Protozoan Community. Water Res. 30(1):135-141.

16363

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Malacea, I.. 1966. Studies on the Acclimation of Fish to High Concentrations of Toxic
Substances. Arch.Hydrobiol. 65(1):74-95 (GER) (ENG TRANSL) (1968).

10020

LT, Con, AF

Malyarevskaya, A.Y., and F.M. Karasina. 1987. Effect of Lead Nitrate on Physiological and
Biochemical Characteristics of Certain Aquatic Invertebrates. Hydrobiol.J.23(1):84-89 /
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12831

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Mao, S., and C. Wang. 1990. The Effect of Some Pollutants on SCE of Grass Carp
(Ctenopharyngodon idellus) Cells. Oceanol.Limnol.Sin./Haiyang Yu Huzhao 21(3):205-211
(CHI) (ENG ABS).

9540

UEndp, Con, AF

382

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ECOTOX
EcoRef #

Rejection Code(s)

Comment

Martinez-Tabche, L., C. German-Faz, B. Ramirez-Mora, and 1. Galar-Castelan. 1995. Effect
of Carbaryl and Lead on Phenols Chlorophyll and Proteins of the Microalga Ankistrodesmus
falcatus. Rev.Latinoam.Microbiol.37(2):93-99 (SPA) (ENG ABS).

18576

UEndp, Dur, AF

Martinez-Tabche, L., M. Martinez Campos, and E. Sanchez-Hidalgo. 1990. Effect of Lead on
the Integrity of the Lysosomal Membrane of the Gills of Fish (Oreochromis hornorum).
An.Esc.Nac.Cienc.Biol.Mex. 33(1-4): 103-109 (SPA) (ENG ABS).

5455

UEndp, AF

Martinez-Tabche, L., N.E. Morales, M.B. Ramirez, C.I. Galar, and G.H. Cardona. 1994.

Effect of Lead on the Reaction of O-Demethylase in p-Nitro Anisole in the Cladoceran Moina
macrocopa. J.Aquat.Ecosyst.Health 3(4):255-258.

17595

UEndp, Dur

Masters, J.A., M.A. Lewis, and D.H. Davidson. 1991. Validation of a Four-Day Ceriodaphnia
Toxicity Test and Statistical Considerations in Data Analysis. Environ.Toxicol.Chem. 10:47-
55.

17743

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Mathew, R., M.K. Kanangaraj, and R. Manavalaramanujam. 1997. Lead Nitrate Toxicity on
Ventilation Frequency, Oxygen Consumption and Haemoglobin Content in Fish, Cyprinus
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45135

AF, Dur

Mathis, B.J., T.F. Cummings, M. Gower, M. Taylor, and C. King. 1979. Dynamics of
manganese cadmium and lead in experimental power plant ponds. Hydrobiologia 67(3): 197-
206.

2745

UEndp, AF, Field

Mayes, R.A., A.W. Mcintosh, and V.L. Anderson. 1977. Uptake of Cadmium and Lead by a
Rooted Aquatic Macrophyte (Elodea canadensis). Ecology 58(5): 1176-1180.

652

UEndp, AF, Field

McConnell, M.A., and R.C. Harrel. 1995. The Estuarine Clam Rangia cuneata (Gray) as a
Biomonitor of Heavy Metals Under Laboratory and Field Conditions. Am.Malacol.Bull.
11 (2): 191-201.

19514

Eff

383

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Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Medina, J., J. Diaz-Mayans, F. Hernandez, A. Pastor, J. Del Ramo, and A. Torreblanca.
1991. Study of the Toxicity and Bioaccumulation of Some Heavy Metals in the Crayfish
Procambarus clarkii (Girard, 1852) of the Albufera Lake of Valencia, Spain. In: Final Reports
on Research Projects Dealing with Mercury, Toxicity and Analytical Techniques, UNEP,
Athens, Greece, MAP Tech.Rep.Ser.No.51 :105-131.

4205

UEndp, Con, AF

Meindl.U., and G. Roderer. 1990. Influence of Inorganic and Triethyl Lead on Nuclear
Migration and Ultrastructure of Micrasterias. Ecotoxicol. Environ.Saf. 19(2): 192-203.

3151

UEndp, AF

Merlini, M., and G. Pozzi. 1977. Lead and Freshwater Fishes: Part l-Lead Accumulation and
Water pH. Environ.Pollut. 12(3): 167-172.

15429

Eff, Con, AF

Merlini, M., and G. Pozzi. 1977. Lead and Freshwater Fishes: Part 2-lonic Lead
Accumulation. Environ.Pollut. 13(1): 119-126.

15430

Eff, Con

Meyer, W., G. Harisch, and A.N. Sagredos. 1986. Biochemical and Histochemical Aspects of
Lead Exposure in Dragonfly Larvae (Odonata: Anisoptera). Ecotoxicol.Environ.Saf.
11 (3):308-319.

12306

UEndp, Con, AF

Meyer, W., M. Kretschmer, A. Hoffmann, and G. Harisch. 1991. Biochemical and
Histochemical Observations on Effects of Low-Level Heavy Metal Load (Lead, Cadmium) in
Different Organ Systems of the Freshwater. Ecotoxicol.Environ.Saf. 21 (2): 137-156.

376

UEndp, AF

Michailova, P., and R. Belcheva. 1990. Different Effect of Lead on External Morphology and
Polytene Chromosomes of Glyptotendipes barbipes (Staeger) (Diptera, Chironomidae). Folia
Biol.(Krakow) 38(1-4):83-88.

45136

UEndp, AF

Migliore, L., and M. Nicola Giudici. 1990. Toxicity of Heavy Metals to Asellus aquaticus (L.)
(Crustacea, Isopoda). Hydrobiologia 203(3):155-164.

10515

LT, Con, AF

Miller, J.C., and R. Landesman. 1978. Reduction of Heavy Metal Toxicity to Xenopus
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2743

UEndp, AF

384

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Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Mishra, R., and S.D. Singh. 1997. Histopathological Studies on the Stomach and Liver of
Clarias batrachus Due to Lead Nitrate and Dichromate. Environ.Ecol. 15(3):614-616.

18207

UEndp, AF

Mizutani, A., E. Ifune, A. Zanella, and C. Eriksen. 1991. Uptake of Lead, Cadmium and Zinc
by the Fairy Shrimp, Branchinecta longiantenna (Crustacea; Anostraca). Hydrobiologia
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3681

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Mohan, B.S., and B.B. Hosetti. 1997. Potential Phytotoxicity of Lead and Cadmium to Lemna
minor Grown in Sewage Stabilization Ponds. Environ.Pollut. 98(2):233-238.

19020

UEndp, AF

Monahan 1976

Det

May be the same as below

Monahan, T.J. 1976. Lead Inhibition of Chlorophycean Microalgae. J.Phycol. 12(3):358-362.

2243

UEndp, AF

Morgan, E.L., Y.C.A. Wu, and J.P. Swigert. 1993. An Aquatic Toxicity Test Using the Moss
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352.

4287

UEndp, AF

Morgan, E.L., Y.C.A. Wu, and R.C. Young. 1990. A Plant Toxicity Test with the Moss
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4203

UEndp, AF

Morgan, W.S.G.. 1976. Fishing for Toxicity: Biological Automonitor for Continuous Water
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Snell, T.W.. 1991. New Rotifer Bioassays for Aquatic Toxicology. Final Report, U.S.Army
Medical Research and Development Command, Ft.Detrick, Frederick, MD :29 p.(U.S.NTIS
AD-A258002).

17689

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Snell, T.W., B.D. Moffat, C. Janssen, and G. Persoone. 1991. Acute Toxicity Tests Using
Rotifers IV. Effects of Cyst Age, Temperature, and Salinity on the Sensitivity of Barachionus
calyciflorus. Ecotoxicol.Environ.Saf. 21(3):308-317 (OECDG Data File).

9385

Dur, AF

Sobotka, J.M., and R.G. Rahwan. 1995. Teratogenesis Induced by Short- and Long-Term
Exposure ofXenopus laevis Progeny to Lead. J.Toxicol.Environ.Health 44(4):469-484.

45121

UEndp

395

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Sola, F., A. Masoni, and J. Isaia. 1994. Effects of Lead Loads on Branchial Osmoregulatory
Mechanisms in the Rainbow Trout Oncorhynchus mykiss. J.Appl.Toxicol. 14(5):343-349.

14449

UEndp, AF, LT

Sordyl, H.. 1990. Influence of Exposure Time and H+ Concentration of the Water on the
Effects of Sublethal Pb2+ Loads on Blood Parameters of the Rainbow Trout (Salmo
gairdneri). Zool.Jahrb.Abt.Allg.Zool.Physiol.Tiere 94:141-152.

45128

UEndp, AF

Soundrapandian, S., and K. Venkataraman. 1990. Effect of Heavy Metal Salts on the Life
History of Daphnia similis Claus (Crustacea: Cladocera). Proc.Indian Acad.Sci.Anim.Sci.
99(5): 411-418.

3945

Eff, Con, AF

Spieler, R.E., A.C. Russo, and D.N. Weber. 1995. Waterborne Lead Affects Circadian
Variations of Brain Neurotransmitters in Fathead Minnows. Bull.Environ.Contam.Toxicol.
55(3):412-418.

14983

UEndp, AF

Spieler, R.E., and D.N. Weber. 1991. Effects of Waterborne Lead on Circulating Thyroid
Hormones and Cortisol in Rainbow Trout. Med.Sci.Res. 19(15):477.

9513

UEndp, AF

Srivastav, R.K., S.K. Gupta, K.D.P. Nigam, and P. Vasudevan. 1994. Use of Aquatic Plants
for the Removal of Heavy Metals from Wastewater. Int.J.Environ.Stud. 45(1):43-50.

16762

Eff, AF

Srivastava, A.K.. 1987. Changes Induced by Lead in Fish Testis. J.Environ.Biol. 8(4):329-
332.

12649

UEndp, Con

Srivastava, A.K., and S. Mishra. 1979. Blood Dyscrasia in a Teleost, Colisa fasciatus After
Acute Exposure to Sublethal Concentrations of Lead. J.Fish Biol. 14(2): 199-203.

5640

Con

Stallwitz, E., and D.P. Hader. 1993. Motility and Phototatic Orientation of the Flagellate
Euglena gracilis Impaired by Heavy Metal Ions. J.Photochem.Photobiol. B:Biol-74.

7299

UEndp, Con

Stallwitz, E., and D.P. Hader. 1994. Effects of Heavy Metals on Motility and Gravitactic
Orientation of the Flagellate, Euglena gracilis. Eur.J.Protistol. 30:18-24.

45123

UEndp, Dur, AF

396

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Starodub, M.E., P.T.S. Wong, and C.I. Mayfield. 1987. Short Term and Long Term Studies
on Individual and Combined Toxicities of Copper, Zinc and Lead to Scenedesmus
quadricauda. Sci.Total Environ. 63:101-110.

12380

Dur, AF

Starodub, M.E., P.T.S. Wong, C.I. Mayfield, and Y.K. Chau. 1987. Influence of Complexation
and pH on Individual and Combined Heavy Metal Toxicity to a Freshwater Green Alga.
Can.J.Fish.Aquat.Sci. 44:1173-1180.

12817

Dur, AF

Stauber, J.L., and T.M. Florence. 1987. Mechanism of Toxicity of Ionic Copper and Copper
Complexes to Algae. Mar.Biol. 94(4):511-519.

12971

UEndp, AF

Steele, C.W., S. Strickler-Shaw, and D.H. Taylor. 1989. Behavior of Tadpoles of the Bullfrog,
Rana catesbeiana, in Response to Sublethal Lead Exposure. Aquat.Toxicol. 14(4):331-344.

3976

UEndp, AF

Steele, C.W., S. Strickler-Shaw, and D.H. Taylor. 1991. Failure of Bufo americanus Tadpoles
to Avoid Lead-Enriched Water. J.Herpetol. 25(2):241-243.

3635

UEndp, AF

Stouthart, et al. 1994.

Det

No Information - Might be same
as below

Stouthart, J.H.X., F.A.T. Spanings, R.A.C. Lock, and S.E. Wendelaar Bonga. 1994. Effects
of Low Water pH on Lead Toxicity to Early Life Stages of the Common Carp (Cyprinus
carpio). Aquat.Toxicol. 30(2):137-151.

16689

UEndp, AF

Stoyanova, D.P., and E.S. Tchakalova. 1993. The Effect of Lead and Copper on the
Photosynthetic Apparatus in Elodea canadensis Rich. Photosynthetica 28(1):63-74.

45125

UEndp, AF

Strickler-Shaw, S., and D.H. Taylor. 1990. Sublethal Exposure of Lead Inhibits Acquisition
and Retention of Discriminate Avoidance Learning in Green Frog (Rana clamitans)
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3189

UEndp, AF

Strickler-Shaw, S., and D.H. Taylor. 1991. Lead Inhibits Acquisition and Retention Learning
in Bullfrog Tadpoles. Neurotoxicol.Teratol. 13:167-173.

45126

UEndp, Dur

397

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Sultana, R., V.U. Devi, and M.N. Prasad. 1991. Effect of Heavy Metals on the Respiration of
the Catfish, Mystus gulio. J.Ecotoxicol.Environ.Monit. 1(3):234-237.

4421

UEndp, AF

Summerfelt, R.C., and W.M. Lewis. 1967. Repulsion of Green Sunfish by Certain Chemicals.
J.Water Pollut.Control Fed.39(12):2030-2038 (Author Communication Used).

2423

UEndp, AF

Swinehart, J.H.. 1990. The Effects of Humic Substances on the Interactions of Metal Ions
wiht Organisms and Liposomes. Final Tech.Rep., Dep.ofChem., Univ.California, Davis, CA
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17696

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Swinehart, J.H.. 1992. The Effects of Humic Substances on the Interactions of Metal Ions
with Organisms and Liposomes. Final Tech.Rep.U.S.G.S.G-1625, Dep.of Chemistry, Univ.of
California, Davis, CA :103.

18060

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Tabche, L.M., C.M. Martinez, and E. Sanchez-Hidalgo. 1990. Comparative Study of Toxic
Lead Effect on Gill and Haemoglobin of Tilapia Fish. J.Appl.Toxicol. 10(3):193-195.

172

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Tang, Y., and E.T. Garside. 1987. Preexposure and Subsequent Resistance to Lead in
Yearling BrookTrout, Salvelinusfontinalis. Can.J.Fish.Aquat.Sci. 44(5):1089-1091.

12973

Tao, S., C. Liu, R. Dawson, J. Cao, and B. Li. 1999. Uptake of Particulate Lead via the Gills
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20577

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Tarzwell, C.M., and C. Henderson. 1960. Toxicity of Less Common Metals to Fishes.
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2042

Con

Tatara, C.P., M.C. Newman, J.T. McCloskey, and P.L. Williams. 1997. Predicting Relative
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18605

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Tatara, C.P., M.C. Newman, J.T. McCloskey, and P.L. Williams. 1998. Use of Ion
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5072

Dur, AF

398

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Tatem, H.E.. 1986. Bioaccumulation of Polychlorinated Biphenyls and Metals From
Contaminated Sediment by Freshwater Prawns, Macrobrachium rosenbergii and Clams,.
Arch.Environ.Contam.Toxicol. 15(2):171 -183.

12002

UEndp, Dur, AF

Tewari, H., T.S. Gill, and J. Pant. 1987. Impact of Chronic Lead Poisoning on the
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12599

UEndp, AF

Thomas, A.. 1915. Effects of Certain Metallic Salts upon Fishes. Trans.Am.Fish.Soc. 44:120-
124.

2865

UEndp, Dur, AF

Tiedemann, G., M. Kublbeck, and J. Rosmanith. 1984. Interaction of Cadmium and Lead in
Fish. (Die Gegenseitige Beeinflussung Von Cadmium Und Blei Im Fischorganismus).
Wiss.Umwelt 3:145-154 (Ger) (Eng Abs).

11828

UEndp, Con, AF

Timmermans, K.R., W. Peeters, and M. Tonkes. 1992. Cadmium, Zinc, Lead and Copper in
Chironomus riparius (Meigen) Larvae (Diptera, Chironomidae): Uptake and Effects.
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6029

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Tomasik, P., C.M. Magadza, S. Mhizha, A. Chirume, M.F. Zaranyika, and S. Muchiriri. 1995.
Metal-Metal Interactions in Biological Systems. Part IV. Freshwater Snail Bulinus globosus.
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16369

UEndp, Dur

Torreblanca et al. 1977.

Det

No Information

Torreblanca, A., J. Del Ramo, and J. Diaz-Mayans. 1989. Gill ATPase Activity in
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3407

UEndp

Torreblanca, A., J. Del Ramo, J.A. Arnau, and J. Diaz-Mayans. 1989. Cadmium, Mercury,
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2695

UEndp, AF

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16187

UEndp, AF

399

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Tsuji, S., Y. Tonogai, Y. Ito, and S. Kanoh. 1986. The Influence of Rearing Temperatures on
the Toxicity of Various Environmental Pollutants for Killifish (Oryzias latipes).
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12497

Dur, Con, AF

Tulasi, S.J., and J.V.R. Rao. 1988. Acid-Base Balance and Blood Gas Changes in the Fresh
Water Field Crab, Barytelphusa guerini, on Exposure to Organic and Inorganic Lead.
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2416

UEndp, AF

Tulasi, S.J., and J.V.R. Rao. 1988. Effects of Lead on Copper Content of Fresh Water Crab
Barytelphusa guerini (H. Miline Edwards). Indian J.Exp.Biol. 26(4):323-324.

13131

UEndp, AF

Tulasi, S.J., P.U.M. Reddy, and J.V. Ramana Rao. 1989. Effects of Lead on the Spawning
Potential of the FreshWater Fish, Anabas testudineus. Bull.Environ.Contam.Toxicol.
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2551

UEndp, AF

Tulasi, S.J., P.U.M. Reddy, and J.V.R. Rao. 1992. Accumulation of Lead and Effects on
Total Lipids and Lipid Derivatives in the Freshwater Fish Anabas testudineus (Bloch).
Ecotoxicol.Environ.Saf. 23:33-38.

3905

UEndp, AF

Tulasi, S.J., R. Yasmeen, and J.V. Ramana Rao. 1988. Physiological Responses of the
Fresh Water Crab, Barytelphusa guerini During Lead Nitrate Toxicity. Comp.Physiol.Ecol.
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3829

UEndp, AF

Tulasi, S.J., R. Yasmeen, and J.V.R. Rao. 1990. Ionic Balance in the Haemolymph of the
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3145

UEndp, AF

Tulasi, S.J., R. Yasmeen, and J.V.R. Rao. 1992. Biochemical Changes in the Haemolymph
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10983

UEndp, AF

Tulasi, S.J., R. Yasmeen, C.P. Reddy, and J.V.R. Rao. 1987. Lead Uptake and Lead Loss in
the FreshWater Field Crab, Barytelphusa guerini, on Exposure to Organic and Inorganic
Lead. Bull.Environ.Contam.Toxicol. 39(1):63-68.

12603

UEndp, Con, AF

400

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Turnbull, H., J.G. Demann, and R.F. Weston. 1954. Toxicity of Various Refinery Materials to
Freshwater Fish. Ind.Eng.Chem. 46(2):324-333.

922

Dur, AF

Twagilimana, L., J. Bohatier, C.A. Groliere, F. Bonnemoy, and D. Sargos. 1998. A New Low-
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20057

Ace, Dur, AF

Van der Werff, M., and M.J. Pruyt. 1982. Long-Term Effects of Heavy Metals on Aquatic
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14480

UEndp, AF

Varanasi, U., and D.J. Gmur. 1978. Influence of Water-Borne and Dietary Calcium on
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15414

Eff, Con

Vareille-Morel, C., and C. Chaisemartin. 1982. Natural Tolerance and Acclimation of
Different Populations of Austropotamobius pallipes (Le.) to Heavy Metals (Chromium and
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15732

Con, AF

Vazquez, M.D., J. Lopez, and A. Carballeira. 1999. Uptake of Heavy Metals to the
Extracellular and Intracellular Compartments in Three Species of Aquatic Bryophyte.
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20585

UEndp, AF

Verrengia Guerrero, N.R., M.N. Mozzarelli, H. Giancarlo, D. Nahabedian, and E. Wider.
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18463

UEndp, AF

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19565

NonRes

Vijayamadhavan, K.T., and T. Iwai. 1975. Histochemical Observations on the Permeation of
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15445

UEndp, Dur, Con, AF

401

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Vymazal, J.. 1990. Uptake of Lead, Chromium, Cadmium and Cobalt by Cladophora
glomerata. Bull.Environ.Contam.Toxicol. 44(2):468-472.

2191

UEndp, AF

Vymazal, J.. 1990. Uptake of Heavy Metals by Cladophora glomerata. Acta
Hydrochim.Hydrobiol. 18(6):657-665.

45131

UEndp, AF

Vymazal, J.. 1995. Influence of pH on Heavy Metals Uptake by Cladophora glomerata.
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45130

UEndp, AF

Waldegger, S., F. Schmidt, T. Herzer, E. Gulbins, A. Schuster, J. Biber, D. Markovich, H.
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45834

UEndp, AF

Wallen, I.E., W.C. Greer, and R. Lasater. 1957. Toxicity to Gambusia affinis of Certain Pure
Chemicals in Turbid Waters. Sewage Ind.Wastes 29(6):695-711.

508

Con, AF

Wallen, I.E., W.C. Greer, and R. Lasater. 1957.

Det

No Information - Might be same
as above

Wang, T.C., J.C. Weissman, G. Ramesh, R. Varadarajan, and J.R. Benemann. 1996.
Parameters for Removal of Toxic Heavy Metals by Water Milfoil (Myriophyllum spicatum).
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20408

UEndp, AF

Wang, W. 1994. Rice Seed Toxicity Tests for Organic and Inorganic Substances.
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45060

Weber, D.N.. 1991. Physiological and Behavioral Effects ofWaterborne Lead on Fathead
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7168

UEndp, Con, AF

Weber, D.N.. 1993. Exposure to Sublethal Levels ofWaterborne Lead Alters Reproductive
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9543

UEndp, AF

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19673

UEndp

402

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Weber, D.N., A. Russo, D.B. Seale, and R.E. Spieler. 1989. Waterborne Lead Affects
Feeding Abilities and Neurotransmitter Levels of Juvenile Fathead Minnows (Pimephales
promelas). Aquat.Toxicol.21:71-80 (1991) / Am.Zool. 29(4):38A (ABS).

5276

UEndp, AF

Weber, D.N., W.M. Dingel, J.J. Panos, and R.E. Steinpreis. 1997. Alterations in
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45129

UEndp, AF

Wehrheim, B., and M. Wettern. 1994. Comparative Studies of the Heavy Metal Uptake of
Whole Cells and Different Types of Cell Walls from Chlorella fusca. Biotechnol.Tech.
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16139

UEndp, AF

Wehrheim, B., and M. Wettern. 1994. Influence of the External REDOX State on Heavy
Metal Adsorption by Whole Cells and Isolated Cell Walls of Chlorella fusca. Biotechnol.Tech.
8:221-226.

45132

UEndp, AF

Weir, P.A., and C.H. Hine. 1970. Effects of Various Metals on Behavior of Conditioned
Goldfish. Arch.Environ.Health 20(1):45-51.

908

Con, AF, UEndp

Weis, J.S., and P. Weis. 1977. Effects of Heavy Metals on Development of the Killifish,
Fundulus heterclitus. J.Fish Biol. 11 (1 ):49-54.

45298

UEndp, AF

Wetzel, A., T. Alexander, S. Brandt, R. Haas, and D. Werner. 1994. Reduction by
Fluoranthene of Copper and Lead Accumulation in Triticum aestivum L.
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13737

UEndp, AF

Whitley, L.S.. 1968. The Resistance of Tubificid Worms to Three Common Pollutants.
Hydrobiologia 32(1/2): 193-205 (Author Communication Used).

15507

Con, Dur, AF

Williams, P.L., and D.B. Dusenbery. 1990. Aquatic Toxicity Testing Using the Nematode,
Caenorhabditis elegans. Environ.Toxicol.Chem. 9(10):1285-1290.

3437

AF, Dur

Wong, P.T.S., Y.K. Chau, J.L. Yaromich, and 0. Kramar. 1987. Bioaccumulation and

Metabolism of Tri- and Dialkyllead Compounds by a Freshwater Alga.

Can.J.Fish.Aquat.Sci.44:1257-1260 / In: J.S.S.Lakshminarayana (Ed.), Proc. 13th Annual

Aquatic Toxicity Workshop, Nov.12-14, 1986, Moncton, New Brunswick,

Can.Tech.Rep.Fish.Aquat.Sci.No.1575 :37-38 (ABS).

12819

Eff, Con, AF

403

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Woodward, D.F., J.N. Goldstein, A.M. Farag, and W.G. Brumbaugh. 1997. Cutthroat Trout
Avoidance of Metals and Conditions Characteristic of a Mining Waste Site: Coeur d'Alene
River, Idaho. Trans.Am.Fish.Soc. 126:699-706.

45186

UEndp, Dur

Yoshitomi, T., C. Nakayasu, S. Hasegawa, A. lida, and N. Okamoto. 1998. Site-Specific
Lead Distribution in Scales of Lead-Administered Carp (Cyprinus carpio) by Non-Destructive
SR-XRF Analysis. Chemosphere 36(10):2305-2310.

18974

UEndp, AF

Ziegenfuss, P.S., W.J. Renaudette, and W.J. Adams. 1986. Methodology for Assessing the
Acute Toxicity of Chemicals Sorbed to Sediments: Testing the Equilibrium Partitioning
Theory. In: T.M.Poston and R.Purdy (Eds.), Aquatic Toxicology and Environmental Fate, 9th
Volume, ASTM STP 921, Philadelphia, PA :479-493.

7884

Con, AF

Zimmermann, S., B. Sures, and H. Taraschewski. 1999. Experimental Studies on Lead
Accumulation in the Eel-Specific Endoparasites Anguillicola crassus (Nematoda) and
Paratenuisentis ambiguus (Acanthocephala) as Compared with Their Host, Anguilla
anguilla. Arch.Environ.Contam.Toxicol. 37(2):190-195.

20449

UEndp,Af

Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

FAV in the most recent national ambient water quality criteria dataset used to derive the CMC , EPA is providing a
transparent rationale as to why they were not utilized (see below).

85 U.S. EPA. 1984. Ambient Water Quality Criteria Documents for Lead. EPA-440/5-84-027.

404

-------
4) For the studies that were not utilized because they were not found to be pertinent to this determination (including
failing the QA/QC procedures listed in Appendix A) upon initial review of the download from ECOTOX, EPA is
providing the code that identifies why EPA determined that the results of the study were not reliable (see Appendix H).

General QA/QC failure because non-resident species in Oregon

The test with the following species was used in the EPA BE of OR WQS for lead in freshwater, but was not considered in the CWA
review and approval/disapproval action of the standards because this species does not have a breeding wild population in Oregon's
waters:

Gammarus

pseudolimnaeus

Scud

Spehar et al. 1978; Call et al. 1983

Other Acute tests failins QA/QC by species

Oncorhynchus mykiss — Rainbow Trout

The following tests were included in EPA's BE of the OR WQS for lead in freshwater, but were not used in this CWA review and
approval/disapproval action of these standards because the tests were not based on the preferred flow-through measured test
conditions; however, other flow-through measured test concentrations were available for these species.

Buhl, K.J. and S.J. Hamilton. 1990. Comparative toxicity of inorganic contaminants released by placer mining to early life
stages of salmonids. Ecotoxicol. Environ. Saf. 20(3): 325-342.

Two LC50 values from S,U tests ranging from 4871 |ig/L to 85954 |ig/L.

Goettl, J.P.Jr., P.H. Davies and J.R. Sinley. 1976. Water Pollution Studies. In: D.B. Cope (Ed.), Colorado Fish. Res. Rev. 1972-
1975, DOW-R-R-F72-75, Colorado Div. of Wildl., Boulder, CO: 68-75.

Two LC50 values from D,U tests ranging from 57931 |ig/L to 77224 |ig/L.

Davies, P.H., J.P. Goettl, Jr., J.R. Sinley and N.F. Smith. 1976. Acute and chronic toxicity of lead to rainbow trout
(Oncorhynchus mykiss) in hard and soft water. Water Res. 10: 199-206.

Two LC50 values from S,U tests ranging from 57931 |ig/L to 77224 |ig/L.

Goettl, J.P., et al. 1972. Laboratory water pollution studies. Colorado Fisheries Research Review.

Two LC50 values from S,U tests ranging from 57931 |ig/L to 77224 |ig/L.

405

-------
Davies, P.H. and W.E. Everhart. 1973. Effects of chemical variations in aquatic environments: Lead toxicity to rainbow trout
and testing application factor concept. EPA-R3-73-011C. National Technical Information Service, Springfield, VA.

Two LC50 values from S,U tests ranging from 57931 |ig/L to 77224 |ig/L.

Oncorhynchus kisutch — Coho salmon

Buhl, K.J. and S.J. Hamilton. 1990. Comparative toxicity of inorganic contaminants released by placer mining to early life
stages of salmonids. Ecotoxicol. Environ. Saf. 20(3): 325-342.

One value, a 24-hr test, was an inappropriate test duration and was not used. Other values from this study were used for this species.
Daphttia magna — Cladoceran

The following tests were included in EPA's BE of the OR WQS for lead in freshwater, but was not used in this CWA review and
approval/disapproval action of these standards because the tests were conducted in river water:

Bringmann, G. and R. Kuhn. 1959a. The toxic effects of waste water on aquatic bacteria, algae, and small crustaceans.
Gesundheints-Ing. 80: 115.

Bringmann, G. and R. Kuhn. 1959b. Water toxicology studies with protozoans as test organisms. Gesundheits-Ing. 80: 239.

Daphnia pulex — Cladoceran

The following test was included in EPA's BE of the OR WQS for lead in freshwater, but was not used in this CWA review and
approval/disapproval action of these standards because the value was deemed an outlier and unacceptable to use for calculating the
SMAV for the species:

Mount, D.I. and T.J. Norberg. 1984. A seven-day life-cycle cladoceran toxicity test. Environ. Toxicol. Chem. 3(3):425-434
(Author Communication Used).

Other Chronic tests failing QA/QC by species

Oncorhynchus mykiss — Rainbow Trout

406

-------
The following tests were included in EPA's BE of the OR WQS for lead in freshwater, but were not used in this CWA review and
approval/disapproval action of these standards because they are duplicate data for another test already used:

Davies, P.H., J.P. Goettl, Jr., J.R. Sinley and N.F. Smith. 1976. Acute and chronic toxicity of lead to rainbow trout
(Oncorhynchus mykiss) in hard and soft water. Water Res. 10: 199-206.

Davies, P.H. and W.E. Everhart. 1973. Effects of chemical variations in aquatic environments: Lead toxicity to rainbow trout
and testing application factor concept. EPA-R3-73-011C. National Technical Information Service, Springfield, VA.

407

-------
Appendix I Lindane (freshwater)
Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

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Cebrian, C., E. Andreu-Moliner, and M. Gamon. 1993. The Effect of Time,
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Chabert, D., and N. Vicente. 1978. Contamination of Mediterranean Molluscs by
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Chen, P.S., Y.N. Lin, and C.L. Chung. 1971. Laboratory Studies on the
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Demael, A., D. Lepot, M. Cossarini-Dunier, and G. Monod. 1987. Effect of
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17456

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Ensenbach, U., and R. Nagel. 1991. Toxicokinetics of Xenobiotics in Zebrafish -
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Ensenbach, U., and R. Nagel. 1995. Toxicity of Complex Chemical Mixtures:
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Estenik, J.F., and W.J. Collins. 1979. In Vivo and In Vitro Studies of Mixed-
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Ferrando, M.D., and E. Andreu-Moliner. 1991. Effects of Lindane on Fish
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11202

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Comment

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Gouda, R.K., N.K. Tripathy, and C.C. Das. 1981. Toxicity of Dimecron, Sevin
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Comment

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20 Emulsified Concentration

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Holland, G.A., J.E. Lasater, E.D. Neumann, and W.E. Eldridge. 1960. Toxic
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Comment

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16999

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16601

48 h EC50 = 1990 ug/L. Test was
static, unmeasured.

This study appears to provide an
appropriate 48 h EC50for C. dubia,
but the paper should be secured to
ensure acceptability. Species is
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568

96 h LC50 = 1350 ug/L. Test was
static, measured.

This study appears to provide an
appropriate 96 h LC50 for Gambusia
affinis, but the paper should be
secured to ensure acceptability.
Species is insensitive to acute
lindane exposure.

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7954

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20 Emulsified Concentration

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Kalafatic, M., D. Znidaric, A. Lui, and M. Wrischer. 1991. Effect of Insecticides
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59925

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12534

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Kanazawa, J.. 1981. Measurement of the Bioconcentration Factors of Pesticides
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15599

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Krishnakumari, M.K.. 1977. Sensitivity of the Alga Scenedesmus acutus to Some
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La Rocca, C., A. Di Domenico, and L. Vittozzi. 1991. Chemiobiokinetic Study in
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6919

Eff

LaBrecque, G.C., J.R. Noe, and J.B. Gahan. 1956. Effectiveness of Insecticides
on Granular Clay Carriers Against Mosquito Larvae. Mosq.News 16:1-3.

2808

UEndp, Dur, Pur

Lakota, S., A. Raszka, J. Roszkowski, S. Hlond, and F. Kozlowski. 1983. Toxic
Effects of DDT, Lindane, and Toxaphene on the Fry of the Carp, Cyprinus
carpio, as Revealed by an Acute Test. Folia Biol.(Krakow) 31(1):94-99.

10842

UEndp, Dur

Lai, B., and T.P. Singh. 1987. Impact of Pesticides on Lipid Metabolism in the
Freshwater Catfish, Clarias batrachus, during the Vitellogenic Phase of its
Annual Reproductive Cycle. Ecotoxicol.Environ.Saf. 13(1): 13-23.

12341

UEndp

Lansing, M.B., W.S. Gardner, and B.J. Eadie. 1993. Catecholamines as
Potential Sub-Lethal Stress Indicators in Great Lakes Macrobenthic
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4997

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417

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ECOTOX
EcoRef#

Rejection Code(s)

Comment

Larsen, J.. 1996. Pilot Ringtest on Five Test Substances Employing Optimized
Test Protocols with the Protozoan Tetrahymena pyriformis. In: W.Pauli and
S.Berger (Eds.), Rep.No.UBA-FB 96-039, Proc.International Workshop on a
Protozoan Test Protocol with Tetrahymena in Aquatic Toxicity Testing,
Umweltbundesamt :67-104.

12482

Ace, Dur

Lay, J.P., A. Muller, L. Peichl, R. Lang, and F. Korte. 1987. Effects of gamma-
BHC (Lindane) on Zooplankton Under Outdoor Conditions. Chemosphere
16(7): 1527-1538.

12670

UEndp, No Org

Le Bras, S., T. Caquet, E. Thybaud, and 0. Jonot. 1992. Ponderal Growth of
Asellus aquaticus L. Under Laboratory Conditions and in Experimental
Mesocosms, Consequences of Lindane Contamination. J.Water
Sci./Rev.Sci.Eau.5(3):431-443 (Fre) (Eng Abs).

7541

UEndp, Dur

Lichtenstein, E.P., K.R. Schulz, R.F. Skrentny, and Y. Tsukano. 1966. Toxicity
and Fate of Insecticide Residues in Water. Arch.Environ.Health 12:199-212.

8020

UEndp

Lilius, H., B. Isomaa, and T. Holmstrom. 1994. A Comparison of the Toxicity of
50 Reference Chemicals to Freshly Isolated Rainbow Trout Hepatocytes and
Daphnia magna. Aquat.Toxicol. 30:47-60.

16756

Dur

Liong, P.C., W.P. Hamzah, and V. Murugan. 1988. Toxicity of Some Pesticides
Towards Freshwater Fishes. Fish.Bull.Dep.Fish.(Malays.) No .57:13.

3296

Pur, Dur

Lohner, T.W., and W.J. Collins. 1987. Determination of Uptake Rate Constants
for Six Organochlorines in Midge Larvae. Environ.Toxicol.Chem. 6(2):137-146.

12298

UEndp, Con

Lombardo, R.J., L. Ferrari, and J.H. Vinuesa. 1991. Effects of Lindane and
Acetone on the Development of Larvae of the Southern King Crab (Lithodes
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136

NonRes

418

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Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Lydy, M.J., K.A. Bruner, D.M. Fry, and S.W. Fisher. 1990. Effects of Sediment
and the Route of Exposure on the Toxicity and Accumulation of Neutral
Lipophilic and Moderately Water-Soluble Metabolizable Compounds in the
Midge, Chironomus riparius. In: W.G.Landis and W.H.Van der Schalie (Eds.),
Aquatic Toxicology and Risk Assessment, 13th Volume, ASTM STP1096,
Philadelphia, PA :140-164.

18935

Dur

MacPhee, C., and R. Ruelle. 1969. Lethal Effects of 1888 Chemicals upon Four
Species of Fish From Western North America. Univ.of Idaho Forest, Wildl.Range
Exp.Station Bull.No.3, Moscow, ID :112 p..

15148

UEndp, Con

Maheshwari, U.K., B.C. Das, S. Paul, S.K. Chouhan, and A.K. Yadav. 1988.
Bioassay Studies of Some Commercial Organic Pesticides to an Exotic Carp
Fry, Hypophthalmichthys molitrix (C. & V). J.Environ.Biol. 9(4):377-380.

580

Dur, Con

Mailhot, H.. 1987. Prediction of Algal Bioaccumulation and Uptake Rate of Nine
Organic Compounds by Ten Physicochemical Properties. Environ.Sci.Technol.
21(10):1009-1013.

12891

Eff, Dur, Con

Malbouisson, J.F.C., T.W.K. Young, and A.W. Bark. 1995. Use of Feeding Rate
and Re-Pairing of Precopulatory Gammarus pulex to Assess Toxicity of gamma-
Hexachlorocyclohexane (Lindane). Chemosphere 30(8): 1573-1583.

16036

UEndp

Marcelle, C., and J.P. Thome. 1983. Acute Toxicity and Bioaccumulation of
Lindane in Gudgeon, Gobio gobio (L.). Bull.Environ.Contam.Toxicol. 31(4):453-
458.

10088

NonRes, Eff

Marcelle, C., and J.P. Thome. 1984. Relative Importance of Dietary and
Environmental Sources of Lindane in Fish. Bull.Environ.Contam.Toxicol.
33(4):423-429.

10753

UEndp, Con

Marchal-Segault, D., and F. Ramade. 1981. The Effects of Lindane, an
Insecticide, on Hatching and Postembryonic Development of Xenopus laevis
(Daudin) Anuran Amphibian. Environ.Res. 24:250-258.

18482

UEndp

419

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Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Mathur, R., and D.M. Saxena. 1986. Effect of Hexachlorocyclohexane (HCH)
Isomers on Growth of, and Their Accumulation in, the Blue-Green Alga,
Anabaena sp. (ARM 310). J.Environ.Biol. 7(1):239-251.

12632

Con, UEndp, Eff

Mathur, R., and D.M. Saxena. 1987. Bioconcentration of HCH Isomers by the
Ciliate Protozoan, Tetrahymena pyriformis Under Laboratory Conditions. Water
Air Soil Pollut. 32(3-4):323-327.

12801

Ace, Eff, Con

Matsuo, K., and T. Tamura. 1970. Laboratory Experiments on the Effect of
Insecticides Against Blackfly Larvae (Diptera: Simuliidae) and Fishes. Sci.Pest
Control/Botyu-Kagaku 35(4): 125-130.

9634

UEndp

Maund, S.J., A. Peither, E.J. Taylor, I. Juttner, R. Beyerle-Pfnur, J.P. Lay, and D.
Pascoe. 1992. Toxicity of Lindane to Freshwater Insect Larvae in Compartments
of an Experimental Pond. Ecotoxicol. Environ.Saf. 23:76-88 (OECDG Data File).

3908

NonRes, Con

McLeay, D.J.. 1976. A Rapid Method for Measuring the Acute Toxicity of
Pulpmill Effluents and Other Toxicants to Salmonid Fish at Ambient Room
Temperature. J.Fish.Res.Board Can. 33(6):1303-1311.

2112

Con

Meliyan, R.I.. 1991. Effect of Pesticides on Reproductive Function of the
Freshwater Amphipod Gammarus kischineffensis. Hydrobiol.J.27(6):33-36 /
Gidrobiol.Zh. 27(3):107-111 (RUS).

7457

UEndp

Metcalf, R.L., I.P. Kapoor, P.Y. Lu, C.K. Schuth, and P. Sherman. 1973. Model
Ecosystem Studies of the Environmental Fate of Six Organochlorine Pesticides.
Environ.Health Perspect. 4:35-44.

740

Eff, Con

Minchew, C.D., and D.E. Ferguson. 1970. Toxicities of Six Insecticides to
Resistant and Susceptible Green Sunfish and Golden Shiners in Static
Bioassays. J.Miss.Acad.Sci. 15:29-32.

9645

Dur, Con

Mitsuhashi, J., T.D.C. Grace, and D.F. Waterhouse. 1970. Effects of Insecticides
on Cultures of Insect Cells. Entomol.Exp.Appl. 13:327-341.

2797

UEndp, Con

Moss, J.L.. 1978. Toxicity of Selected Chemicals to the Fairy Shrimp,
Streptocephalus seali, Under Laboratory and Field Conditions. Prog.Fish-Cult.
40(4): 158-160.

6248

UEndp, Pur

420

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Mostafa, I.Y., A.E. El Arab, and S.M.A. Zayed. 1987. Fate of 14C-Lindane in a
Rice-Fish Model Ecosystem. J.Environ.Sci.Health B22(2):235-243.

4471

UEndp

Mourad, M.H.. 1990. Effects of Lindane on the Electrocardiogram of Eel,
Anguilla anguilla L. Acta Ichthyol.Piscatoria 20(2):77-84.

11325

UEndp, Con

Mourad, M.H.. 1991. Cardiovascular and Respiratory Changes in Eel, Anguilla
anguilla L. During Exposure to Lethal Doses of Lindane at Different Water
Temperatures. Acta Ichthyol.Piscatoria 21(1):73-79.

6662

UEndp

Murthy, B.N., K.S. Prasad, C. Madhu, and K.V.R. Rao. 1986. Toxicity of Lindane
to Freshwater Fish Tilapia mossambica. C.A.Sel.-Environ.Pollut.4:106-45416P
(1987) / Environ.Ecol. 4(1):20-23.

12786

Dur, Con

Naqvi, S.M.Z.. 1973. Toxicity of Twenty-Three Insecticides to a Tubificid Worm
Branchiura sowerbyi From the Mississippi Delta. J.Econ.Entomol. 66(1):70-74.

2798

UEndp, Con

Neugebaur-Buchler, K.E., F.J. Zieris, and W. Huber. 1991. Reactions of an
Experimental Outdoor Pond to Lindane Application. Z.Wasser-Abwasser-Forsch.
24(2):81-92.

3806

No Org, UEndp

Nishiuchi, Y., and Y. Hashimoto. 1969. Toxicity of Pesticides to Some Fresh
Water Organisms. Rev.Plant Protec.Res. 2:137-139.

2682

Con, Dur

Oikari, A., J. Kukkonen, and V. Virtanen. 1992. Acute Toxicity of Chemicals to
Daphnia magna in Humic Waters. Sci.Total Environ. 117/118:367-377.

5679

Dur, Con

Oliver, B.G., and A.J. Niimi. 1985. Bioconcentration Factors of Some
Halogenated Organics for Rainbow Trout: Limitations in Their Use for Prediction
of Environmental Residues. Environ.Sci.Technol. 19(9):842-849.

14353

Eff

Panwar, R.S., D. Kapoor, H.C. Joshi, and R.A. Gupta. 1976. Toxicity of Some
Insecticides to the Weed Fish, Trichogaster fasciatus (Bloch and Schneider).
J.Inl.Fish.Soc.India 8:129-130.

7881

Con, Pur

20 Emulsified Concentration

421

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Panwar, R.S., R.A. Gupta, H.C. Joshi, and D. Kapoor. 1982. Toxicity of Some
Chlorinated Hydrocarbon and Organophosphorus Insecticides to Gastropod,
Viviparus bengalensis Swainson. J.Environ.Biol. 3(1):31-36.

14311

Pur, Dur

20 Emulsified Concentration

Pawar, K.R., and M. Katdare. 1983. Acute Toxicity of Sumithion, BHC and
Furadan to Some Selected Fresh Water Organisms. Biovigyanam 9:67-72.

10265

Con

Pawar, K.R., and M. Katdare. 1984. Effect of Sublethal and Lethal
Concentrations of Fenitrothion, BHC and Carbofuran on Behaviour and Oxygen
Consumption of the Freshwater Prawn. Arch.Hydrobiol. 99(3):398-403.

11445

UEndp, Dur

Persoone, G., and G. Uyttersprot. 1975. The Influence of Inorganic and Organic
Pollutants on the Rate of Reproduction of a Marine Hypotrichous Ciliate:
Euplotes vannus Muller. Rev.lnt.Oceanogr.Med. 37-38:125-151.

5922

UEndp, Ace

Peterson, R.H.. 1976. Temperature Selection of Juvenile Atlantic Salmon (Salmo
salar) as Influenced by Various Toxic Substances. J.Fish.Res.Board Can.
33(8): 1722-1730.

5160

UEndp, Dur

Ramachandran, S., N. Rajendran, R. Nandakumar, and V.K. Venugopalan.
1984. Effect of Pesticides on Photosynthesis and Respiration of Marine
Macrophytes. Aquat.Bot. 19:395-399.

10569

NonRes, Dur, Con

Ramalingam, R., and Y.S. Reddy. 1982. Kinetics of Dose-Response
Relationship in the Bimodal Respiration of Colisa lalia (Hamilton-Buchanan)
Exposed to Lindane (gamma-BHC). Water Res. 16(1 ):1 -5.

15332

NonRes, Con

Rao, K.J., C. Madhu, V.A. Rao, and K. Ramamurthy. 1984. Hyperglycemia
Induced by Insecticides in Oreochromis mossambicus (Trewavas). J.Curr.Biosci.
1 (3): 115-116.

2603

Dur, Con

Rao, P.S.B.. 1985. Lindane Induced Respiratory Changes in Juveniles of an
Estuarine Fish Therapon jarbua. Mahasagar Bull.Natl.Inst.Oceanogr. 18(3):413-
416.

14189

NonRes, UEndp

Rao, T.S., S. Dutt, and K. Mangaiah. 1967. TLM Values of Some Modern
Pesticides to the Freshwater Fish - Puntius puckelli. Environ.Health (Nagpur)
9:103-109.

6722

NonRes, Pur

422

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Reddy, M.S., and K.V.R. Rao. 1989. Effects of Phosphamidon and Lindane on
the Limb Regeneration of Penaeid Prawn, Penaeus monodon.
Bull.Environ.Contam.Toxicol. 42(1 ):154-158.

2983

NonRes, UEndp

Reddy, M.S., and K.V.R. Rao. 1992. Toxicity of Selected Insecticides to the
Penaeid Prawn, Metapenaeus monoceros (Fabricius).

Bull. Environ.Contam .Toxicol. 48(4):622-629.

14969

NonRes

Reddy, M.S., Y. Venkateswarlu, P. Surendranath, and K.V.R. Rao. 1986.
Phosphamidon and Lindane Induced Changes in the Hemolymph Biochemistry
of a Penaeid Prawn, Metapenaeus monoceros (Fabricius).
Natl.Acad.Sci.Lett.(India) 9(5):155-157.

2393

Dur, Con

Rongsriyam, Y., S. Prownebon, and S. Hirakoso. 1968. Effects of Insecticides on
the Feeding Activity of the Guppy, a Mosquito-Eating Fish, in Thailand.
Bull.W.H.O. 39:977-980.

3663

Con, Dur

Rozados, M.V., M.D. Andres, and M.A. Aldegunde. 1991. Preliminary Studies on
the Acute Effect of Lindane (gamma-HCH) on Brain Serotoninergic System in
Rainbow Trout Oncorhynchus mykiss. Aquat.Toxicol. 19(1):33-40.

3554

UEndp, Dur

Salanki, J., and I. Varanka. 1978. Effect of Some Insecticides on the Periodic
Activity of the Fresh-Water Mussel (Anodonta cygnea L.). Acta
Biol.Acad.Sci.Hung. 29(2):173-180.

7158

Dur, Pur

Sanders, H.O., and O.B. Cope. 1968. The Relative Toxicities of Several
Pesticides to Naiads of Three Species of Stoneflies. Limnol.Oceanogr.
13(1): 112-117 (Author Communication Used) (Publ in Part As 6797).

889

Dur, Con

Schulz, R., and M. Liess. 1995. Chronic Effects of Low Insecticide
Concentrations on Freshwater Caddisfly Larvae. Hydrobiologia 299(2): 103-113.

16023

NonRes, UEndp, Dur

Seuge, J., and R. Bluzat. 1979. Chronic Toxicity to Carbaryl and Lindane to the
Freshwater Mollusc Lymnea stagnalis L. Water Res. 13(3):285-293 (FRE) (ENG
ABS).

6775

UEndp, Con

Seuge, J., and R. Bluzat. 1983. Chronic Toxicity of Three Insecticides (Carbaryl,
Fenthion and Lindane) in the Freshwater Snail Lymnaea stagnalis.
Hydrobiologia 106(1):65-72.

11221

UEndp, Dur

423

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Shafiei, T.M., and H.H. Costa. 1990. The Susceptibility and Resistance of Fry
and Fingerlings of Oreochromis mossambicus Peters to Some Pesticides
Commonly used in Sri Lanka. J.Appl.lchthyol./Z.Angew.lchthyol. 6(2):73-80.

9253

Con, Dur

Sherstneva, L.A.. 1978. Effect of Some Pesticides on the Fresh Water
Crustaceans. Rybn.Khoz.(2):33-35 (RUS).

7170

UEndp, Con

Shim, J.C., and L.S. Self. 1973. Toxicity of Agricultural Chemicals to Larvivorous
Fish in Korean Rice Fields. Trop.Med. 15(3): 123-130.

8977

Dur, Con

Singh, P.B., and D.E. Kime. 1994. In Vivo Incorporation of [1-14C]Acetic Acid
into Liver Lipids of Goldfish, Carassius auratus, During gamma-
Hexachlorocyclohexane Exposure. Aquat.Toxicol. 30(3):237-248.

17568

UEndp

Singh, P.B., and T.P. Singh. 1992. Impact of Malathion and gamma-BHC on
Steroidogenesis in the Freshwater Catfish, Heteropmeustes fossilis.
Aquat.Toxicol. 22:69-80.

5064

NonRes

Singh, P.B., D.E. Kime, and T.P. Singh. 1993. Modulatory Actions of Mystus
Gonadotropin on gamma-BHC-lnduced Histological Changes, Cholesterol, and
Sex Steroid Levels in Heteropneustes fossilis. Ecotoxicol.Environ.Saf. 25:141-
153.

6653

NonRes, UEndp

Singh, P.B., D.E. Kime, P. Epler, and J. Chyb. 1994. Impact of gamma-
Hexachlorocyclohexane Exposure on Plasma Gonadotropin Levels and In Vitro
Stimulation of Gonadal Steroid Production by Carp Hypophyseal Homogenate in
Carassius auratus. J.Fish Biol. 44(2):195-204.

65305

UEndp

Singh, S., and S. Sahai. 1984. Histopathological Changes in the Gills of Rasbora
daniconius Induced by gamma-BHC. J.Environ.Biol. 5(2):65-69.

10793

UEndp, Con

Singh, S., and T.P. Singh. 1987. Evaluation of Toxicity Limit and Sex Hormone
Production in Response to Cythion and BHC in the Vitellogenic Catfish Clarias
batrachus. Environ.Res. 42(2):482-488.

12689

Con

Sugiura, K.. 1992. A Multispecies Laboratory Microcosm for Screening
Ecotoxicological Impacts of Chemicals. Environ.Toxicol.Chem. 11:1217-1226.

3972

UEndp, No Org

424

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Taylor, E.J., J.E. Morrison, S.J. Blockwell, A. Tarr, and D. Pascoe. 1995. Effects
of Lindane on the Predator-Prey Interaction Between Hydra oligactis Pallas and
Daphnia magna Strauss. Arch.Environ.Contam.Toxicol. 29(3):291-296.

14928

UEndp

Taylor, E.J., S.J. Blockwell, S.J. Maund, and D. Pascoe. 1993. Effects of
Lindane on the Life-Cycle of a Freshwater Macroinvertebrate Chironomus
riparius Meigen (Insecta: Diptera). Arch.Environ.Contam.Toxicol. 24(2):145-150.

6689

NonRes, UEndp, LT

Thybaud, E.. 1990. Toxicite Aigue et Bioconcentration du Lindane et de la
Deltamethrine par les Tetards de Rana temporaria et les Gambusies (Gambusia
affinis). Hydrobiologia 190(2): 137-145 (FRE) (ENG ABS).

761

UEndp

Thybaud, E., and S. Le Bras. 1988. Absorption and Elimination of Lindane by
Asellus aquaticus (Crustacea, Isopoda). Bull.Environ.Contam.Toxicol. 40(5):731-
735.

6052

Eff, Con

Thybaud, E., and T. Caquet. 1991. Uptake and Elimination of Lindane by
Lymnaea-palustris (Mollusca: Gastropoda): A Pharmacokinetic Approach.
Ecotoxicol.Environ.Saf. 21(3):365-376.

9318

Eff, Con

Tidou, A.S., J.C. Moreteau, and F. Ramade. 1992. Effects of Lindane and
Deltamethrin on Zooplankton Communities of Experimental Ponds.
Hydrobiologia 232(2):157-168.

6042

UEndp, No Org

Tsuji, S., Y. Tonogai, Y. Ito, and S. Kanoh. 1986. The Influence of Rearing
Temperatures on the Toxicity of Various Environmental Pollutants for Killifish
(Oryzias latipes). J.Hyg.Chem./Eisei Kagaku 32(1):46-53 (JPN) (ENG ABS).

12497

Con, Dur

Twagilimana, L., J. Bohatier, C.A. Groliere, F. Bonnemoy, and D. Sargos. 1998.
A New Low-Cost Microbiotest with the Protozoan Spirostomum teres: Culture
Conditions and Assessment of Sensitivity of the Ciliate to 14 Pure Chemicals.
Ecotoxicol.Environ.Saf. 41(3):231-244.

20057

Ace, Dur

Udoidiong, O.M., and P.M. Akpan. 1991. Toxicity of Cadmium, Lead and
Lindane to Egeria radiata Lamarck (Lamellibranchia, Donacidae).
Rev.Hydrobiol.Trop. 24(2): 111-117.

8515

NonRes, Pur

Emulsified Concentration

425

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Varanka, 1.. 1977. The Effect of Some Pesticides on the Rhythmic Activity of
Adductor Muscle of Fresh-Water Mussel Larvae. Acta Biol.Acad.Sci.Hung.
28(3):317-332.

6065

Dur, Con

Varanka, I.. 1979. Effect of Some Pesticides on the Rhythmic Adductor Muscle
Activity of Fresh-Water Mussel Larvae. Symp.Biol.Hung. 19:177-196.

7285

Dur, Con

Veith, G.D., D.L. De Foe, and B.V. Bergstedt. 1979. Measuring and Estimating
the Bioconcentration Factor of Chemicals in Fish. J.Fish.Res.Board Can.
36(9): 1040-1048 (April 14, 1980 G.D.Veith Memo to C.E.Stephan, U.S.EPA,
Duluth, MN) (Feb.7, 1980 D.L.Defoe Memo to W.A.Brungs, U.S.EPA, Duluth,
MN) (Author Communication Used) (OECDG Data File).

616

Eff, Con

Verma, S.R., I.P. Tonk, A.K. Gupta, and M. Saxena. 1984. Evaluation of an
Application Factor for Determining the Safe Concentration of Agricultural and
Industrial Chemicals. Water Res. 18(1 ):111 -115.

10575

Con, Pur

20 Emulsified Concentration

Verma, S.R., S.K. Bansal, A.K. Gupta, N. Pal, A.K. Tyagi, M.C. Bhatnagar, V.
Kumar, and R.C. Dalela. 1982. Bioassay Trials with Twenty Three Pesticides to
a Fresh Water Teleost, Saccobranchus fossilis. Water Res. 16(5):525-529.

15179

NonRes, Pur

20 Emulsified Concentration

Verma, S.R., S.P. Gupta, and M.P. Tyagi. 1975. Studies on the Toxicity of
Lindane on Colisa fasciatus (Part I: TLM Measurements and Histopathological
Changes in Certain Tissues). Gegenbaurs Morphol.Jahrb. 121(1):38-54.

8463

Con, Pur

Vigano, L., S. Galassi, and M. Gatto. 1992. Factors Affecting the
Bioconcentration of Hexachlorocyclohexanes in Early Life Stages of
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5884

Eff, Con

Virtanen, V., J. Kukkonen, and A. Oikari. 1989. Acute Toxicity of Organic
Chemicals to Daphnia magna in Humic Waters. In: A.Oikari (Ed.), Nordic
Symposium on Organic Environmental Chemicals, University of Joensuu,
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16674

48 h LC50 = 1790 ug/L. Test was
static, unmeasured.

This study appears to provide an
appropriate 48 h LC50 for D. magna,
but the paper should be secured to
ensure acceptability. Species is
insensitive to acute lindane
exposure.

Vranken, G., R. Vandergaeghen, and C. Heip. 1991. Effects of Pollutants on
Life-History Parameters of the Marine Nematode Monhystera disjuncta. ICES J
Mar Sci 48:325-334.

7215

Con

426

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Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Wellborn, T.L.J.. 1971. Toxicity of Some Compounds to Striped Bass
Fingerlings. Prog.Fish-Cult. 33(1):32-36.

966

Con

Whitten, B.K., and C.J. Goodnight. 1966. Toxicity of Some Common Insecticides
to Tubificids. J.Water Pollut.Control Fed. 38(2):227-235.

8046

Con, No Org

Wiger, R.. 1985. Variability of Lindane Toxicity in Tetrahymena pyriformis with
Special Reference to Liposomal Lindane and the Surfactant Tween 80.
Bull.Environ.Contam.Toxicol. 35(4):452-459.

11665

Ace, Dur

Zambriborshch, F.C., and B. Lai. 1978. Effect of Hexachloran on Oxygen
Consumption of Neogobius melanostomus and Neogobius fluviatilis.
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7225

NonRes, Pur

Zambriborshch, F.S., and B. Lai. 1976. The Effect of Hexachloran on the
Variability of Macropodus opercularis. Gidrobiol.Zh. 12(1 ):118-121 (RUS).

5874

Dur

Zambriborshch, F.S., and B. Lay. 1976. The Effect of Hexachlorane
(Hexachlorocyclohexane [HCCH]) and Chlorophos on Underyearlings of the
Leaping Gray Mullet Mugil saliens. J.lchthyol.16(5):841 -847;
Vopr.lkhtiol.16(5):3930 (RUS).

7418

NonRes, Con, Pur

Zayapragassarazan, A., and V. Anandan. 1996. Effect of gamma-HCH on the
Protein Profiles of Selected Tissues of the Air-Breathing Fish Anabas
testudineus (Bloch). Environ.Ecol. 14(1):55-59.

18184

NonRes

Zou, E., and M. Fingerman. 1997. Effects of Estrogenic Xenobiotics on Molting
of the Water Flea, Daphnia magna. Ecotoxicol.Environ.Saf. 38(3):281-285.

18976

Dur

2456

UEndp, Dur, Con, Pur

Ref # only given

Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

3) For the studies that were not utilized, but the most representative SMAV/2 fell below the criterion, or, if the studies
were for a species associated with one of the four most sensitive genera used to calculate the FAY in the most recent

427

-------
national ambient water quality criteria dataset used to derive the CMC86, EPA is providing a transparent rationale as to
why they were not utilized (see below).

General QA/QC failure because non-resident species in Oregon

The test with the following species was used in the EPA BE of OR WQS for lindane in freshwater, but was not considered in the
CWA review and approval/disapproval action of the standards because this species does not have a breeding wild population in
Oregon's waters:

Asellus

brevicaudus

Aquatic sowbug

Mayer and Ellersieck 1986

Clarias

batrachus

Walking catfish

Kudesia and Bali 1984

Other Acute tests failins QA/QC by species
Clarias batrachus - Walking catfish

The following tests were included in EPA's BE of the OR WQS for lindane in freshwater, but were not used in this CWA review and
approval/disapproval action of these standards because the purity of the chemical was too low:

Kudesia, V.P. and N.P. Bali. 1984. Study of pesticides in Kalinadi River and evaluation of toxicity of some pesticides on fish
Clarias batrachus. Acta Ciencia Indica 10(4): 245-254.

Purity was 68.38%. This also uses a non-resident species. This was the only study for this species, and the SMAV/2 would have
fallen below the CMC had this study been used.

86 U.S. EPA. 1980. Ambient Water Quality Criteria for Hexachlorocyclohexane. EPA-440/5-80-054.

428

-------
Appendix J Nickel (freshwater)
Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Abraham, T.J., K.Y.M. Salih, and J. Chacko. 1986. Effects of Heavy Metals on the
Filtration Rate of Bivalve Villorita cyprinoides (Hanley) Var. Cochinensis. Indian
J.Mar.Sci. 15(3): 195-196.

12315

Con, AF

Agrawal, S.J., A.K. Srivastava, and H.S. Chaudhry. 1979. Haematological Effects of
Nickel Toxicity on a Fresh Water Teleost, Colisa fasciatus. Acta Pharmacol.Toxicol.
45(3):215-217.

15705

Con, UEndp

Alam, M.K., and O.E. Maughan. 1992. The Effect of Malathion, Diazinon, and Various
Concentrations of Zinc, Copper, Nickel, Lead, Iron, and Mercury on Fish. Biol.Trace
Elem.Res. 34(3):225-236.

7085

Alam, M.K., and O.E. Maughan. 1995. Acute Toxicity of Heavy Metals to Common
Carp (Cyprinus carpio). J.Environ.Sci.Health Part A 30(8): 1807-1816.

45566

AF, UEndp

Better data used in CORE

Alikhan, M.A., and S. Zia. 1989. Nickel Uptake and Regulation in a Copper-Tolerant
Decapod, Cambarus bartoni (Fabricus) (Decapoda, Crustacea).
Bull.Environ.Contam.Toxicol. 42(1 ):94-102.

621

UEndp, AF

Alikhan, M.A., G. Bagatto, and S. Zia. 1990. The Crayfish as a "Biological Indicator" of
Aquatic Contamination by Heavy Metals. Water Res. 24(9):1069-1076.

9117

UEndp, AF

Alkahem, H.F.. 1994. The Toxicity of Nickel and the Effects of Sublethal Levels on
Haematological Parameters and Behaviour of the Fish, Oreochromis niloticus.
J.Univ.Kuwait Sci. 21(2):243-251.

16861

Alkahem, H.F.. 1995. Effects of Nickel on Carbohydrate Metabolism of Oreochromis
niloticus. Dirasat (Pure Appl.Sci.) 22 B(1):83-88.

20533

Anderson, B.G.. 1948. The Apparent Thresholds of Toxicity to Daphnia magna for
Chlorides of Various Metals when Added to Lake Erie Water. Trans.Am.Fish.Soc.
78:96-113.

2054

AF, Dur

429

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Anderson, D.R.. 1981. The Combined Effects of Nickel, Chlorine and Temperature on
the Mortality of Rainbow Trout, Salmo gairdneri. Ph.D.Thesis, University of
Washington, Seattle, WA :202.

3710

96 h LC50 approx. 25700 ug/L dissolved
nickel normalized to 100 mg/L as CaC03
hardness. Test was flow-through,
measured.

This study appears to
provide an appropriate 96 h
LC50 for Oncorhynchus
mykiss, but the paper should
be secured to ensure
acceptability. Species is
relatively insensitive to acute
nickel exposure

Anderson, P.D., and L.J. Weber. 1975. Toxic Response As a Quantitative Function of
Body Size. Toxicol.Appl.Pharmacol. 33(3):471-483.

2137

96 h LC50 approx. 8030 ug/L dissolved
nickel normalized to 100 mg/L as CaC03
hardness. Test was flow-through,
measured.

This study appears to
provide an appropriate 96 h
LC50 for Poecilia reticulata,
but the paper should be
secured to ensure
acceptability. Species is
relatively insensitive to acute
nickel exposure

Angadi, S.B., and P. Mathad. 1994. Effect of Chromium and Nickel on Scenedesmus
quadricauda (Turp.) de Breb. Phykos 33(1/2):99-103.

17433

UEndp, AF

Angadi, S.B., S. Hiremath, and S. Pujari. 1996. Toxicity of Copper, Nickel, Manganese
and Cadmium on Cyanobacterium Hapalosiphon stuhlmannii. J.Environ.Biol.
17(2): 107-113.

17771

UEndp, AF

Azeez, P.A., and D.K. Banerjee. 1987. Influence of Light on Chlorophyll, a Content of
Blue-Green Algae Treated with Heavy Metals. Bull.Environ.Contam.Toxicol.
38(6): 1062-1069.

12558

UEndp, AF, Dur

Azeez, P.A., and D.K. Banerjee. 1991. Nickel Uptake and Toxicity in Cyanobacteria.
Toxicol.Environ.Chem. 30:43-50.

4167

Bardeggia, M., and M.A. Alikhan. 1991. The Relationship Between Copper and Nickel
Levels in the Diet, and Their Uptake and Accumulation by Cambarus bartoni
(Fabricius) (Decapoda, Crustacea). Water Res. 25(10):1187-1192.

5234

UEndp, AF

Baudouin, M.F., and P. Scoppa. 1974. Acute Toxicity of Various Metals to Freshwater
Zooplankton. Bull.Environ.Contam.Toxicol. 12(6):745-751.

5339

Becker, C.D., and M.G. Wolford. 1980. Thermal Resistance of Juvenile Salmonids
Sublethally Exposed to Nickel, Determined by the Critical Thermal Maximum Method.
Environ.Pollut. 21 (3):181-189.

478

UEndp, Con

430

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Bentley, R.E., T. Heitmuller, B.H. Sleight III, and P.R. Parrish. 1975. Acute Toxicity of
Nickel to Bluegill (Lepomis macrochirus), Rainbow Trout (Salmo gairdneri), and Pink
Shrimp (Penaeus duorarum). U.S.EPA, Criteria Branch, WA-6-99-1414-B,
Washington, D.C ,:14.

3779

Con, Dur

Birge, W.J.. 1978. Aquatic Toxicology of Trace Elements of Coal and Fly Ash. In:
J.H.Thorp and J.W.Gibbons (Eds.), Dep.Energy Symp.Ser., Energy and
Environmental Stress in Aquatic Systems, Augusta, GA 48:219-240.

5305

Dur

Birge, W.J., J.A. Black, A.G. Westerman, and J.E. Hudson. 1980. Aquatic Toxicity
Tests on Inorganic Elements Occurring in Oil Shale. In: C.Gale (Ed.), EPA-600/9-80-
022, Oil Shale Symposium: Sampling, Analysis and Quality Assurance, March 1979,
U.S.EPA, Cincinnati, OH :519-534 (U.S.NTIS PB80-221435).

11838

Dur

Birge, W.J., J.A. Black, and A.G. Westerman. 1979. Evaluation of Aquatic Pollutants
Using Fish and Amphibian Eggs as Bioassay Organisms. In: S.W.Nielsen, G.Migaki,
and D.G.Scarpelli (Eds.), Symp.Animals Monitors Environ.Pollut., 1977, Storrs, CT
12:108-118.

4943

Dur

Birge, W.J., J.E. Hudson, J.A. Black, and A.G. Westerman. 1978. Embryo-Larval
Bioassays on Inorganic Coal Elements and in Situ Biomonitoring of Coal-Waste
Effluents. In: Symp.U.S.Fish Wildl.Serv., Surface Mining Fish Wildl.Needs in Eastern
U.S., W.VA:97-104.

6199

Dur

Blaise, C., R. Legault, N. Bermingham, R. Van Coillie, and P. Vasseur. 1986. A
Simple Microplate Algal Assay Technique for Aquatic Toxicity Assessment.
Toxic. Assess. 1:261-281.

12748

Con, AF

Blaylock, B.G., and M.L. Frank. 1979. A Comparison of the Toxicity of Nickel to the
Developing Eggs and Larvae of Carp (Cyprinus carpio). Bull.Environ.Contam.Toxicol.
21 (4/5):604-611.

5364

Eff, Con, Dur

Bogaerts, P., J. Senaud, and J. Bohatier. 1998. Bioassay Technique Using
Nonspecific Esterase Activities of Tetrahymena pyriformis for Screening and
Assessing Cytotoxicity of Xenobiotics. Environ.Toxicol.Chem. 17(8): 1600-1605.

18353

UEndp, Dur, AF

431

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Bornatowicz, N.. 1983. Assessment of the Acute Toxicity of Nickel Sulfate to Rainbow
Trout (Bestimmung der Akuten Toxizitact von NiS04 an Regenbogenforellen).
Oesterreichisches Forschungszentrum Seibersdorf, G.m.b.H.lnst.fuer Biologie,
Germany:22 p.(GER) (ENG ABS) (U.S.NTIS PB-84232073).

17276

Dur, AF

Boutet, C., and C. Chaisemartin. 1973. Specific Toxic Properties of Metallic Salts in
Austropotamobius pallipes pallipes and Orconectes limosus. C.R.Soc.Biol.(Paris)
167(12):1933-1938 (FRE) (ENG TRANSL).

5421

Con, AF

Bringmann, G., and R. Kuhn. 1959. The Toxic Effects of Waste Water on Aquatic
Bacteria, Algae, and Small Crustaceans. Tr-Ts-0002; Gesund.lng.80:115-120
53:17390G-(GER)(ENG TRANSL).

607

UEndp, AF

Bringmann, G., and R. Kuhn. 1959. Water Toxicological Studies with Protozoa as Test
Organisms. TR-80-0058, Literature Research Company:13 p.; Gesund.-lng.80:239-
242 (GER); Chem.Abstr. 53:22630D-(GER)(ENG TRANSL).

2394

UEndp, Dur

Bringmann, G., and R. Kuhn. 1977. The Effects of Water Pollutants on Daphnia
magna. Wasser-Abwasser-Forsch. 10(5):161-166(ENG TRANSL)(OECDG Data
File)(GER)(ENG ABS).

5718

Dur, Con

Bringmann, G., and R. Kuhn. 1978. Investigation of Biological Harmful Effects of
Chemical Substances Which are Classified as Dangerous for Water on Protozoa.
Z.Wasser-Abwasser-Forsch.11 (6):210-215, TR-80-0307, Literature Research
Company :13 p. (ENG TRANSL) (OECDG Data File).

6601

UEndp, AF

Brown, V.M., and R.A. Dalton. 1970. The Acute Lethal Toxicity to Rainbow Trout of
Mixtures of Copper, Phenol, Zinc and Nickel. J.Fish Biol. 2(3):211-216.

6202

Dur, Con

Buikema, A.L.J., J. Cairns Jr., and G.W. Sullivan. 1974. Evaluation of Philodina
acuticornis (Rotifera) as Bioassay Organisms for Heavy Metals. Water
Resour.Bull.Am.Water Res.Assoc. 10(4):648-661.

2019

NonRes

432

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Calamari, D., G.F. Gaggino, and G. Pacchetti. 1982. Toxicokinetics of Low Levels of
Cd, Cr, Ni and Their Mixture in Long-Term Treatment on Salmo gairdneri Rich.
Chemosphere 11(1):59-70.

15454

Eff, Con

Calgan, D.T., and 0. Yenigun. 1996. Toxicity of Arsenic, Cadmium and Nickel on the
Cyanobacterium Anabaena cylindrica. Environ.Technol. 17(5):533-540.

19504

UEndp, AF

Better data used in CORE

Campbell, P.M., and G.D. Smith. 1986. Transport and Accumulation of Nickel Ions in
the Cyanobacterium Anabaena cylindrica. Arch.Biochem.Biophys. 244:470-477.

17265

UEndp, AF

Chapman, G.A., S. Ota, and F. Recht. 1980. Effects of Water Hardness on the
Toxicity of Metals to Daphnia magna. U.S.EPA, Corvallis, OR:17 p.(Author
Communication Used).

3621

Con

Chaudhry, H.S.. 1984. Nickel Toxicity on Carbohydrate Metabolism of a Freshwater
Fish, Colisa fasciatus. Toxicol.Lett. 20(1): 115-121.

10057

UEndp, Dur

Chong, A.M.Y., Y.S. Wong, and N.F.Y. Tam. 2000. Performance of Different
Microalgal Species in Removing Nickel and Zinc from Industrial Wastewater.
Chemosphere 41 (1/2):251-257.

48217

UEndp, Dur, AF

Dave, G., and R. Xiu. 1991. Toxicity of Mercury, Copper, Nickel, Lead, and Cobalt to
Embryos and Larvae of Zebrafish, Brachydanio rerio. Arch.Environ.Contam.Toxicol.
21:126-134.

3680

Dur

El Hissy, F.T., A.M. Khallil, and A.M. Abdel-Raheem. 1993. Effect of Some Heavy
Metals on the Mycelial Growth of Achlya racemosa and Alatospora acuminata.
Zentralbl.Mikrobiol. 148(8):535-542.

13857

UEndp, AF

Ellis, M.M.. 1937. Detection and Measurement of Stream Pollution. In:
Bull.Bur.Fish.No.22, U.S.Dep.Commerce, Washington, D.C. :365-437.

916

UEndp, Dur, AF

Enserink, E.L., J.L. Maas-Diepeveen, and C.J. Van Leeuwen. 1991. Combined Effects
of Metals; An Ecotoxicological Evaluation. Water Res. 25(6):679-687.

45212

Dur

Ewell, W.S., J.W. Gorsuch, R.O. Kringle, K.A. Robillard, and R.C. Spiegel. 1986.
Simultaneous Evaluation of the Acute Effects of Chemicals on Seven Aquatic
Species. Environ.Toxicol.Chem. 5(9):831-840.

11951

Con, AF

433

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Fezy et al. 1979

Gavrilenko, Y.Y., and Y.Y. Zolotukhina. 1989. Accumulation and Interaction of
Copper, Zinc, Manganese, Cadmium, Nickel and Lead Ions Absorbed by Aquatic
Macrophytes. Hydrobiol.J. 25(5):54-61.

9369

UEndp, AF

Genin-Durbert, C., Y. Champetier, and P. Blazy. 1988. Metallic Bioaccumulation in
Aquatic Plants. (Bioaccumulation des Metaux Dans les Vegetaux Aquatiques).
C.R.Acad.Sci.Ser.lll 307:1875-1877 (FRE) (ENG ABS).

UEndp, Con, AF

Gerhards, U., and H. Weller. 1977. The Uptake of Mercury, Cadmium and Nickel by
Chlorella pyrenoidosa (Die Aufnahme von Quecksilber, Cadmium und Nickel durch
Chlorella pyrenoidosa). Z.Pflanzenphysiol.82:292-300 (GER) (ENG ABS).

14113

UEndp, Dur, AF

Gill, T.S., and J.C. Pant. 1981. Toxicity of Nickel to the Fish Puntius conchonius
(Ham.) and its Effects on Blood Glucose and Liver Glycogen. Comp.Physiol.Ecol.
6(2):99-102.

15423

Dur, Con

Goettl, J.P.J., J.R. Sinley, and P.H. Davies. 1974. Water Pollution Studies. Job
Progress Report, Federal Aid Project F-33-R-9, DNR, Boulder, CO :96 p..

285

UEndp, Dur, AF

Gottofrey, J., K. Borg, S. Jasim, and H. Tjaelve. 1988. Effect of Potassium
Ethylxanthate and Sodium Diethyldithiocarbamate on the Accumulation and
Disposition of Nickel in the Brown Trout (Salmo. Pharmacol.Toxicol. 63:46-51.

13087

UEndp, Con, AF

Gray, B.R., and W.R. Hill. 1995. Nickel Sorption by Periphyton Exposed to Different
Light Intensities. J.N.Am.Benthol.Soc. 14(2):299-305.

14887

UEndp, AF

Gupta, P.K., B.S. Khangarot, and V.S. Durve. 1981. Studies on the Acute Toxicity of
Some Heavy Metals to an Indian Freshwater Pond Snail Viviparus bengalensis L.
Arch.Hydrobiol. 91(2):259-264 (Publ in Part as 15716).

15745

Con

Hale, J.G. 1977. Toxicity of Metal Mining Wastes. Bull.Environ.Contam.Toxicol.
17(1 ):66-73.

861

434

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Hall, T.. 1978. Nickel Uptake, Retention and Loss in Daphnia magna. M.S.Thesis,
University of Toronto, Toronto, Ontario, Canada :205 p..

9867

AF, Eff, UEndp, Dur

Herkovits, J., C.S. Perez-Coll, and F.D. Herkovits. 2000. Evaluation of Nickel-Zinc
Interactions by Means of Bioassays with Amphibian Embryos. Ecotoxicol.Environ.Saf.
45(3):266-273.

50151

Hiraoka, Y., S. Ishizawa, T. Kamada, and H. Okuda. 1985. Acute Toxicity of 14
Different Kinds of Metals Affecting Medaka Fry. Hiroshima J.Med.Sci. 34(3):327-330.

12151

UEndp, Dur

Hutchinson 1973

Janauer, G.A.. 1985. Heavy Metal Accumulation and Physiological Effects on Austrian
Macrophytes. Symp.Biol.Hung. 29:21-30.

16938

UEndp, AF

Jaworska, M., A. Gorczyca, J. Sepiol, and P. Tomasik. 1997. Effect of Metal Ions on
the Entomopathogenic Nematode Heterorhabditis bacteriophora Poinar (Nematode:
Heterohabditidae) Under Laboratory Conditions. Water Air Soil Pollut. 93:157-166.

40155

UEndp, AF

Jennett, J.C., J.E. Smith, and J.M. Hassett. 1982. Factors Influencing Metal
Accumulation by Algae. EPA 600/2-82-100, U.S.EPA, Cincinnati, OH :133 p..

14512

UEndp, Dur, AF

Jha, M.M., A.K. Jha, and B.S. Jha. 1994. Testicular Injury Under Chronic Stress of
Nickel Chloride in the Freshwater Climbing Perch, Anabas testudineus.
J.Ecotoxicol.Environ.Monit. 4(2):127-131.

17574

UEndp, AF

Jin, X., C. Nalewajko, and D.J. Kushner. 1996. Comparative Study of Nickel Toxicity
to Growth and Photosynthesis in Nickel-Resistant and -Sensitive Strains of
Scenedesmus acutusf. alternans. Microb.Ecol. 31(1): 103-114.

8576

AF, Dur

Jones, J.R.E.. 1939. The Relation Between the Electrolytic Solution Pressures of the
Metals and Their Toxicity to the Stickleback (Gasterosteus aculeatus L.). J.Exp.Biol.
16(4):425-437.

2851

UEndp, Con, AF

Jones, J.R.E.. 1940. A Further Study of the Relation Between Toxicity and Solution
Pressure, with Polycelis nigra As Test Animal. J.Exp.Biol. 17:408-415.

10012

UEndp, Con, AF

435

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Kabila, V., P.S. Bhavan, and P. Geraldine. 1999. The Freshwater Prawn
Macrobrachium malcolmsonii - an Accumulator of Nickel?. J.Environ.Biol. 20(4):307-
312.

50767

UEndp, Dur

Kahkonen, M.A., and T. Kairesalo. 1998. The Effects of Nickel on the Nutrient Fluxes
and on the Growth of Elodea canadensis. Chemosphere 37(8):1521-1530.

19822

UEndp, AF

Khangarot, B.S., and P.K. Ray. 1987. Sensitivity of Toad Tadpoles, Bufo
melanostictus (Schneider), to Heavy Metals. Bull.Environ.Contam.Toxicol. 38(3):523-
527.

12339

NonRes, Con

Khangarot, B.S., and P.K. Ray. 1988. Sensitivity of Freshwater Pulmonate Snails,
Lymnaea luteola L., to Heavy Metals. Bull.Environ.Contam.Toxicol. 41 (2):208-213.

12943

NonRes, Con

Khangarot, B.S., S. Mathur, and V.S. Durve. 1982. Comparative Toxicity of Heavy
Metals and Interaction of Metals on a Freshwater Pulmonate Snail Lymnaea
acuminata (Lamarck). Acta Hydrochim.Hydrobiol. 10(4):367-375.

11099

NonRes, Con

Khangarot, B.S.. 1981. Lethal Effects of Zinc and Nickel on Freshwater Teleosts. Acta
Hydrochim.Hydrobiol. 9(3):297-302.

15138

Dur

Khangarot, B.S., and P.K. Ray. 1989. Investigation of Correlation Between
Physicochemical Properties of Metals and Their Toxicity to the Water Flea Daphnia
magna Straus. Ecotoxicol.Environ.Saf. 18(2):109-120.

6631

Dur, Con, AF

Khangarot, B.S., and P.K. Ray. 1990. Acute Toxicity and Toxic Interaction of
Chromium and Nickel to Common Guppy Poecilia reticulata (Peters).

Bull. Environ.Contam .Toxicol. 44(6):832-839.

3276

Con, AF

Khangarot, B.S., and V.S. Durve. 1982. Note on the Acute Toxicity of Zinc, and the
Interactions of Zinc and Nickel to a Freshwater Teleost Channa punctatus (Bloch).
Indian J.Anim.Sci. 52(8):722-725.

11083

NonRes, Con

Khangarot, B.S., V.S. Durve, and V.K. Rajbanshi. 1981. Toxicity of Interactions of
Zinc-Nickel, Copper-Nickel and Zinc-Nickel-Copper to a Freshwater Teleost, Lebistes
reticulatus (Peters). Acta Hydrochim.Hydrobiol. 9(5):495-503.

10343

Dur

436

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Klerks, P.L., and P.C. Fraleigh. 1997. Uptake of Nickel and Zinc by the Zebra Mussel
Dreissena polymorphs. Arch.Environ.Contam.Toxicol. 32(2):191-197.

17850

UEndp, Dur, AF

Kszos, L.A., A.J. Stewart, and P.A. Taylor. 1992. An Evaluation of Nickel Toxicity to
Ceriodaphnia dubia and Daphnia magna in a Contaminated Stream and in Laboratory
Tests. Environ.Toxicol.Chem. 11 (7): 1001-1012.

5920

UEndp

Kuhn, R., and M. Pattard. 1990. Results of the Harmful Effects of Water Pollutants to
Green Algae (Scenedesmus subspicatus) in the Cell Multiplication Inhibition Test.
Water Res. 24(1):31-38 (OECDG Data File).

2997

Kuhn, R., M. Pattard, K. Pernak, and A. Winter. 1989. Results of the Harmful Effects
of Water Pollutants to Daphnia magna in the 21 Day Reproduction Test. Water Res.
23(4):501-510 (OECDG Data File).

847

AF, Dur

Kumar, N., and K. Nath. 1987. Toxicity of Nickel to a FreshWater Teleost, Colisa
fasciatus. Acta Hydrochim.Hydrobiol. 15(3):313-315.

12577

Lee, C.L., T.C. Wang, C.H. Hsu, and A.A. Choiu. 1998. Heavy Metals Sorption by
Aquatic Plants in Taiwan. Bull.Environ.Contam.Toxicol. 61:497-504.

19419

Eff, AF

Lopez, J., M.D. Vazquez, and A. Carballeira. 1994. Stress Responses and Metal
Exchange Kinetics Following Transplant of the Aquatic Moss Fontinalis antipyretica.
Freshw.Biol. 32:185-198.

45134

UEndp, AF

Madoni, P.. 2000. The Acute Toxicity of Nickel to Freshwater Ciliates. Environ.Pollut.
109(1):53-59.

51792

Ace, Dur

Migliore, L., and M. Nicola Giudici. 1990. Toxicity of Heavy Metals to Asellus
aquaticus (L.) (Crustacea, Isopoda). Hydrobiologia 203(3):155-164.

10515

Con, AF

Better data used in CORE

Munzinger, A.. 1990. Effects of Nickel on Daphnia magna During Chronic Exposure
and Alterations in the Toxicity to Generations Pre-Exposed to Nickel. Water Res.
24(7):845-852.

3063

UEndp, AF

437

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Munzinger, A.. 1994. The Influence of Nickel on Population Dynamics and on Some
Demographic Parameters of Daphnia magna. Hydrobiologia 277(2):107-120.

13952

UEndp

Better data used in CORE

Munzinger, A., and F. Monicelli. 1991. A Com parison of the Sensitivity of Three
Daphnia magna Populations Under Chronic Heavy Metal Stress.
Ecotoxicol.Environ.Saf. 22:24-31.

3950

UEndp, AF

Muramoto, S.. 1983. Influence of Complexans (NTA,EDTA) on the Toxicity of Nickel
Chloride and Sulfate to Fish at High Concentrations. J.Environ.Sci.Health A18(6):787-
795.

10773

UEndp, AF

Mwangi, S.M., and M.A. Alikhan. 1993. Cadmium and Nickel Uptake by Tissues of
Cambarus bartoni (Astacidae, Decapoda, Crustacea): Effects on Copper and Zinc
Stores. Water Res. 27(5):921-927.

6986

UEndp, Dur

Nalecz-Jawecki, G., and J. Sawicki. 1998. Toxicity of Inorganic Compounds in the
Spirotox Test: A Miniaturized Version of the Spirostomum ambiguum Test.

Arch. Environ.Contam .Toxicol. 34( 1): 1 -5.

18997

Ace, Dur

Nanda, P., B.N. Panda, and M.K. Behera. 2000. Nickel Induced Alterations in Protein
Level of Some Tissues of Heteropneustes fossilis. J.Environ.Biol. 21 (2):117-119.

52565

NonRes, AF

Nath, K., and N. Kumar. 1989. Nickel-Induced Histopathological Alterations in the Gill
Architecture of a Tropical Freshwater Perch, Colisa fasciatus (Bloch and Schn.).
Sci.Total Environ. 80(2-3):293-296.

747

UEndp, AF

Nath, K., and N. Kumar. 1990. Gonadal Histopathology Following Nickel Intoxication
in the Giant Gaurami Colisa fasciatus (Bloch and Schneider), a Freshwater Tropical
Perch. Bull.Environ.Contam.Toxicol. 45(2):299-304.

3330

UEndp, AF

O'Neill, J.G.. 1981. The Humoral Immune Response of Salmo trutta L. and Cyprinus
carpio L. Exposed to Heavy Metals. J.Fish Biol. 19(3):297-306.

15193

UEndp, Con

Pandey, S.N., and A.K. Tripathi. 1985. The Toxicity of Nickel to Chlorella vulgaris Beij.
and Phormidium foveolarum (Mont.) Gomont. Comp.Physiol.Ecol. 10(3):117-120.

2373

UEndp, AF

438

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Patrick, R., T. Bott, and R. Larson. 1975. The Role of Trace Elements in Management
of Nuisance Growths. EPA 600/2-75-008, U.S.EPA, Corvallis, OR :250 p.(U.S.NTIS
PB-241985).

14692

UEndp, Dur

Phipps, G.L., V.R. Mattson, and G.T. Ankley. 1995. Relative Sensitivity of Three
Freshwater Benthic Macroinvertebrates to Ten Contaminants.
Arch.Environ.Contam.Toxicol. 28(3):281-286.

14907

AF, Dur

Powlesland, C., and J. George. 1986. Acute and Chronic Toxicity of Nickel to Larvae
of Chironomus riparis (Meigen). Environ.Pollut.Ser.A Ecol.Biol. 42(1):47-64.

11989

AF, Dur

Rai, L.C., and M. Raizada. 1985. Effect of Nickel and Silver Ions on Survival, Growth,
Carbon Fixation and Nitrogenase Activity in Nostoc muscorum: Regulation of Toxicity
by EDTA and. J.Gen.Appl.Microbiol. 31 (4):329-337.

13292

UEndp, AF

Rao, T.S., M.S. Rao, and S.B.S. Prasad. 1975. Median Tolerance Limits of Some
Chemicals to the Fresh Water Fish "Cyprinus carpio". Indian J.Environ.Health
17(2): 140-146.

2077

96 h LC50 approx. 14500 ug/L dissolved
nickel normalized to 100 mg/L as CaC03
hardness. Test was renewal, measured.

This study appears to
provide an appropriate 96 h
LC50 for C. carpio, but the
paper should be secured to
ensure acceptability.
Species is relatively
insensitive to acute nickel
exposure

Ray, D., and S.K. Banerjee. 1998. Hematological and Histopathological Changes in
Clarias batrachus (Linn) Exposed to Nickel and Vanadium. Environ.Ecol. 16(1 ):151 -
156.

19046

UEndp, AF

Ray, D., S.K. Banerjee, and M. Chatterjee. 1990. Bioaccumulation of Nickel and
Vanadium in Tissues of the Catfish Clarias batrachus. J.lnorg.Chem. 38(3): 169-173.

3696

UEndp, AF

Rehwoldt, R., L. Lasko, C. Shaw, and E. Wirhowski. 1973. The Acute Toxicity of
Some Heavy Metal Ions Toward Benthic Organisms. Bull.Environ.Contam.Toxicol.
10(5):291-294.

2020

Con

Saltabas, O., and G. Akcin. 1994. Removal of Chromium, Copper and Nickel by Water
Hyacinth (Eichhornia crassipes). Toxicol.Environ.Chem. 41:131-134.

14541

UEndp, AF

Santiago-Fandino, V.J.R.. 1983. The Effects of Nickel and Cadmium on the Growth
Rate of Hydra littoralis and an Assessment of the Rate of Uptake of 63Ni and 14C by
the Same Organism. Water Res. 17(8):917-923.

15786

UEndp, Dur

439

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Sauser, K.R., J.K. Liu, and T.Y. Wong. 1997. Identification of a Copper-Sensitive
Ascorbate Peroxidase in the Unicellular Green Alga Selenastrum capricornutum.
Biometals 10(3): 163-168.

19840

UEndp, AF

Saxena, O.P., and A. Parashari. 1983. Comparative Study of the Toxicity of Six Heavy
Metals to Channa punctatus. J.Environ.Biol. 4(2):91-94.

10762

NonRes

Schweiger, G.. 1957. The Toxic Action of Heavy Metals Salts on Fish and Organisms
on Which Fish Feed. Arch.Fischereiwiss. 8:54-78.

725

UEndp, Con, AF

Shcherban, E.P.. 1977. Toxicity of Some Heavy Metals for Daphnia magna Strauss,
As a Function of Temperature. Hydrobiol J.13(4):75-80 / Gidrobiol.Zh. 13(4):86-91
(RUS).

5924

UEndp, Con, AF

Snell, T.W., B.D. Moffat, C. Janssen, and G. Persoone. 1991. Acute Toxicity Tests
Using Rotifers IV. Effects of Cyst Age, Temperature, and Salinity on the Sensitivity of
Barachionus calyciflorus. Ecotoxicol.Environ.Saf. 21(3):308-317 (OECDG Data File).

9385

Dur, AF

Sornaraj, R., P. Baskaran, and S. Thanalakshmi. 1995. Effects of Heavy Metals on
Some Physiological Responses of Air-Breathing Fish Channa punctatus (Bloch).
Environ.Ecol. 13(1):202-207.

17380

Sreedevi, P., A. Suresh, B. Sivaramakrishna, B. Prabhavathi, and K.
Radhakrishnaiah. 1992. Bioaccumulation of Nickel in the Organs of the Freshwater
Fish, Cyprinus carpio, and the Freshwater Mussel, Lamellidens marginalis, Under
Lethal and Sublethal Nickel Stress. Chemosphere 24(1):29-36.

3880

UEndp, Dur, AF

Sreedevi, P., B. Sivaramakrishna, A. Suresh, and K. Radhakrishnaiah. 1992. Effect of
Nickel on Some Aspects of Protein Metabolism in the Gill and Kidney of the
Freshwater Fish, Cyprinus carpio L. Environ.Pollut. 77(1):59-63.

5829

UEndp, Dur, AF

Srivastav, R.K., S.K. Gupta, K.D.P. Nigam, and P. Vasudevan. 1994. Treatement of
Chromium and Nickel in Wastewater by Using Aquatic Plants. Water Res. 28(7): 1631-
1638.

4438

Eff, AF, UEndp

440

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Stauber, J.L., and T.M. Florence. 1987. Mechanism of Toxicity of Ionic Copper and
Copper Complexes to Algae. Mar.Biol. 94(4):511-519.

12971

UEndp, AF

Stratton, G.W., and C.T. Corke. 1979. The Effect of Mercuric, Cadmium, and Nickel
Ion Combinations on a Blue-Green Alga. Chemosphere 8(10):731-740.

15822

UEndp, AF

Stuijfzand, S.C., M.H.S. Kraak, Y.A. Wink, and C. Davids. 1995. Short-Term Effects of
Nickel on the Filtration Rate of the Zebra Mussel Dreissena polymorpha.
Bull.Environ.Contam.Toxicol. 54(3):376-381.

14958

UEndp, Dur

Sunderman, F.William Jr. 1992. Embryotoxicity and Teratogenicity of Ni2+ and Co2+
in Xenopus laevis. Science and Technology Letters :467-474.

7578

Suzuki, K.. 1959. The Toxic Influence of Heavy Metal Salts upon Mosquito Larvae.
Hokkaido Univ.J.Fac.Sci.Ser. 6(14):196-209.

2701

AF, LT

Tarzwell, C.M., and C. Henderson. 1960. Toxicity of Less Common Metals to Fishes.
Ind.Wastes 5:12.

2042

Con

Tatara, C.P., M.C. Newman, J.T. McCloskey, and P.L. Williams. 1997. Predicting
Relative Metal Toxicity with Ion Characteristics: Caenorhabditis elegans LC50.
Aquat.Toxicol. 39(3/4):279-290.

18605

Dur, AF

Tatara, C.P., M.C. Newman, J.T. McCloskey, and P.L. Williams. 1998. Use of Ion
Characteristics to Predict Relative Toxicity of Mono-, Di- and Trivalent Metal Ions:
Caenorhabditis elegans. Aquat.Toxicol. 42:255-269.

5072

Dur, AF

Thatheyus, A.J.. 1992. Behavioral Alterations Induced by Nickel and Chromium in
Common Carp Cyprinus carpio Var communis (Linn). Environ.Ecol. 10(4):911-913.

8279

Con, AF

Thomas, A.. 1915. Effects of Certain Metallic Salts upon Fishes. Trans.Am.Fish.Soc.
44:120-124.

2865

UEndp, AF

Tjalve, H., J. Gottofrey, and K. Borg. 1988. Bioaccumulation, Distribution and
Retention of 63Ni2+ in the Brown Trout (Salmo trutta). Water Res. 22(9):1129-1136.

13242

Eff, Con, AF

441

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Van Hoof, F., and J.P. Nauwelaers. 1984. Distribution of Nickel in the Roach (Rutilus
rutilus L.) After Exposure to Lethal and Sublethal Concentrations. Chemosphere
13(9): 1053-1058.

10671

UEndp, Dur, AF

Vazquez, M.D., J. Lopez, and A. Carballeira. 1999. Uptake of Heavy Metals to the
Extracellular and Intracellular Compartments in Three Species of Aquatic Bryophyte.
Ecotoxicol. Environ. Saf. 44(1): 12-24.

20585

UEndp, Dur, AF

Verma, S.R., M. Jain, and R.C. Dalela. 1982. A Laboratory Study to Assess Separate
and In-Combination Effects of Zinc, Chromium and Nickel to the Fish Mystus vittatus.
Acta Hydrochim.Hydrobiol. 10(1):23-29.

15793

Con, AF

Vymazal, J.. 1990. Uptake of Heavy Metals by Cladophora glomerata. Acta
Hydrochim.Hydrobiol. 18(6):657-665.

45131

UEndp, AF

Vymazal, J.. 1995. Influence of pH on Heavy Metals Uptake by Cladophora
glomerata. Pol.Arch.Hydrobiol. 42(3):231-237.

45130

UEndp, AF

Wang, T.C., J.C. Weissman, G. Ramesh, R. Varadarajan, and J.R. Benemann. 1996.
Parameters for Removal of Toxic Heavy Metals by Water Milfoil (Myriophyllum
spicatum). Bull.Environ.Contam.Toxicol. 57(5):779-786.

20408

UEndp, Dur, AF

Wang, W.. 1987. Toxicity of Nickel to Common Duckweed (Lemna minor).
Environ.Toxicol.Chem. 6(12):961-967.

12694

Con, AF

Wang, W.. 1994. Rice Seed Toxicity Tests for Organic and Inorganic Substances.
Environ.Monit.Assess. 29:101 -107.

45060

AF, Dur

Williams, P.L., and D.B. Dusenbery. 1990. Aquatic Toxicity Testing Using the
Nematode, Caenorhabditis elegans. Environ.Toxicol.Chem. 9(10): 1285-1290.

3437

Wong, P.K., and C.K. Wong. 1990. Toxicity of Nickel and Nickel Electroplating Water
to Chlorella pyrenoidosa. Bull.Environ.Contam.Toxicol. 45(5):752-759.

3493

Dur, AF

Wong, C.K.. 1992. Effects of Chromium, Copper, Nickel, and Zinc on Survival and
Feeding of the Cladoceran Moina macrocopa. Bull.Environ.Contam.Toxicol. 49:593-
599.

45188

UEndp, AF

Better data used in CORE

442

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Wong, C.K.. 1993. Effects of Chromium, Copper, Nickel, and Zinc on Longevity and
Reproduction of the Cladoceran Moina macrocopa. Bull.Environ.Contam.Toxicol.
50:633-639.

6973

LT, Dur, AF

Wooldridge, C.R., and D.P. Wooldridge. 1969. Internal Damage in an Aquatic Beetle
Exposed to Sublethal Concentrations of Inorganic Ions. Ann.Entomol.Soc.Am.
62(4):921-933.

2868

UEndp, AF

Zia, S., and M.A. Alikhan. 1989. A Laboratory Study of the Copper and Nickel Uptake
and Regulation in a Copper - Tolerant Decapod, Cambarus bartoni (Fabricius)
(Decapoda, Crustacea). Arch.Int.Physiol.Biochim. 97:211-219.

20705

UEndp, AF

Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

FAV in the most recent national ambient water quality criteria dataset used to derive the CMC , EPA is providing a
transparent rationale as to why they were not utilized (see below).

General QA/QC failure because non-resident species in Oregon

The test with the following species was used in the EPA BE of OR WQS for nickel in freshwater, but was not considered in the CWA
review and approval/disapproval action of the standards because these species do not have a breeding wild population in Oregon's
waters:

Anodonta

imbecillis

Mussel

Keller and Zam 1991

Moina

macrocopa

Cladoceran

Pokethitiyook et al. 1987

87 U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient Water. EPA-820-B-96-001.

443

-------
Ambloplites

rupestris

Rock bass

Lind et al. 1978

Ephemerella

subvaria

Mayfly

Warnick and Bell 1969

Other Acute tests failins QA/QC by species

Daphnia magna — cladoceran

Khangarot, B.S., P.K. Ray, and H. Chandra. 1987. Daphnia magna as a model to assess heavy metal toxicity: Comparative
assessment with mouse system. Acta Hydrochim. Hydrobiol. 15(4): 427-432.

Test temperature (15°C) was below ASTM recommendations for the species (20°C) and life stage was not provided (should be neonate
<24 h).

Anderson, B.G. 1948. The apparent threshold to toxicity to Daphnia magna for chlorides of various metals when added to lake
Erie water. Trans. Am. Fish. Soc. 78: 96-113.

This study had no hardness recorded in the 1986 ALC. In addition, it is a greater than value.

The following tests were included in EPA's BE of the OR WQS for nickel in freshwater, but were not used in this CWA review and
approval/disapproval action of these standards because the species were determined to be non-North American residents. Were they
Oregon residents, the SMAVs/2 would have fallen below the CMC:

Lymnaea luteola— pond snail

Khangarot, B.S. and P.K. Ray. 1988. Sensitivity of freshwater pulmonate snails, Lymnaea luteola L., to heavy metals. Bull.
Environ. Contam. Toxicol. 41(2): 208-213.

Lymnaea acuminata— pond snail

Khangarot, B.S., S. Mathur and V.S. Durve. 1982. Comparative toxicity of heavy metals and interaction of metals on a
freshwater pulmonate snail Lymnaea acuminata (Lamarck). Acta Hydrochim. Hydrobiol. 10(4): 367-375.

Other Chronic tests failins QA/QC by species

Daphnia magna - cladoceran

444

-------
Lazareva, L.P. 1985. Changes in biological characteristics of Daphnia magna from chronic action of copper and nickel at low
concentrations. Hydrobiol. J. 21(5): 59-62.

No hardness; Unacceptable effects at all concentrations tested.

445

-------
Appendix K Pentachlorophenol (freshwater)
Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Citation

ECOTOX
EcoRef#

Rejection
Code(s)

Comment

Aben, N.W.H. Houx, and M. Leistra. 1992.
Toxicity of Pentachlorophenol and Chlorpyrifos in Soil
and in Solution to a Nematode and a Plant Species.
Rep.No.59, U.S. Dep.of Commerce,
Agric.Res.Dept.Winand Staring Center for Integrated
Land, Soil and Water Res., Wageningen, Netherlands
(U.S.NTIS PB93-221216) :39 p.

44356

AF, Form

Adema, D.M.M. 1978. Daphnia magna as a Test Animal
in Acute and Chronic Toxicity Tests. Hydrobiologia
59(2): 125-134.

2018

AF, Dur

Table 6 in WQC
document

Agrawal, H.P. 1987. Evaluation of the Toxicity of Phenol
and Sodium Pentachlorophenate to the Snail
Indoplanorbis exustus (Deshayes).
J.Anim.Morphol.Physiol. 34(1-2):107-112.

9973

AF, Dur, Form

Alabaster, J.S. 1969. Survival of Fish in 164 Herbicides,
Insecticides, Fungicides, Wetting Agents and
Miscellaneous Substances. Int.Pest Control 11(2):29-35
(Author Communication Used).

542

AF, Dur

Alexander, D.G., and R.M.V. Clarke. 1978. The Selection
and Limitations of Phenol As a Reference Toxicant to
Detect Differences in Sensitivity Among Groups of
Rainbow Trout (Salmo gairdneri). Water Res.
12(12):1085-1090.

6262

Uendp, Dur

Bali, H.S., S. Singh, and D.P. Singh. 1984. Trial of Some
Molluscicides on Snails Melanoides tuberculatus and
Vivipara bengalensis in Laboratory. Indian J.Anim.Sci.
54(4):401-403.

10207

AF, Dur

Basack, S.B., M.L. Oneto, N.R. Verrengia Guerrero, and
E.M. Kesten. 1997. Accumulation and Elimination of
Pentachlorophenol in the Freshwater Bivalve Corbicula
fluminea. Bull.Environ.Contam.Toxicol. 58(3):497-503.

18004

Form

446

-------
Citation

ECOTOX
EcoRef#

Rejection
Code(s)

Comment

Belliyappa, G., and S.R. Reddy. 1986. Growth and
Conversion Efficiency of the Catfish Heteropneustes
fossilis (Bloch) Exposed to Sub-Lethal Concentrations of
Sodium Pentachlorophenate. Pol.Arch.Hydrobiol.
33(1): 115-120.

12702

AF, Con, Form

Bennett, W.R., and A.P. Farrell. 1998. Acute Toxicity
Testing with Juvenile White Sturgeon (Acipenser
transmontanus). Water Qual.Res.J.Can. 33(1):95-110.

20400

Uendp, Dur, Form

Berglind, R., and G. Dave. 1984. Acute Toxicity of
Chromate, DDT, PCP, TPBS, and Zinc to Daphnia
magna Cultured in Hard and Soft Water.
Bull.Environ.Contam.Toxicol. 33(1):63-68.

10871

Dur, Con

Not in WQC Doc

Bierkens, J., J. Maes, and F. Vander Plaetse. 1998.
Dose-Dependent Induction of Heat Shock Protein 70
Synthesis in Raphidocelis subcapitata Following
Exposure to Different Classes of Environmental.
Environ.Pollut. 101:91-97.

19649

Plant, UEndp, AF

Plants do not drive
criteria, and
therefore, are not
included in CWA
review and approval
of OR WQS

Bitton, G., K. Rhodes, and B. Koopman. 1996.
CerioFAST: An Acute Toxicity Test Based on
Ceriodaphnia dubia Feeding Behavior.
Environ. Toxicol. Chem. 15(2): 123-125.

17097

AF, Dur

Bitton, G., K. Rhodes, B. Koopman, and M. Cornejo.
1995. Short-Term Toxicity Assay Based on Daphnid
Feeding Behavior. Water Environ.Res. 67(3):290-293.

19602

AF, Form

Blackman, G.E., M.H. Parke, and G. Garton. 1955. The
Physiological Activity of Substituted Phenols. I.
Relationships between Chemical Structure and
Physiological Activity. Arch.Biochem.Biophys. 54:45-54.

2231

Plant, Con

Plants do not drive
criteria, and
therefore, are not
included in CWA
review and approval
of OR WQS

18353

AF, UEndp, Dur

Borgmann, U., and K.M. Ralph. 1986. Effects of
Cadmium, 2,4-Dichlorophenol, and Pentachlorophenol on
Feeding, Growth, and Particle-Size-Conversion Efficiency
ofWhite. Arch.Environ.Contam.Toxicol. 15(5):473-480.

11938

UEndp, Con, AF

447

-------
Citation

ECOTOX
EcoRef#

Rejection
Code(s)

Comment

Borgmann, U., K.M. Ralph, and W.P. Norwood. 1989.
Toxicity Test Procedures for Hyalella azteca, and Chronic
Toxicity of Cadmium and Pentachlorophenol to H. azteca,
Gammarus fasciatus, and Daphnia magna.
Arch.Environ.Contam.Toxicol. 18(5):756-764.

772

UEndp

Bresch, H.. 1982. Investigation of the Long-Term Action
of Xenobiotics on Fish with Special Regard to
Reproduction. Ecotoxicol.Environ.Saf. 6(1): 102-112.

10392

Con

Brockway, D.L.. 1963. Some Effects of Sub-Lethal Levels
of Pentachlorophenol and Cyanide on the Physiology and
Behavior of a Cichlid Fish Cichlasoma bimaculatum
(Linnaeus). M.S.Thesis, Oregon State University,

Corvalis, 0 R:56.

5591

Dur

Canton, J.H., and D.M.M. Adema. 1978. Reproducibility
of Short-Term and Reproduction Toxicity Experiments
with Daphnia magna and Comparison of the Sensitivity of
Daphnia magna with Daphnia pulex and Daphnia
cucullata in Short-Term Experiments. Hydrobiologia
59(2): 135-140 (Used Reference 2018).

2017

AF, Con

In current WQC Doc,
but no pH value given

Carlson, R.W.. 1990. Ventilatory Patterns of Bluegill
(Lepomis macrochirus) Exposed to Organic Chemicals
with Different Mechanisms of Toxic Action.

Com p. Biochem. Physiol .C 95(2): 181 -196.

3461

UEndp, AF

12208

UEndp, Con, AF

Centeno, M.D., L. Brendonck, and G. Persoone. 1993.
Cyst-Based Toxicity Tests. III. Development and
Standardization of an Acute Toxicity Test with the
Freshwater Anostracan Crustacean Streptocephalus. In:
A.M.V.M.Soares and P.Calow (Eds.), Progress in
Standardization of Aquatic Toxicity Tests, Lewis
Publishers :37-55.

14250

Dur

Centeno, M.D.F., G. Persoone, and M.P. Goyvaerts.
1995. Cyst-Based Toxicity Tests. IX. The Potential of
Thamnocephalus platyurus as Test Species in
Comparison with Streptocephalus proboscideus
(Crustacea. Environ.Toxicol.Water Qual. 10(4):275-282.

14017

AF, Dur

448

-------
Citation

ECOTOX
EcoRef#

Rejection
Code(s)

Comment

Centeno, M.D.F., L. Brendonck, and G. Persoone. 1993.
Influence of Production, Processing, and Storage
Conditions of Resting Eggs of Streptocephalus
proboscideus (Crustacea: Branchiopoda: Anostraca) on.
Bull.Environ.Contam.Toxicol. 51(6):927-934.

8130

AF, Dur

Chapman, G.A.. 1969. Toxicity of Pentachlorophenol to
Trout Alevins. Ph.D.Thesis, Oregon State University,
Corvallis, OR :87 p..

151

Dur

Chapman, G.A., and D.L. Shumway. 1978. Effects of
Sodium Pentachlorophenate on Survival and Energy
Metabolism of Embryonic and Larval Steelhead Trout. In:
K.R.Rao (Ed.), Pentachlorophenol: Chemistry,
Pharmacology, and Environmental Toxicology, Plenum
Press, New York, NY :285-299.

15219

AF, Dur, Con

Chapman, P.M., M.A. Farrell, and R.O. Brinkhurst. 1982.
Effects of Species Interactions on the Survival and
Respiration of Limnodrilus hoffmeisteri and Tubifex
tubifex (Oligochaeta, Tubificidae) Exposed to. Water Res.
16(9): 1405-1408.

15207

See comment

Table 6 because
tests included
sediment

Charoy, C., and C.R. Janssen. 1999. The Swimming
Behaviour of Brachionus calyciflorus (Rotifer) Under
Toxic Stress. II. Comparative Sensitivity of Various
Behavioural Criteria. Chemosphere 38(14):3247-3260.

20070

UEndp, Dur

Chowdary, V.D., P.V. Rao, and R. Narayanan. 1979.
Effect of Copper Sulfate and Sodium Pentachlorophenate
on Adenine and Andenosine Phosphates in Lymnaea
luteola (Mollusca: Gastropoda).

Bull. Environ.Contam .Toxicol. 23(4-5):615-619.

6804

AF, Dur, Con

Christoffers, D., and D.E.W. Ernst. 1983. The In-Vivo
Fluorescence of Chlorella fusca as a Biological Test for
the Inhibition of Photosynthesis. Toxicol.Environ.Chem.
7:61-71.

45160

Plant, AF, UEndp

Plants do not drive
criteria, and
therefore, are not
included in CWA
review and approval
of OR WQS

Clemens, H.P., and K.E. Sneed. 1959. Lethal Doses of
Several Commercial Chemicals for Fingerling Channel
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934

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449

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EcoRef#

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Code(s)

Comment

Cleveland, L., D.R. Buckler, F.L. Mayer, and D.R.
Branson. 1982. Toxicity of Three Preparations of
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15155

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Crandall, C.A., and C.J. Goodnight. 1959. The Effect of
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Crandall, C.A., and C.J. Goodnight. 1962. Effects of
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Crandall, C.A., and C.J. Goodnight. 1963. The Effects of
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Cravedi, J.P., C. Gillet, and G. Monod. 1995. In Vivo
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Cressman III, C.P., and P.L. Williams. 1997. Reference
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19999

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Dalela, R.C., S. Rani, S. Rani, and S.R. Verma. 1980.
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De Coen, W.M., M.L. Vangheluwe, and C.R. Janssen.
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Comment

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17456

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Donkin, S.G., and P.L. Williams. 1995. Influence of
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Douglas, M.T., D.O. Chanter, I.B. Pell, and G.M. Burney.
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Ferrando, M.D., C.R. Janssen, E. Andreu, and G.
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Fisher, S.W.. 1986. Effects of Temperature on the Acute
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Comment

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19965

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Freitag, D., H. Geyer, A. Kraus, R. Viswanathan, D.
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Geyer, H., G. Politzki, and D. Freitag. 1984. Prediction of
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11297

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11677

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included in CWA
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Goel, H.C., and C.P. Srivastava. 1981. Laboratory
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Comment

Gossiaux, D.C., P.F. Landrum, and S.W. Fisher. 1996.
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Graney, R.L.Jr.. 1986. Effects of Long-Term Exposure to
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12265

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Gupta, P.K.. 1983. Acute Toxicity of Pentachlorophenol
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Gupta, P.K., and P.S. Rao. 1982. Toxicity of Phenol,
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10558

NonRes

Gupta, P.K., and V.S. Durve. 1984. Evaluation of the
Toxicity of Sodium Pentachlorophenate,
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10686

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Gupta, P.K., and V.S. Durve. 1984. A Study on the Effect
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Gupta, P.K., and V.S. Durve. 1986. A Study of the
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3089

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Gupta, P.K., and V.S. Durve. 1986. Histopathological
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12057

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453

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ECOTOX
EcoRef#

Rejection
Code(s)

Comment

Gupta, P.K., P.S. Rao, and V.S. Mujumdar. 1984. Studies
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11136

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Gupta, S., and R.C. Dalela. 1986. Liver Damage in
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14155

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Gupta, S., R.C. Dalela, and P.K. Saxena. 1983. Influence
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10913

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Gupta, S., R.C. Dalela, and P.K. Saxena. 1983. Influence
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15491

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Gupta, S., S.R. Verma, and P.K. Saxena. 1982. Toxicity
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10532

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Halbach, U., M. Siebert, M. Westermayer, and C. Wissel.
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Hallas, T.E.. 1973. On the Accumulation and
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Hanke, W„ G. Gluth, H. Bubel, and R. Muller. 1983.
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Hanumante, M.M., and S.S. Kulkarni. 1979. Acute
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454

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Comment

Hashimoto, Y., and J. Fukami. 1969. Toxicity of Orally
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Hashimoto, Y., E. Okubo, T. Ito, M. Yamaguchi, and S.
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Hashimoto, Y., T. Makita, N. Ohnuma, and T. Noguchi.
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Hattori, M., K. Senoo, S. Harada, Y. Ishizu, and M. Goto.
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Hattula, M.L., V.M. Wasenius, H. Reunanen, and A.U.
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Hickey, C.W., and M.L. Vickers. 1992. Comparison of the
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6309

Hickie, B.E., and D.G. Dixon. 1987. The Influence of Diet
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Hickie, B.E., D.G. Dixon, and J.F. Leatherland. 1989. The
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3390

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ECOTOX
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Comment

Hodson, P.V., and B.R. Blunt. 1981. Temperature
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M. Olsson. 1972. Metabolic Effects of Technical
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Huckins, J.N., and J.D. Petty. 1983. Dynamics of Purified
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Inglis, A., and E.L. Davis. 1972. Effects of Water
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2135

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Only 8% PCP

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2138

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Comment

Jayaweera, R., R. Petersen, and P. Smejtek. 1982.
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Johansen, P.H., R.A. Mathers, and J.A. Brown. 1987.
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Juchelka, C.M., and T.W. Snell. 1994. Rapid Toxicity
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Khangarot, B.S., A. Sehgal, and M.K. Bhasin. 1985.

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Khangarot, B.S., A. Sehgal, and M.K. Bhasin. 1985. Man
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11521

NonRes

Kimura, T., and H.L. Keegan. 1966. Toxicity of Some
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ECOTOX
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Rejection
Code(s)

Comment

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16366

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17483

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15897

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Kobayashi, K., and T. Kishino. 1980. Effect of pH on the
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6539

Dur, Con

Table 6 in WQC Doc
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458

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Citation

ECOTOX
EcoRef#

Rejection
Code(s)

Comment

Korte, F., D. Freitag, H. Geyer, W. Klein, A.G. Kraus, and
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17753

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LeBlanc, G.A., B. Hilgenberg, and B.J. Cochrane. 1988.
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Lee, S.K., D. Freitag, C. Steinberg, A. Kettrup, and Y.H.
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Lilius, H., B. Isomaa, and T. Holmstrom. 1994. A
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Lu, P.Y., and R.L. Metcalf. 1975. Environmental Fate and
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Lydy, M.J., K.A. Bruner, D.M. Fry, and S.W. Fisher. 1990.
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18935

UEndp, Dur

459

-------
Citation

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EcoRef#

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Code(s)

Comment

Lydy, M.J., W.L. Hayton, A.E. Staubus, and S.W. Fisher.
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13521

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MacPhee, C., and R. Ruelle. 1969. Lethal Effects of 1888
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15148

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Makela, P., and A.O.J. Oikara. 1990. Uptake and Body
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Makela, P., T. Petanen, and A. Oikari. 1989. Uptake,
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18811

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Makela, T.P., and A.O.J. Oikari. 1995. Pentachlorophenol
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16155

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Matida, Y., S. Kimura, M. Yokote, H. Kumada, and H.
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9389

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Mattson, V.R., J.W. Arthur, and C.T. Walbridge. 1976.
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719

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11533

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460

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Citation

ECOTOX
EcoRef#

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Code(s)

Comment

McKim, J.M., P.K. Schmieder, and R.J. Erickson. 1986.
Toxicokinetic Modeling of [14C]Pentachlorophenol in the
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12076

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McKim, J.M., P.K. Schmieder, R.W. Carlson, E.P. Hunt,
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12181

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Morgan, W.S.G.. 1976. Fishing for Toxicity: Biological
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5462

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Muraleedharan, K., S.P. Kumar, K.S. Hedge, and V.S.
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8155

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Nagendran, R., and K. Shakuntala. 1979. Studies on
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6145

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Negilski, D.S.. 1973. Individual and Combined Effects of
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15432

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Nguyen, L.T.H., C.R. Janssen, and F.A.M. Volckaert.
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20030

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Niimi, A.J., and C.A. McFadden. 1982. Uptake of Sodium
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10437

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Niimi, A.J., and C.Y. Cho. 1983. Laboratory and Field
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10705

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461

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EcoRef#

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Comment

Nimmo, D.W.R., D. Link, LP. Parrish, G.J. Rodriguez, W.
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69474

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Nishiuchi, Y.. 1976. Toxicity of Formulated Pesticides to
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7874

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2682

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Notenboom, J., K. Cruys, J. Hoekstra, and P. Van
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5975

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Ogawa, M., and H. Kitamura. 1988. Biological Assay of
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3228

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Plants do not drive
criteria, and
therefore, are not
included in CWA
review and approval
of OR WQS

Oikari, A.O.J.. 1987. Acute Lethal Toxicity of Some
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Parks, L.G., and G.A. LeBlanc. 1996. Reductions in
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Peer, M.M., J. Nirmala, and M.N. Kutty. 1983. Effects of
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10659

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462

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ECOTOX
EcoRef#

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Code(s)

Comment

Peterson, R.H.. 1976. Temperature Selection of Juvenile
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5160

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Pierce, R.H.J.. 1978. Fate and Impact of
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Preston, B.L., T.W. Snell, T.L. Robertson, and B.J.
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Randall, T.L., and P.V. Knopp. 1980. Detoxification of
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11517

NonRes

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3611

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Samis, A.J.W., P.W. Colgan, and P.H. Johansen. 1993.
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4247

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463

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ECOTOX
EcoRef#

Rejection
Code(s)

Comment

Samis, A.J.W., P.W. Colgan, and P.H. Johansen. 1994.
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16812

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20176

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Sharma, H.A., J.T. Barber, H.E. Ensley, and M.A. Polito.
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17665

Plant, AF

Plants do not drive
criteria, and
therefore, are not
included in CWA
review and approval
of OR WQS

Shedd, T.R., M.W. Widder, M.W. Toussaint, M.C. Sunkel,
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Shigeoka, T., T. Yamagata, T. Minoda, and F. Yamauchi.
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753

Plant, AF, Dur, Con

Plants do not drive
criteria, and
therefore, are not
included in CWA
review and approval
of OR WQS

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13171

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Plants do not drive
criteria, and
therefore, are not
included in CWA
review and approval
of OR WQS

Shim, J.C., and L.S. Self. 1973. Toxicity of Agricultural
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Comment

Shumway, D.L., and J.R. Palensky. 1973. Impairment of
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Slabbert, J.L., and W.S.G. Morgan. 1982. A Bioassay
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11048

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17278

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Slooff, W. 1979. Detection Limits of a Biological
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Slooff, W.. 1983. Benthic Macroinvertebrates and Water
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15788

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9740

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Smith, A.D., A. Bharath, C. Mallard, D. Orr, L.S. McCarty,
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Smith, P.D., D.L. Brockway, and F.E. Standi Jr.. 1987.
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EcoRef#

Rejection
Code(s)

Comment

Snell, T.W.. 1991. New Rotifer Bioassays for Aquatic
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Snell, T.W., and B.D. Moffat. 1992. A 2-D Life Cycle Test
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Snell, T.W., and M.J. Carmona. 1995. Comparative
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Snell, T.W., B.D. Moffat, C. Janssen, and G. Persoone.
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Statham, C.N., and J.J. Lech. 1975. Potentiation of the
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5550

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Stehly, G.R., and W.L. Hayton. 1988. Detection of
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Stehly, G.R., and W.L. Hayton. 1989. Disposition of
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Stehly, G.R., and W.L. Hayton. 1990. Effect of pH on the
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Stephenson, G.L., N.K. Kaushik, and K.R. Solomon.
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174

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466

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Citation

ECOTOX
EcoRef#

Rejection
Code(s)

Comment

Stephenson, G.L., N.K. Kaushik, and K.R. Solomon.
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Surtikanti, H.K.. 1994. The Influence of Food (Algae)
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20175

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Tachikawa, M., A. Hasegawa, R. Sawamura, A. Takeda,
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12737

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Tachikawa, M., and R. Sawamura. 1994. The Effects of
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13665

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Tomizawa, C., and H. Kazano. 1979. Environmental Fate
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6553

Plant, AF, UEndp

Plants do not drive
criteria, and
therefore, are not
included in CWA
review and approval
of OR WQS

Twagilimana, L., J. Bohatier, C.A. Groliere, F. Bonnemoy,
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Dur

Vallejo-Freire, A., 0. Fonseca Ribeiro, and I. Fonseca
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2334

UEndp, Dur

467

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EcoRef#

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Code(s)

Comment

Van Leeuwen, C.J., G. Niebeek, and M. Rijkeboer. 1988.
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Van Leeuwen, C.J., P.S. Griffioen, W.H.A. Vergouw, and
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11519

AF, Con, Form

In Table 1 ofWQC
doc with pH, but no
pH reported in
ECOTOX

Veith, G.D., D.L. De Foe, and B.V. Bergstedt. 1979.
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W.A.Brungs, U.S.EPA, Duluth, MN) (Author
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Venegas, W., I. Hermosilla, L. Quevedo, and G. Montoya.
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Verma, S.R., I.P. Tonk, A.K. Gupta, and M. Saxena.
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10575

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Verma, S.R., S. Rani, A.K. Tyagi, and R.C. Dalela. 1980.
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Verma, S.R., S. Rani, and R.C. Dalela. 1981. Synergism,
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15670

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468

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ECOTOX
EcoRef#

Rejection
Code(s)

Comment

Versteeg, D.J.. 1990. Comparison of Short-and Long-
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17639

Plant, Dur

Plants do not drive
criteria, and
therefore, are not
included in CWA
review and approval
of OR WQS

Whitley, L.S. 1968. The Resistance of Tubificid Worms to
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15507

Dur - 24 h, Con

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Yount, J.D., and J.E. Richter. 1986. Effects of
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12104

Plant, AF, Uendp, Form

Plants do not drive
criteria, and
therefore, are not
included in CWA
review and approval
of OR WQS

Zischke, J.A., J.W. Arthur, R.O. Hermanutz, S.F. Hedtke,
and J.C. Helgen. 1985. Effects of Pentachlorophenol on
Invertebrates and Fish in Outdoor Experimental
Channels. Aquat.Toxicol. 7(1-2):37-58.

2652

UEndp, Field, NoOrg

Whitley, L.S. 1968. The Resistance of Tubificid Worms to
Three Common Pollutants. Hydrobiologia 32(1/2):193-
205 (Author Communication Used).

15507

Dur

Table 6

Winner, R.W. 1988. Evaluation of the Relative
Sensitivities of 7-D Daphnia magna and Ceriodaphnia
dubia Toxicity Tests for Cadmium and Sodium
Pentachlorophenate. Environ.Toxicol.Chem. 7(2): 153-
159.

2443

Form, Dur, Unknown
Endpoint, Chronic Renewal
and Unmeasured, No pH

Yount, J.D., and J.E. Richter. 1986. Effects of
Pentachlorophenol on Periphyton Communities in
Outdoor Experimental Streams.
Arch.Environ.Contam.Toxicol. 15(1 ):51 -60.

12104

Form, Species, Field,
Unknown Endpoint, No pH

Zischke, J.A., J.W. Arthur, R.O. Hermanutz, S.F. Hedtke,
and J.C. Helgen. 1985. Effects of Pentachlorophenol on
Invertebrates and Fish in Outdoor Experimental
Channels. Aquat.Toxicol. 7(1-2):37-58.

2652

Species, Field, Dur,

Unknown Endpoint, Endpoint
(Lethal)

Not in WQC Doc

469

-------
Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

calculate the FAV in the most recent national ambient water quality criteria dataset used to derive the CMC , EPA
is providing a transparent rationale as to why they were not utilized (see below).

2 For the studies that were not utilized because they were not found to be pertinent to this determination (including
failing the QA/QC procedures listed in Appendix A) upon initial review of the download from ECOTOX, EPA is
providing the code that identifies why EPA determined that the results of the study were not reliable (see Appendix
K).

General QA/QC failure because non-resident species in Oregon

Tests with the following several species were used in the EPA BE of OR WQS for pentachlorophenol in freshwater, but were not
considered in the CWA review and approval/disapproval action of the standards because these species do not have a breeding wild
population in Oregon's waters:

Ceriodaphnia

reticulata

Cladoceran

Hedtke et al. 1986

Oncorhynchus

clarki (stomias)

Greenback cutthroat trout

Sappington et al. 2001

Oncorhynchus

gilae

Apache trout

Sappington et al. 2001

Other Acute tests failins QA/QC by species

Oncorhynchus clarki - Cutthroat Trout

Mayer, F.L.J, and M.R. Ellersieck. 1986. Manual of Acute Toxicity: Interpretation and Data Base for 410 Chemicals and 66
Species of Freshwater Animals. Resour. Publ. No. 160, U.S. Dep. Interior, Fish Wildl. Serv., Washington, DC: 505 p. (USGS
Data File).

88 U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient Water. EPA-820-B-96-001.

470

-------
The LC50s from this extensive aquatic toxicity data compendium were included in EPA's BE of the OR WQS for pentachlorophenol
in freshwater, but were not used for determining the most representative SMAV in this CWA review and approval of these standards
because the values included in EPA's ECOTOX database that were used for the BE were erroneous when checked against the original
source. No 96-h LC50 is provided, only a lower bound of 10 ug/L and an upper bound of 100 ug/L about some unspecified 96-h
LC50. Also, the same test data appears to be entered for the commercial formulation of pentachlorphenol - Dowicide EC-7 (88%
purity) and NaPCP (see pages 374 and 375 in the compendium). The lower bound value of 10 ug/L for three forms of
pentachlorophenol (technical, Dowicide and NaPCP) was recorded as the mean 96 h LC50 in ECOTOX.

Ictalurus punctatus — Channel catfish

Phipps, G.L. and G.W. Holcombe. 1985. A method for aquatic multiple species toxicant testing: Acute toxicity of 10 chemicals
to 5 vertebrates and 2 invertebrates. Environ. Pollut. Ser. A Ecol. Biol. 38(2): 141-157 (Author Communication Used)
(OECDG Data File).

An LC50 included in EPA's BE of the OR WQS for pentachlorophenol in freshwater was not used for determining the most
representative SMAV in this CWA review and approval of these standards because it was a less than value and two other LC50s from
the same study were available for use, as per the 1986 ALC document.

Mayer, F.L.J, and M.R. Ellersieck. 1986. Manual of Acute Toxicity: Interpretation and Data Base for 410 Chemicals and 66
Species of Freshwater Animals. Resour. Publ. No. 160, U.S. Dep. Interior, Fish Wildl. Serv., Washington, DC: 505 p. (USGS
Data File).

Four LC50s from S and F tests where it was unknown whether they were measured or not with original values ranging from 66 to 200
ug/L.

Johnson, W.W. and M.T. Finley. 1980. Handbook of Acute Toxicity of Chemicals to Fish and Aquatic Invertebrates. Resource
Publ. 137. U.S. Fish and Wildlife Service, Washington, DC.: 58 p.

Two LC50 values from S,U tests ranging from 64.01 to 65.28 ug/L.

Oncorhynchus kisutch - Coho salmon

Davis, J.C. and R.A.W. Hoos. 1975. Use of sodium pentachlorophenate and dehydroabietic acid as reference toxicants for
salmonid bioassays. J. Fish. Res. Board Can. 32(3): 411-416.

471

-------
One of the two LC50s reported in ECOTOX and included in the BE from this study was not used because it was estimated using the
nomographic method and an LC50 calculated using log-probit was provided for the same test.

Oncorhynchus nerka - Sockeye salmon

Davis, J.C. and R.A.W. Hoos. 1975. Use of sodium pentachlorophenate and dehydroabietic acid as reference toxicants for
salmonid bioassays. J. Fish. Res. Board Can. 32(3): 411-416.

One of the two LC50s reported in ECOTOX and included in the BE from this study was not used because it was estimated using the
nomographic method and an LC50 calculated using log-probit was provided for the same test.

Oncorhynchus mykiss — Rainbow Trout

The following tests were included in EPA's BE of the OR WQS for pentachlorophenol in freshwater, but were not used for
determining the most representative SMAV in this CWA review and approval/disapproval action of these standards because the tests
were not based on the preferred flow-through measured test conditions; however, other flow-through measured test concentrations
were available for these species.

Bentley, R.E., T. Heitmuller, B.H. Sleight III and P.R. Parrish. 1975. Acute Toxicity of Pentachlorophenol to Bluegill (Lepomis
macrochirus), Rainbow Trout (Salmo gairdneri), and Pink Shrimp (Penaeus duorarum). U.S. EPA, Criteria Branch, WA-6-99-
1414-B, Washington, D.C: 13.

Two LC50 values from S,U tests ranging from 75 to 92 |ig/L.

Brooke, L.T., D.J. Call, D.E. Hammermeister, A. Hoffman and C.E. Northcott. Manuscript. Acute Toxicities of Five
Chemicals in Different Natural Waters. Center for Lake Superior Environmental Studies, University of Wisconsin-Superior,
Superior, WI.

One LC50 value from S,M test of 47.2 |ig/L

Davis, J.C. and R.A.W. Hoos. 1975. Use of sodium pentachlorophenate and dehydroabietic acid as reference toxicants for
salmonid bioassays. J. Fish. Res. Board Can. 32(3): 411-416.

Eleven LC50 values from S,U tests ranging from 44 to 106 |ig/L.

Dominguez, S.E. and G.A. Chapman. 1984. Effect of pentachlorophenol on the growth and mortality of embryonic and
juvenile steelhead trout. Arch. Environ. Contam. Toxicol. 13: 739-743.

472

-------
One LC50 value from F,U test of 66 |ig/L

Johnson, W.W. and M.T. Finley. 1980. Handbook of Acute Toxicity of Chemicals to Fish and Aquatic Invertebrates. Resource
Publ. 137. U.S. Fish and Wildlife Service, Washington, DC.: 58 p.

Two LC50 values from S,U tests ranging from 45.72 to 49.92 |ig/L.

Kennedy, C.J. 1990. Toxicokinetic Studies of Chlorinated Phenols and Polycyclic Aromatic Hydrocarbons in Rainbow Trout
(Oncorhynchus mykiss). Ph.D. Thesis, Simon Fraser University, Canada: 188 p.; Diss. Abstr. Int. B Sci. Eng. 53(1): 18

One LC50 value from a renewal test of 153 |ig/L

Mayer, F.L.J, and M.R. Ellersieck. 1986. Manual of Acute Toxicity: Interpretation and Data Base for 410 Chemicals and 66
Species of Freshwater Animals. Resour. Publ. No. 160, U.S. Dep. Interior, Fish Wildl. Serv., Washington, DC: 505 p. (USGS
Data File).

Ten LC50 values from S and F tests where it was unknown whether they were measured or not with original values ranging from 34 to
300 |ig/L.

Sappington, L.C., F.L. Mayer, F.J. Dwyer, D.R. Buckler, J.R. Jones and M.R. Ellersieck. 2001. Contaminant sensitivity of
threatened and endangered fishes compared to standard surrogate species. Environ. Toxicol. Chem. 20(12): 2869-2876.

One LC50 value from S,M test of 160 |ig/L

Six LC50 values from S,U tests ranging from 18 to 3000 |ig/L.

Vigers, G.A. and A.W. Maynard. 1977. The residual oxygen bioassay: A rapid procedure to predict effluent toxicity to
rainbow trout. Water Res. 11(4): 343-346.

One LC50 value from S,U test of 83 |ig/L.

473

-------
Appendix L Silver (freshwater)
Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Anderson, B.G.. 1948. The Apparent
Thresholds of Toxicity to Daphnia magna for
Chlorides of Various Metals when Added to
Lake Erie Water. Trans.Am.Fish.Soc. 78:96-
113.

2054

AF, UEndp, Dur

Barera, Y., and W.J. Adams. 1983. Resolving
Some Practical Questions About Daphnia
Acute Toxicity Tests. In: W.E.Bishop (Ed.),
Aquatic Toxicology and Hazard Assessment,
6th Symposium, ASTM STP 802, Philadelphia,
PA :509-518.

14533

UEndp

Baudin, J.P., and J. Garnier-Laplace. 1994.
Accumulation, Release, and Tissue
Distribution of 110mAg from Natural Food
(Gammarus pulex) by the Common Carp,
Cyprinus carpio L.

Arch.Environ.Contam.Toxicol. 27(4):459-465.

13680

AF, UEndp, RouExp,
Dur

Baudin, J.P., J. Garnier-Laplace, and A.
Lambrechts. 1994. Uptake from Water,
Depuration and Tissue Distribution of 110mAg
in a Freshwater Fish, Cyprinus carpio L. Water
Air Soil Pollut. 72(1 -4): 129-141.

14183

AF, UEndp, Dur

Berthet, B., J.C. Amiard, C. Amiard-Triquet, M.
Martoja, and A.Y. Jeantet. 1992.
Bioaccumulation, Toxicity and Physico-
Chemical Speciation of Silver in Bivalve
Molluscs: Ecotoxicological and Health
Consequences. Sci.Total Environ. 125:97-122.

6930

AF, UEndp, Dur

Birge, W.J., and J.A. Zuiderveen. 1996. The
Comparative Toxicity of Silver to Aquatic Biota.
In: A.W.Andren and T.W.Bober (Eds.), 3rd
Int.Conf.Proc.Transport, Fate and Effects of
Silver in the Environment, Aug.6-9, 1995,
Washington, D.C. :79-87.

20262

Dur

Birge, W.J., J.A. Black, A.G. Westerman, and
J.E. Hudson. 1980. Aquatic Toxicity Tests on
Inorganic Elements Occurring in Oil Shale. In:
C.Gale (Ed.), EPA-600/9-80-022, Oil Shale
Symposium: Sampling, Analysis and Quality
Assurance, March 1979, U.S.EPA, Cincinnati,
OH :519-534 (U.S.NTIS PB80-221435).

11838

Dur, Lifestage

474

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Birge, W.J., J.A. Black, and A.G. Westerman.
1979. Evaluation of Aquatic Pollutants Using
Fish and Amphibian Eggs as Bioassay
Organisms. In: S.W.Nielsen, G.Migaki, and
D.G.Scarpelli (Eds.), Symp.Animals Monitors
Environ.Pollut., 1977, Storrs, CT 12:108-118.

4943

Dur, Lifestage

Birge, W.J., J.E. Hudson, J.A. Black, and A.G.
Westerman. 1978. Embryo-Larval Bioassays
on Inorganic Coal Elements and In Situ
Biomonitoring of Coal-Waste Effluents. In:
Symp., U.S.Fish Wildl.Serv., Dec.3-6, 1978,
Surface Mining Fish Wildl.needs in Eastern
U.S., WV:97-104.

6199

Dur, Lifestage

Birge, W.J.. 1978. Aquatic Toxicology of Trace
Elements of Coal and Fly Ash. In: J.H.Thorp
and J.W.Gibbons (Eds.), Dep.Energy
Symp.Ser., Energy and Environmental Stress
in Aquatic Systems, Augusta, GA 48:219-240.

5305

Dur, Lifestage

Bitton, G., K. Rhodes, and B. Koopman. 1996.
CerioFAST: An Acute Toxicity Test Based on
Ceriodaphnia dubia Feeding Behavior.
Environ. Toxicol. Chem. 15(2): 123-125.

17097

AF, UEndp, Dur

Bringmann, G., and R. Kuhn. 1959.
Comparative Water-Toxicological
Investigations on Bacteria, Algae, and
Daphnia. Gesundheitsingenieur 80(4):115-120.

61194

Plant, UEndp

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of OR
WQS

Bringmann, G., and R. Kuhn. 1959. The Toxic
Effects of Waste Water on Aquatic Bacteria,
Algae, and Small Crustaceans. Tr-Ts-0002
53:17390G / Gesund.lng. 80:115-120
(GER)(ENG TRANSL).

607

AF, UEndp

Bringmann, G., and R. Kuhn. 1959. Water
Toxicological Studies with Protozoa as Test
Organisms. TR-80-0058, Literature Research
Company:13 p./ Gesund.-lng.80:239-242
(GER) / Chem.Abstr. 53:22630D-(GER)(ENG
TRANSL).

2394

UEndp, Dur, Eff

Bringmann, G., and R. Kuhn. 1977. The
Effects of Water Pollutants on Daphnia magna
(Befunde der Schadwirkung
Wassergefahrdender Stoffe Gegen Daphnia
magna). Z.Wasser-Abwasser-Forsch.
10(5):161-166(ENG TRANSL)(OECDG Data
File)(GER)(ENG ABS).

5718

Dur, Con

475

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Bringmann, G., and R. Kuhn. 1978.
Investigation of Biological Harmful Effects of
Chemical Substances Which are Classified as
Dangerous for Water on Protozoa. Z.Wasser-
Abwasser-Forsch. 11 (6):210-215, TR-80-0307,
Literature Research Company :13 p. (ENG
TRANSL) (OECDG Data File).

6601

AF, UEndp, Dur

Brown, B.T., and B.M. Rattigan. 1979. Toxicity
of Soluble Copper and Other Metal Ions to
Elodea canadensis. Environ.Pollut. 20(4):303-
314.

2255

Plant, UEndp, AF, Con

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of OR
WQS

Buikema, A.L.Jr., J. Cairns Jr., and G.W.
Sullivan. 1974. Evaluation of Philodina
acuticornis (Rotifera) as Bioassay Organisms
for Heavy Metals. Water Resour.Bull.
10(4):648-661.

2019

UEndp, Dur

Coleman, R.L., and J.E. Cearley. 1974. Silver
Toxicity and Accumulation in Largemouth Bass
and Bluegill. Bull.Environ.Contam.Toxicol.
12(1 ):53-61.

8517

UEndp, Dur, Con

Cosson, R.P.. 1994. Heavy Metal Intracellular
Balance and Relationship with Metallothionein
Induction in the Liver of Carp After
Contamination by Silver, Cadmium and.
Biometals 7(1 ):9-19.

4994

UEndp, Dur

Davies, P.H.Jr.. 1978. Evaluation of the
Potential Impacts of Silver and/or Silver Iodide
on Rainbow Trout in Laboratory and High
Mountain Lake Environments. Environ.Impacts
Artif.lce Nucleating Agents : 149-161.

7303

UEndp, Con

Diamond, J.M., D.E. Koplish, J. Mcmahon III,
and R. Rost. 1997. Evaluation of the Water-
Effect Ratio Procedure for Metals in a Riverine
System. Environ.Toxicol.Chem. 16(3):509-520.

17591

Lifestage

Diamond, J.M., E.L. Winchester, D.G. Mackler,
and D. Gruber. 1992. Use of the Mayfly
Stenonema modestum (Heptageniidae) in
Subacute Toxicity Assessments.
Environ.Toxicol.Chem. 11 (3):415-425.

16355

Eff

Fitzgerald, G.P.. 1967. The Algistatic
Properties of Silver. Water Sewage Works
Chicago 114:185-188.

17270

Plant, AF, UEndp

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of OR
WQS

476

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Galvez, F„ and C.M. Wood. 1997. The
Relative Importance of Water Hardness and
Chloride Levels in Modifying the Acute Toxicity
of Silver to Rainbow Trout (Oncorhynchus
mykiss). Environ.Toxicol.Chem. 16(11):2363-
2368.

18133

UEndp, Dur

Galvez, F., C. Hogstrand, and C.M. Wood.
1998. Physiological Responses of Juvenile
Rainbow Trout to Chronic Low Level Exposure
of Waterborne Silver.
Comp.Biochem.Physiol.C 119(2): 131-137.

19141

UEndp, Eff

Gamier, J., and J.P. Baudin. 1989.
Accumulation and Depuration of 110mAg by a
Planktonic Alga, Scenedesmus obliquus.
Water Air Soil Pollut. 45(3/4):287-299.

3155

Plant, AF, Con, UEndp

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of OR
WQS

Gamier, J., and J.P. Baudin. 1990. Retention
of Ingested Ag110m by a Freshwater Fish,
Salmo trutta L. Water Air Soil Pollut.50
3/4:409-421.

3255

AF, UEndp, Dur, Con

Gamier, J., J.P. Baudin, and L. Foulquier.
1990. Accumulation from Water and
Depuration of 110mAg by a Freshwater Fish,
Salmo trutta L. Water Res. 24(11): 1407-1414.

3487

AF, UEndp, Dur

Ghosh, T.K., J.P. Kotangale, and K.P.
Krishnamoorthi. 1990. Toxicity of Selective
Metals to Freshwater Algae, Ciliated Protozoa
and Planktonic Crustaceans. Environ.Ecol.
8(1 B):356-360.

3432

Plant, Dur, Con

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of OR
WQS

Goettl, J.P.J., and P.H. Davies. 1976. Water
Pollution Studies. Job Progress Report,
Federal Aid Project F-33-R-11, DNR, Boulder,
CO :58.

10208

Con

Goettl, J.P.Jr., and P.H. Davies. 1975. Water
Pollution Studies. Job Prog.Rep., Fed.Aid
Proj.F-33-R-10, Jan 1-Dec 31, 1974, Colorado
:29 p.

20720

UEndp, Eff

Goettl, J.P.Jr., P.H. Davies, and J.R. Sinley.
1976. Water Pollution Studies. In: D.B.Cope
(Ed.), Colorado Fish.Res.Rev.1972-1975,
DOW-R-R-F72-75, Colorado Div.of Wildl.,
Boulder, CO :68-75.

14367

Nom, UEndp

All

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Grosell, M., C. Hogstrand, C.M.Wood, and
H.J.M. Hansen. 2000. A Nose-to-Nose
Comparison of the Physiological Effects of
Exposure to Ionic Silver Versus Silver Chloride
in the European Eel (Anguilla anguilla) and the
Rainbow Trout (Oncorhynchus mykiss).
Aquat.Toxicol. 48(2/3):327-342.

49762

AF, UEndp, Dur,
NonRes

Hale, J.G.. 1977. Toxicity of Metal Mining
Wastes. BulI.Environ.Contam.Toxicol.
17(1):66-73.

861

Hamilton, S.J., and K.J. Buhl. 1990. Safety
Assessment of Selected Inorganic Elements to
Fry of Chinook Salmon (Oncorhynchus
tshawytscha). Ecotoxicol.Environ.Saf.
20(3):307-324.

3526

AF, UEndp, Con

Haung, Y., L. Mo, J. Ma, L. Liu, W. Lin, and L.
Lu. 1988. Effects of Heavy Metal Ions on
Cough Response of Mud Carp. Acta
Sci.Circumstant.(Huanjing Kexue Xuebao)
8(2):216-222 (CHI) (ENG ABS).

3476

AF, UEndp, Dur

Hiraoka, Y., S. Ishizawa, T. Kamada, and H.
Okuda. 1985. Acute Toxicity of 14 Different
Kinds of Metals Affecting Medaka Fry.
Hiroshima J.Med.Sci. 34(3):327-330.

12151

UEndp, Dur

Huang, Y., L. Mo, J. Ma, M. Wu, and M. Chen.
1987. The Effects of Heavy Metal Ions (Cu2+,
Hg2+, Ag+) on the Respiratory Movements in
Carp and Crucian Carp. Acta
Sci.Nat.Univ.Sunyatseni 4:80-85 (CHI) (ENG
ABS).

9956

AF, UEndp, Dur, Con

Janes, N., and R.C. Playle. 1995. Modeling
Silver Binding to Gills of Rainbow Trout
(Oncorhynchus mykiss).
Environ.Toxicol.Chem. 14(11 ):1847-1858.

16381

UEndp, Dur

Jones, J.R.E.. 1939. The Relation Between the
Electrolytic Solution Pressures of the Metals
and Their Toxicity to the Stickleback
(Gasterosteus aculeatus L.). J.Exp.Biol.
16(4):425-437.

2851

AF, UEndp, Dur, Con

Jones, J.R.E.. 1940. A Further Study of the
Relation Between Toxicity and Solution
Pressure, with Polycelis nigra as Test Animal.
J.Exp.Biol. 17:408-415.

10012

AF, UEndp, Dur, Con

Khangarot, B.S., and P.K. Ray. 1987.
Sensitivity of Toad Tadpoles, Bufo
melanostictus (Schneider), to Heavy Metals.
Bull.Environ.Contam.Toxicol. 38(3):523-527.

12339

NonRes, Con

478

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Khangarot, B.S., A. Sehgal, and M.K. Bhasin.
1985. "Man and Biosphere" - Studies on the
Sikkim Himalayas. Part 5: Acute Toxicity of
Selected Heavy Metals on the Tadpoles of
Rana hexadactyla. Acta Hydrochim.Hydrobiol.
13(2):259-263.

11438

Con

Khangarot, B.S., and P.K. Ray. 1988.
Sensitivity of Freshwater Pulmonate Snails,
Lymnaea luteola L., to Heavy Metals.
Bull.Environ.Contam.Toxicol. 41 (2):208-213.

12943

Con

Khangarot, B.S., P.K. Ray, and H. Chandra.
1987. Daphnia magna as a Model to Assess
Heavy Metal Toxicity: Comparative
Assessment with Mouse System. Acta
Hydrochim.Hydrobiol. 15(4):427-432.

12575

Dur

Klaine, S.J., T.W. La Point, G.P. Cobb, B.L.
Forsythe II, T.P. Bills, M.D. Wenholz, and
R.D.Jeffers.. 1996. Influence of Water Quality
Parameters on Silver Toxicity: Preliminary
Result. In: A.W.Andren and T.W.Bober (Eds.),
3rd Int.Conf.Proc.Transport, Fate and Effects
of Silver in the Environment, Aug.6-9, 1995,
Washington, D.C. :65-77.

20261

Con

McGeer, J.C., and C.M. Wood. 1998.

Protective Effects of Water CI- on Physiological
Responses to Waterborne Silver in Rainbow
Trout. Can.J.Fish.Aquat.Sci. 55(11):2447-
2454.

52067

AF, UEndp, Dur

Morgan, I.J., R.P. Henry, and C.M. Wood.
1997. The Mechanism of Acute Silver Nitrate
Toxicity in Freshwater Rainbow Trout
(Oncorhynchus mykiss) is Inhibition of Gill Na+
and CI- Transport. Aquat.Toxicol. 38:145-163.

18359

AF, UEndp, Dur

Nalecz-Jawecki, G., and J. Sawicki. 1998.
Toxicity of Inorganic Compounds in the
Spirotox Test: A Miniaturized Version of the
Spirostomum ambiguum Test.
Arch.Environ.Contam.Toxicol. 34(1 ):1-5.

18997

Ace

Nasu, Y., and M. Kugimoto. 1981. Lemna
(Duckweed) as an Indicator of Water Pollution
I. The Sensitivity of Lemna paucicostata to
Heavy Metals. Arch.Environ.Contam.Toxicol.
10(2): 159-169.

9489

Plant, AF, UEndp, Con

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of OR
WQS

479

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Nasu, Y., K. Hirabayashi, and M. Kugimoto.
1988. The Toxicity of Some Water Pollutants
for Lemnaceae (Duckweed) Plant. Proc.lCMR
Semin. 8:485-491.

9057

Plant, AF, UEndp

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of OR
WQS

Nehring, R.B.. 1976. Aquatic Insects as
Biological Monitors of Heavy Metal Pollution.
Bull.Environ.Contam.Toxicol. 15(2):147-154.

10198

AF, UEndp, Dur

Nishiuchi, Y.. 1979. Toxicity of Pesticides to
Animals in Freshwater. LXII. The Aquiculture
(Suisan Zoshoku) 27(2): 119-124 (JPN).

6956

Norberg-King, T.J.. 1987. An Evaluation of the
Fathead Minnow Seven-Day Subchronic Test
for Estimating Chronic Toxicity. M.S.Thesis,
University of Wyoming, Laramie, WY :80 p..

17878

AF, UEndp

Norberg-King, T.J.. 1989. An Evaluation of the
Fathead Minnow Seven-Day Subchronic Test
For Estimating Chronic Toxicity.
Environ.Toxicol.Chem. 8(11): 1075-1089.

5313

AF, Con

Office of Pesticide Programs. 2000. Pesticide
Ecotoxicity Database (Formerly:
Environmental Effects Database (EEDB)).
Environmental Fate and Effects Division,
U.S.EPA, Washington, D.C..

344

Patil, H.S., and M.B. Kaliwal. 1986. Relative
Sensitivity of a Freshwater Prawn
Macrobrachium hendersodyanum to Heavy
Metals. Environ.Ecol. 4(2):286-288.

12787

AF, Con

Rai, L.C., and M. Raizada. 1985. Effect of
Nickel and Silver Ions on Survival, Growth,
Carbon Fixation and Nitrogenase Activity in
Nostoc muscorum: Regulation of Toxicity by
EDTAand. J.Gen.Appl.Microbiol. 31(4):329-
337.

13292

Plant, AF, UEndp

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of OR
WQS

Rao, T.S., M.S. Rao, and S.B.S.K. Prasad.
1975. Median Tolerance Limits of Some
Chemicals to the Fresh Water Fish "Cyprinus
carpio". Indian J.Environ.Health 17(2): 140-146.

2077

See Comment

The test data provided in
ECOTOX for this study appears
to be useful. The hardness
normalized dissolved LC50 for 96
h R,M test would be 1.72 ug/L,
making the most representative
species SMAV approximately
0.86 ug/L, which falls well below
the CMC of 3.2 ug/L. This datum
has been incorporated in the
evaluation.

480

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Rombough, P. J.. 1985. The Influence of the
Zona radiata on the Toxicities of Zinc, Lead,
Mercury, Copper and Silver Ions to Embryos of
Steelhead Trout Salmo gairdneri.
Comp.Biochem.Physiol.C 82(1 ):115-117.

11219

AF, UEndp, Con

Shivaraj, K.M., and H.S. Patil. 1988. Toxicity of
Silver Chloride to a Fresh Water Fish
Lepidocephalichthyes guntea. Environ. Ecol.
6(3):713-716.

806

AF, Dur, Con

Snell, T.W., B.D. Moffat, C. Janssen, and G.
Persoone. 1991. Acute Toxicity Tests Using
Rotifers IV. Effects of Cyst Age, Temperature,
and Salinity on the Sensitivity of Brachionus
calyciflorus. Ecotoxicol.Environ.Saf. 21(3):308-
317 (OECDG Data File).

9385

AF, Dur

Snell, T.W.. 1991. New Rotifer Bioassaysfor
Aquatic Toxicology. Final Report, U.S.Army
Medical Research and Development
Command, Ft.Detrick, Frederick, MD :29
p.(U.S.NTIS AD-A258002).

17689

AF, Dur

Stangenberg, M.. 1975. The Influence of the
Chemical Composition of Water on the Pike
Perch (Lucioperca lucioperca L.) Fry from the
Lake Gopio. Limnologica 9(3):421-426.

2700

AF, UEndp,Dur

Suzuki, K.. 1959. The Toxic Influence of Heavy
Metal Salts upon Mosquito Larvae. Hokkaido
Univ.J.Fac.Sci.Ser. 6(14): 196-209.

2701

AF, UEndp, Eff, Dur

Tsuji, S., Y. Tonogai, Y. Ito, and S. Kanoh.
1986. The Influence of Rearing Temperatures
on the Toxicity of Various Environmental
Pollutants for Killifish (Oryzias latipes).
J.Hyg.Chem.(Eisei Kagaku) 32(1):46-53 (JPN)
(ENG ABS).

12497

AF, Dur, Con

Turbak, S.C., S.B. Olson, and G.A. McFeters.
1986. Comparison of Algal Assay Systems for
Detecting Waterborne Herbicides and Metals.
Water Res. 20(1):91-96.

11780

Plant, AF, Dur

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of OR
WQS

Wang, W.. 1994. Rice Seed Toxicity Tests for
Organic and Inorganic Substances.
Environ.Monit.Assess. 29:101 -107.

45060

Plant, AF, Dur

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of OR
WQS

Webb, N.A., and C.M. Wood. 1998.
Physiological Analysis of the Stress Response
Associated with Acute Silver Nitrate Exposure
in Freshwater Rainbow Trout (Oncorhynchus

18939

UEndp, Dur

481

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

mykiss). Environ.Toxicol.Chem. 17(4):579-588.

Williams, P.L., and D.B. Dusenbery. 1990.
Aquatic Toxicity Testing Using the Nematode,
Caenorhabditis elegans.
Environ.Toxicol.Chem. 9(10): 1285-1290.

3437

Wilson, W.B., and L.R. Freeburg. 1980.
Toxicity of Metals to Marine Phytoplankton
Cultures. EPA-600/3-80-025, U.S.EPA,
Narragansett, Rl :110 p.(U.S.NTIS PB80-
182843).

5557

Plant, AF, Dur

Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of OR
WQS

Wood, C.M., C. Hogstrand, F. Galvez, and
R.S. Munger. 1996. The Physiology of
Waterborne Silver Toxicity in Freshwater
Rainbow Trout (Oncorhynchus mykiss) 1. The
Effects of Ionic Ag+. Aquat.Toxicol. 35(2):93-
109.

18582

UEndp, Eff, Dur

Ziegenfuss, P.S., W.J. Renaudette, and W.J.
Adams. 1986. Methodology for Assessing the
Acute Toxicity of Chemicals Sorbed to
Sediments: Testing the Equilibrium
Partitioning Theory. In: T.M.Poston and
R.Purdy (Eds.), Aquatic Toxicology and
Environmental Fate, 9th Volume, ASTM STP
921, Philadelphia, PA:479-493.

7884

AF, Dur, Con

Zuiderveen, J.A., and W.J. Birge. 1996.
Interaction of Silver and Metal Chelators on
Ceriodaphnia dubia Survival and
Reproduction. In: A.W.Andren and T.W.Bober
(Eds.), 3rd Int.Conf.Proc.Transport, Fate and
Effects of Silver in the Environment, Aug.6-9,
1995, Washington, D.C. : 135-142.

20264

AF, UEndp, Dur

Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

1 For the studies that were not utilized, but the most representative SMAV/2 or most representative

SMCV fell below the criterion, or, if the studies were for a species associated with one of the four most

482

-------
sensitive genera used to calculate the FAV in the most recent national ambient water quality criteria

dataset used to derive the CMC , EPA is providing a transparent rationale as to why they were not
utilized (see below).

2 For the studies that were not utilized because they were not found to be pertinent to this determination
(including failing the QA/QC procedures listed in Appendix A) upon initial review of the download
from ECOTOX, EPA is providing the code that identifies why EPA determined that the results of the
study were not reliable (see Appendix L).

General QA/QC failure because non-resident species in Oregon

Tests with the following several species were used in the EPA BE of OR WQS for silver in freshwater, but were not considered in the
CWA review and approval/disapproval action of the standards because these species do not have a breeding wild population in
Oregon's waters:

Poecilia

reticulata

Guppy

Khangarot and Ray 1988

Gammarus

pseudolimnaeus

Scud

Lima et al. 1982

Jordanella

floridae

Flagfish

Lima et al. 1982

Other Acute tests failins QA/QC by species

Daphnia magna - Cladoceran

The following test was included in EPA's BE of the OR WQS and the 1980 ALC document for silver in freshwater, but were not used
in this CWA review and approval/disapproval action of these standards because the tests were not based on the preferred flow-through
measured test conditions; however, other flow-through measured test concentrations were available for this species.

Nebeker, A.V., C.K. McAuliffe, R. Mshar and D.G. Stevens. 1983. Toxicity of silver to steelhead and rainbow trout, fathead
minnows and Daphnia magna. Environ. Toxicol. Chem. 2: 95-104.

Two LC50 values from S,M tests ranging from 2.58 to 4.94 |ig/L.

Chapman, G.A. 1980. Memorandum to Q. Pickering (Newtown Fish Toxicology Station, July 14).

89 U.S. EPA. 1980. Ambient Water Quality Criteria Documents for Silver. Unpublished document authored by W. A. Brungs and D.J. Hansen, U.S. EPA ERL-
Narragansett and Gulf Breeze, respectively.

483

-------
One LC50 value from S,M test of 0.75 |ig/L.

Elnabarawy, M.T., A.N. Welter and R.R. Robideau. 1986. Relative sensitivity of three daphnid species to selected organic and
inorganic chemicals. Environ. Toxicol. Chem. 5: 393-398.

One LC50 value from S,U test of 0.28 |ig/L.

Khangarot, B.S. and P.K. Ray. 1989. Investigation of correlation between physicochemical properties of metals and their
toxicity to the water flea Daphttia magna Straus. Ecotoxicol. Environ. Saf. 18: 109-120.

One LC50 value from S,U test of 1.89 |ig/L.

Lemke, A.E. 1981. Interlaboratory Comparison Acute Testing Set. EPA 600/3-81-005 or PB81-160772. National Technical
Information Service, Springfield, VA.

Ten LC50 values from static tests ranging from 1.17 to 20.77 |ig/L.

Erickson, R.J., L.T. Brooke, M.C. Kahl, F. Vande Venter. S.L. Harting, T.P. Markee and R.L. Spehar. 1998. Effects of
laboratory test conditions on the toxicity of silver to aquatic organisms. Environ. Toxicol. Chem. 17: 572-578.

One LC50 value from S,M test of 1.74 |ig/L.

LeBlanc, G.A. 1980. Acute toxicity of priority pollutants to water flea (Daphnia magna). Bull. Environ. Contam. Toxicol. 24:
684-691.

One LC50 value from S,M test of 2.24 |ig/L.

Karen, D.J., D.R. Ownby, B.L. Forsythe, T.P. Bills, T.W. La Point, G.B. Cobb and S.J. Klaine. 1999. Influence of water quality
on silver toxicity to rainbow trout (O. my kiss), fathead minnows (P. promelas), and the waterflea (D. magna). Environ. Toxicol.
Chem. 18(1): 63-70.

Twenty-four LC50 values from static tests ranging from 0.15 to 2.77 |ig/L.

Pimephales promelas — Fathead minnow

484

-------
Nebeker, A.V., C.K. McAuliffe, R. Mshar and D.G. Stevens. 1983. Toxicity of silver to steelhead and rainbow trout, fathead
minnows and Daphttia magna. Environ. Toxicol. Chem. 2: 95-104.

One LC50 value from S,M test of 42.20 |ig/L.

Bury, N.R., F. Galvez and C.M. Wood. 1999a. Effects of chloride, calcium and dissolved organic carbon on silver toxicity:
Comparison between rainbow trout and fathead minnows. Environ. Toxicol. Chem. (in press).

Seven LC50 values from R,U tests ranging from 2.55 to 1954.53 |ig/L.

Holcombe, G.W., G.L. Phipps and J.T. Fiandt. 1983. Toxicity of selected priority pollutants to various aquatic organisms.
Ecotoxicol. Environ. Safety 7: 400-409.

One LC50 value from S,M test of 47.35 |ig/L.

Erickson, R.J., L.T. Brooke, M.C. Kahl, F. Vande Venter, S.L. Harting, T.P. Markee and R.L. Spehar. 1998. Effects of
laboratory test conditions on the toxicity of silver to aquatic organisms. Environ. Toxicol. Chem. 17: 572-578.

Twelve LC50 values from S,M tests ranging from 2.37 to 46.71 |ig/L.

Lemke, A.E. 1981. Interlaboratory Comparison Acute Testing Set. EPA 600/3-81-005 or PB81-160772. National Technical
Information Service, Springfield, VA.

Ten LC50 values from S,M tests ranging from 12.13 to 91.41 |ig/L. Some data used for this species from this study.

Karen, D.J., D.R. Ownby, B.L. Forsythe, T.P. Bills, T.W. La Point, G.B. Cobb and S.J. Klaine. 1999. Influence of water quality
on silver toxicity to rainbow trout (O. mykiss), fathead minnows (P. promelas), and the waterflea (D. magna). Environ. Toxicol.
Chem. 18(1): 63-70.

Twenty-three LC50 values from S,U tests ranging from 0.71 to 27.22 |ig/L.

Forsythe, B.L., II. 1996. Silver in a Freshwater Ecosystem: Acute Toxicity and Trophic Transfer. Ph.D. Thesis. Clemson
University, Clemson, SC: 149 pp.

Thirty-two LC50 values from S,M tests ranging from 0.72 to 73.37 |ig/L.

The following test was included in EPA's 1980 ALC document for silver in freshwater, but was not used in this CWA review and
approval/disapproval action of these standards because some detail was missing and numerous other representative F,M tests were
available to calculate the SMAV for the species. The two LC50s reported for fathead minnow from the study were 3.9 and 4.8 |ig/L in
soft and hard water, respectively.

485

-------
Goettl, J.P., Jr. and P.H. Davies. 1978. Water Pollution Studies. Job Progress Report. Colorado Division of Wildlife,
Department of Natural Resources, Boulder, CO.

The following test was included in EPA's BE of the OR WQS document for silver in freshwater, but was not used in this CWA review
and approval/disapproval action of these standards because the same data existed in another study that had been used to calculate the
SMAV:

LeBlanc, G.A., J.D. Maston, A.P. Paradice, B.F. Wilson, H.B. Lockhart, Jr. and K.A. Robillard. 1984. The influence of
speciation on the toxicity of silver to fathead minnow (Pimephalespromelas). Environ. Toxicol. Chem. 3: 37-46.

486

-------
Appendix M Tributyltin (freshwater)
Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Alabaster, J.S.. 1969. Survival of Fish in 164 Herbicides, Insecticides, Fungicides,
Wetting Agents and Miscellaneous Substances. Int. Pest Control 11(2):29-35 (Author
Communication Used).

542

Dur, Con

Avery, S.V., G.A. Codd, and G.M. Gadd. 1993. Biosorption of Tributyltin and Other
Organotin Compounds by Cyanobacteria and Microalgae. Appl.Microbiol.Biotechnol.
39(6):812-817.

16761

Dur, UEndp

Baldwin, I.G., M.M.I. Harman, and D.A. Neville. 1994. Performance Characteristics of a
Fish Monitor for Detection of Toxic Substances -1. Laboratory Trails. Water Res.
28(10):2191-2199.

4437

Dur, UEndp

Bodar, C.W.M., E.G. Van Donselaar, and H.J. Herwig. 1990. Cytopathological
Investigations of Digestive Tract and Storage Cells in Daphnia magna Exposed to
Cadmium and Tributyltin. Aquat.Toxicol. 17(4):325-338.

3509

Dur, UEndp

Borgmann, U., Y.K. Chau, P.T.S. Wong, M. Brown, and J. Yaromich. 1996. The
Relationship Between Tributyltin (TBT) Accumulation and Toxicity to Hyalella azteca for
Use in Identifying TBT Toxicity in the Field. J.Aquat.Ecosyst.Health 5(3):199-206.

7104

Dur

Boyer, L., and L.R. Sherman. 1990. A Study in the Threshold Toxicity of bis-Tri-n-
Butyltin Oxide upon the Comet Goldfish, Carassius auratus.
J.Pa.Acad.Sci.63(Suppl.):207 (ABS).

216

Dur, Con, UEndp

Bruggemann, R., J. Schwaiger, and R.D. Negele. 1995. Applying Hasse Diagram
Technique for the Evaluation of Toxicological Fish Tests. Chemosphere 30(9):1767-
1780.

16035

Endpoint (HIS)

Buzinova, N.S., and O.V. Parina. 1984. Action of a Pollutant on Plastic Metabolism of
Fish. C.A.Sel.-Environ.Pollut.25(101):2 / In: M.M.Telitchenko (Ed.)
Sb.Tr.Vses.Soveshch.Sanit.Gidrobiol.4th 1991:97-102 (RUS).

11008

Dur, Insuff. Control, Endpoint (Lethal)

487

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Clayton, M.E., R. Steinmann, and K. Fent. 2000. Different Expression Patterns of Heat
Shock Proteins hsp 60 and hsp 70 in Zebra Mussels (Dreissena polymorpha) Exposed
to Copper and Tributyltin. Aquat.Toxicol. 47(3/4):213-226.

48289

Dur, Endpoint (ACC)

Das, V.G.K., L.Y. Kuan, K.I. Sudderuddin, C.K. Chang, V. Thomas, C.K. Yap, M.K. Lo,
G.C.Ong, W.K.Ng, and Y.Hoi-Sen. 1984. The Toxic Effects of Triorganotin (IV)
Compounds on the Culicine Mosquito, Aedes aegypti (L). Toxicology 32(1):57-66.

11009

Dur

De Vries, H., A.H. Penninks, N.J. Snoeij, and W. Seinen. 1991. Comparative Toxicity of
Organotin Compounds to Rainbow Trout (Oncorhynchus mykiss) Yolk Sac Fry.

Sci.Total Environ. 103(2/3):229-243.

5674

Dur, Endpoint (LC100, LOEC)

Dojmi di Delupis, G., and R. Miniero. 1989. Preliminary Studies on the TBTO Effects on
FreshWater Biotic Communities. Riv.ldrobiol. 28(1/2):63-68.

8704

Dur, Unknown Endpoint

Douglas, M.T., D.O. Chanter, I.B. Pell, and G.M. Burney. 1986. A Proposal for the
Reduction of Animal Numbers Required for the Acute Toxicityto Fish Test (LC50
Determination). Aquat.Toxicol. 8(4):243-249.

12210

Insuff. Control

Fargasova, A.. 1997. The Effects of Organotin Compounds on Growth, Respiration
Rate, and Chlorophyll a Content of Scenedesmus quadricauda. Ecotoxicol.Environ.Saf.
37:193-198.

18323

Dur, Endpoint (PHY, Unknown)

Fargasova, A.. 1998. Comparison of Tributyltin Compound Effects on the Alga
Scenedesmus quadricauda and the Benthic Organisms Tubifex tubifex and Chironomus
plumosus. Ecotoxicol.Environ.Saf. 41(3):222-230.

20058

Dur, Endpoint (PHY)

Plants do not drive
criteria, and therefore, are
not included in CWA
review and approval of
ORWQS

Fargasova, A., and M. Drtil. 1996. Respirometric Toxicity Test: Freshwater Alga
Scenedesmus quadricauda Sensitivity to Organotin Compounds.
Bull.Environ.Contam.Toxicol. 56(6):993-999.

17429

Dur, Endpoint (PHY)

Fent, K.. 1991. Bioconcentration and Elimination of Tributyltin Chloride by Embryos and
Larvae of Minnows Phoxinus phoxinus. Aquat.Toxicol. 20:147-158.

5319

Non-NA, Dur, Endpoint (ACC)

488

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Fent, K.. 1992. Embryotoxic Effects of Tributyltin on the Minnow Phoxinus phoxinus.
Environ.Pollut. 76(3):187-194.

5845

Non-NA, Dur, Insuff. Control, Endpoint
(DVP, Lethal, Unknown)

Fent, K., and J. Hunn. 1993. Uptake and Elimination of Tributyltin in Fish-Yolk-Sac
Larvae. Mar.Environ.Res. 35(1/2):65-71.

4181

Non-NA, Dur, Insuff. Control, Endpoint
(ACC)

Fent, K., and P.W. Looser. 1995. Bioaccumulation and Bioavailability of Tributyltin
Chloride: Influence of pH and Humic Acids. Water Res. 29(7): 1631-1637.

15019

Non-NA, Dur, Endpoint (ACC)

Fent, K., and W. Meier. 1992. Tributyltin-lnduced Effects on Early Life Stages of
Minnows Phoxinus phoxinus. Arch.Environ.Contam.Toxicol. 22(4):428-438.

11253

Dur, Endpoint (HIS, Unknown)

Geiger, D.L., L.T. Brooke, and D.J. Call. 1990. Acute Toxicities of Organic Chemicals to
Fathead Minnows (Pimephales promelas), Vol. 5. Center for Lake Superior
Environmental Stud., Univ.of Wisconsin-Superior, Superior, Wl 1:332 p..

3217

Secondary

Same data used from a
different study reported by
the authors in a
subsequent peer-reviewed
article

Grinwis, G.C.M., A. Boonstra, E.J. Van den Brandhof, J.A.M. Dormans, M. Engelsma,
and R.V.Kuiper. ... 1998. Short-Term Toxicity of Bis(tri-n-butyltin)Oxide in Flounder
(Platichthys flesus): Pathology and Immune Function. Aquat.Toxicol. 42(1):15-36.

19152

Dur, Endpoint (FDB, HIS, IMM, MPH,
Unknown)

Hooftman, R.N., D.M.M. Adema, and J. Kauffman-Van Bommel. 1989. Developing a
Set of Test Methods for the Toxicological Analysis of the Pollution Degree of
Waterbottoms. Rep. No. 16105, Netherlands Organization for Applied Scientific
Research:68 p.(DUT).

5356

Non-NA, Dur

Itow, T., R.E. Loveland, and M.L. Botton. 1998. Developmental Abnormalities in
Horseshoe Crab Embryos Caused by Exposure to Heavy Metals.
Arch.Environ.Contam.Toxicol. 35(1):33-40.

19470

Endpoint (Lethal)

Kuhn, R., and M. Pattard. 1990. Results of the Harmful Effects of Water Pollutants to
Green Algae (Scenedesmus subspicatus) in the Cell Multiplication Inhibition Test.
Water Res. 24(1):31-38 (OECDG Data File).

2997

Dur

Kuhn, R., M. Pattard, K. Pernak, and A. Winter. 1989. Results of the Harmful Effects of
Water Pollutants to Daphnia magna in the 21 Day Reproduction Test. Water Res.
23(4):501-510 (OECDG Data File).

847

Dur, Insuff. Control

489

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Laughlin, R., and 0. Linden. 1982. Sublethal Responses of the Tadpoles of the
European Frog Rana temporaria to Two Tributyltin Compounds.
Bull.Environ.Contam.Toxicol. 28(4):494-499.

15464

Dur, Unknown Endpoint

Lewis, J.W., A.N. Kay, and N.S. Hanna. 1995. Responses of Electric Fish (Family
Mormyridae) to Inorganic Nutrients and Tributyltin Oxide. Chemosphere 31(7):3753-
3769.

16156

Dur, Endpoint (PHY)

Machado, J., J. Coimbra, and C. Sa. 1989. Shell Thickening in Anodonta cygnea by
TBTO Treatments. Comp.Biochem.Physiol.C 92(1):77-80.

796

Dur, Insuff. Control, Unknown Endpoint

Maguire, R.J., P.T.S. Wong, and J.S. Rhamey. 1984. Accumulation and Metabolism of
Tri-N-Butyltin Cation by a Green Alga, Ankistrodesmus falcatus. Can.J.Fish.Aquat.Sci.
41 (3):537-540.

10827

Dur, Insuff. Control, Endpoint (ACC)

Mathijssen-Spiekman, E.A.M., J.H. Canton, and C.J. Roghair. 1989. Research After the
Toxicity of TBTO for a Number of Fresh Water Organisms. Rep. No.668118-001,
Natl.Inst.Public Health and Environ.Hyg.:48 p.(DUT).

5337

Non-NA, Dur, Endpoint (DVP, HIS,
Unknown)

Meador, J.P.. 1986. An Analysis of Photobehavior of Daphnia magna Exposed to
Tributyltin. In: Oceans '86 Conference Records: Science-Engineering-Adventure, Vol.4,
Organotin Symp., Washington, DC, Sept.23-25, IEEE Publ.Serv., NY :1213-1218.

12847

Dur

Nagase, H., T. Hamasaki, T. Sato, H. Kito, Y. Yoshioka, and Y. Ose. 1991. Structure-
Activity Relationships for Organotin Compounds on the Red Killifish Oryzias latipes.
Appl.Organomet.Chem. 5:91-97.

18537

Non-NA, Dur

Oberdorster, E., D. Rittschof, and G.A. LeBlanc. 1998. Alteration of [14C]-Testosterone
Metabolism After Chronic Exposure of Daphnia magna to Tributyltin.
Arch.Environ.Contam.Toxicol. 34(1):21-25.

19000

Endpoint (DVP, No Effect, Unknown)

Orthuber, G.. 1991. Clinical and Haematological Studies of the Subacute Toxicity of bis
(Tri-n-Butyltin) Oxide in Rainbow Trout (Oncorhynchus mykiss). Ph.D.Thesis, Ludwig-
Maximilians Univ., Muenchen, Germany:194 p.(GER) (ENG ABS).

17357

Endpoint (PHY, Unknown)

490

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Parina, O.V., and R.D. Ozrina. 1989. Evaluation of the Toxic Effect of Organotin
Compounds in Carp as Related to Their Accumulation and Excretion. Hydrobiol.J.
25(1):72-77.

3186

Dur, Insuff. Control, Endpoint (ACC,
Unknown)

Quick, T., and N.F. Cardarelli. 1977. Environmental Impact of Controlled Release
Molluscicides and Their Degradation Products: A Preliminary Report. In:
Proc.Int.Controlled Release Pestic.Symp. :90-104.

68590

Dur, Endpoint (LT100, Lethal, Unknown),
LT

Rurangwa, E., A. Biegniewska, E. Slominska, E.F. Skorkowski, and F. Ollevier. 2002.
Effect of Tributyltin on Adenylate Content and Enzyme Activities of Teleost Sperm: A
Biochemical Approach to Study the Mechanisms of Toxicant Reduced Spermatozoa
Motility. Comp.Biochem.Physiol.C 131 (3):335-344.

65145

Dur, Endpoint (PHY, Unknown)

Santos, A.T.Jr., M.J. Santos, B.L. Bias, and E.A. Banez. 1977. Field Trials Using Slow
Release Rubber Molluscicide Formulations, MT-1E (BioMet SRM) and CBL-9B. In:
R.L.Goulding (Ed.), Proc.-Int.Controlled Release Pestic.Symp., Oregon State Univ.,
Corvallis, OR :114-123.

68589

Field, Endpoint (Lethal, Unknown)

Sarojini, R., B. Indira, and R. Nagabhushanam. 1990. Effect of the Lethal and Sublethal
Concentrations of Two Antifouling Organometallic Compounds CuS04 and TBTO on
the Eyestalks of Freshwater Prawn. J.Freshw.Biol. 2(1):29-35.

3719

Endpoint (HIS)

Scadding, S.R.. 1990. Effects of Tributyltin Oxide on the Skeletal Structures of
Developing and Regenerating Limbs of the Axolotl Larvae, Ambystoma mexicanum.
Bull.Environ.Contam.Toxicol. 45(4):574-581.

68550

Endpoint (DVP, Lethal, No Effect,
Unknown)

Schulte-Oehlmann, U., C. Bettin, P. Fioroni, J. Oehlmann, and E. Stroben. 1995. Marisa
cornuarietis (Gastropoda, Prosobranchia): A Potential TBT Bioindicator for Freshwater
Environments. Ecotoxicology 4(6):372-384.

18104

Endpoint (ACC, Unknown)

Schwaiger, J., F. Bucher, H. Ferling, W. Kalbfus, and R.D. Negele. 1992. A Prolonged
Toxicity Study on the Effects of Sublethal Concentrations of Bis(Tri-n-Butyltin)Oxide
(TBTO): Histopathological and Histochemical. Aquat.Toxicol. 23(1):31-48.

6126

Endpoint (ACC, HIS)

491

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Snell, T.W., B.D. Moffat, C. Janssen, and G. Persoone. 1991. Acute Toxicity Tests
Using Rotifers IV. Effects of Cyst Age, Temperature, and Salinity on the Sensitivity of
Barachionus calyciflorus. Ecotoxicol.Environ.Saf. 21(3):308-317 (OECDG Data File).

9385

Dur

Tas, J.W., A. Keizer, and A. Opperhuizen. 1996. Bioaccumulation and Lethal Body
Burden of Four Triorganotin Compounds. Bull.Environ.Contam.Toxicol. 57(1): 146-154.

17079

Dur, Endpoint (ACC)

Triebskorn, R., H.R. Kohler, J. Flemming, T. Braunbeck, R.D. Negele, and H. Rahmann.
1994. Evaluation of bis(Tri-n-Butyltin)Oxide (TBTO) Neurotoxicity in Rainbow Trout
(Oncorhynchus mykiss). I. Behaviour, Weight Increase, and Tin Content.
Aquat.Toxicol. 30(3): 189-197.

17449

Endpoint (ACC, Unknown)

Triebskorn, R., H.R. Kohler, K.H. Kortje, R.D. Negele, H. Rahmann, and T. Braunbeck.
1994. Evaluation of bis(Tri-n-Butyltin)Oxide (TBTO) Neurotoxicity in Rainbow Trout
(Oncorhynchus mykiss). II. Ultrastructural Diagnosis and Tin Localization by Energy
Filtering Transmission Electron Microscopy (EFTEM). Aquat.Toxicol. 30(3):199-213.

17448

Endpoint (ACC, HIS)

Tsuda, T., H. Nakanishi, S. Aoki, and J. Takebayashi. 1988. Bioconcentration and
Metabolism of Butyltin Compounds in Carp. Water Res. 22(5):647-651.

12977

Dur, Insuff. Control, Endpoint (ACC)

Tsuda, T., M. Wada, S. Aoki, and Y. Matsui. 1987. Excretion of Bis(Tri-n-Butyltin)Oxide
and Triphenyltin Chloride from Carp. Toxicol.Environ.Chem. 16(1 ):17-22.

7771

Dur, Insuff. Control, Endpoint (ACC)

Tsuda, T., S. Aoki, M. Kojima, and H. Harada. 1990. The Influence of pH on the
Accumulation of Tri-N-Butyltin Chloride and Triphenyltin Chloride in Carp.

Com p. Biochem. Physiol. C 95(2): 151 -153.

3463

Dur, Insuff. Control, Endpoint (ACC)

Tsuda, T., S. Aoki, M. Kojima, and H. Harada. 1990. Differences Between Freshwater
and Seawater-Acclimated Guppies in the Accumulation and Excretion of Tri-N-Butyltin
Chloride and Triphenyltin Chloride. Water Res. 24(11):1373-1376.

3486

Dur, Insuff. Control, Endpoint (ACC)

492

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Tsuda, T., S. Aoki, M. Kojima, and H. Harada. 1991. Accumulation of Tri-n-Butyltin
Chloride and Triphenyltin Chloride by Oral and Via Gill Intake of Goldfish (Carassius
auratus). Comp.Biochem.Physiol.C 99(1/2):69-72.

9240

Endpoint (ACC)

Tsuda, T., S. Aoki, M. Kojima, and T. Fujita. 1992. Accumulation and Excretion of Tri-n-
Butyltin Chloride and Triphenyltin Chloride by Willow Shiner. Comp.Biochem.Physiol.C
101(1):67-70.

3999

Insuff. Control, Endpoint (ACC)

Umezu, T.. 1991. Saponins and Surfactants Increase Water Flux in Fish Gills.
Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan Gakkaishi) 57(10):1891-1896.

7136

Non-NA, Dur, Endpoint (PHY)

Upatham, E.S., M. Koura, M.D. Ahmed, and A.H. Awad. 1980. Laboratory Trials of
Controlled Release Molluscicides on Bulinus (Ph.) abyssinicus the Intermediate Host of
Schistosoma haematobium in Somalia. In: R.Baker (Ed.), Controlled Release of
Bioactive Materials, Academic Press, NY :461-469.

67506

Dur, Endpoint (LT100), LT

Vighi, M., and D. Calamari. 1985. QSARs for Organotin Compounds on Daphnia
magna. Chemosphere 14(11 -12):1925-1932.

12391

Dur, Insuff. Control

Walker, K.E.. 1977. Organotin Contact Studies. In: R.L.Goulding (Ed.), Proc.-
Int.Controlled Release Pestic.Symp., Oregon State Univ., Corvallis, OR : 124-131.

68588

Dur, Unknown Endpoint

Wang, W.X., J. Widdows, and D.S. Page. 1992. Effects of Organic Toxicants on the
Anoxic Energy Metabolism of the Mussel Mytilus edulis. Mar.Environ.Res. 34(1-4):327-
331.

4391

Dur, Insuff. Control, Endpoint (PHY)

Wester, P.W., and J.H. Canton. 1987. Histopathological Study of Poecilia reticulata
(Guppy) After Long-Term Exposure to Bis(Tri-n-Butyltin)oxide (TBTO) and Di-n-
Butyltindichloride. Aquat.Toxicol. 10(2-3): 143-165.

12607

Nom, Insuff. Control, Endpoint (HIS)

Wester, P.W., J.H. Canton, A.A.J. Van lersel, E.I. Krajnc, and H.A.M. Vaessen. 1990.
The Toxicity of Bis(Tri-n-Butyltin)Oxide (TBTO) and Di-n-Butyltindichloride (DBTC) in
the Small Fish Species Oryzias latipes (Medaka) and Poecilia. Aquat.Toxicol. 16(1 ):53-
72.

3003

Endpoint (ACC, HIS, Unknown)

493

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Wong, P.T.S., Y.K. Chau, 0. Kramar, and G.A. Bengert. 1982. Structure-Toxicity
Relationship of Tin Compounds on Algae. Can.J.Fish.Aquat.Sci. 39(3):483-488.

15764

Species, Dur, Insuff. Control, Endpoint
(PHY)

Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

3) For the studies that were not utilized, but the most representative SMAV/2 or most representative SMCV fell below the
criterion, or, if the studies were for a species associated with one of the four most sensitive genera used to calculate the
FAV in the most recent national ambient water quality criteria dataset used to derive the CMC90, EPA is providing a
transparent rationale as to why they were not utilized (see below).

General QA/QC failure because non-resident species in Oregon

The tests with the following species were used in the EPA BE of OR WQS for tributyltin in freshwater, but were not considered in the
CWA review and approval/disapproval action of the standards because these species do not have a breeding wild population in
Oregon's waters:

Hydra

oligactis

Hydra

TAI 1989a

Hydra

littoralis

Hydra

TAI 1989a; TAI 1989b

Chlorohydra

viridissima

Hydra

TAI 1989b

Gammarus

pseudolimnaeus

Scud

Brooke et al. 1986

90 U.S. EPA. 2003. Ambient Water Quality Criteria Document for Tributyltin (TBT) - Final. EPA-822/R-03-031.

494

-------
Appendix N Zinc (freshwater)
Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Abbasi, S.A., and R. Soni. 1986. An
Examination of Environmentally Safe Levels of
Zinc (II), Cadmium (II) and Lead (II) with
Reference to Impact on Channelfish Nuria
denricus. Environ.Pollut.Ser.A Ecol.Biol.
40(1):37-51.

11078

AF, Dur, Con

Abbasi, S.A., P.C. Nipaney, and R. Soni. 1985.
Environmental Consequences of the Inhibition
in the Hatching of Pupae of Aedesaegypti by
Mercury, Zinc and Chromium-the Abnormal
Toxicity of Zinc. Int. J.Environ.Stud. 24(2):107-
114.

10797

AF, UEndp, Dur

Abbasi, S.A., P.C. Nipaney, and R. Soni. 1988.
Studies on Environmental Management of
Mercury (II), Chromium (VI) and Zinc (II) with
Respect to the Impact on Some Arthropods and
Protozoans -. Int.J.Environ.Stud. 32:181-187.

13255

AF, Dur, Con

Abel, T.H., and F. Barlocher. 1984. Effects of
Cadmium on Aquatic Hyphomycetes.
Appl.Environ.Microbiol. 48(2):245-251.

11030

AF, UEndp

Admiraal, W., H. Blanck, M. Buckert-De Jong,
H. Guasch, N. Ivorra, V. Lehmann, B.A.H.
Nystrom, M.Paulsson, and S.Sabater. 1999.
Short-Term Toxicity of Zinc to Microbenthic
Algae and Bacteria in a Metal Polluted Stream.
Water Res. 33(9): 1989-1996.

20376

Plant, NoOrg, AF,
UEndp, Dur

Agrawal, S.C.. 1984. The Effects of Zinc
Sulphate on the Ultraviolet Light Sensitivity of
Chlorella vulgaris Beijernick. Curr.Sci.
53(18):989-990.

19907

Plant, AF, UEndp, Dur

Alam, M.K., and O.E. Maughan. 1992. The
Effect of Malathion, Diazinon, and Various
Concentrations of Zinc, Copper, Nickel, Lead,
Iron, and Mercury on Fish. Biol.Trace Elem.Res.
34(3):225-236.

7085

AF, UEndp, Dur

495

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Alam, M.K., and O.E. Maughan. 1995. Acute
Toxicity of Heavy Metals to Common Carp
(Cyprinus carpio). J.Environ.Sci.Health Part A
30(8):1807-1816.

45566

Anderson, B.G.. 1948. The Apparent
Thresholds of Toxicity to Daphnia magna for
Chlorides of Various Metals when Added to
Lake Erie Water. Trans.Am.Fish.Soc. 78:96-
113.

2054

Anderson, P.D., and L.J. Weber. 1975. Toxic
Response As a Quantitative Function of Body
Size. Toxicol.Appl.Pharmacol. 33(3):471-483.

2137

See comment

Not used in 1987 ALC
document

Anderson, R.L., C.T. Walbridge, and J.T. Fiandt.
1980. Survival and Growth of Tanytarsus
dissimilis (Chironomidae) Exposed to Copper,
Cadmium, Zinc, and Lead.

Arch. Environ.Contam.Toxicol.9(3):329-335
(Author Communication Used).

5249

Con

Annune, P.A., A.A. Oladimeji, and S. Ebele.
1991. Acute Toxicity of Zinc to the Fingerlings of
Clarias lazera Cuvier and Valenciennes and
Oreochromis niloticus (Trewavas). J.Aquat.Sci.
6:19-22.

17157

NonRes

Annune, P.A., and T.T. lyaniwura. 1993.
Accumulation of Two Trace Metals in Tissues of
Freshwater Fishes, Oreochromis niloticus and
Clarias gariepinus. J.Aquat.Food Product
Technol. 2(3):5-18.

16167

AF, UEndp, Dur

Arambasic, M.B., S. Bjelic, and G. Subakov.
1995. Acute Toxicity of Heavy Metals (Copper,
Lead, Zinc), Phenol and Sodium on Allium cepa
L., Lepidium sativum L. and Daphnia magna St.:
Comparative. Water Res. 29(2):497-503.

13712

Back, H.. 1983. Interactions, Uptake and
Distribution of Barium, Cadmium, Lead and Zinc
in Tubificid Worms (Annelida, Oligochaeta). In:
4th Int.Conf.on Heavy Metals in the
Environment, Heidelberg, Vol.1, Sept. 1983,
CEP Consultants Ltd., Edinburgh, U.K. :370-
371.

11865

AF, UEndp, Dur

Back, H.. 1990. Epidermal Uptake of Pb, Cd,
and Zn in Tubificid Worms. Oecologia
85(2):226-232.

20568

AF, UEndp, Dur

496

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Baird, D.J., 1. Barber, M. Bradley, A.M.V.M.
Soares, and P. Calow. 1991. A Comparative
Study of Genotype Sensitivity to Acute Toxic
Stress Using Clones of Daphnia magna Straus.
Ecotoxicol.Environ.Saf. 21 (3):257-265.

2493

Con

Baker, L., and D. Walden. 1984. Acute Toxicity
of Copper and Zinc to Three Fish Species from
the Alligator Rivers Region. Tech.Memorandum
No.8, Supervising Scientist for the Alligator
Rivers Region, Australian Gov.Publ.Serv.,
Canberra, Australi a:27.

4126

NonRes

Banerjee, V., and K. Kumari. 1988. Effect of
Zinc, Mercury and Cadmium on Erythrocyte and
Related Parameters in the Fish Anabas
testudineus. Environ.Ecol. 6(3):737-739.

803

AF, Dur, Con

Bantle, J.A., D.J. Fort, and B.L. James. 1989.
Identification of Developmental Toxicants Using
the Frog Embryo Teratogenesis Assay-Xenopus
(FETAX). Hydrobiologia 188/189:577-585.

3122

AF, Con, Eff

Bartlett, L„ F.W. Rabe, and W.H. Funk. 1974.
Effects of Copper, Zinc and Cadmium on
Selanastrum capricornutum. Water Res.
8(3): 179-186.

2254

Plant, UEndp, Dur

Bascombe, A.D., J.B. Ellis, D.M. Revitt, and
R.B.E. Shutes. 1990. The Development of
Ecotoxicological Criteria in Urban Catchments.
Water Sci.Technol. 22(10/11): 173-179.

19322

NonRes

Baudin, J.P.. 1985. Accumulation Simultanee
Par Les Voies Directe et Trophique Due 65Zn
Par Cyprinus carpio L. (Pisces, Cyprinidae).
Acta Oecol.Oecol.Appl. 6(3):259-268 (FRE)
(ENG ABS).

11697

AF, RouExp, UEndp,
Con

Baudin, J.P.. 1987. Investigation into the
Retention of 65Zn Absorbed by the Trophic
Pathway in Cyprinus carpio L. Influence of the
Ingestion Frequency and the. Water Res.
21(3):285-294 (FRE) (ENG ABS).

12611

AF, RouExp, UEndp,
Con

497

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Baudouin, M.F., and P. Scoppa. 1974. Acute
Toxicity of Various Metals to Freshwater
Zooplankton. Bull.Environ.Contam.Toxicol.
12(6):745-751.

5339

AF, Dur

Belanger, S.E., J.L. Farris, D.S. Cherry, and J.
Cairns Jr.. 1986. Growth of Asiatic Clams
(Corbicula sp.) During and After Long-Term Zinc
Exposure in Field-Located and Laboratory
Artificial Streams. Arch.Environ.Contam.Toxicol.
15(4):427-434.

11931

UEndp, Field

Bengeri, K.V., and H.S. Patil. 1986. Influence of
Hardness on the Toxicity of Zinc Sulfate to Fish
Lepidocephalichthyes guntea.
Environ.Ecol.4(1):115-117 /

Aquat.Sci. Fish.Abstr. 16(5):8451 -1Q16.

243

Dur, NonRes

Bengeri, K.V., and H.S. Patil. 1986.
Histopathological Changes Induced by Zinc in
the Intestine of a Freshwater Fish Labeo rohita
(Ham). Matsya 11:92-95.

9955

AF, NonRes, UEndp

Bengeri, K.V., and H.S. Patil. 1986. Influence of
pH on the Toxicity and Accumulation of Zinc in
the Freshwater Fish Lepidocephalichthyes
guntea. C.A.Sel.-Environ.Pollut. 15:107-19100G
(1987) / Pollut.Res. 5(3/4): 147-151.

12114

AF, Con, NonRes

Bengeri, K.V., and H.S. Patil. 1986. Respiration,
Liver Glycogen and Bioaccumulation in Labeo
rohita Exposed to Zinc. Indian
J.Comp.Anim.Physiol. 4(2):79-84.

13091

Dur, NonRes

Bengtsson, B.E.. 1974. The Effects of Zinc on
the Mortality and Reproduction of the Minnow,
Phoxinus phoxinus L.

Arch.Environ.Contam.Toxicol. 2(4):342-355.

5379

UEndp, NonRes

Bengtsson, B.E.. 1974. Effect of Zinc on Growth
of the Minnow Phoxinus phoxinus. Oikos
25(1):370-373.

8411

UEndp, NonRes

Bengtsson, B.E.. 1974. Vertebral Damage to
Minnows Phoxinus phoxinus Exposed to Zinc.
Oikos 25(2):134-139.

8485

UEndp, NonRes

498

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Bengtsson, B.E., and B. Bergstrom. 1987. A
Flowthrough Fecundity Test with Nitocra
spinipes (Harpacticoidea Crustacea) for Aquatic
Toxicity. Ecotoxicol.Environ.Saf. 14:260-268.

2332

AF, NonRes, Con

Benson, W.H., and W.J. Birge. 1983. Heavy
Metal Tolerance and Metallothionein Induction
in Fathead Minnows: Results From Field and
Laboratory Investigations.
Environ.Toxicol.Chem.4(2):209-217 (1983) /
J.Am.Coll.Toxicol. 2(2):240 (ABS).

10551

Con

Bentley, P.J.. 1992. Influx of Zinc by Channel
Catfish (Ictalurus punctatus): Uptake from
External Environmental Solutions.

Comp. Biochem. Physiol. C 101 (2):215-217.

6512

AF, UEndp, Dur, Con

Berglind, R.. 1986. Combined and Separate
Effects of Cadmium, Lead and Zinc on Ala-D
Activity, Growth and Hemoglobin Content in
Daphnia magna. Environ.Toxicol.Chem. 5:989-
995.

12155

UEndp, Dur

Berglind, R., and G. Dave. 1984. Acute Toxicity
of Chromate, DDT, PCP, TPBS, and Zinc to
Daphnia magna Cultured in Hard and Soft
Water. Bull.Environ.Contam.Toxicol. 33(1 ):63-
68.

10871

Dur, Con

Bervoets, L., and R. Blust. 2000. Effects of pH
on Cadmium and Zinc Uptake by the Midge
Larvae Chironomus riparius. Aquat.Toxicol.
49:145-157.

47526

AF, UEndp, Dur

Bervoets, L., R. Blust, and R. Verheyen. 1996.
Uptake of Zinc by the Midge Larvae
Chironomus riparius at Different Salinities: Role
of Speciation, Acclimation, and Calcium.
Environ.Toxicol. Chem. 15(8):1423-1428.

17236

AF, UEndp, Dur

Bervoets, L., R. Blust, and R. Verheyen. 1996.
Effect of Temperature on Cadmium and Zinc
Uptake by the Midge Larvae Chironomus
riparius. Arch.Environ.Contam.Toxicol.
31(4):502-511.

18235

AF, UEndp, Dur

Bieniarz, K., P. Epler, and M. Sokolowska-
Mikolajczyk. 1994. Effect of Zinc on Guppy
(Poecilia reticulata) Reproduction.

Pol .Arch. Hydrobiol. 41 (4):489-493.

17334

AF, UEndp

499

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Billard, R., and P. Roubaud. 1985. The Effect of
Metals and Cyanide on Fertilization in Rainbow
Trout (Salmo gairdneri). Water Res. 19(2):209-
214.

10552

AF, UEndp

Birge, W.J.. 1978. Aquatic Toxicology of Trace
Elements of Coal and Fly Ash. In: J.H.Thorp
and J.W.Gibbons (Eds.), Dep.Energy
Symp.Ser., Energy and Environmental Stress in
Aquatic Systems, Augusta, GA 48:219-240.

5305

Dur

Birge, W.J., J.A. Black, A.G. Westerman, and
B.A. Ramey. 1983. Fish and Amphibian
Embryos - A Model System for Evaluating
Teratogenicity. Fundam.Appl.Toxicol. 3:237-
242.

19124

Dur

Birge, W.J., J.A. Black, A.G. Westerman, and
J.E. Hudson. 1980. Aquatic Toxicity Tests on
Inorganic Elements Occurring in Oil Shale. In:
C.Gale (Ed.), EPA-600/9-80-022, Oil Shale
Symposium: Sampling, Analysis and Quality
Assurance, March 1979, U.S.EPA, Cincinnati,
OH :519-534 (U.S.NTIS PB80-221435).

11838

Dur

Birge, W.J., J.A. Black, and A.G. Westerman.
1979. Evaluation of Aquatic Pollutants Using
Fish and Amphibian Eggs as Bioassay
Organisms. In: S.W.Nielsen, G.Migaki, and
D.G.Scarpelli (Eds.), Symp.Animals Monitors
Environ.Pollut., 1977, Storrs, CT 12:108-118.

4943

Dur

Birge, W.J., J.E. Hudson, J.A. Black, and A.G.
Westerman. 1978. Embryo-Larval Bioassays on
Inorganic Coal Elements and in Situ
Biomonitoring of Coal-Waste Effluents. In:
Symp.U.S.Fish Wildl.Serv., Surface Mining Fish
Wildl.Needs in Eastern U.S., W.VA :97-104.

6199

Dur

Birge, W.J., W.H. Benson, and J.A. Black. 1983.
The Induction of Tolerance to Heavy Metals in
Natural and Laboratory Populations of Fish.
Res.Rep.No. 141, Water Resour.Res.Inst.,
University of Kentucky, Lexington, Kentucky
Y:26.

10237

Dur

500

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Bisbini, P., M. Marinelli, F. Bianucci, and P.

Legnani. 1976. Effect of Body Weight on the

Sensitivity of Alburnus alburnus alborella to

some Toxicants. Nuovi

Ann.Ig.Microbiol.27(6):557-568 (ITA) (ENG

ABS).

7728

AF, UEndp, Dur, Con

Bitton, G., K. Rhodes, and B. Koopman. 1996.
CerioFAST: An Acute Toxicity Test Based on
Ceriodaphnia dubia Feeding Behavior.
Environ.Toxicol. Chem. 15(2):123-125.

17097

AF, Eff, Dur

Bitton, G., K. Rhodes, B. Koopman, and M.
Cornejo. 1995. Short-Term Toxicity Assay
Based on Daphnid Feeding Behavior. Water
Environ. Res. 67(3):290-293.

19602

AF, RouExp

Black, J.A., and W.J. Birge. 1980. An Avoidance
Response Bioassay for Aquatic Pollutants.
Res.Report No. 123, Water Resour.Res.Inst.,
University of Kentucky, Lexington, Kentucky
Y:34-180490.

5272

Dur

Blaise, C., R. Legault, N. Bermingham, R. Van
Coillie, and P. Vasseur. 1986. A Simple
Microplate Algal Assay Technique for Aquatic
Toxicity Assessment. Toxic.Assess. 1:261-281.

12748

Plant, Af, Con

Bodar, C.W.M., A.V.D. Zee, P.A. Voogt, H.
Wynne, and D.I. Zandee. 1989. Toxicity of
Heavy Metals to Early Life Stages of Daphnia
magna. Ecotoxicol.Environ.Saf. 17(3):333-338.

3854

AF, UEndp, Dur, Con

Bogaerts, P., J. Senaud, and J. Bohatier. 1998.
Bioassay Technique Using Nonspecific
Esterase Activities of Tetrahymena pyriformis
for Screening and Assessing Cytotoxicity of
Xenobiotics. Environ.Toxicol.Chem. 17(8):1600-
1605.

18353

Ace, AF, UEndp, Dur

Borgmann, U.. 1980. Interactive Effects of
Metals in Mixtures on Biomass Production
Kinetics of Freshwater Copepods.
Can.J.Fish.Aquat.Sci. 37(8): 1295-1302.

9757

AF, UEndp, Dur, Con

Borgmann, U., and W.P. Norwood. 1995.
Kinetics of Excess (Above Background) Copper
and Zinc in Hyalella azteca and Their
Relationship to Chronic Toxicity.
Can.J.Fish.Aquat.Sci. 52(4):864-874.

16181

UEndp

501

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Borgmann, U., W.P. Norwood, and C. Clarke.
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Bringmann, G., and R. Kuhn. 1959. Water
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Cairns, J.Jr., K.W. Thompson, and A.C.
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Carter, J.W., and I.L. Cameron. 1973. Toxicity
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Castren, M., and A. Oikari. 1987. Changes of
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Chapman, G.A., S. Ota, and F. Recht. 1980.
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Crandall, C.A., and C.J. Goodnight. 1963. The
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Comment

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Dive, D., S. Robert, E. Angrand, C. Bel, H.
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Rejection Code(s)

Comment

Eddy, F.B., and J.E. Fraser. 1982. Sialic Acid
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Ewell, W.S., J.W. Gorsuch, R.O. Kringle, K.A.
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EcoRef#

Rejection Code(s)

Comment

Fleming, T.P., and K.S. Richards. 1982. Uptake
and Surface Adsorption of Zinc by the Fresh-
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ECOTOX
EcoRef#

Rejection Code(s)

Comment

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2122

Con

512

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Gomez, S., C. Villar, and C. Bonetto. 1998. Zinc
Toxicity in the Fish Cnesterodon
decemmaculatus in the Parana River and Rio
de la Plata Estuary. Environ.Pollut. 99(2):159-
165.

19136

Goodman, J.R.. 1951. Toxicity of Zinc for
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8070

AF, UEndp, Dur

Graham, J.M., P. Arancibia-Avila, and L.E.
Graham. 1996. Effects of pH and Selected
Metals on Growth of the Filamentous Green
Alga Mougeotia Under Acidic Conditions.
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19862

Plant, AF, UEndp

Grande, M.. 1966. Effect of Copper and Zinc on
Salmonid Fishes. Adv.Water Pollut.Res. 1:97-
111.

3524

AF, UEndp

Graney, R.L.Jr., D.S. Cherry, and J. Cairns Jr..
1983. Heavy Metal Indicator Potential of the
Asiatic Clam (Corbicula fluminea) in Artificial
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10815

UEndp, Field

Greene, J.C., W.E. Miller, T. Shiroyama, and E.
Merwin. 1973. Toxicity of Zinc to the Green Alga
Selenastrum capricornutum as a Function of
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14432

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Griffiths, P.R.E.. 1980. Morphological and
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5280

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Grobler, E., H.H. Du Preez, and J.H.J. Van
Vuren. 1989. Toxic Effects of Zinc and Iron on
the Routine Oxygen Consumption of Tilapia
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Comp.Biochem.Physiol.C 94(1):207-214.

3066

AF, UEndp, Dur

Grobler-Van Heerden, E., J.H.J. Van Vuran, and
H.H. Du Preez. 1991. Bioconcentration of
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Comp.Biochem. Physiol. C 100(3):629-633.

3935

AF, UEndp, Dur, Con

513

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Guilhermino, L., T.C. Diamantino, R. Ribeiro, F.
Goncalves, and A.M.V.M. Soares. 1997.
Suitability of Test Media Containing EDTAfor
the Evaluation of Acute Metal Toxicity to
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38(3):292-295.

18978

AF, Dur

Gupta, P.K., B.S. Khangarot, and V.S. Durve.
1981. Studies on the Acute Toxicity of Some
Heavy Metals to an Indian Freshwater Pond
Snail Viviparus bengalensis L. Arch.Hydrobiol.
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15745

Con

Guth, D.J., H.D. Blankespoor, and J. Cairns Jr..
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8355

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Haider, G., and W. Wunder. 1983. Experiments
with Young Spawners of Rainbow Trout (Salmo
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Muscular Damage After Long-Time Exposure to
Heavy Metals (Zinc) (Langzeit versuche mit
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10981

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Hale, J.G.. 1977. Toxicity of Metal Mining
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861

Hall, W.S., K.L. Dickson, F.Y. Saleh, J.H.
Rodgers Jr., D. Wilcox, and A. Entazami. 1986.
Effects of Suspended Solids on the Acute
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12267

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Hamilton, S.J., and K.J. Buhl. 1990. Safety
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3526

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Handy, R.D., and F.B. Eddy. 1990. The
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281

AF, UEndp, Dur, Con

514

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Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Hatakeyama, S.. 1989. Effect of Copper and
Zinc on the Growth and Emergence of Epeorus
latifolium (Ephemeroptera) in an Indoor Model
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14344

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Hatakeyama, S., and Y. Sugaya. 1989. A
Freshwater Shrimp (Paratya compressa
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Pesticides. Environ.Pollut. 59(4):325-336.

984

AF, Dur

Heath, A.G.. 1987. Effects ofWaterborne
Copper or Zinc on the Osmoregulatory
Response of Bluegill to a Hypertonic NaCI
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2986

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Hemalatha, S., and T.K. Banerjee. 1993. Acute
Toxicity of the Heavy Metal-Zinc (a Trace
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Modified Gill Structure) of the Air-Breathing
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13478

AF, Con

Herbert, D.W.M., and D.S. Shurben. 1963. A
Preliminary Study of the Effect of Physical
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8005

Dur

Herbert, D.W.M., and D.S. Shurben. 1964. The
Toxicity to Fish of Mixtures of Poisons I. Salts of
Ammonia and Zinc. Ann.Appl.Biol. 53:33-41.

8006

Dur

Herbert, D.W.M., and J.M. Vandyke. 1964. The
Toxicity to Fish of Mixtures of Poisons. II.
Copper-Ammonia and Zinc-Phenol Mixtures.
Ann.Appl.Biol. 53(3):415-421.

10193

Dur

Hickey, C.W., and M.L. Vickers. 1992.
Comparison of the Sensitivity to Heavy Metals
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Deleatidium spp. and the Cladoceran Daphnia
magna. N.Z.J.Mar.Freshwater Res. 26(1):87-93.

6309

Hilmy, A.M., N.A. El Domiaty, A.Y. Daabees,
and A. Alsarha. 1987. The Toxicity to Clarias
lazera of Copper and Zinc Applied Jointly.
Comp.Biochem.Physiol.C 87(2):309-314.

12717

AF, UEndp, Dur

515

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Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Hiraoka, Y., S. Ishizawa, T. Kamada, and H.
Okuda. 1985. Acute Toxicity of 14 Different
Kinds of Metals Affecting Medaka Fry.
Hiroshima J.Med.Sci. 34(3):327-330.

12151

UEndp, Dur

Hodson, P.V.. 1975. Zinc Uptake by Atlantic
Salmon (Salmo salar) Exposed to a Lethal
Concentration of Zinc at 3, 11, and 19C.
J.Fish.Res.Board Can. 32(12):2552-2556.

8364

UEndp, Dur

Hodson, P.V., B.R. Blunt, D.J. Spry, and K.
Austen. 1977. Evaluation of Erythrocyte Delta-
Amino Levulinic Acid Dehydratase Activity As a
Short-Term Indicator in Fish of a Harmful
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34(4):501-508.

15460

UEndp

Hogstrand, C., R.W. Wilson, D. Polgar, and
C.M. Wood. 1994. Effects of Zinc on the
Kinetics of Branchial Calcium Uptake in
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Waterborne Zinc. J.Exp.Biol. 186:55-73.

4226

AF, Dur, Con

Hogstrand, C., S.D. Reid, and C.M. Wood.
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18846

AF, UEndp, Dur

Honig, R.A., M.J. McGinniss, A.L. Buikema Jr.,
and J. Cairns Jr.. 1980. Toxicity Tests of
Aquatic Pollutants Using Chilomonas
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5253

Plant, AF

Home, M.T., and W.A. Dunson. 1995. Effects of
Low pH, Metals, and Water Hardness on Larval
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16131

AF, UEndp

Home, M.T., and W.A. Dunson. 1995. Toxicity
of Metals and Low pH to Embryos and Larvae of
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jeffersonianum. Arch. Environ. Contam .Toxicol.
29(1): 110-114.

18213

AF, UEndp

516

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Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Huebert, D.B., and J.M. Shay. 1992. Zinc
Toxicity and Its Interaction with Cadmium in the
Submerged Aquatic Macrophyte Lemna trisulca
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3977

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Huebert, D.B., and J.M. Shay. 1992. The Effect
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Ontario, Can.Tech.Rep.Fish.Aquat.Sci.No. 1863
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8818

AF, UEndp

Hughes, G.M., and L. Tort. 1985. Cardio-
Respiratory Responses of Rainbow Trout
During Recovery From Zinc Treatment.
Environ.Pollut.Ser.A Ecol.Biol. 37(3):255-266.

10647

UEndp, Dur

Hughes, G.M., and R. Flos. 1978. Zinc Content
of the Gills of Rainbow Trout (S. gairdneri) After
Treatment with Zinc Solutions Under Normoxic
and Hyposic Conditions. J.Fish Biol. 13:717-
728.

8274

UEndp, Dur

Hughes, G.M., and R.J. Adeney. 1977. The
Effects of Zinc on the Cardiac and Ventilatory
Rhythms of Rainbow Trout (Salmo gairdneri,
Richardson) and Their Responses to. Water
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10415

UEndp

Hughes, J.S.. 1973. Acute Toxicity of Thirty
Chemicals to Striped Bass (Morone saxatilis).
La.Dep.Wildl.Fish.318-343-2417:15 p.(Used
963 As Reference).

2012

Ishio, S.. 1965. Behavior of Fish Exposed to
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14092

AF, UEndp, Dur

Ismail, P.. 1988. Influence of Salinity on the
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2882

AF, Dur, Con

Jain, S.K., P. Vasudevan, and N.K. Jha. 1990.
Azolla pinnata R.Br, and Lemna minor L. for
Removal of Lead and Zinc from Polluted Water.
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45092

AF, UEndp

517

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Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

James, R.. 1990. Individual and Combined
Effects of Heavy Metals on Behaviour and
Respiratory Responses of Oreochromis
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9593

AF, UEndp

James, R., K. Sampath, and K.P. Ponmani.
1992. Effect of Metal Mixtures on Activity of Two
Respiratory Enzymes and Their Recovery in
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8972

Jamil, K., and S. Hussain. 1992. Biotransfer of
Metals to the Insect Neochetina eichhornae Via
Aquatic Plants. Arch.Environ.Contam.Toxicol.
22(4):459-463.

6395

AF, UEndp, Con

Janssen, C.R., and G. Persoone. 1993. Rapid
Toxicity Screening Tests for Aquatic Biota. 1.
Methodology and Experiments with Daphnia
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6516

AF, Dur, Con

Janssen, M.P.M., C. Oosterhoff, G.J.S.M.
Heijmans, and H. Van der Voet. 1995. The
Toxicity of Metal Salts and the Population
Growth of the Ciliate Colpoda cucculus.
Bull.Environ.Contam.Toxicol. 54(4):597-605.

20277

Ace, AF

Jaworska, M., A. Gorczyca, J. Sepiol, and P.
Tomasik. 1997. Effect of Metal Ions on the
Entomopathogenic Nematode Heterorhabditis
bacteriophora Poinar (Nematode:
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Water Air Soil Pollut. 93:157-166.

40155

AF, UEndp

Jeng, S.S., and L.T. Sun. 1981. Effects of
Dietary Zinc Levels on Zinc Concentrations in
Tissues of Common Carp. J.Nutr. 111:134-140.

2194

AF, UEndp, Con

Jenner, H.A., and J.P.M. Janssen-Mommen.
1993. Duckweed Lemna minor as a Tool for
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Sediments. Arch.Environ.Contam.Toxicol.
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16698

Jennett, J.C., J.E. Smith, and J.M. Hassett.
1982. Factors Influencing Metal Accumulation
by Algae. EPA 600/2-82-100, U.S.EPA,
Cincinnati, OH :133 p..

14512

Plant, AF, UEndp, Dur

518

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Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Johnson, 1., and P. Delaney. 1998.
Development of a 7-Day Daphnia magna
Growth Test Using Image Analysis.
Bull.Environ.Contam.Toxicol. 61:355-362.

19809

AF, UEndp

Jones, J.R.E.. 1938. The Relative Toxicity of
Salts of Lead, Zinc and Copper to the
Stickleback (Gasterosteus aculeatus L.) and the
Effect of Calcium on the Toxicity of Lead and
Zinc Salts. J.Exp.Biol. 15(3):394-407.

2657

AF, UEndp, Dur, Con

Jones, J.R.E.. 1940. A Further Study of the
Relation Between Toxicity and Solution
Pressure, with Polycelis nigra As Test Animal.
J.Exp.Biol. 17:408-415.

10012

AF, UEndp, Dur, Con

Joshi, S.N., and P. Chamoli. 1987. Toxicity of
Zinc Sulfate to the Hill Stream Fish
Noemacheilus montanus.
Aquat.Sci.Fish.Abstr. 17(8, Pt.1 ):11826-1Q17 /
Environ.Ecol. 5(1):170-172.

12782

AF, Dur, Con

Joshi, S.N., and V.P. Semwal. 1990. Toxicity of
Zinc Sulphate and Copper Sulphate to a Hill-
Stream Cobitid Fish Noemacheilus rupicola.
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14198

AF, UEndp

Kargin, F., and H.Y. Cogun. 1999. Metal
Interactions During Accumulation and
Elimination of Zinc and Cadmium in Tissues of
the Freshwater Fish Tilapia nilotica.
Bull.Environ.Contam.Toxicol. 63(4):511-519.

20648

UEndp

Karntanut, W., and D. Pascoe. 2000. A
Comparison of Methods for Measuring Acute
Toxicity to Hydra vulgaris. Chemosphere
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50836

Dur, NonRes

Khangarot, B.S.. 1981. Effect of Zinc, Copper
and Mercury on Channa marulius (Hamilton).
Acta Hydrochim.Hydrobiol. 9(6):639-649.

10721

NonRes

Khangarot, B.S.. 1981. Lethal Effects of Zinc
and Nickel on Freshwater Teleosts. Acta
Hydrochim. Hydrobiol. 9(3):297-302.

15138

Dur, NonRes

Khangarot, B.S.. 1982. Studies on the Acute
Toxicity of Zinc to a Freshwater Teleost:
Channa punctatus (Bloch). Acta
Hydrochim.Hydrobiol. 10(3):285-292.

10722

NonRes

519

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Khangarot, B.S.. 1982. Histopathological
Changes in the Branchial Apparatus of Puntius
sophore (Hamilton) Subjected to Toxic Doses of
Zinc. Arch.Hydrobiol. 93(3):352-358.

11082

Dur, NonRes

Khangarot, B.S.. 1982. The Effects of Time
Intervals Before Feeding Since the Tolerance of
Common Guppy (Lebistes reticulatus Peters) to
Zinc. Acta Hydrochim.Hydrobiol. 10(4):405-408.

11604

UEndp, Dur

Khangarot, B.S.. 1982. Acute Toxicity of Zinc to
Channa punctatus (Bloch), As a Result of
Temperature, pH and Solubility Variations. Acta
Hydrochim.Hydrobiol. 10(4):401-404.

11847

Dur, NonRes

Khangarot, B.S.. 1983. Zinc Induced Lesions in
the Gills of Rasbora Daniconius neilgeriensis
(Hamilton). Acta Hydrochim.Hydrobiol.
11 (6):675-677.

11101

AF, UEndp, Dur, Con

Khangarot, B.S.. 1991. Toxicity of Metals to a
Freshwater Tubificid Worm, Tubifex tubifex
(Muller). Bull.Environ.Contam.Toxicol. 46:906-
912.

2918

AF, Dur, Con

Khangarot, B.S., A. Sehgal, and M.K. Bhasin.
1984. Man and Biosphere - Studies on Sikkim
Himalayas. Part 2: Acute Toxicity of Mixed
Copper-Zinc Solutions on Common Carp,
Cyprinus carpio (Linn.). Acta
Hydrochim. Hydrobiol. 12(2): 131 -135.

10782

Dur

Khangarot, B.S., A. Sehgal, and M.K. Bhasin.
1985. Man and Biosphere - Studies on the
Sikkim Himalayas. Part 4: Effects of Chelating
Agent EDTA on the Acute Toxicity of Copper
and Zinc on. Acta Hydrochim.Hydrobiol.
13(1 ):121 -125.

11395

Dur

Khangarot, B.S., A. Sehgal, and M.K. Bhasin.
1985. Man and Biosphere-Studies on the Sikkim
Himalayas. Part 5: Acute Toxicity of Selected
Heavy Metals on the Tadpoles of Rana
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11438

Dur, Con

Khangarot, B.S., and P.K. Ray. 1987. Sensitivity
of Toad Tadpoles, Bufo melanostictus
(Schneider), to Heavy Metals.

Bui I. Environ. Contam. Toxicol. 38(3):523-527.

12339

Con

520

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Khangarot, B.S., and P.K. Ray. 1987. Zinc
Sensitivity of a Freshwater Snail, Lymnaea
luteola L., in Relation to Seasonal Variations in
Temperature. Bull.Environ.Contam.Toxicol.
39(1):45-49.

12574

NonRes

Khangarot, B.S., and P.K. Ray. 1988. Sensitivity
of Freshwater Pulmonate Snails, Lymnaea
luteola L., to Heavy Metals.

Bui I. Environ. Contam. Toxicol. 41 (2):208-213.

12943

Dur, Con

Khangarot, B.S., and P.K. Ray. 1989.
Investigation of Correlation Between
Physicochemical Properties of Metals and Their
Toxicity to the Water Flea Daphnia magna
Straus. Ecotoxicol.Environ.Saf. 18(2):109-120.

6631

AF, Con

Khangarot, B.S., and V.K. Rajbanshi. 1979.
Experimental Studies on Toxicity of Zinc to a
Freshwater Teleost, Rasbora daniconius
(Hamilton). Hydrobiologia 65(2):141-144.

5321

Dur, NonRes

Khangarot, B.S., and V.S. Durve. 1982. Note on
the Acute Toxicity of Zinc, and the Interactions
of Zinc and Nickel to a Freshwater Teleost
Channa punctatus (Bloch). Indian J.Anim.Sci.
52(8):722-725.

11083

NonRes

Khangarot, B.S., S. Mathur, and V.S. Durve.
1982. Comparative Toxicity of Heavy Metals
and Interaction of Metals on a Freshwater
Pulmonate Snail Lymnaea acuminata
(Lamarck). Acta Hydrochim.Hydrobiol.
10(4):367-375.

11099

Con

Khangarot, B.S., V.S. Durve, and V.K.

Rajbanshi. 1981. Toxicity of Interactions of Zinc-
Nickel, Copper-Nickel and Zinc-Nickel-Copper
to a Freshwater Teleost, Lebistes reticulatus
(Peters). Acta Hydrochim.Hydrobiol. 9(5):495-
503.

10343

Dur

Kiffney, P.M., and W.H. Clements. 1994.
Structural Responses of Benthic
Macroinvertebrate Communities from Different
Stream Orders to Zinc. Environ.Toxicol.Chem.
13(3):389-395.

4012

UEndp, NoOrg

521

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Klaverkamp, J.F., and D.A. Duncan. 1987.
Acclimation to Cadmium Toxicity by White
Suckers: Cadmium Binding Capacity and Metal
Distribution in Gill and Liver Cytosol.
Environ.Toxicol. Chem. 6(4):275-289.

12412

AF, UEndp, Con

Klerks, P.L., and P.C. Fraleigh. 1997. Uptake of
Nickel and Zinc by the Zebra Mussel Dreissena
polymorpha. Arch.Environ.Contam.Toxicol.
32(2):191-197.

17850

AF, UEndp, Dur

Kock, G., and F. Bucher. 1997. Accumulation of
Zinc in Rainbow Trout (Oncorhynchus mykiss)
after Waterborne and Dietary Exposure.

Bui I. Environ. Contam. Toxicol. 58(2):305-310.

17922

UEndp, RouExp

Kock, G., F. Bucher, and R. Hofer. 1990. Effects
of Zinc in Water and Diet on Rainbow Trout:
Accumulation and Histopathology. In: 12th
ESCPB - Conference, Physiological and
Biochemical Approaches to the Toxicological
Assessment of Environmental Pollution, Royal
Netherlands Chemical Society, Aug.27-31,
1990, Utrecht, Netherlands:2 p.(ABS).

4025

AF, UEndp, RouExp

Kothari, S., and G. Suneeta. 1990. Studies on
the Accumulation and Toxicity of Zinc Sulfate in
the Liver of a Catfish Heteropneustes fossilis
(Bloch). In: R.Hirano and I.Hanyu (Eds.), Proc.of
the 2nd Asian Fisheries Forum, Apr. 17-22,
1989, Tokyo, Japan, Asian Fisheries Society,
Manila, Philippines :947-950.

4044

AF, UEndp

Kraak, M.H.S., D. Lavy, M. Toussaint, H.
Schoon, W.H.M. Peeters, and C. Davids. 1993.
Toxicity of Heavy Metals to the Zebra Mussel
(Dreissena polymorpha). In: T.F.Nalepa and
D.W.Schloesser (Eds.), Zebra Mussels -
Biology, Impacts, and Control, Chapter 29,
Lewis Publishers, Boca Raton, FL :491-502.

17556

AF, UEndp, Dur

Kraak, M.H.S., M. Toussaint, D. Lavy, and C.
Davids. 1994. Short-Term Effects of Metals on
the Filtration Rate of the Zebra Mussel
Dreissena polymorpha. Environ.Pollut. 84:139-
143.

16692

AF, UEndp, Dur

522

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Kraak, M. Toussaint, E.A.J. Bleeker,
and D. Lavy. 1993. Metal Regulation in Two
Species of Freshwater Bivalves. In: R.Dallinger
and P.S.Rainbow (Eds.), Ecotoxicology of
Metals in Invertebrates, Lewis Publ. :175-186.

13830

AF, UEndp, Dur

Kraak, M.H.S., Y.A. Wink, S.C. Stuijfzand, M.C.
Buckert-De Jong, C.J. De Groot, and W.
Admiraal. 1994. Chronic Ecotoxicity of Zn and
Pb to the Zebra Mussel Dreissena polymorpha.
Aquat.Toxicol. 30(1):77-89.

14043

Dur, UChron

Kumar, S., and S.C. Pant. 1981. Histopathologic
Effects of Acutely Toxic Levels of Copper and
Zinc on Gills, Liver and Kidney of Puntius
conchonius (Ham.). Indian J.Exp.Biol.

19(2): 191 -194.

9475

UEndp, Dur, Con

Lalande, M., and B. Pinel-Alloul. 1983. Acute
Toxicity of Cadmium, Copper, Mercury and Zinc
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4258

Three 48 h EC50s
ranging from approx.
1700 to 5600 ug/L
dissolved zinc
normalized to 100
mg/L as CaC03
hardness. Tests were
static, unmeasured.

This study appears to
provide an appropriate
48 h EC50 for C.
sphaericus, but the
paper should be
secured to ensure
acceptability. Species
is relatively insensitive
to acute zinc exposure

Lalande, M., and B. Pinel-Alloul. 1984. Heavy
Metals Toxicity on Planktonic Crustacea of the
Quebec Lakes (Toxicite des Metaux Lourds sur
les Crustaces Planctoniques des Lacs du
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10724

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Lalande, M., and B. Pinel-Alloul. 1986. Acute
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12292

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4487

AF, UEndp, Dur

523

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Larsen, J., and B. Svensmark. 1991. Labile
Species of Pb, Zn and Cd Determined by
Anodic Stripping Staircase Voltammetry and
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3716

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Laskowski, R., and S.P. Hopkin. 1996. Effect of
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45063

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LeBlanc, G.A.. 1982. Laboratory Investigation
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11065

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Lee, C.L., T.C. Wang, C.H. Hsu, and A.A.
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19419

Plant, AF, UEndp

Lee, D.R.. 1976. Development of an
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3402

Acute test with adults

<24 h neonates
preferred

Lefcort, H., R.A. Meguire, L.H.Wilson, and W.F.
Ettinger. 1998. Heavy Metals Alter the Survival,
Growth, Metamorphosis, and Antipredatory
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Arch.Environ.Contam.Toxicol. 35(3):447-456.

20181

AF, UEndp, Field

Les, A., and R.W. Walker. 1984. Toxicity and
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Blue-Green Alga, Chroococcus paris. Water Air
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11020

Plant, AF, UEndp

Lewander, M., M. Greger, L. Kautsky, and E.
Szarek. 1996. Macrophytes as Indicators of
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19971

Plant, AF, UEndp

524

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Lewis, S.D., and W.M. Lewis. 1971. The Effect
of Zinc and Copper on the Osmolality of Blood
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T rans.Am. Fish.Soc. 100(4):639-643.

9382

UEndp, Dur, Con

Lewis, T.E., and A.W. Mcintosh. 1986. Uptake
of Sediment-Bound Lead and Zinc by the
Freshwater Isopod Asellus communis at Three
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Arch. Environ. Contam.Toxicol. 15(5):495-504.

12027

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Litzke, J., and K. Hubel. 1993. Aquarium
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4248

AF, UEndp, Con

Lloyd, R.. 1960. The Toxicity of Zinc Sulphate to
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14412

UEndp, Dur

Lloyd, R.. 1961. The Toxicity of Mixtures of Zinc
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104

UEndp, Con

Loez, C.R., and M.L. Topalian. 1999. Use of
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51619

Plant, AF, UEndp,
NoOrg

Lopez, J., M.D. Vazquez, and A. Carballeira.
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45134

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15656

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Madoni, P., D. Davoli, and G. Gorbi. 1994.
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13671

Ace, AF, UEndp, Dur

525

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Madoni, P., D. Davoli, G. Gorbi, and L. Vescovi.
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Activated Sludge Protozoan Community. Water
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16363

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NoOrg

Madoni, P., G. Esteban, and G. Gorbi. 1992.
Acute Toxicity of Cadmium, Copper, Mercury,
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5116

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Maeda, S., M. Mizoguchi, A. Ohki, and T.
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239

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Maeda, S., M. Mizoguchi, A. Ohki, J. Inanaga,
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240

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Malacea, I.. 1966. Studies on the Acclimation of
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10020

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Marshall, J.S., J.I. Parker, D.L. Mellinger, and C.
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11256

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Mathur, S., B.S. Khangarot, and V.S. Durve.
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15629

Acute test with adults

<24 h neonates
preferred

Matthiessen, P., and A.E. Brafield. 1973. The
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8913

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Matthiessen, P., and A.E. Brafield. 1977.
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11149

UEndp, Dur

526

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Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Mayer, F.L.J., and M.R. Ellersieck. 1986.

Manual of Acute Toxicity: Interpretation and
Data Base for 410 Chemicals and 66 Species of
Freshwater Animals. Resour.Publ.No.160,
U.S.Dep.Interior, Fish Wildl.Serv., Washington,
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6797

Dur, Form

McHardy, B.M., and J.J. George. 1990.
Bioaccumulation and Toxicity of Zinc in the
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Environ.Pollut. 66(1):55-66.

3424

Plant, AF, UEndp

McKenney, C.L.J., and J.M. Neff. 1979.
Individual Effects and Interactions of Salinity,
Temperature, and Zinc on Larval Development
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15812

AF, UEndp

Meisner, J.D., and W.Q. Hum. 1987. Acute
Toxicity of Zinc to Juvenile and Subadult
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Bui I. Environ. Contam. Toxicol. 39(5):898-902.

12581

Memmert, U.. 1987. Bioaccumulation of Zinc in
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12349

AF, UEndp

Migliore, L., and M. Nicola Giudici. 1990.
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10515

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Miller, M.P., and A.C. Hendricks. 1996. Zinc
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16983

UEndp

Millington, P.J., and K.F.Walker. 1983.
Australian Freshwater Mussel Velesunio
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11151

Dur

Mills, W.L.. 1976. Water Quality Bioassay Using
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14392

Ace, AF, Dur

527

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Mirenda, R.J.. 1986. Acute Toxicity and
Accumulation of Zinc in the Crayfish,
Orconectes virilis (Hagen).
Bull.Environ.Contam.Toxicol. 37(3):387-394.

11975

NonRes

Mishra, S., and A.K. Srivastava. 1979.
Hematology as Index of Sublethal Toxicity of
Zinc in a Freshwater Teleost.

Bui I. Environ. Contam. Toxicol. 22(4/5):695-698.

8401

Con

Mizutani, A., E. Ifune, A. Zanella, and C.
Eriksen. 1991. Uptake of Lead, Cadmium and
Zinc by the Fairy Shrimp, Branchinecta
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3681

AF, UEndp, Dur

Mowbray, D.L.. 1988. Assessment of the
Biological Impact of Ok Tedi Mine Tailings,
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17356

Mukhopadhyay, M.K., and S.K. Konar. 1984.
Toxicity of Copper, Zinc and Iron to Fish,
Plankton and Worm. Geobios (Jodhpur) 11:204-
207.

11539

Mukhopadhyay, M.K., and S.K. Konar. 1988.
Skeletal Abnormalities in the Fish Tilapia
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Environ.Ecol. 6(2):519-521.

13220

AF, UEndp

Muller, K.W., and H.D. Payer. 1980. The
Influence of Zinc and Light Conditions on the
Cadmium-Repressed Growth of the Green Alga
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14390

Plant, AF, UEndp, Dur

Munzinger, A., and F. Monicelli. 1991. A
Comparison of the Sensitivity of Three Daphnia
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3950

AF, UEndp

Munzinger, A., and M.L. Guarducci. 1988. The
Effect of Low Zinc Concentrations on Some
Demographic Parameters of Biomphalaria
glabrata (Say), Mollusca: Gastropoda.
Aquat.Toxicol. 12(1 ):51 -61.

12894

AF, UEndp

528

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Muramoto, S.. 1980. Effect of Complexans
(EDTA, NTA and DTPA) on the Exposure to
High Concentrations of Cadmium, Copper, Zinc
and Lead. Bull.Environ.Contam.Toxicol.
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6698

AF, UEndp, Dur, Con

Murti, R., and G.S. Shukla. 1984. Toxicity of
Copper Sulphate and Zinc Sulphate to
Macrobrachium lamarrei (H. Milne Edwards)
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11155

AF, Dur, Con

Nakagawa, H., and S. Ishio. 1989. Aspects of
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Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan
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3210

AF, UEndp, Dur

Nalecz-Jawecki, G., and J. Sawicki. 1998.
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Arch.Environ.Contam.Toxicol. 34(1): 1-5.

18997

Ace, Dur, Eff

Nasu, Y., K. Hirabayashi, and M. Kugimoto.
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9057

Plant, AF, UEndp

Negilski, D.S.. 1973. Individual and Combined
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15432

UEndp

Nehring, R.B.. 1976. Aquatic Insects As
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Bull. Environ. Contam.Toxicol. 15(2): 147-154.

10198

UEndp

Nehring, R.B.Jr.. 1974. Acute Toxicity of a Zinc-
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5535

Dur

Nelson, S.M., and R.A. Roline. 1998. Evaluation
of the Sensitivity of Rapid Toxicity Tests
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Bull.Environ.Contam.Toxicol. 60:292-299.

18961

529

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Newman, M.C., and S.V. Mitz. 1988. Size
Dependence of Zinc Elimination and Uptake
From Water by Mosquitofish Gambusia affinis
(Baird and Girard). Aquat.Toxicol. 12(1 ):17-32.

12897

AF, UEndp, Con

Nicolau, A., M. Mota, and N. Lima. 1999.
Physiological Responses of Tetrahymena
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Triton X-100. FEMS (Fed.Eur.Microbiol.Soc.)
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20637

Ace, AF, UEndp, Dur

Niederlehner, B.R.Jr.. 1992. Community
Response to Cumulative Toxic Impact: Effects
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Can.J.Fish.Aquat.Sci. 49(10):2155-2163.

19367

UEndp, Dur, NoOrg

Niederlehner, B.R.Jr.. 1993. Effects of Previous
Zinc Exposure on pH Tolerance of Periphyton
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753.

6543

UEndp, Ace, NoOrg

Nilov, V.I.. 1980. Concentration of 65Zn and
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9866

AF, UEndp, Dur, Con

Norberg, T.J., and D.I. Mount. 1985. A New
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11182

AF, Con

Norberg-King, T.J.. 1989. An Evaluation of the
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Environ.Toxicol.Chem. 8(11):1075-1089.

5313

Nom, Con

Notenboom, J., K. Cruys, J. Hoekstra, and P.
Van Beelen. 1992. Effect of Ambient Oxygen
Concentration upon the Acute Toxicity of
Chlorophenols and Heavy Metals to the
Groundwater Copepod Parastenocaris
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143.

5975

AF, Dur

Oikari, A., J. Kukkonen, and V. Virtanen. 1992.
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5679

AF, Con

530

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

O'Neill, J.G.. 1981. The Humoral Immune
Response of Salmo trutta L. and Cyprinus
carpio L. Exposed to Heavy Metals. J.Fish Biol.
19(3):297-306.

15193

UEndp, Con

Ozoh, P.T.E., and C.O. Jacobson. 1979.
Embryotoxicity and Hatchability in Cichlasoma
nigrofasciatum (Guenther) Eggs and Larvae
Briefly Exposed to Low Concentrations of Zinc
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21(6):782-786.

15571

AF, UEndp, Dur, Con

Pant, S.C., S. Kumar, and S.S. Khanna. 1980.
Toxicity of Copper Sulphate and Zinc Sulphate
to Fresh Water Teleost Puntius conchonius
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567

NonRes

Patil, H.S., and M.B. Kaliwal. 1983. Influence of
Cadmium, Copper and Zinc on Oxygen
Consumption Rate of a Freshwater Prawn
Macrobrachium hendersodyanum.
Aquat.Sci.Fish.Abstr. 14(7, Pt.1):257 (1984) /
Environ. Ecol. 1(3):175-177.

11545

AF, UEndp, Con

Patil, H.S., and M.B. Kaliwal. 1986. Relative
Sensitivity of a Freshwater Prawn
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12787

AF, Con

Patrick, F.M., and M.W. Loutit. 1978. Passage
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2709

AF, UEndp, Con,
RouExp

Patrick, R., J. Cairns Jr., and A. Scheier. 1968.
The Relative Sensitivity of Diatoms, Snails, and
Fish to Twenty Common Constituents of
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140 (Author Communication Used) (Publ in Part
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949

AF, Con

Peterson, R.H.. 1976. Temperature Selection of
Juvenile Atlantic Salmon (Salmo salar) as
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5160

AF, UEndp, Dur, Con

Phipps, G.L., V.R. Mattson, and G.T. Ankley.
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14907

531

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Pittinger, C.A., D.J. Versteeg, B.A. Blatz, and
E.M. Meiers. 1992. Environmental Toxicology of
Succinate Tartrates. Aquat.Toxicol. 24(1/2):83-
102.

6561

AF, UEndp

Pokethitiyook, P., E.S. Upatham, and 0.
Leelhaphunt. 1987. Acute Toxicity of Various
Metals to Moina macrocopa.
Nat.Hist.Bull.Siam.Soc. 35(1/2):47-56.

45061

Popken, G.J.. 1990. Effects of Calcium on the
Toxicity of Zinc to Embryos and Larvae of the
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M.S.Thesis, Eastern Kentucky University,
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8695

UEndp

Porter, K.R., and D.E. Hakanson. 1976. Toxicity
of Mine Drainage to Embryonic and Larval
Boreal Toads (Bufonidae: Bufo boreas). Copeia
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18483

AF, UEndp

Postma, J.F., S.Mol., H. Larsen, and W.
Admiraal. 1995. Life-Cycle Changes and Zinc
Shortage in Cadmium-Tolerant Midges,
Chironomus riparius (Diptera), Reared in the
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13725

AF, UEndp

Pratt, J.R., D. Mochan, and Z. Xu. 1997. Rapid
Toxicity Estimation Using Soil Ciliates:
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Bull.Environ.Contam.Toxicol. 58(3):387-393.

20289

Ace, AF, Dur

Qureshi, A.A., K.W. Flood, S.R. Thompson,
S.M. Janhurst, C.S. Inniss, and D.A. Rokosh.
1982. Comparison of a Luminescent Bacterial
Test with Other Bioassays for Determining
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Effluents. In: J.G.Pearson, R.B.Foster and
W.E.Bishop (Eds.), Aquatic Toxicology and
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15923

AF, Con

Qureshi, S.A., and A.B. Saksena. 1980. The
Acute Toxicity of Some Heavy Metals to Tilapia
mossambica (Peters). Aqua.Sci.Tech.Reviews
(India) 1:19-20.

5627

Con

532

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Rabe, F.W., and C.W. Sappington. 1970.
Biological Productivity of the Coeur D'Alene
River as Related to Water Quality (The Acute
Toxicity of Zinc to Cutthroat Trout (Salmo
clarki)). Res.Project Tech.Completion Rep.,
Project A-024-IDA, Water Resour.Res.lnstit.,
University of Idah o:16.

15108

AF, Dur, Con

Rachlin, J.W., T.E. Jensen, B. Warkentine, and
H.H. Lehman. 1982. The Growth Response of
the Green Alga (Chlorella Saccharophila) to
Selected Concentrations of the Heavy Metals
Cd, Cu, Pb, and Zn. In: D.D.Hemphill (Ed.),
Trace Substances in Environmental Health XVI,
University of Missouri, Columbia, MO :145-154.

14310

Plant, AF, UEndp, Dur

Radhakrishnaiah, K., A. Suresh, P.C.
Victoriamma, and B. Sivaramakrishna. 1991.
Influence of Zinc on the Protein of Freshwater
Fish Cyprinus carpio (Linnaeus). Environ.Ecol.
9(3):612-616.

3899

AF, UEndp

Rahel, F.J.. 1981. Selection for Zinc Tolerance
in Fish: Results From Laboratory and Wild
Populations. Trans.Am. Fish.Soc. 110:19-28
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2464

UEndp, Con

Rao, I.J., and M.N. Madhyastha. 1987.
Toxicities of Some Heavy Metals to the
Tadpoles of Frog, Microhyla ornata (Dumeril &
Bibron). Toxicol.Lett. 36(2):205-208.

6357

Dur, NonRes

Rao, M.B., and N. Jayasree. 1987. Toxicity of
Copper and Zinc to Adults and Juveniles of the
Freshwater Prosobranch Snail Bellamya
dissimilis (Muller). In: K.S.Rao and S.Shrivasta
(Eds.), Perspectives in Hydrobiology Symp.,
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3104

AF, Con

Rao, S.V.R.. 1985. A Note on the Feasibility of
Degradation of Phenol by Some Crustacean
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11797

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Rao, T.S., M.S. Rao, and S.B.S. Prasad. 1975.
Median Tolerance Limits of Some Chemicals to
the Fresh Water Fish "Cyprinus carpio". Indian
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2077

Dur

533

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Reed, P., D. Richey, and D. Roseboom. 1980.
Acute Toxicity of Zinc to Some Fishes in High
Alkalinity Water. 111. State Water Surv.Circ.
142:1-21.

5359

Dilut

Rehwoldt, R., L. Lasko, C. Shaw, and E.
Wirhowski. 1973. The Acute Toxicity of Some
Heavy Metal Ions Toward Benthic Organisms.
Bull. Environ. Contam.Toxicol. 10(5):291-294.

2020

Uncharacterized River
Water

Richelle, E., Y. Degoudenne, L. Dejonghe, and
G. Van de Vyver. 1995. Experimental and Field
Studies on the Effect of Selected Heavy Metals
on Three Freshwater Sponge Species:
Ephydatia fluviatilis, Ephydatia muelleri.
Arch.Hydrobiol. 135(2):209-231.

19534

AF, UEndp, Dur

Roales, R.R., and A. Perlmutter. 1974. Toxicity
of Zinc and Cygon, Applied Singly and Jointly,
to Zebrafish Embryos.

Bui I. Environ. Contam. Toxicol. 12(4):475-480.

8688

AF, Dur, Con

Rojickova-Padrtova, R., and B. Marsalek. 1999.
Selection and Sensitivity Comparisons of Algal
Species for Toxicity Testing. Chemosphere
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19852

Plant, AF

Rombough, P.J.. 1985. The Influence of the
Zona radiata on the Toxicities of Zinc, Lead,
Mercury, Copper and Silver Ions to Embryos of
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Comp.Biochem.Physiol.C 82(1): 115-117.

11219

AF, Con

Roy, R., and P.G.C. Campbell. 1995. Survival
Time Modeling of Exposure of Juvenile Atlantic
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16109

Roy, U.K., A.K. Gupta, and P. Chakrabarti.
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13933

UEndp

Ruthven, J.A.Jr.. 1973. The Response of Fresh-
Water Protozoan Artificial Communities to
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2863

Ace, UEndp

534

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Sabodash, V.M.. 1977. Size of Eggs and Ovule
of Female Carp of Various Age, Both Under
Normal Conditions and Exposed to Increase
Doses of Zinc Sulfate. Biol.Nauki (Mosc.)
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15237

AF, Dur, Con

Salanki, J., and L. Hiripi. 1990. Effect of Heavy
Metals on the Serotonin and Dopamine
Systems in the Central Nervous System of the
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Comp.Biochem.Physiol.C 95(2):301-305.

3456

UEndp, Dur

Sankaraperumal, G., M.K. Rajan, and A.
Mohandoss. 1990. Synergistic Effect of
Cadmium and Zinc on the Erythrocytes and
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1216.

5853

AF, UEndp

Sappington, K.G., P.M. Stewart, and J. Cairns
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Va.J.Sci. 35(2):97 (ABS).

2397

Plant, AF, Uendp, Con

Sastry, K.V., and S. Subhadra. 1984. Effect of
Cadmium and Zinc on Intestinal Absorption of
Xylose and Tryptophan in the Fresh Water
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Chemosphere 13(8):889-898.

10483

AF, UEndp, NonRes

Satoh, S., T. Takeuchi, and T. Watanabe. 1987.
Availability to Rainbow Trout of Zinc in White
Fish Meal and of Various Zinc Compounds.
Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan
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12644

AF, UEndp, RouExp

Sauvant, M.P., D. Pepin, C.A. Groliere, and J.
Bohatier. 1995. Effects of Organic and Inorganic
Substances on the Cell Proliferation of L-929
Fibroblasts and Tetrahymena pyriformis GL
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14980

Ace, AF, UEndp, Dur

Sauvant, M.P., D. Pepin, J. Bohatier, and C.A.
Groliere. 1995. Microplate Technique for
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16142

Ace, AF, Dur

535

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Saxena, K.K., A.K. Dubey, and R.R.S.
Chauhan. 1993. Experimental Studies on
Toxicity of Zinc and Cadmium to
Heteropneustes fossilis (Bl.). J.Freshw.Biol.
5(4):343-346.

16939

NonRes

Saxena, O.P., and A. Parashari. 1983.
Comparative Study of the Toxicity of Six Heavy
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10762

Dur, NonRes

Sayer, M.D.J., J.P. Reader, and R. Morris.
1989. The Effect of Calcium Concentration on
the Toxicity of Copper, Lead and Zinc to Yolk-
Sac Fry of Brown Trout, Salmo trutta L., in Soft,
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13930

UEndp

Sayer, M.D.J., J.P. Reader, and R. Morris.
1991. Embryonic and Larval Development of
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Metal Mixtures in Soft Water. J.Fish Biol.
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45197

AF, UEndp

Sayer, M.D.J., J.P. Reader, and R. Morris.
1991. Effects of Six Trace Metals on Calcium
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45198

AF, UEndp

Saygideger, S.. 1998. Bioaccumulation and
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18985

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Sehgal, R., and A.B. Saxena. 1986. Toxicity of
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11792

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Sharma, A., and M.S. Sharma. 1993. Vertebral
Defects in Lebistes reticulatus (Peters) and
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14417

AF, UEndp

Shazili, N.A.M., and D. Pascoe. 1986. Variable
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Bull.Environ.Contam.Toxicol. 36(3):468-474.

11738

Dur, Con

536

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Shedd, T.R., M.W. Widder, M.W. Toussaint,
M.C. Sunkel, and E. Hull. 1999. Evaluation of
the Annual Killifish Nothobranchius guentheri as
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20487

Dur

Skidmore, J.F., and I.C. Firth. 1983. Acute
Sensitivity of Selected Australian Freshwater
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12401

Skidmore, J.F., and P.W.A. Tovell. 1972. Toxic
Effects of Zinc Sulphate on the Gills of Rainbow
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9197

UEndp, Dur, Con

Slabbert, J.L., and J.P. Maree. 1986. Evaluation
of Interactive Toxic Effects of Chemicals in
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Screening Test. Water S.A. 12(2):57-62.

12836

Ace, Af, UEndp, Dur

Slabbert, J.L., and W.S.G. Morgan. 1982. A
Bioassay Technique Using Tetrahymena
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11048

Ace, AF, UEndp, Dur

Snell, T.W.. 1991. New Rotifer Bioassaysfor
Aquatic Toxicology. Final Report, U.S.Army
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Ft.Detrick, Frederick, MD :29 p.(U.S.NTIS AD-
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17689

AF, Dur

Snell, T.W., B.D. Moffat, C. Janssen, and G.
Persoone. 1991. Acute Toxicity Tests Using
Rotifers IV. Effects of Cyst Age, Temperature,
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317 (OECDG Data File).

9385

AF, Dur

Solbe, J.F.D.. 1974. The Toxicity of Zinc Sulfate
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2111

Dur

Solbe, J.F.D., and V.A. Flook. 1975. Studies on
the Toxicity of Zinc Sulphate and of Cadmium
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15989

Con

537

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Sornaraj, R., P. Baskaran, and S.
Thanalakshmi. 1995. Effects of Heavy Metals
on Some Physiological Responses of Air-
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17380

AF, NonRes

Soundrapandian, S., and K. Venkataraman.
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3945

AF, Con

Sparks, R.E., W.T. Waller, and J. Cairns Jr..
1972. Effect of Shelters on the Resistance of
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J.Fish.Res.Board Can. 29(9):1356-1358.

9198

AF, UEndp, Dur

Spehar, R.L., E.N. Leonard, and D.L. De Foe.
1978. Chronic Effects of Cadmium and Zinc
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Trans.Am.Fish.Soc. 107(2):354-360.

15954

UEndp

Speranza, A.W., R.J. Seeley, V.A. Seeley, and
A. Perlmutter. 1977. The Effect of Sublethal
Concentrations of Zinc on Reproduction in the
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8447

AF, UEndp

Sprague, J.B.. 1964. Lethal Concentrations of
Copper and Zinc for Young Atlantic Salmon.
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2067

AF, Dur

Spry, D.J., and C.M. Wood. 1985. Ion Flux
Rates, Acid-Base Status, and Blood Gases in
Rainbow Trout, Salmo gairdneri, Exposed to
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Can.J.Fish.Aquat.Sci. 42:1332-1341.

11350

AF, UEndp, Dur

Spry, D.J., and C.M. Wood. 1989. A Kinetic
Method for the Measurement of Zinc Influx In
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856

AF, UEndp, Dur

Spry, D.J., P.V. Hodson, and C.M. Wood. 1988.
Relative Contributions of Dietary and
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12913

UEndp

538

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Srivastav, R.K., S.K. Gupta, K.D.P. Nigam, and
P. Vasudevan. 1994. Use of Aquatic Plants for
the Removal of Heavy Metals from Wastewater.
Int.J.Environ.Stud. 45(1):43-50.

16762

AF, UEndp

Srivastava, M., M.M.S. Rawat, and A.K.
Srivastava. 1991. Effect of Different
Concentrations of Zinc on the Survival and
Growth Behaviour of Chorella vulgaris.
Pollut.Res. 10(1 ):49-51.

7568

AF, UEndp, Dur

St.Laurent, D., C. Blaise, P. MacQuarrie, R.
Scroggins, and B. Trottier. 1992. Comparative
Assessment of Herbicide Phytotoxicity to
Selenastrum capricornutum Using Microplate
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Environ.Toxicol.Water Qual. 7:35-48.

45196

Plant, AF

Stanley, R.A.. 1974. Toxicity of Heavy Metals
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Arch.Environ.Contam.Toxicol. 2(4):331-341.

2262

Plant, Af, Con

Starodub, M.E., P.T.S. Wong, and C.I. Mayfield.
1987. Short Term and Long Term Studies on
Individual and Combined Toxicities of Copper,
Zinc and Lead to Scenedesmus quadricauda.
Sci.Total Environ. 63:101-110.

12380

Plant, AF, Dur

Starodub, M.E., P.T.S. Wong, C.I. Mayfield, and
Y.K. Chau. 1987. Influence of Complexation and
pH on Individual and Combined Heavy Metal
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Can.J.Fish.Aquat.Sci. 44:1173-1180.

12817

Plant, AF, Dur, Con

Stary, J., and K. Kratzer. 1982. The Cumulation
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14286

Plant, AF, UEndp, Dur

Stary, J., B. Havlik, K. Kratzer, J. Prasilova, and
J. Hanusova. 1983. Cumulation of Zinc,
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14088

Plant, AF, UEndp, Dur

539

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Stary, J., K. Kratzer, B. Havlik, J. Prasilova, and
J. Hanusova. 1982. The Cumulation of Zinc and
Cadmium in Fish (Poecilia reticulata).
Int.J.Environ.Anal.Chem. 11:117-120.

16091

AF, UEndp, RouExp

Stauber, J.L., and T.M. Florence. 1987.
Mechanism of Toxicity of Ionic Copper and
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12971

Plant, UEndp

Stuhlbacher, A., M.C. Bradley, C. Naylor, and P.
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Comp.Biochem. Physiol. C 101(3):571-577.

6453

AF, Con

Subramanian, V.V., V. Sivasubramanian, and
K.P. Gowrinathan. 1994. Uptake and Recovery
of Heavy Metals by Immobilized Cells of
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18777

Plant, AF, UEndp, Dur

Sultana, R., and V.U. Devi. 1995. Oxygen
Consumption in a Catfish, Mystus gulio (Ham.)
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16626

AF, UEndp, Dur

Suzuki, K.. 1959. The Toxic Influence of Heavy
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2701

AF, UEndp, Dur, Con

Svensmark, B., and J. Larsen. 1988.
Determination of the Labile Species of Zinc by
Anodic Stripping Staircase Voltammetry, With
Special Refernce to Correlation With the
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790

Ace, AF, Dur

Svobodova, Z., and B. Vykusova. 1988.
Comparing the Sensitivity of Rainbow Trout and
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315

AF, Dur, Con

Swinehart, J.H.. 1990. The Effects of Humic
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17696

AF, UEndp, Dur

540

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Takamura, N., F. Kasai, and M.M. Watanabe.
1989. Effects of Cu, Cd and Zn on
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J.Appl.Phycol. 1 (1):39-52.

3095

Plant, AF, NoOrg,
UEndp, Dur, Con

Tatara, C.P., M.C. Newman, J.T. McCloskey,
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18605

AF, Dur

Tatara, C.P., M.C. Newman, J.T. McCloskey,
and P.L. Williams. 1998. Use of Ion
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269.

5072

AF, Dur

Taylor, J.L.. 1978. Toxicity of Copper and Zinc
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15578

Dur

Thompson, K.W., A.C. Hendricks, and J. Cairns
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Bull.Environ.Contam.Toxicol. 25(1): 122-129.

586

Two 96 h LC50s
approx. 7600 ug/L
dissolved zinc
normalized to 100
mg/L as CaC03
hardness. Tests were
flow-through,
measured.

This study appears to
provide appropriate 96
h LC50s for L.
macrochirus, but the
paper should be
secured to ensure
acceptability. Species
is relatively insensitive
to acute zinc exposure

Thompson, K.W., M.L. Deaton, R.V. Foutz, J.
Cairns Jr., and A.C. Hendricks. 1982.
Application of Time-Series Intervention Analysis
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Can.J.Fish.Aquat.Sci. 39(3):518-521.

15057

AF, UEndp, Con

Thorp, V.J., and P.S. Lake. 1974. Toxicity
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8731

NonRes

Timmermans, K.R., and P.A. Walker. 1989. The
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Environ.Pollut. 62(1):73-85.

2729

AF, UEndp

541

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Timmermans, K.R., E. Spijkerman, M. Tonkes,
and H. Govers. 1992. Cadmium and Zinc
Uptake by Two Species of Aquatic Invertebrate
Predators from Dietary and Aqueous Sources.
Can.J.Fish.Aquat.Sci. 49(4):655-662.

13427

AF, UEndp

Timmermans, K.R., W. Peeters, and M. Tonkes.
1992. Cadmium, Zinc, Lead and Copper in
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6029

AF, UEndp, Con

Ting, Y.P., F. Lawson, and I.G. Prince. 1989.
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3362

Plant, AF, Uendp, Con

Tishinova, V.. 1977. A Study of the Toxic Effect
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8459

Dur, Con

Tsuji, S., Y. Tonogai, Y. Ito, and S. Kanoh.
1986. The Influence of Rearing Temperatures
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12497

AF, Dur, Con

Turbak, S.C., S.B. Olson, and G.A. McFeters.
1986. Comparison of Algal Assay Systems for
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11780

Plant, AF

Tuurala, H.. 1983. Relationships between
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11454

AF, UEndp, Dur

Tuurala, H., and A. Soivio. 1982. Structural and
Circulatory Changes in the Secondary Lamellae
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10588

AF, UEndp

542

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Twagilimana, L., J. Bohatier, C.A. Groliere, F.
Bonnemoy, and D. Sargos. 1998. A New Low-
Cost Microbiotest with the Protozoan
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20057

Ace, AF, Dur

Van Dam, R.A., M.J. Barry, J.T. Ahokas, and
D.A. Holdway. 1999. Investigating Mechanisms
of Diethylenetriamine Pentaacetic Acid Toxicity
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Aquat.Toxicol. 46(3):191-210.

20351

AF, UEndp, Dur

Van der Werff, M., and M.J. Pruyt. 1982. Long-
Term Effects of Heavy Metals on Aquatic
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14480

Plant, AF, UEndp

Van Ginneken, L., M.J. Chowdhury, and R.

Blust. 1999. Bioavailability of Cadmium and Zinc
to the Common Carp, Cyprinus carpio, in
Complexing Environments: A Test for the
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Environ.Toxicol. Chem. 18(10):2295-2304.

20483

AF, UEndp, Dur, Form

Van Leeuwen, C.J., E.M.M. Grootelaar, and G.
Niebeek. 1990. Fish Embryos as Teratogenicity
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2852

AF, UEndp, Con

Vardia, H.K., P.S. Rao, and V.S. Durve. 1988.
Effect of Copper, Cadmium and Zinc on Fish-
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12365

AF, Con

Vasseur, P., P. Pandard, and D. Burnel. 1988.
Influence of Some Experimental Factors on
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752

Plant, Af, Con

Vazquez, M.D., J. Lopez, and A. Carballeira.
1999. Uptake of Heavy Metals to the
Extracellular and Intracellular Compartments in
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Ecotoxicol. Environ.Saf. 44(1): 12-24.

20585

Plant, AF, UEndp, Dur

543

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Verma, S.R., I.P. Tonk, A.K. Gupta, and M.
Saxena. 1984. Evaluation of an Application
Factor for Determining the Safe Concentration
of Agricultural and Industrial Chemicals. Water
Res. 18(1): 111 -115.

10575

Con

Verma, S.R., M. Jain, and R.C. Dalela. 1982. A
Laboratory Study to Assess Separate and In-
Combination Effects of Zinc, Chromium and
Nickel to the Fish Mystus vittatus. Acta
Hydrochim. Hydrobiol. 10(1):23-29.

15793

AF, Con

Vijayamadhavan, K.T., and T. Iwai. 1975.
Histochemical Observations on the Permeation
of Heavy Metals Into Taste Buds of Goldfish.
Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan
Gakkaishi) 41(6):631-639.

15445

AF, UEndp, Dur, Con

Vijayaraman, K., G. John, P. Sivakumar, and
R.R. Mohamed. 1999. Uptake and Loss of
Heavy Metals by the Freshwater Prawn,
Macrobrachium malcolmsonii. J.Environ.Biol.
20(3):217-222.

55226

UEndp

Vijayram, K., and P. Geraldine. 1996.
Regulation of Essential Heavy Metals (Cu, Cr,
and Zn) by the Freshwater Prawn
Macrobrachium malcolmsonii (Milne Edwards).
Bull.Environ.Contam.Toxicol. 56(2):335-342.

16442

UEndp

Vincent, M.J.D., and B. Penicaut. 1986.
Comparative Studies on the Toxicity of Metal
Chlorides and of a Synthetic Organic
Molluscicide, N-Trityl-Morpholine, upon Two
Aquatic Amphipod. Ann.Rech.Vet. 17(4):441-
446.

12420

AF, Con

Vymazal, J.. 1990. Uptake of Heavy Metals by
Cladophora glomerata. Acta
Hydrochim. Hydrobiol. 18(6):657-665.

45131

Plant, AF, UEndp, Dur

Vymazal, J.. 1995. Influence of pH on Heavy
Metals Uptake by Cladophora glomerata.
Pol .Arch. Hydrobiol. 42(3):231-237.

45130

Plant, AF, UEndp

544

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Wagh, S.B., K. Shareef, and S. Shaikh. 1985.
Acute Toxicity of Cadmium Sulphate, Zinc
Sulphate and Copper Sulphate to Barbus ticto
(Ham.): Effect on Oxygen Consumption and Gill
Histology. J.Environ.Biol. 6(4):287-293.

11483

Con

Wagner, G.F., and B.A. McKeown. 1982.
Changes in Plasma Insulin and Carbohydrate
Metabolism of Zinc-Stressed Rainbow Trout,
Salmo gairdneri. Can.J.Zool. 60(9):2079-2084.

11352

UEndp

Wang, T.C., J.C. Weissman, G. Ramesh, R.
Varadarajan, and J.R. Benemann. 1996.
Parameters for Removal of Toxic Heavy Metals
by Water Milfoil (Myriophyllum spicatum).

Bui I. Environ. Contam. Toxicol. 57(5):779-786.

20408

Plant, AF, UEndp, Dur

Wang, W.. 1986. Toxicity Tests of Aquatic
Pollutants by Using Common Duckweed.
Environ.Pollut.Ser.B Chem.Phys. 11 (1): 1 -14.

11789

Plant, Af, Con

Wang, W.. 1994. Rice Seed Toxicity Tests for
Organic and Inorganic Substances.

Environ. Monit.Assess. 29:101 -107.

45060

Plant, AF, Dur

Water Pollution Research Board. 1962. Effects
of Pollution on Fish: Toxicity of Mixtures of Zinc
Sulphate and Ammonium Chloride. In: Water
Pollution Research 1961, Water Pollution
Research Board, Dep.of Scientific and Industrial
Research, H.M.Stationery Office, London :90-
93.

2515

AF, Dur, Con

Water Pollution Research Board. 1968. Effects
of Pollution on Fish: Chronic Toxicity of
Ammonia to Rainbow Trout. In: Water Pollution
Research 1967, Water Pollution Research
Board, Dep.of Scientific and Industrial
Research, H.M.Stationery Office, London :56-
65.

10185

AF, Dur, Con

Water Pollution Research Laboratory. 1967.
Effects of Pollution on Fish. In: Water Pollution
Research 1966, Ministry of Technology,
London, England :50-61.

14394

UEndp

545

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Watson, T.A., and B.A. McKeown. 1976. The
Effect of Sublethal Concentrations of Zinc on
Growth and Plasma Glucose Levels in Rainbow
Trout, Salmo gairdneri (Richardson). J.Wildl.Dis.
12(2):263-270.

8470

UEndp

Watson, T.A., and B.A. McKeown. 1976. The
Activity of Delta 5-3 beta Hydroxysteriod
Dehydrogenase Enzyme in the Interrenal Tissue
of Rainbow Trout (Salmo gairdneri Richardson).
Bull.Environ.Contam.Toxicol. 16(2): 173-181.

15996

UEndp

Wehr, J.D., M.G. Kelly, and B.A. Whitton. 1987.
Factors Affecting Accumulation and Loss of Zinc
by the Aquatic Moss Rhynchostegium
riparioides (Hedw.) C. Jens. Aquat.Bot. 29:261-
274.

15013

Plant, AF, UEndp

Wekell, J.C., K.D. Shearer, and C.R. Houle.
1983. High Zinc Supplementation of Rainbow
Trout Diets. Prog.Fish-Cult. 45(3):144-147.

11257

AF, UEndp, RouExp

Whitley, L.S.. 1968. The Resistance of Tubificid
Worms to Three Common Pollutants.
Hydrobiologia 32(1/2): 193-205 (Author
Communication Used).

15507

AF, Dur, Con, NoOrg

Williams, P.L., and D.B. Dusenbery. 1990.
Aquatic Toxicity Testing Using the Nematode,
Caenorhabditis elegans. Environ.Toxicol.Chem.
9(10):1285-1290.

3437

AF, Dur

Willis, M.. 1988. Experimental Studies of the
Effects of Zinc on Ancylus fluviatilis (Mueller)
(Mollusca; Gastropoda) From the Afon Crafnant,
N. Wales. Arch.Hydrobiol. 112(2):299-316.

13067

Willis, M.. 1989. Experimental Studies on the
Effects of Zinc on Erpobdella octulata (L.)
(Annelida: Hirudinea) from the Afon Crafnant, N.
Wales. Arch.Hydrobiol. 116(4):449-469.

8529

Winner, R.W.. 1981. A Comparison of Body
Length, Brood Size, and Longevity as Indices of
Chronic Copper and Zinc Stresses in Daphnia
magna. Environ.Pollut.Ser.A Ecol.Biol. 26:33-
37.

3543

AF, UEndp

546

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Winner, R.W., and J.D. Gauss. 1986.
Relationship Between Chronic Toxicity and
Bioaccumulation of Copper, Cadmium and Zinc
As Affected by Water Hardness and Humic
Acid. Aquat.Toxicol. 8(3):149-161.

12009

AF, UEndp, Con

Wolterbeek, H.T., A. Viragh, J.E. Sloof, G.
Bolier, B. Van der Veer, and J. De Kok. 1995.
On the Uptake and Release of Zinc (65 Zn) in
the Growing Alga Selenastrum capricornutum
Printz. Environ.Pollut. 88:85-90.

13741

Plant, AF, UEndp

Wong, C.K.. 1992. Effects of Chromium,
Copper, Nickel, and Zinc on Survival and
Feeding of the Cladoceran Moina macrocopa.
Bull.Environ.Contam.Toxicol. 49:593-599.

45188

AF, UEndp

Wong, C.K.. 1993. Effects of Chromium,
Copper, Nickel, and Zinc on Longevity and
Reproduction of the Cladoceran Moina
macrocopa. Bull.Environ.Contam.Toxicol.
50:633-639.

6973

Wong, M.H., K.C. Luk, and K.Y. Choi. 1977.
The Effects of Zinc and Copper Salts on
Cyprinus carpio and Ctenopharyngodon idellus.
Acta Anat. 99(4):450-454.

15701

UEndp, Dur

Wong, M.H., S.H. Kwan, and F.Y. Tam. 1980.
Comparative Toxicity of Manganese and Zinc
on Chlorella pyrenoidosa, Chlorella salina and
Scenedesmus quadricauda. Microbios Lett.
12(45):37-46.

5872

Plant, Af, Con

Wong, P.T.S., and Y.K. Chau. 1990. Zinc
Toxicity to Freshwater Algae. Toxic.Assess.
5(2): 167-177.

180

Plant, AF, Dur, Con

Woodall, C., N. MacLean, and F. Crossley.
1988. Responses of Trout Fry (Salmo gairdneri)
and Xenopus laevis Tadpoles to Cadmium and
Zinc. Comp.Biochem.Physiol.C 89(1):93-99.

6074

Dur

Wooldridge, C.R., and D.P. Wooldridge. 1969.
Internal Damage in an Aquatic Beetle Exposed
to Sublethal Concentrations of Inorganic Ions.
Ann. Entomol. Soc.Am. 62(4):921 -933.

2868

AF, UEndp

547

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Wren, M.J., and D. McCarroll. 1990. A Simple
and Sensitive Bioassay for the Detection of
Toxic Materials Using a Unicellular Green Alga.
Environ.Pollut. 64(1):87-91.

3265

Plant, Af, Con

Xu, Q., and D. Pascoe. 1993. The
Bioconcentration of Zinc by Gammarus pulex
(L.) and the Application of a Kinetic Model to
Determine Bioconcentration Factors. Water
Res. 27(11):1683-1688.

9228

UEndp

Xu, Q., and D. Pascoe. 1993. Autoradiographic
Study of Zinc in Gammarus pulex (Amphipoda).
In: R.Dallinger and P.S.Rainbow (Eds.),
Ecotoxicology of Metals in Invertebrates, Lewis
Publ. :187-199.

13826

UEndp

Xu, Q., and D. Pascoe. 1994. The Importance of
Food and Water as Sources of Zinc During
Exposure of Gammarus pulex (Amphipoda).
Arch.Environ.Contam.Toxicol. 26(4):459-465.

13662

UEndp, RouExp

Yager, C.M., and H.W. Harry. 1964. The Uptake
of Radioactive Zinc, Cadmium and Copper by
the Freshwater Snail, Taphius glabratus.
Malacologia 1(3):339-353.

14058

AF, UEndp, Dur

Yang, H.N., and H.C. Chen. 1996. The
Influence of Temperature on the Acute Toxicity
and Sublethal Effects of Copper, Cadmium and
Zinc to Japanese Eel, Anguilla japonica. Acta
Zool.Taiwan. 7(1):29-38.

18914

NonRes

Zia, S., and D.G. McDonald. 1994. Role of the
Gills and Gill Chloride Cells in Metal Uptake in
the Freshwater-Adapted Rainbow Trout,
Oncorhynchus mykiss. Can.J.Fish.Aquat.Sci.
51(11):2482-2492.

17464

AF, UEndp, Dur

Zitko, V., and W.G. Carson. 1976. A Mechanism
of the Effects of Water Hardness on the
Lethality of Heavy Metals to Fish. Chemosphere
5(5):299-303.

8483

UEndp, Dur

Zou, E.. 1997. Effects of Sublethal Exposure to
Zinc Chloride on the Reproduction of the Water
Flea, Moina irrasa (Cladocera).
Bull.Environ.Contam.Toxicol. 58(3):437-441.

18008

UEndp

548

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Zou, E., and S. Bu. 1994. Acute Toxicity of
Copper, Cadmium, and Zinc to the Water Flea,
Moina irrasa (Cladocera).

Bui I. Environ. Contam. Toxicol. 52(5):742-748.

13762

Dur, NonRes

Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

1 For the studies that were not utilized, but the most representative SMAV/2 or most representative SMCV fell below
the criterion, or, if the studies were for a species associated with one of the four most sensitive genera used to calculate
the FAV in the most recent national ambient water quality criteria dataset used to derive the CMC91, EPA is providing
a transparent rationale as to why they were not utilized (see below).

General QA/QC failure because non-resident species in Oregon

The tests with the following species were used in the EPA BE of OR WQS for zinc in freshwater, but were not considered in the CWA
review and approval/disapproval action of the standards because these species do not have a breeding wild population in Oregon's
waters:

Morone

americana

White perch

Rehwoldt et al. 1971; Rehwoldt et al. 1972

Jordanella

floridae

Flagfish

Spehar 1976a;b

Agosia

chrysogaster

Longfin dace

Lewis 1978

Other Acute tests failins QA/QC by species

Daphnia pulex - Cladoceran

U.S. EPA. 1996. 1995 Updates: Water Quality Criteria Documents for the Protection of Aquatic Life in Ambient Water. EPA-820-B-96-001.

549

-------
The following test was included in EPA's BE of the OR WQS for zinc in freshwater, but were not used in this CWA review and
approval/disapproval action of these standards because a more sensitive lifestage was available.

Jindal, R., and A. Verma. 1990. Heavy Metal Toxicity to Daphnia pulex. Indian J. Environ. Health 32(3): 289-292.

Daphttia magna - Cladoceran

The following tests were included in EPA's BE of the OR WQS for zinc in freshwater, but were not used used in this CWA review
and approval/disapproval action of these standards because the tests were not based on the preferred flow-through measured test
conditions; however other flow-through measured test concentrations were available for this species.

Anderson, B.G. 1948. The apparent thresholds of toxicity to Daphnia magna for chlorides of various metals when added to
Lake Erie water. Trans. Am. Fish. Soc. 78: 96-113.

One LC50 value from S,U test, also a less than value, of <71.95 |ig/L.

Biesinger, K.E. and G.M. Christensen. 1972. Effects of Various Metals on Survival, Growth, Reproduction and Metabolism of
Daphnia magna. J. Fish Res. Board Can. 29: 1691-1700.

One LC50 value from S,U test of 191.31 |ig/L.

Cairns, J., Jr., A.L. Buikema, A.G. Heath and B.C. Parker. 1978. Effects of Temperature on Aquatic Organism Sensitivity to
Selected Chemicals. Va. Water Resour. Res. Center, Bull. 106, Office of Water Res. and Technol., OWRT Project B-084-VA,
VA. Polytech. Inst. State Univ., Blacksburg, VA: 1-88.

One LC50 value from S,M test of 538.68 |ig/L.

Mount, D.I. and T.J. Norberg. 1984. A Seven-Day Life-Cycle Cladoceran Toxicity Test. Environ. Toxicol. Chem. 3(3): 425-434
(Author Communication Used).

One LC50 value from S,U test of 130.82 |ig/L.

Chapman, G.A., S. Ota and F. Recht. Manuscript. Effects of water hardness on the toxicity of metals to Daphnia magna.
Available from: C.E. Stephan, U.S. EPA, Duluth, MN.

Three LC50 values from S,M tests ranging from 362.20 to 550.59 |ig/L.

550

-------
Magliette, R.J., F.G. Doherty, D. McKinney, and E.S. Venkataramani. 1995. Need for Environmental Quality Guidelines
Based on Ambient Freshwater Quality Criteria in Natural Waters—Case Study "Zinc." Bull. Environ. Contam. Toxicol. 54(4):
626-632.

Two LC50 values from S,M tests ranging from 488.26 to 692.65 |ig/L.

Brata, C., D.J. Baird, and S.J. Markich. 1998. Influence of Genetic and Environmental Factors on the Tolerance of Daphnia
magna Straus to Essential and Non-Essential Metals. Aquat. Toxicol. 42(2): 115-137.

Six LC50 values from S,M tests ranging from 358.90 to 1126.07 |ig/L.

Khangarot, B.S., P.K. Ray and H. Chandra. 1987. Daphnia magna as a Model to Assess Heavy Metal Toxicity: Comparative
Assessment with Mouse System. Acta Hydrochim. Hydrobiol. 15(4): 427-432.

One LC50 value from S,U test of 321.39 |ig/L.

Morone saxatilis — Striped bass

The following tests were included in EPA's BE of the OR WQS for zinc in freshwater, but were not used in this CWA review and
approval/disapproval action of these standards because the 1987 ALC document deemed the values too high and therefore were
outliers for this species.

Rehwoldt, R., G. Bida and B. Nerrie. 1971. Acute Toxicity of Copper, Nickel, and Zinc Ions to Some Hudson River Fish
Species. Bull. Environ. Contam. Toxicol. 6(5): 445-448.

Rehwoldt, R., L.W. Menapace, B. Nerrie and D. Allessandrello. 1972. The Effect of Increased Temperature upon the Acute
Toxicity of Some Heavy Metal Ions. Bull. Environ. Contam. Toxicol. 8(2): 91-96.

Morone americana — White perch

The following tests were included in EPA's BE of the OR WQS for zinc in freshwater, but were not used in this CWA review and
approval of these standards because the 1987 ALC document deemed the values too high and therefore were outliers for this species.

Rehwoldt, R., G. Bida and B. Nerrie. 1971. Acute Toxicity of Copper, Nickel, and Zinc Ions to Some Hudson River Fish
Species. Bull. Environ. Contam. Toxicol. 6(5): 445-448.

551

-------
Rehwoldt, R., L.W. Menapace, B. Nerrie and D. Allessandrello. 1972. The Effect of Increased Temperature upon the Acute
Toxicity of Some Heavy Metal Ions. Bull. Environ. Contam. Toxicol. 8(2): 91-96.

Other Chronic tests failing QA/QC by species

Daphnia magna - Cladoceran

The following tests were included in EPA's BE of the OR WQS for zinc in freshwater, but were not used in this CWA review and
approval/disapproval action of these standards because the tests were not based on measured test conditions, as per the Guidelines.

Magliette, R.J., F.G. Doherty, D. McKinney, and E.S. Venkataramani. 1995. Need for Environmental Quality Guidelines
Based on Ambient Freshwater Quality Criteria in Natural Waters—Case Study "Zinc." Bull. Environ. Contam. Toxicol. 54(4):
626-632.

This was also only a 48-hr chronic test

Paulaskis, J.D. and R.W. Winner. 1988. Effects of Water Hardness and Humic Acid on Zinc Toxicity to Daphnia magna.
Toxicology 12: 273-290..

552

-------
Appendix O Cadmium (Saltwater)
Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Abdullah, A.M., and M.P. Ireland. 1986. Cadmium Content,
Accumulation and Toxicity in Dog Whelks Collected Around
the Welsh Coastline. Mar.Pollut.Bull. 17(12):557-561.

6801

UEndp

Ahsanullah, M., and A.R. Williams. 1991. Sublethal Effects
and Bioaccumulation of Cadmium, Chromium, Copper, and
Zinc in the Marine Amphipod Allorchestes compressa.
Mar.Biol. 108:59-65.

331

Eff

Ahsanullah, M., and W. Ying. 1993. Tidal Rhythms and
Accumulation of Cadmium from Water and Sediment by
Soldier Crabs. Mar.Pollut.Bull. 26(1):20-23.

7147

UEndp, Eff

Ahsanullah, M., M.C. Mobley, and P. Rankin. 1988. Individual
and Combined Effects of Zinc, Cadmium and Copper on the
Marine Amphipod Allorchestes compressa.
Aust.J.Mar.Freshwater Res. 39(1):33-37.

13187

NonRes

Alderdice, D.F., H. Rosenthal, and F.P.J. Velsen. 1979.
Influence of Salinity and Cadmium on Capsule Strength in
Pacific Herring Eggs. Helgol.Wiss.Meeresunters. 32:149-162.

2575

UEndp, Eff, Dur

Alderdice, D.F., T.R. Rao, and H. Rosenthal. 1979. Osmotic
Responses of Eggs and Larvae of the Pacific Herring to
Salinity and Cadmium. Helgol.Wiss.Meeresunters. 32(4):508-
538.

9352

UEndp, Eff, Dur, Con

Amiard-Triquet, C., J.C. Amiard, R. Ferrand, A.C. Andersen,
and M.P. Dubois. 1986. Disturbance of a Met-Enkephalin-Like
Hormone in the Hepatopancreas of Crabs Contaminated by
Metals. Ecotoxicol.Environ.Saf. 11(2): 198-209.

12111

UEndp, Eff

553

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Arasu, S.M., and P.S. Reddy. 1994. Alterations in Oxidative
Metabolism in the Gill and Muscle of Marine Bivalve Perna
viridis During Cadmium and Copper Exposure. Fresenius
Environ.Bull. 3(12):721-727.

16831

Dur, AF

Has 48hr LC50 for Perna viridis(an invasive
species to North America)

Arnott, G.H., and M. Ahsanullah. 1979. Acute Toxicity of
Copper, Cadmium and Zinc to Three Species of Marine
Copepod. Aust.J.Mar.Freshwater Res. 30(1):63-71.

5563

Dur, Con

only 24hr

Aunaas, T., S. Einarson, T.E. Southon, and K.E.
Zachariassen. 1991. The Effects of Organic and Inorganic
Pollutants on Intracellular Phosphate Compounds in Blue
Mussels (Mytilus edulis). Comp.Biochem.Physiol.C
100(1/2):89-93.

3968

UEndp, Eff

Bahner, L.H., and D.R. Nimmo. 1975. Methods to Assess
Effects of Combinations of Toxicants, Salinity and
Temperature on Estuarine Animals. Trace
Subst. Environ. Health 9:169-177.

2839

UEndp, Eff, Dur, Con

Bailey, H.C., J.L. Miller, M.J. Miller, and B.S. Dhaliwal. 1995.
Application of Toxicity Identification Procedures to the
Echinoderm Fertilization Assay to Identify Toxicity in a
Municipal Effluent. Environ.Toxicol.Chem. 14(12):2181 -2186.

16375

Dur

40m i

Bat, L.. 1997. Studies on the Uptake of Copper, Zinc and
Cadmium by the Amphipod Corophium volutator (Pallas) in the
Laboratory. Turk.J.Mar.Sci. 3(2):93-109.

19858

UEndp, Eff

Bebianno, M.J., and W.J. Langston. 1992. Cadmium Induction
of Metallothionein Synthesis in Mytilus galloprovincialis.

Com p. Biochem. Physiol .C 103(1 ):79-85.

6497

UEndp, Eff

Bebianno, M.J., and W.J. Langston. 1992. Metallothionein
Induction in Littorina littorea (Mollusca: Prosobranchia) on
Exposure to Cadmium. J.Mar.Biol.Assoc.U.K. 72(2):329-342.

7153

UEndp, Eff

554

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Bebianno, M.J., J.A. Nott, and W.J. Langston. 1993. Cadmium
Metabolism in the Clam Ruditapes decussata: The Role of
Metallothioneins. Aquat.Toxicol. 27(3/4):315-334.

12440

UEndp, Eff, UChron

Bebianno, M.J., M.A.P. Serafim, and M.F. Rita. 1994.
Involvement of Metallothionein in Cadmium Accumulation and
Elimination in the Clam Ruditapes decussata.
Bull.Environ.Contam.Toxicol. 53(5):726-732.

13747

UEndp, Eff, UChron

Berail, G., P. Prudent, C. Massiani, and M. Pellegrini. 1992.
Isolation of Heavy Metal-Binding Proteins from a Brown
Seaweed Cystoseira barbata f. repens Cultivated in Copper or
Cadmium Enriched Seawater. In: E.Merian and W.Haerdi
(Eds.), Metal Compounds in Environment and Life,
4.Interrelation Between Chemistry and Biology, Science and
Technology Letters, Northwood, Middlesex, UK :55-62.

2351

UEndp, Eff

Bervoets, L., R. Blust, and R. Verheyen. 1995. The Uptake of
Cadmium by the Midge Larvae Chironomus riparius as a
Function of Salinity. Aquat.Toxicol. 33(3/4):227-243.

16117

UEndp, Eff, Dur

Birmelin, C., J. Cuzin-Roudy, M. Romeo, M. Gnassia-Barelli,
and S. Puiseux-Dao. 1995. The Mysid Siriella armata as a
Test Organisms in Toxicology: Effects of Cadmium.
Mar.Environ.Res. 39(1 -4):317-320.

16897

UEndp, Eff, NonRes

Bjerregaard, P., and M.H. Depledge. 1994. Cadmium
Accumulation in Littorina littorea, Mytilus edulis and Carcinus
maenas: The Influence of Salinity and Calcium Ion
Concentrations. Mar.Biol. 119(3):385-395.

16407

UEndp, Eff, UChron

Bjerregaard, P., and T. Vislie. 1985. Effects of Cadmium on
Hemolymph Composition in the Shore Crab Carcinus maenas.
Mar. Ecol. Prog.Ser. 27(1): 135-142.

8043

Dur, UChron, Con

555

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Bjerregaard, P.. 1982. Accumulation of Cadmium and
Selenium and Their Mutual Interaction in the Shore Crab
Carcinus maenas (L.). Aquat.Toxicol. 2(2):113-125.

6873

UEndp, Eff, UChron

Bjerregaard, P.. 1985. Effect of Selenium on Cadmium Uptake
in the Shore Crab Carcinus maenas (L.). Aquat.Toxicol.
7(3):177-189.

6944

UEndp, Eff, UChron

Bjerregaard, P.. 1988. Effect of Selenium on Cadmium Uptake
in Selected Benthic Invertebrates. Mar.Ecol.Prog.Ser.
48(1): 17-28.

2974

UEndp, Eff, UChron, Con

Bjerregaard, P.. 1988. Interaction between Selenium and
Cadmium in the Hemolymph of the Shore Crab Carcinus
maenas (L.). Aquat.Toxicol. 13(1 ):1 -12.

13132

Eff, Dur

Bjerregaard, P.. 1991. Relationship Between Physiological
Condition and Cadmium Accumulation in Carcinus maenas
(L.). Comp.Biochem.Physiol.A 99(1/2):75-83.

20017

UEndp, Eff, UChron

Blasco, J., and J. Puppo. 1999. Effect of Heavy Metals (Cu,
Cd and Pb) on Aspartate and Alanine Aminotransferase in
Ruditapes phillippinarum (Mollusca: Bivalvia).

Com p. Biochem. Physiol .C 122(2):253-263.

20072

Eff, Dur, UChron

Blust, R., E. Kockelbergh, and M. Baillieul. 1992. Effect of
Salinity on the Uptake of Cadmium by the Brine Shrimp
Artemia franciscana. Mar.Ecol.Prog.Ser. 84(3):245-254.

7554

UEndp, Eff, Dur

Blust, R., M. Baillieul, and W. Decleir. 1995. Effect of Total
Cadmium and Organic Complexing on the Uptake of Cadmium
by the Brine Shrimp, Artemia franciscana. Mar.Biol. 123(1):65-
73.

18288

UEndp, Eff, Dur

Borchardt, T.. 1983. Influence of Food Quantity on the Kinetics
of Cadmium Uptake and Loss Via Food and Seawater in
Mytilus edulis. Mar.Biol. 76(1):67-76.

11783

UEndp, Eff, Dur, UChron

556

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Braek, G.S., D. Malnes, and A. Jensen. 1980. Heavy Metal
Tolerance of Marine Phytoplankton. IV. Combined Effect of
Zinc and Cadmium on Growth and Uptake in Some Marine
Diatoms. J.Exp.Mar.BioI.Ecol. 42:39-54.

9761

UEndp, Dur, UChron, Con

Brand, G.W., G.J. Fabris, and G.H. Arnott. 1986. Reduction of
Population Growth in Tisbe holothuriae Humes (Copepoda:
Harpacticoida) Exposed to Low Cadmium Concentrations.
Aust.J.Mar.Freshwater Res. 37(4):475-479.

12048

UEndp

Brand, L.E., W.G. Sunda, and R.R.L. Guillard. 1986.
Reduction of Marine Phytoplankton Reproduction Rates by
Copper and Cadmium. J.Exp.Mar.BioI.Ecol. 96(3):225-250.

12014

UEndp, UChron

Bresler, V., and V. Yanko. 1995. Acute Toxicity of Heavy
Metals for Benthic Epiphytic Foraminifera Pararotalia spinigera
(Le Calvez) and Influence of Seaweed-Derived DOC.
Environ.Toxicol.Chem. 14(10):1687-1695.

15933

Dur

24hr only

Bressan, M., and R. Brunetti. 1988. The Effects of Nitriloacetic
Acid, Cd and Hg on the Marine Algae Dunaliella tertiolecta and
Isochrysis galbana. Water Res. 22(5):553-556.

12936

UEndp

Brinkhuis, B.H., W.F. Penello, and A.C. Churchill. 1980.
Cadmium and Manganese Flux in Eelgrass Zostera marina. II.
Metal Uptake by Leaf and Root-Rhizome Tissue. Mar. Biol.
58(3): 187-196.

6194

Eff, Dur, Con

Brouwer, M., and T. Brouwer-Hoexum. 1984. Cadmium
Accumulation by the Blue Crab, Callinectes sapidus:
Involvement of Hemocyanin and Characterization of
Cadmium-Binding Proteins. Mar.Environ.Res. 14(1-4):71-88.

14642

UEndp, Eff, Dur

Brown, B., and M. Ahsanullah. 1971. Effect of Heavy Metals
on Mortality and Growth. Mar.Pollut.Bull. 2:182-187.

2467

Dur, UChron, Con

557

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Brown, C.L., and S.N. Luoma. 1995. Use of the Euryhaline
Bivalve Potamocorbula amurensis as a Biosentinel Species to
Assess Trace Metal Contamination in San Francisco Bay.
Mar. Ecol. Prog. Ser. 124(1-3): 129-142.

18036

UEndp, Eff, Dur, UChron

Burdin, K.S., and K.T. Bird. 1994. Heavy Metal Accumulation
by Carrageenan and Agar Producing Algae. Bot.Mar. 37:467-
470.

45156

UEndp, Eff, Dur

24hr only

Calabrese, A., F.P. Thurberg, and E. Gould. 1977. Effects of
Cadmium, Mercury and Silver on Marine Animals. MFR Paper
1244, Mar Fish Rev 39:5-11.

12206

UEndp, Eff, UChron

Calabrese, A., F.P. Thurberg, M.A. Dawson, and D.R.
Wenzloff. 1975. Sublethal Physiological Stress Induced by
Cadmium and Mercury in the Winter Flounder,
Pseudopleuronectes americanus. In: J.H.Koeman and
J.J.T.W.A.Strik (Eds.), Sublethal Effects of Toxic Chemicals on
Aquat.Animals, Elsevier Sci.Publ., Amsterdam, NY : 15-21.

15525

UEndp, Eff, UChron, Con

Calabrese, A., R.S. Collier, and J.E. Miller. 1974. Physiological
Response of the Cunner, Tautogolabrus adspersus, to
Cadmium. I. Introduction and Experimental Design. Noaa
Tech.Rep.Nmfs Ssr F-681:1-3.

6444

UEndp

Calapaj, G.G.. 1974. Ricerche Di Laboratorio
SuH'Inquinamento Chimico Dei Mitili Nota II: Cadmio, Zinco.
(Chemical Pollution of Mytilus. II. Cadmium and Zinc). Ig.Mod.
67(2): 136-145 (ITA) (ENG ABS).

8508

UEndp, Eff, UChron

Canli, M., and R.W. Furness. 1993. Toxicity of Heavy Metals
Dissolved in Sea Water and Influences of Sex and Size on
Metal Accumulation and Tissue Distribution in the Norway
Lobster. Mar.Environ.Res. 36(4):217-236.

4563

UEndp, Eff, UChron

558

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Canli, M., and R.W. Furness. 1995. Mercury and Cadmium
Uptake from Seawater and from Food by the Norway Lobster
Nephrops norvegicus. Environ.Toxicol.Chem.. 14(5):819-828.

15120

UEndp, Eff, UChron

Canterford, G.S., A.S. Buchanan, and S.C. Ducker. 1978.
Accumulation of Heavy Metals by the Marine Diatom Ditylum
brightwellii (West) Grunow. Aust.J.Mar.Freshwater Res.
29(5):613-622.

15455

UEndp, Eff, Dur, UChron, Con

Carmichael, N.G., and B.A. Fowler. 1981. Cadmium
Accumulation and Toxicity in the Kidney of the Bay Scallop
Argopecten irradians. Mar.Biol. 65(1):35-43.

15347

UEndp, Eff, Con

Carr, R.S., and J.M. Neff. 1982. Biochemical Indices of Stress
in the Sandworm Neanthes virens (Sars). II. Sublethal
Responses to Cadmium. Aquat.Toxicol. 2(5-6):319-333.

6153

Eff, UChron

Carr, R.S., J.W. Williams, F.I. Saksa, R.L. Buhl, and J.M. Neff.
1985. Bioenergetic Alterations Correlated with Growth,
Fecundity and Body Burden of Cadmium for Mysids
(Mysidopsis bahia). Environ.Toxicol.Chem. 4(2):181-188.

11581

UEndp, Eff, UChron

Carvalho, R.A., M.C. Benfield, and P.H. Santschi. 1999.
Comparative Bioaccumulation Studies of Colloidally
Complexed and Free-Ionic Heavy Metals in Juvenile Brown
Shrimp Penaeus aztecus (Crustacea: Decapoda: Penaeidae).
Limnol.Oceanogr. 44(2):403-414.

48059

UEndp, Eff, Dur

Casini, S., and M.H. Depledge. 1997. Influence of Copper,
Zinc, and Iron on Cadmium Accumulation in the Talitrid
Amphipod, Platorchestia platensis.

Bull. Environ.Contam.Toxicol. 59:500-506.

18370

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Cattani, 0., R. Serra, G. Isani, G. Raggi, P. Cortesi, and E.
Carpene. 1996. Correlation Between Metallothionein and
Energy Metabolism in Sea Bass, Dicentrarchus labrax,
Exposed to Cadmium. Comp.Biochem.Physiol.C 113(2): 193-
199.

16851

UEndp, Eff, Dur, UChron

559

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Chan, H.M., P. Bjerregaard, P.S. Rainbow, and M.H.
Depledge. 1992. Uptake of Zinc and Cadmium by Two
Populations of Shore Crabs Carcinus maenas at Different
Salinities. Mar.Ecol.Prog.Ser. 86(1):91-97.

7546

UEndp, Eff

Chapman, P.M., M.A. Farrell, and R.O. Brinkhurst. 1982.
Relative Tolerances of Selected Aquatic Oligochaetes to
Combinations of Pollutants and Environmental Factors.
Aquat.Toxicol. 2(1):69-78.

10602

No Code

ECOTOX provides three 96-h LC50s of
125000 -135000 |jg/L for Monopylephorus
cuticulatus for this study. This value could
have been considered for EPA's evaluation of
saltwater cadmium, but the species is
relatively insensitive to cadmium compared to
others. Note, this test was not used in the
2001 cadmium WQC doc. Other LC50s for
this and other species were enterted into
ECOTOX as approximate values or ranges.

Chelomin, V.P., and N.N. Belcheva. 1992. The Effect of Heavy
Metals on Processes of Lipid Peroxidation in Microsomal
Membranes from the Hepatopancreas of the Bivalve Mollusc
Mizuhopecten. Comp.Biochem.Physiol.C 103(2):419-422.

6730

UEndp, Eff, UChron

Chelomin, V.P., E.A. Bobkova, O.N. Lukyanova, and N.M.
Chekmasova. 1995. Cadmium-Induced Alterations in Essential
Trace Element Homoeostasis in the Tissues of Scallop
Mizuhopecten yessoensis. Com p. Biochem. Physiol. C
110(3):329-335.

16150

UEndp, Eff, Dur, UChron

Chen, J.C., and P.C. Liu. 1987. Accumulation of Heavy Metals
in the Nauplii of Artemia salina. J.World Aquacult.Soc.
18(2):84-93.

2749

UEndp, Eff, Dur

Coleman, N., T.F. Mann, M. Mobley, and N. Hickman. 1986.
Mytilus edulis planulatus: An "Integrator" of Cadmium
Pollution?. Mar.Biol. 92(1): 1-5.

2486

UEndp

Coleman, N.. 1980. The Effect of Emersion on Cadmium
Accumulation by Mytilus edulis. Mar.Pollut.Bull. 11(12):359-
362.

9254

UEndp, Eff, Dur, Con

Congiu, A.M., E. Calendi, and G. Ugazio. 1984. Effects of
Metal Ions and CCI4 on Sea Urchin Embryo (Paracentrotus
lividus). Res.Commun.Chem.Pathol.Pharmacol. 43(2):317-
323.

625

UEndp, Dur

560

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Cui, K., Y. Liu, and L. Hou. 1987. Effects of Six Heavy Metals
on Hatching Eggs and Survival of Larval of Marine Fish.
Oceanol.Limnol.Sin./Haiyang Yu Huzhao 18(2):138-144 (CHI)
(ENG ABS).

3222

NonRes

D'Agostino, A., and C. Finney. 1974. The Effect of Copper and
Cadmium on the Development of Tigriopus japonicus. In:
F.J.Vernberg and W.B.Vernberg (Eds.), Pollution and
Physiology of Mar.Organisms, Academic Press, NY :445-463.

15558

UEndp, Dur, UChron

Dalla Via, G.J., R. Dallinger, and E. Carpene. 1989. Effects of
Cadmium on Murex trunculus from the Adriatic Sea. II.
Oxygen Consumption and Acclimation Effects.
Arch.Environ.Contam.Toxicol. 18(4):562-567.

2557

UEndp, Eff, Dur, Con

Darmono, D.. 1990. Uptake of Cadmium and Nickel in Banana
Prawn (Penaeus merguiensis de Man).

Bull. Environ.Contam .Toxicol. 45(3):320-328.

18787

UEndp, Eff, UChron

Darmono, G.R.W.D., and R.S.F. Campbell. 1990. The
Pathology of Cadmium and Nickel Toxicity in the Banana
Shrimp (Penaeus merguiensis de Man). Asian Fish.Sci.
3(3):287-297.

9711

UEndp, Eff, UChron

Davies, I.M., G. Topping, W.C. Graham, C.R. Falconer, A.D.
Mcintosh, and D. Saward. 1981. Field and Experimental
Studies on Cadmium in the Edible Crab Cancer pagurus.
Mar.Biol. 64:291-297.

14333

UEndp, Eff, UChron

Davies, N.A., M.G. Taylor, and K. Simkiss. 1997. The
Influence of Particle Surface Characteristics on Pollutant Metal
Uptake by Cells. Environ.Pollut. 96(2): 179-184.

18661

UEndp, Eff, Dur

Dawson, M.A., E. Gould, F.P. Thurberg, and A. Calabrese.
1977. Physiological Response of Juvenile Striped Bass,
Morone saxatilis, to Low Levels of Cadmium and Mercury.
Chesapeake Sci. 18(4):353-359.

15770

UEndp, Eff, UChron

561

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

16911

UEndp, Eff

Brine Shrimp

DeLisle, P.F.Jr.. 1994. The Effect of Salinity on Cadmium
Toxicity in the Estuarine Mysid Mysidopsis bahia: Roles of
Osmoregulation and Calcium. Mar.Environ.Res. 37(1):47-62.

4110

UEndp

Demuynck, S., and N. Dhainaut-Courtois. 1994. Metal-Protein
Binding Patterns in the Polychaete Worm Nereis diversicolor
During Short-Term Acute Cadmium Stress.
Comp.Biochem.Physiol.C 108(1):59-64.

16755

Eff, Dur

Den Besten, P.J., E.G. Van Donselaar, H.J. Herwig, D.I.
Zandee, and P.A. Voogt. 1991. Effects of Cadmium on
Gametogenesis in the Sea Star Asterias rubens L.
Aquat.Toxicol. 20:83-94.

5251

Field, UEndp, Eff

DeNicola, M., N. Cardellicchio, C. Gambardella, S.M. Guarino,
and C. Marra. 1993. Effects of Cadmium on Survival,
Bioaccumulation, Histopathology, and PGM Polymorphism in
the Marine Isopod Idotea baltica. In: R.Dallinger and
P.S.Rainbow (Eds.), Ecotoxicology of Metals in Invertebrates,
Lewis Publ. : 103-116.

13827

UEndp, Eff, Dur, UChron

Denton, G.R.W., and C. Burdon-Jones. 1981. Influence of
Temperature and Salinity on the Uptake, Distribution and
Depuration of Mercury, Cadmium and Lead by the Black-Lip
Oyster Saccostrea echinata. Mar.Biol. 64:317-326.

14335

UEndp, Eff

Denton, G.R.W., and C. Burdon-Jones. 1986. Environmental
Effects on Toxicity of Heavy Metals to Two Species of Tropical
Marine Fish from Northern Australia. Chem.Ecol. 2(3):233-
249.

4327

NonRes

562

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Devi, V.U., and Y.P. Rao. 1989. Cadmium Accumulation in
Fiddler Crabs Ilea annulipesLatrelle and Ilea triangularis
(Milne Edwards). Water Air Soil Pollut. 43(3-4):309-321.

891

UEndp, Eff, Dur, UChron, Con

Devi, V.U., and Y.P. Rao. 1989. Heavy Metal Toxicity to
Fiddler Crabs, Ilea annulipes Latreille and Ilea triangularis
(Milne Edwards): Respiration on Exposure to Copper,
Mercury,. Bull.Environ.Contam.Toxicol. 43(1 ):165-172.

2150

UEndp, Eff, Dur

Devi, V.U.. 1987. Heavy Metal Toxicity to Fiddler Crabs, Ilea
annulipes latreille and Uca triangularis (Milne Edwards):
Tolerance to Copper, Mercury, Cadmium.
Bull.Environ.Contam.Toxicol. 39:1020-1027.

2602

NonRes

Devineau, J., and C.A. Triquet. 1985. Patterns of
Bioaccumulation of an Essential Trace Element (Zinc) and a
Pollutant Metal (Cadmium) in Larvae of the Prawn Palaemon
serratus. Mar.Biol. 86(2): 139-143.

10835

UEndp, Eff, Dur, UChron

Duquesne, S., A.E. Flowers, and J.C. Coll. 1995. Preliminary
Evidence for a Metallothionein-Like Heavy Metal-Binding
Protein in the Tropical Marine Bivalve Tridacna crocea.
Comp.Biochem. Physiol. C 112(1):69-78.

18848

UEndp, Eff, Dur, UChron

Eertman, R.H.M., W. Zurburg, C.A. Schipper, B. Sandee, and
A.C. Smaal. 1996. Effects of PCB 126 and Cadmium on the
Anaerobic Metabolism of the Mussel Mytilus edulis L..
Comp.Biochem.Physiol.C 113(2):267-272.

16854

UEndp, Eff, UChron, LT

Eisler, R., G.E. Zaroogian, and R.J. Hennekey. 1972.
Cadmium Uptake by Marine Organisms. J.Fish.Res.Board
Can. 29(9): 1367-1369.

9100

UEndp, Eff

Eldon, J., M. Pekkarinen, and R. Kristoffersson. 1980. Effects
of Low Concentrations of Heavy Metals on the Bivalve
Macoma balthica. Ann.Zool.Fenn. 17:233-242.

17309

UEndp, Eff, Dur

563

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Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Elliott, N.G., R. Swain, and D.A. Ritz. 1986. Metal Interaction
During Accumulation by the Mussel Mytilus edulis planulatus.
Mar.Biol. 93(3):395-399.

12054

UEndp, Eff, Dur, UChron

Emery, V.L.J., D.W. Moore, B.R. Gray, B.M. Duke, A.B.
Gibson, R.B.Wright, and J.D. Farrar. 1997. Development of a
Chronic Sublethal Sediment Bioassay Using the Estuarine
Amphipod Leptocheirus plumulosus (Shoemaker).
Environ.Toxicol.Chem. 16(9): 1912-1920.

18159

No Code; See note

ECOTOX provides thirteen 96-h LC50s
ranging from 20 to 100 |jg/L for this study.
The saltwater criteria falls within this range/2.
Note, this test was not used in the 2001
cadmium WQC doc. No definitive values
given.

Emson, S., and M. Crane. 1994. A Comparison of the Toxicity
of Cadmium to the Mysid Shrimps Neomysis integer (Leach)
and Mysidopsis bahia (Molenock). Water Res. 28(8): 1711 -
1713.

4439

Con

Engel, D.W.. 1983. The Intracellular Partitioning of Trace
Metals in Marine Shellfish. Sci.Total Environ. 28:129-140.

10911

UEndp, Eff, UChron, Con

Engel, D.W.. 1999. Accumulation and Cytosolic Partitioning of
Metals in the American Oyster Crassostrea virginica.
Mar. Environ. Res. 47:89-102.

20626

UEndp, Eff, UChron

Espiritu, E.Q., C.R. Janssen, and G. Persoone. 1995. Cyst-
Based Toxicity Tests. VII. Evaluation of the 1-h Enzymatic
Inhibition Test (Fluotox) with Artemia nauplii.
Environ.Toxicol.Water Qual. 10:25-34.

16031

Dur

Brine Shrimp

Establier, R., and M. Gutierrez. 1980. Cadmium Accumulation
From Sea Water on Dicentrarchus labrax and Sparus aurata
and its Histopathological Effects. Invest.Pesq.44(1 ):43-54
(Spa) (Eng Abs).

9794

UEndp, Eff, UChron, Con

Everaarts, J.M.. 1990. Uptake and Release of Cadmium in
Various Organs of the Common Mussel, Mytilus edulis (L.).
Bull.Environ.Contam.Toxicol. 45(4):560-567.

3497

UEndp, Eff, UChron

Fabris, G.J., J.E. Harris, and J.D. Smith. 1982. Uptake of
Cadmium by the Seagrass Heterozostera tasmanica from
Corio Bay and Western Port, Victoria. Aust.J.Mar.Freshwater
Res. 33(5):829-836.

13458

UEndp, Eff, Dur

564

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Faraday, W.E., and A.C. Churchill. 1979. Uptake of Cadmium
by the Eelgrass Zostera marina. Mar.Biol. 53(3):293-298.

15650

UEndp, Eff, Dur

Fernandez, T.V., and N.V. Jones. 1990. Studies on the
Toxicity of Zinc and Copper Applied Singly and Jointly to
Nereis diversicolor at Different Salinities and Temperatures.
Trop.Ecol. 31(1):47-55.

7744

UEndp, Eff, Dur, Con, LT

Fernandez-Leborans, G., and A. Novillo. 1994. Experimental
Approach to Cadmium Effects on a Marine Protozoan
Community. Acta Hydrochim.Hydrobiol. 22(1):19-27 (OECDG
Data File).

16339

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Fernandez-Leborans, G., and Y.O. Herrero. 1999. Toxicity and
Bioaccumulation of Cadmium in Marine Protozoa
Communities. Ecotoxicol.Environ.Saf. 43(3):292-300.

20428

UEndp, Eff, Dur

Fisher, N.S., and G.J. Jones. 1981. Heavy Metals and Marine
Phytoplankton: Correlation of Toxicity and Sulfhydryl-Binding.
J.Phycol. 17(1): 108-111.

14681

NonRes, Dur

Fisher, N.S., M. Bohe, and J.L. Teyssie. 1984. Accumulation
and Toxicity of Cd, Zn, Ag, and Hg in Four Marine
Phytoplankters. Mar.Ecol.Prog.Ser. 18(3):201-213.

11805

UEndp, Eff

Forbes, V.E., and M.H. Depledge. 1992. Cadmium Effects on
the Carbon and Energy Balance of Mudsnails. Mar.Biol.
113(2):263-269.

6411

UEndp, Eff, Dur, UChron

Forbes, V.E.. 1991. Response of Hydrobia ventrosa (Montagu)
to Environmental Stress: Effects of Salinity Fluctuations and
Cadmium Exposure on Growth. Funct.Ecol. 5(5):642-648.

7304

UEndp, UChron

Forget, J., J.F. Pavilion, M.R. Menasria, and G. Bocquene.
1998. Mortality and LC50 Values for Several Stages of the
Marine Copepod Tigriopus brevicornis (Muller) Exposed to the
Metals Arsenic and Cadmium and the. Ecotoxicol.Environ.Saf.
40(3):239-244.

19281

NonRes

565

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Fowler, B.A., N.G. Carmichael, K.S. Squibb, and D.W. Engel.
1981. Factors Affecting Trace Metal Uptake and Toxicity to
Estuarine Organisms. II. Cellular Mechanisms. In: J.Vernberg,
A.Calabrese, F.P.Thurberg and W.B.Vernberg (Eds.),
Biological Monitoring of Marine Pollutants, Academic Press,
New York, NY :145-163.

20311

UEndp, Eff, Dur, UChron

Francesconi, K.A., E.J. Moore, and J.S. Edmonds. 1994.
Cadmium Uptake from Seawater and Food by the Western
Rock Lobster Panulirus cygnus. Bull.Environ.Contam.Toxicol.
53(2):219-223.

13704

UEndp, Eff, Dur, UChron

Francesconi, K.A., J. Gailer, J.S. Edmonds, W. Goessler, and
K.J. Irgolic. 1999. Uptake of Arsenic-Betaines by the Mussel
Mytilus edulis. Comp.Biochem.Physiol.C 122(1 ):131 -137.

19960

UEndp, Eff, Dur, UChron

Francesconi, K.A.. 1989. Distribution of Cadmium in the Pearl
Oyster, Pinctada albina albina (Lamarck), Following Exposure
to Cadmium in Seawater. Bull.Environ.Contam.Toxicol.
43(2):321-328.

3322

UEndp, Eff, Dur, UChron

Frazier, J.M., and S.G. George. 1983. Cadmium Kinetics in
Oysters - A Comparative Study of Crassostrea gigas and
Ostrea edulis. Mar.Biol. 76(1):55-61.

10716

UEndp, Eff, UChron

Gajbhiye, S.N., and R. Hirota. 1990. Toxicity of Heavy Metals
to Brine Shrimp Artemia. J.Indian Fish.Assoc. 20:43-50.

17792

UEndp, Dur

Brine Shrimp

Gardner, G.R.. 1975. Chemically Induced Lesions in Estuarine
or Marine Teleosts. In: W.E.Ribelin and G.Migaki (Eds.),
Pathology of Fishes, Univ.of Wl Press, Madison, Wl :657-693.

15562

UEndp, Eff, UChron

566

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Gaudy, R., J.P. Guerin, and P. Kerambrun. 1991. Sublethal
Effects of Cadmium on Respiratory Metabolism, Nutrition,
Excretion and Hydrolase Activity in Leptomysis lingvura
(Crustacea: Mysidacea). Mar.Biol. 109(3):493-501.

3802

UEndp, Eff, Dur, Com

George, S.G., and T.L. Coombs. 1977. The Effects of
Chelating Agents on the Uptake and Accumulation of
Cadmium by Mytilus edulis. Mar.Biol. 39(3):261-268.

15622

Eff, Con

George, S.G., P.A. Hodgson, P. Tytler, and K. Todd. 1996.
Inducibility of Metallothionein mRNA Expression and Cadmium
Tolerance in Larvae of a Marine Teleost, the Turbot
(Scophthalmus maximus). Fundam.Appl.Toxicol. 33(1):91-99.

8931

NonRes

Gil, J.M., J.A. Marigomez, and E. Angulo. 1989.
Histopathology of Polysaccharide and Lipid Reserves in
Various Tissues of Littorina littorea Exposed to Sublethal
Concentrations of Cadmium. Comp.Biochem.Physiol.C
94(2):641-648.

709

UEndp, Eff, UChron

Giraud, A.S., L.K. Webster, J.G. Fabris, L.C. Collett, and N.D.
Yeomans. 1986. Absence of Histopathological Response to
Cadmium in Gill and Digestive Diverticula of the Mussel,
Mytilus edulis. Bull.Environ.Contam.Toxicol. 36(1): 146-149.

11808

UEndp, Eff, UChron

Gnassia-Barelli, M., M. Romeo, and S. Puiseux-Dao. 1995.
Effects of Cadmium and Copper Contamination on Calcium
Content of the Bivalve Ruditapes decussatus.
Mar.Environ.Res. 39(1-4):325-328.

16894

UEndp, Eff, Dur, UChron

Gnezdilova, S.M., I.G. Lipina, and N.K. Khristoforova. 1987.
Accumulation of Cadmium in the Gonads of Sea Urchins and
Its Effect on Gametogenesis and Embryogenesis. Exp.Water
Toxicol.(Eksp.Vodn.Toksikol.) 12:68-72 (RUS) / C.A.Select -
Environ.Pollut. 110:2329c.

300

UEndp, Dur, UChron

Species(non-NA)????

567

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Gnezdilova, S.M., I.G. Lipina, and N.K. Khristoforova. 1987.
Morphological Changes in the Ovaries of the Sea Urchin
Strongylocentrotus intermedius Exposed to Cadmium.
Dis.Aquat.Org. 2(2): 127-133.

2438

UEndp, Eff, UChron

Gnezdilova, S.M., I.G. Lipina, V.B. Durkina, I.V. Burovina, and
K.Y. Ukhanov. 1988. The Content of Cadmium in the Gonad of
the Sea Urchin Strongylocentrotus intermedius and its Effects
on Gametes and Offspring. C.A.Sel.-Environ.Pollut. 18:109-
68396H / Biol.Morya (Vladivost.) 2:46-51 (RUS).

13144

UEndp, Eff, UChron, Con

Greenwood, J.G., and D.R. Fielder. 1983. Acute Toxicity of
Zinc and Cadmium to Zoeae of Three Species of Portunid
Crabs (Crustacea: Brachyura). Comp.Biochem.Physiol.C
75(1): 141-144.

10063

NonRes, Dur

Gutierrez-Galindo, E.A.. 1980. Study of the Removal of
Cadmium by Mytilus edulis in the Presence of EDTA and
Phosphate. Chemosphere 9(7/8):495-500 (FRE) (ENG ABS).

9820

UEndp, Eff, UChron, Con

Haglund, K., M. Bjorklund, S. Gunnare, A. Sandberg, U.
Olander, and M. Pedersen. 1996. New Method for Toxicity
Assessment in Marine and Brackish Environments Using the
Macroalga Gracilaria tenuistipitata (Gracilariales,
Rhodophyta). Hydrobiologia 326/327:317-325.

18453

NonRes

Hall, L.W.Jr., M.C. Ziegenfuss, R.D. Anderson, and B.L.
Lewis. 1994. The Effect of Salinity on the Acute Toxicity of
Total Dissolved and Free Cadmium to the Copepod
Eurytemora affinis and the Larval Fish Cyprinodon.
Chesapeake Bay Program, CBP/TRS 130/94, U.S.EPA,
Annapolis, MD :46 p.(U.S.NTIS PB95-179925).

17219

Has Six 96hr LC50's for Sheephead and
Copepod

568

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Hall, L.W.Jr., M.C. Ziegenfuss, R.D. Anderson, and B.L.
Lewis. 1995. The Effect of Salinity on the Acute Toxicity of
Total and Free Cadmium to a Chesapeake Bay Copepod and
Fish. Mar.Pollut.Bull. 30(6):376-384.

18671

Has Six 96hr LC50's for Sheephead and
Copepod

Hannan, P.J., and C. Patouillet. 1972. Effects of Pollutants on
Growth of Algae. Rep.NRL (Nav.Res.Lab.) Prog.:1-8 (Author
Communication Used).

9095

UEndp, Dur

Hansen, D.J. 1983. Section on Acute Toxicity Tests to be
Inserted in the April 1983 Report on Site Specific FAV's.
U.S.EPA, Narragansett, Rl :7.

3732

No Code; See note

ECOTOX provides a 96-h LC50s of 310 |jg/L
for this study. This value could have been
considered for EPA's evaluation of saltwater
cadmium, but the species is relatively
insensitive to cadmium compared to others.
Note, this test was not used in the 2001
cadmium WQC doc.

Hansen, I.V., J.M. Weeks, and M.H. Depledge. 1995.
Accumulation of Copper, Zinc, Cadmium and Chromium by
the Marine Sponge Halichondria panicea Pallas and the
Implications for Biomonitoring. Mar.Pollut.Bull. 31 (1 -3):133-
138.

18038

UEndp, Eff, Dur, UChron

Haritonidis, S., H.J. Jager, and H.O. Schwantes. 1983.
Accumulation of Cadmium, Zinc, Copper and Lead by Marine
Macrophyceae Under Culture Conditions. Angew.Bot.
57(5/6):311-330.

11369

UEndp, Eff, Dur, UChron

Haritonidis, S.. 1985. Uptake of Cd, Zn, Cu and Pb by Marine
Macrophyceae Under Culture Conditions. Mar. Environ. Res.
17(2-4): 198-199.

6414

UEndo, Eff, Con

Hawkins, W.E., L.G. Tate, and T.G. Sarphie. 1980. Acute
Effects of Cadmium on the Spot Leiostomus xanthurus
(Teleostei): Tissue Distribution and Renal Ultrastructure.
J.Toxicol.Environ.Health 6:283-295 (Author Communication
Used).

5263

UEndp, Eff, Dur

Henry, M., W. Huang, C. Cornet, M. Belluau, and J.P. Durbec.
1984. Accidental Contamination by Cadmium of the Mollusc
Ruditapes decussatus: Bioaccumulation and Toxicity (LD50,
96H). Oceanol.Acta 7(3):329-325 (1984) (Fre) (Eng Abs).

11394

NonRes

569

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Hernandez-Pascual, M.D., and L. Tort. 1989. Metabolic
Effects After Short-Term Sublethal Cadmium Exposure to
Dogfish (Scyliorhinus canicula). Comp.Biochem.Physiol.C
94(1 ):261-264.

3062

UEndp, Eff

Hollibaugh, J.T., D.L.R. Seibert, and W.H. Thomas. 1980. A
Comparison of the Acute Toxicities of Ten Heavy Metals to
Phytoplankton From Saanich Inlet, B.C., Canada.

Estuar. Coast. Mar. Sci. 10(1):93-105.

5282

UEndp, Dur, Con

Hoppenheit, M.. 1977. On the Dynamics of Exploited
Populations of Tisbe holothuriae (Copepoda, Harpacticoida).
V. The Toxicity of Cadmium: Response to Sub-Lethal.
Helgol.Wiss.Meeresunters. 29(4):503-523.

8368

UEndp, UChron, Con

Hori, H., M. Tateishi, K. Takayanagi, and H. Yamada. 1996.
Applicability of Artificial Seawater as a Rearing Seawater for
Toxicity Tests of Hazardous Chemicals by Marine Fish
Species. Nippon Suisan Gakkaishi
/Bull.Jpn.Soc.Sci.Fish.(4):614-622 (JPN) (ENG ABS).

16999

Eff, Dur, Uchron

Howard, C.L., and C.S. Hacker. 1990. Effects of Salinity,
Temperature, and Cadmium on Cadmium-Binding Protein in
the Grass Shrimp, Palaemonetes pugio.
Arch.Environ.Contam.Toxicol. 19(3):341-347.

3170

ECOTOX provides two 96-h LC50s of 189
|jg/L and 2405 |jg/L for this study. Combined
with the other LC50s for Palaemonetes
pugio, the SMAV would have been 1283
|jg/L. Although this is lower than the species'
current SMAV, it is not sensitive relative to
other species. Note, this test was not used in
the 2001 cadmium WQC doc

Hu, S., C.H. Tang, and M. Wu. 1996. Cadmium Accumulation
by Several Seaweeds. Sci.Total Environ. 187:65-71.

18733

UEndp, Eff, Dur

Hung, Y.W. 1982. Effects of Temperature and Chelating
Agents on Cadmium Uptake in the American Oyster.
Bull.Environ.Contam.Toxicol. 28:546-551.

14338

UEndp, Eff

Hutcheson, M., D.C. Miller, and A.Q.White. 1985. Respiratory
and Behavioral Responses of the Grass Shrimp
Palaemonetes pugio toCadmium and Reduced Dissolved
Oxygen. Mar.Biol. 88(1):59-66.

11892

UEndp, Eff, Dur

570

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Hutcheson, M.S.. 1974. The Effect of Temperature and
Salinity on Cadmium Uptake by the Blue Crab, Callinectes
sapidus. Chesapeake Sci. 15(4):237-241.

8580

UEndp, Eff, Con

Hutchinson, T.H., and M.J. Manning. 1996. Effect of In Vivo
Cadmium Exposure on the Respiratory Burst of Marine Fish
(Limanda limanda L.) Phagocytes. Mar.Environ.Res.
41 (4):327-342.

20572

UEndp, Eff, NonRes

Hylland, K., T. Kaland, and T. Andersen. 1994. Subcellular Cd
Accumulation and Cd-Binding Proteins in the Netted Dog
Whelk, Nassarius reticulatus L. Mar.Environ.Res. 38(3):169-
193.

16733

UEndp, Eff, Dur

Ikuta, K.. 1987. Cadmium Accumulation by a Top Shell Batillus
cornutus. Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan Gakkaishi)
53(7): 1237-1242.

2628

UEndp, Eff, UChron

Ikuta, K.. 1987. Concentration Thresholds in Accumulation of
Heavy Metals by Haliotis discus and Batillus cornutus.
Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan Gakkaishi) 53(9):1673-
1678.

2630

UEndp, Eff, UChron

Ikuta, K.. 1987. Localization of Cadmium in the Viscera and
the Muscular Tissues of Carnivorous Gastropods Before and
After Exposure. Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan
Gakkaishi) 53(12):2275-2278.

5844

UEndp, Eff, Dur

Ikuta, K.. 1987. Localization of Heavy Metals in the Viscera

and the Muscular Tissues of Haliotis discus Exposed to

Selected Metal Concentration Gradients.

Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan Gakkaishi) 53(12):2269-

2274.

3215

UEndp, Eff, UChron

Itow, T., R.E. Loveland, and M.L. Botton. 1998. Developmental
Abnormalities in Horseshoe Crab Embryos Caused by
Exposure to Heavy Metals. Arch.Environ.Contam.Toxicol.
35(1):33-40.

19470

UEndp, Dur

571

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Itow, T., T. Igarashi, M.L. Botton, and R.E. Loveland. 1998.
Heavy Metals Inhibit Limb Regeneration in Horseshoe Crab
Larvae. Arch.Environ.Contam.Toxicol. 35(3):457-463.

20180

UEndp, UChron

Jackim, E., G. Morrison, and R. Steele. 1977. Effects of
Environmental Factors on Radiocadmium Uptake by Four
Species of Marine Bivalves. Mar.Biol. 40:303-308.

10416

UEndp, Eff, Dur, UChron

Jackim, E., J.M. Hamlin, and S. Sonis. 1970. Effects of Metal
Poisoning on Five Liver Enzymes in the Killifish (Fundulus
heteroclitus) (Auth. communication used). J.Fish.Res.Board
Can. 27(2):383-390.

9700

ECOTOX provides one 96-h LC50 of 27,000
|jg/L for this study. Combined with the other
LC50s for Fundulus heteroclitus, the SMAV
would have been 22.034 |jg/L. This SMAV is
higher than the original and is not sensitive
relative to other species. Note, this test was
not used in the 2001 cadmium WQC doc

Janssen, H.H., and N. Scholz. 1979. Uptake and Cellular
Distribution of Cadmium in Mytilus edulis. Mar.Biol. 55(2):133-
142.

9836

UEndp, Eff, Con

Jenkins, K.D., and A.Z. Mason. 1988. Relationships Between
Subcellular Distributions of Cadmium and Perturbations in
Reproduction in the Polychaete Neanthes arenaceodentata.
Aquat.Toxicol. 12(3):229-244.

5037

UEndp, UChron, Con

Jenkins, K.D., and B.M. Sanders. 1985. Relationships
Between Free Cadmium Ion Activity in Sea Water and
Cadmium Metabolism, Growth and Reproduction in
Polychaetes. Aquat.Sci.Fish.Abstr.16(10):16007-1Q16 (1986)
/ Mar.Environ.Res. 17(2-4):200.

6478

UEndp, UChron, Con

Jenkins, K.D., and B.M. Sanders. 1986. Relationships
between Free Cadmium Ion Activity in Seawater, Cadmium
Accumulation and Subcellular Distribution, and Growth in
Polychaetes. Environ.Health Perspect. 65:205-210.

12940

UEndp, UChron

Jennings, J.R., and P.S. Rainbow. 1979. Studies on the
Uptake of Cadmium by the Crab Carcinus maenas in the
Laboratory. I. Accumulation From Seawater and a Food
Source. Mar.Biol. 50(2):131-139.

15534

UEndp, Eff, Dur, UChron

572

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Jonczyk, E„ K.G. Doe, P.C.Wells, and S.G. Yee. 1991.
Technical Evaluation of the Sea Urchin Fertilization Test:
Proceedings of a Workshop in Dartmouth, Nova Scotia. In:
P.Chapman, F.Bishay, E.Power, K.Hall, L.Harding, D.McLeay,
M.Nassichuk and W.Knapp (Eds.), Proc.17th Annual Aquatic
Toxicity Workshop, Nov.5-7, 1990, Vol.1, Vancouver, B.C.,
Can.Tech.Rep.Fish Aquat.Sci.No.1774 :323-330.

8788

Dur

Juchelka, C.M., and T.W. Snell. 1995. Rapid Toxicity
Assessment Using Ingestion Rate of Cladocerans and
Ciliates. Arch.Environ.Contam.Toxicol. 28(4):508-512.

14918

Eff, Dur

Kaland, T., T. Andersen, and K. Hylland. 1993. Accumulation
and Subcellular Distribution of Metals in the Marine Gastropod
Nassarius reticulatus L. In: R.Dallinger and P.S.Rainbow
(Eds.), Ecotoxicology of Metals in Invertebrates, Lewis Publ.
:37-53.

13829

UEndp, Eff, Dur

Karbe, L.. 1972. Marine Hydroids as Test Organisms for
Assessing the Toxicity of Water Pollutants. The Effect of
Heavy Metals on Colonies of Eirene viridula. Mar.Biol.
12(4):316-328 (GER) (ENG ABS).

15654

UEndp, Eff, UChron, Con

Karez, C.S., M. Romeo, and M. Gnassia-Barelli. 1988. Uptake
of Zn and Cd by Coastal Phytoplankton Species in Culture. In:
U.Seeliger, L.D.De Lacerda, and S.R.Patchineelam (Eds.)
Metals in Coastal Environments of Latin America, Springer-
Verlag New York, Inc., Secaucus, NJ :130-139.

13214

UEndp, Eff, Dur

Karez, C.S., S. Bonotto, and S. Puiseux-Dao. 1989. Response
of the Unicellular Giant Alga Acetabularia acetabulum to
Cadmium Toxicity and Accumulation. Toxicol.Environ.Chem.
19(3-4):223-232.

2101

UEndp, UChron, Con

Karlson, K.. 1994. An Investigation on the Sensitivity to Heavy
Metals of the Tiger Shrimp Penaeus monodon, a
Commercially Important Tropical Shrimp. Fish.Dev.Ser.,
Natl.Swed.Board Fish.No. 82:29.

16769

UEndp, Eff, Dur, UChron

573

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Karlsson-Norrgren, L., P. Runn, C. Haux, and L. Forlin. 1985.
Cadmium-Induced Changes in Gill Morphology of Zebrafish,
Brachydanio rerio (Hamilton-Buchanan), and Rainbow Trout,
Salmo gairdneri Richardson. J.Fish Biol. 27(1):81-95.

11497

UEndp, Eff, UChron

Kayser, H., and K.R. Sperling. 1980. Cadmium Effects and
Accumulation in Cultures of Prorocentrum micans (Dinophyta).
Helgol.Wiss.Meeresunters. 33(1/4):89-102.

9841

UEndp, Eff, UChron, Con

Kerfoot, W.B., and S.A. Jacobs. 1976. Cadmium Accrual in
Combined Wastewater Treatment-Aquaculture System.
Envi ron. Sci .Technol. 10(7) :662-667.

5265

UEndp, Eff, Dur

Khan, A., J. Barbieri, S. Khan, and F. Sweeney. 1992. A New
Short-Term Mysid Toxicity Test Using Sexual Maturity as an
Endpoint. Aquat.Toxicol. 23(2):97-105.

6179

UEndp, Dur

Kissa, E., M. Moraitou-Apostolopoulou, and V. Kiortsis. 1984.
Effects of Four Heavy Metals on Survival and Hatching Rate of
Artemia salina (L.). Arch.Hydrobiol. 102(2):255-264.

11259

Dur

Brine Shrimp

Klockner, K.. 1979. Uptake and Accumulation of Cadmium by
Ophryotrocha diadema (Polychaeta). Mar.Ecol.Prog.Ser. 1:71-
76.

14282

UEndp, Eff, UChron

Kluytmans, J.H., D.I. Zandee, and E.L. Enserink. 1988. Effects
of Cadmium on the Reproduction of Mytilus edulis L.
Aquat.Toxicol. 11 (3/4):427-428 (ABS).

13012

Eff, UChron, Con

Kobayashi, N.. 1971. Fertilized Sea Urchin Eggs As an
Indicatory Material for Marine Pollution Bioassay, Preliminary
Experiments. Mar.Biol.Lab 18(6):379-406.

2963

UEndp, Dur

Kobayashi, N.. 1990. Marine Pollution Bioassay by Sea Urchin
Eggs, an Attempt to Enhance Sensitivity. Publ.Seto
Mar.Biol.Lab. 34(4-6):225-237.

9717

UEndp, Dur

574

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Kohler, K., and H.U. Riisgard. 1982. Formation of
Metallothioneins in Relation to Accumulation of Cadmium in
the Common Mussel Mytilus edulis. Mar.Biol. 66(1):53-58.

10563

UEndp, Eff

Kohn, N.P., J.Q. Word, D.K. Niyogi, L.T. Ross, T. Dillon, and
D.W. Moore. 1994. Acute Toxicity of Ammonia to Four
Species of Marine Amphipod. Mar.Environ.Res. 38(1): 1 -15.

17293

UEndp, Nom, See note

ECOTOX provides one 96-h LC50 of 3121
|jg/L for Grandidierella japonica and two 96-
hr LC50s of 526.8 |jg/L and 1908 |jg/L for
Rhepoxynius abronius. Combined with the
other LC50s for the species, the SMAV would
have been 1905 |jg/L for Grandidierella
japonica and 1003 |jg/L for Rhepoxynius
abronius. This SMAVs are is not sensitive
relative to other species. Note, this test was
not used in the 2001 cadmium WQC doc

Kozuch, J., and J. Pempkowiak. 1996. Molecular Weight of
Humic Acids as a Major Property of the Substances
Influencing the Accumulation Rate of Cadmium by a Blue
Mussel (Mytilus edulis). Environ.Int. 22(5):585-589.

19499

UEndp, Eff, Dur, UChron

Krishnaja, A.P., M.S. Rege, and A.G. Joshi. 1987. Toxic
Effects of Certain Heavy Metals (Hg, Cd, Pb, As and Se) on
the Intertidal Crab Scylla serrata. Mar.Environ.Res. 21(2):109-
119.

12413

UEndp, Eff, Dur, Con

Kumarasamy, P., and A. Karthikeyan. 1999. Effect of
Cadmium on Oxygen Consumption and Filtration Rate at
Different Salinities in an Estuarine Clam Meretrix casta
(Chemnitz). J.Environ.Biol. 20(2):99-102.

20324

UEndp, Eff

Kuroshima, R., and S. Kimura. 1990. Changes in Toxicity of
Cd and Its Accumulation in Girella and Goby with Their
Growth. Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan Gakkaishi)
56(3):431-435.

221

NonRes

Kuroshima, R., S. Kimura, K. Date, and Y. Yamamoto. 1993.
Kinetic Analysis of Cadmium Toxicity to Red Sea Bream,
Pagrus major. Ecotoxicol.Environ.Saf. 25:300-314.

6751

NonRes

575

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Kuroshima, R.. 1987. Cadmium Accumulation and its Effect on
Calcium Metabolism in the Girella girella punctata during a
Long Term Exposure. Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan
Gakkaishi) 53(3):445-450.

5774

UEndp, Eff

Kuroshima, R.. 1992. Cadmium Accumulation in the
Mummichog, Fundulus heteroclitus, Adapted to Various
Salinities. Bull.Environ.Contam.Toxicol. 49(5):680-685.

5787

UEndp, Eff, Dur

Kuroshima, R.. 1992. Comparison of Cadmium Accumulation
in Tissues Between Carp Cyprinus carpio and Red Sea Bream
Pagrus major. Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan
Gakkaishi) 58(7): 1237-1242.

7830

UEndp, Eff

Langston, W.J., and M. Zhou. 1986. Evaluation of the
Significance of Metal-Binding Proteins in the Gastropod
Littorina littorea. Mar.Biol. 92(4):505-515.

12946

UEndp, Dur, Con

Langston, W.J., and M. Zhou. 1987. Cadmium Accumulation,
Distribution and Elimination in the Bivalve Macoma balthica:
Neither Metallothionein nor Metallothionein-Like.

Mar. Environ. Res. 21 (3):225-237.

8587

Eff, UChron

Larrain, A., A. Riveras, J. Silva, and E. Bay-Schmith. 1999.
Toxicity of Metals and Pesticides Using the Sperm Cell
Bioassay with the Sea Urchin Arbacia spatuligera.
Bull.Environ.Contam.Toxicol. 62(6):749-757.

20469

Dur

Larsson, A., B.E. Bengtsson, and C. Haux. 1981. Disturbed
Ion Balance in Flounder, Platichthys flesus L. Exposed to
Sublethal Levels of Cadmium. Aquat.Toxicol. 1 (1): 19-35.

3639

UEndp, Eff

Le Dean, L., and J. Devineau. 1985. In Search of
Standardisation: A Comparison of Toxicity Bioassays on Two
Marine Crustaceans (Paleomon serratus and Tigriopus
brevicornis). Rev.Trav.lnst.Peches Marit.Nantes 49(3/4):187-
198.

3291

UEndp, Dur, UChron

Has one 45d LC50 for common pink shrimp

576

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Leborans, G.F., and A. Novillo. 1996. Toxicity and
Bioaccumulation of Cadmium in Olisthodiscus luteus
(Raphidophyceae). Water Res. 30(1):57-62.

19913

UEndp, Eff

Lee, H.H., and C.H. Xu. 1984. Differential Response of Marine
Organisms to Certain Metal and Agrichemical Pollutants.
Bull.Environ.Contam.Toxicol. 33(4):460-467.

10612

UEndo, Dur

Lee, H.H., and C.H. Xu. 1984. Effects of Metals on Sea Urchin
Development: A Rapid Bioassay. Mar.Pollut.Bull. 15(1 ):18-21.

10086

UEndp, Dur

Lee, J.G., B.A. Ahner, and F.M.M. Morel. 1996. Export of
Cadmium and Phytochelatin by the Marine Diatom
Thalassiosira weissflogii. Environ.Sci.Technol. 30(6):1814-
1821.

5881

UEndp, Eff, Dur

LeMaire-Gony, S., and P. LeMaire. 1992. Interactive Effects of
Cadmium and Benzo(a)Pyrene on Cellular Structure and
Biotransformation Enzymes of the Liver of the European Eel
Anguilla anguilla. Aquat.Toxicol. 22(2): 145-160.

6148

UEndp, Eff, UChron

LeMaire-Gony, S., P. LeMaire, and A.L. Pulsford. 1995.
Effects of Cadmium and Benzo(a)pyrene on the Immune
System, Gill ATPase and EROD Activity of European Sea
Bass Dicentrarchus labrax. Aquat.Toxicol. 31(4):297-313.

14878

UEndp, Eff, Dur, UChron

Lemay, J.A., and D.J. Reish. 1987. The Transfer of Cadmium
from the Polychaete, Neanthes arenaceodentata, to the Arrow
Goby, Clevelandia ios. In: Malagrino,G.and H.Santoyo (Eds.),
Proc.of the 5th Symp.of Marine Biology, 24-26 October 1984,
La Paz, B.C.S., Mexico, Autonoma de Baja California Sur, La
Paz, B.C.S. :31-37.

4082

Eff, Dur, Uchron

Lin, W., M.A. Rice, and P.K. Chien. 1992. The Effects of
Copper, Cadmium and Zinc on Particle Filtration and Uptake
of Glycine in the Pacific Oyster Crassostrea gigas.

Com p. Biochem. Physiol .C 103(1): 181 -187.

6506

UEndp, Eff, Dur

577

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Lipina, I.G., S.M. Gnezdilova, and N.K. Khristoforova. 1987.
Cadmium Distribution in Gonads of the Sea Urchin
Strongylocentrotus intermedius. Mar.Ecol.Prog.Ser. 36(3):263-
266.

8593

UEndp, Eff, Dur, UChron, Con

Liu, P.C., and J.C. Chen. 1987. Effects of Heavy Metals on the
Hatching Rates of Brine Shrimp Artemia salina Cysts. J.World
Aquacult.Soc. 18(2):78-83.

4256

UEndp, Dur

Brine Shrimp

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Lucu, C., V. Obersnel, and 0. Jelisavcic. 1991. Transport and
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14601

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ECOTOX provides one 96-h LC50 of 198.8
|jg/L for Acartia clausi and two 96-hr LC50s
of 1641 |jg/L and 1071 |jg/L for Eurytemora
affinis. Combined with the other LC50s for
the species, the SMAV would have been
168.7 |jg/L for Acartia clausi and 636.5 |jg/L
for Eurytemora affinis. These SMAVs are not
sensitive relative to other species. Note, this
test was not used in the 2001 cadmium WQC
doc

578

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Lussier, S.M., W.S. Boothman, S. Poucher, D. Champlin, and
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51695

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MacDonald, J.M., J.D. Shields, and R.K. Zimmer-Faust. 1988.
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UEndp

Maclnnes, J.R., and F.P. Thurberg. 1973. Effects of Metals on
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15722

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Marcaillou-Le Baut, C.. 1988. Development of a Test with
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3520

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Marigomez, I., M.P. Ireland, and E. Angulo. 1990. Correlation
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3638

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579

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3504

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Marigomez, J.A., M.P. Cajaraville, and E. Angulo. 1990.
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Markham, J.W., B.P. Kremer, and K.R. Sperling. 1980.
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18954

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Mason, A.Z., and K.D. Jenkins. 1990. Effects of Feeding on
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Mazon, L.I., G. Gonzalez, A. Vicario, A. Estomba, and A.
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20054

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McClurg, T.P.. 1984. Effects of Fluoride, Cadmium and
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10090

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580

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Comment

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15399

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15632

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Mirkes, D.Z., W.B. Vernberg, and P.J. Decoursey. 1978.
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Mizrahi, L., and Y. Achituv. 1994. Effects of Cd, Hg and Zn on
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17414

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581

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8404

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17742

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582

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Rejection Code(s)

Comment

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52573

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18422

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19512

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Nasu, Y., and M. Kugimoto. 1981. Lemna (Duckweed) As an
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Negilski, D.S.. 1976. Acute Toxicity of Zinc, Cadmium and
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6225

NonRes

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Nielsen, G., and P. Bjerregaard. 1991. Interaction Between
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5044

UEndp, Eff, UChron

583

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Rejection Code(s)

Comment

Nimmo et al. . 1977b. Effects of Cadmium on the Shrimps,
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17458

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Has a 30d LC50 for northern pink shrimp

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8938

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ECOTOX
EcoRef #

Rejection Code(s)

Comment

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10098

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ECOTOX
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Rejection Code(s)

Comment

Papathanassiou, E.. 1983. Effects of Cadmium and Mercury
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8418

NonRes

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4073

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ECOTOX
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Rejection Code(s)

Comment

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7835

Dur, Con, See note

ECOTOX provides six well-defined 96-h
LC50s ranging from 85.48 |jg/L to 309.1 |jg/L
for this study. Combined with the other
LC50s for Nereis arenaceodentata, the
SMAV would have been 725.2 |jg/L. This
SMAV is significantly lower than the original
but is not sensitive relative to other species.
Three F,M 96-hr LC50s were greater than
values and were not used. Note, this test
was not used in the 2001 cadmium WQC doc

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19926

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Plants do not drive criteria, and therefore, are
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587

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ECOTOX
EcoRef #

Rejection Code(s)

Comment

Phelps, H.L.. 1979. Cadmium Sorption in Estuarine Mud-Type
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Pietilainen, K.. 1976. Synergistic and Antagonistic Effects of
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12548

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588

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ECOTOX
EcoRef #

Rejection Code(s)

Comment

Price, R.K.J., and R.F. Uglow. 1980. Cardiac and Ventilatory
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Pringle, B.H., et al.. 1968. Trace metal accumulation by
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Pruell, R.J., and F.R. Engelhardt. 1980. Liver Cadmium
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Rabsch, U., and M. Elbraechter. 1980. Cadmium and Zinc
Uptake, Growth, and Primary Production in Coscinodiscus
granii Cultures Containing Low Levels of Cells and Dissolved
Organic Carbon. Helgol.Wiss.Meeresunters. 33(1/4):79-88.

9881

UEndp

Rainbow, P.S., and S.L. White. 1989. Comparative Strategies
of Heavy Metal Accumulation by Crustaceans: Zinc, Copper
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18778

UEndp, Eff

Rainbow, P.S., I. Malik, and P. O'Brien. 1993.
Physicochemical and Physiological Effects on the Uptake of
Dissolved Zinc and Cadmium by the Amphipod Crustacean
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7010

UEndp, Eff

Rainbow, P.S.. 1985. Accumulation of Zn, Cu and Cd by
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9713

UEndp, Eff

Ralph, P.J., and M.D. Burchett. 1998. Photosynthetic
Response of Halophila ovalis to Heavy Metal Stress.
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19866

UEndp, Eff

589

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Raspor, B., J. Pavicic, and M. Branica. 1989. Cadmium-
Induced Proteins from Mytilus galloprovincialis - Polarographic
Characterization and Study of Their Interaction with Cadmium.
Mar.Chem. 28(1-3):199-214.

4041

UEndp, Eff, Con

Ray, S., D.W. McLeese, B.A. Waiwood, and D. Pezzack.
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9857

Eff, Dur, Con

Rebhun, S., and A. Ben Amotz. 1984. The Distribution of
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10169

UEndp, Eff

Reddy, P.S., and M. Fingerman. 1995. Effect of Cadmium
Chloride on Physiological Color Changes of the Fiddler Crab,
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15248

UEndp, Eff, Dur

Reddy, P.S., L.K. Nguyen, P. Obih, and M. Fingerman. 1997.
Effect of Cadmium Chloride on the Distal Retinal Pigment
Cells of the Fiddler Crab, Ilea pugilator.

Bull. Environ.Contam .Toxicol. 58(3):504-510.

18003

UEndp, Eff

Regoli, F., E. Orlando, M. Mauri, M. Nigra, and G.A. Cognetti.
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8705

UEndp, Eff, Dur

Reish, D.J., and R.S. Carr. 1978. The Effect of Heavy Metals
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8428

UEndp, UChron

590

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Reish, D.J., and T.V. Gerlinger. 1984. The Effects of
Cadmium, Lead, and Zinc on Survival and Reproduction in the
Polychaetous annelid Neanthes arenaceodentata
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Int.Polychaete Conf., Sydney, Aust., July 1983, The Linnean
Society of New South Wales, Australia :383-389.

4007

Con, UChron

Reish, D.J., C.E. Pesch, J.H. Gentile, G. Bellan, and D.
Bellan-Santini. 1978. Interlaboratory Calibration Experiments
Using the Polychaetous Annelid Capitella capitata.
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5934

Eff, UChron

Relexens, J.C.. 1989. Ecotoxicology in a Miniaturized
Sediment Environment (EMISEM) - Final Report. Effects of
Pollutants on the Physiology Respiratory of Meiofauna. Oecd-
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3516

UEndp, Eff

Riisgard, H.U., E. Bjornestad, and F. Mohlenberg. 1987.
Accumulation of Cadmium in the Mussel Mytilus edulis:
Kinetics and Importance of Uptake Via Food and Sea Water.
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12907

UEndp, Eff

Rijstenbil, J.W., A. Sandee, J. Van Drie, and J.A. Wijnholds.
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Detoxification in the Planktonic Diatoms Ditylum brightwellii
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14606

UEndp, Eff, Dur

Ringwood, A.H.. 1989. Accumulation of Cadmium by Larvae
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3268

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Ringwood, A.H.. 1992. Comparative Sensitivity of Gametes
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3886

Dur, Eff

591

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Ringwood, A.H.. 1992. Effects of Chronic Cadmium Exposures
on Growth of Larvae of an Hawaiian Bivalve, Isognomon
californicum. Mar.Ecol.Prog.Ser. 83(1):63-70.

7634

UEndp, Dur

Ringwood, A.H.. 1993. Age-Specific Differences in Cadmium
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4364

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Ritterhoff, J., and G.P. Zauke. 1997. Bioaccumulation of Trace
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18598

UEndp, Eff

Ritterhoff, J., G.P. Zauke, and R. Dallinger. 1996. Calibration
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17081

Eff, Dur, UChron

Roberts, M.H.J., J.E. Warinner, C.F. Tsai, D. Wright, and L.E.
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10443

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Roberts, R.O., and S.G. Berk. 1990. Development of a
Protozoan Chemoattraction Bioassay for Evaluating Toxicity of
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9812

Dur

only 24hr. Has 24hr LC50 for a ciliate

Roed, K.H.. 1979. The Effects of Interacting Salinity,
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8434

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Roed, K.H.. 1980. Effects of Salinity and Cadmium Interaction
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9887

Eff, Con

592

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Roesijadi, G., and P.L. Klerks. 1989. Kinetic Analysis of
Cadmium Binding to Metallothionein and Other Intracellular
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3514

UEndp, Dur

Roesijadi, G., K.M. Hansen, and M.E. linger. 1996. Cadmium-
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19745

UEndp, Eff

Roman, G., A. Rudolph, and R. Ahumada. 1994. Seasonal
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19344

NonRes

Rosenberg, R., and J.D. Costlow Jr.. 1976. Synergistic Effects
of Cadmium and Salinity Combined with Constant and Cycling
Temperatures on the Larval Development of Two Estuarine
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15637

UEndp, UChron

Sarasquete, M.C., M.L. Gonzales de Canales, and S. Gimeno.
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9518

UEndp, Eff

Sathya, K.S., and K.P. Balakrishnan. 1988. Physiology of
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12966

UEndp, Eff

Sauer, G.R.. 1987. The Effect of Cadmium and Zinc on
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4904

UEndp, Eff

593

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Schlekat, C.E., B.L. Mcgee, and E. Reinharz. 1992. Testing
Sediment Toxicity in Chesapeake Bay with the Amphipod
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3911

See note

ECOTOX provides one 96-h LC50 of 298.2
|jg/L for this study. Combined with the other
LC50s for Leptocheirus plumulosus, the
SMAV would have been 495.6 |jg/L. This
SMAV is not sensitive relative to other
species. A 96-hr LC50 for Hyalella azteca of
188.9 |jg/L, however, this species was not
used in the analysis. Note, this test was not
used in the 2001 cadmium WQC doc

Scholz, N.. 1980. Accumulation, Loss and Molecular
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9894

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Schroder, H.C., H.M.A. Hassanein, S. Lauenroth, C. Koziol,
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20048

UEndp, Eff

Scott-Fordsmand, J.J., and M.H. Depledge. 1993. The
Influence of Starvation and Copper Exposure on the
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13334

UEndp, UChron

Selvakumar, S., and T.M. Haridasan. 2000. Toxic Effects of
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54052

UEndp, UChron

Selvakumar, S., S.A. Khan, and A.K. Kumaraguru. 1996.
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Soluble Fractions of Diesel Oil to the Larvae of Some
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18580

NoOrg

ECOTOX provides one 96-h LC50 of 99.40
|jg/L for Nanosesarma sp. for this study. This
SMAV is not sensitive relative to other
species. Note, this test was not used in the
2001 cadmium WQC doc

Serra, R., E. Carpene, A.C. Marcantonio, and G. Isani. 1995.
Cadmium Accumulation and Cd-Binding Proteins in the
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111 (2): 165-174.

16028

UEndp, UChron

594

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Shazili, N.A.M.. 1995. Effects of Salinity and Pre-exposure on
Acute Cadmium Toxicity to Seabass, Lates calcarifer.
Bull.Environ.Contam.Toxicol. 54(1):22-28.

14994

NonRes

Shuster, C.N.Jr., and B.H. Pringle. 1969. Trace Metal
Accumulation by the American Eastern Oyster, Crassostrea
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19929

UEndp, UChron

Sick, L.V., and G.J. Baptist. 1979. Cadmium Incorporation by
the Marine Copepod Pseudodiaptomus coronatus.
Limnol.Oceanogr. 24(3):453-462.

15521

UEndp, Eff

Sick, L.V., and H.L. Windom. 1975. Effects of Environmental
Levels of Mercury and Cadmium on Rates of Metal Uptake
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59194

UEndp, Eff

Sidoumou, Z., M. Gnassia-Barelli, and M. Romeo. 1997.
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Bull. Environ.Contam .Toxicol. 58(2):318-325.

17918

UEndp, Eff

Simoes Goncalves, M.L.S., M.F.C. Vilhena, L.M.V. Machado,
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2275

Con

Skul'sky, I .A., I.V. Burovina, V.F. Vasilyeva, O.N. Lukyanova,
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898

UEndp, Eff

595

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Skwarzec, B., A. Kentzer-Baczewska, E. Styczynska-
Jurewicz, and E. Neugebauer. 1984. Influence of
Accumulation of Cadmium on the Content of Other
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10124

UEndp, Eff

Smith, M.A.. 1983. The Effect of Heavy Metals on the
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11036

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Snell, T.W., and G. Persoone. 1989. Acute Toxicity Bioassays
Using Rotifers. I. A Test for Brackish and Marine
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3827

Dur

24hr only

Snell, T.W., B.D. Moffat, C. Janssen, and G. Persoone. 1991.
Acute Toxicity Tests Using Rotifers. III. Effects of
Temperature, Strain, and Exposure Time on the Sensitivity of
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16539

Dur

24hr only

Sorgeloos, P., C. Remiche-Van der Wielen, and G. Persoone.
1978. The Use of Artemia nauplii for Toxicity Tests - A Critical
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5419

UEndp, Eff

Soria-Dengg, S., and D. Ochavillo. 1990. Comparative
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20706

UEndp, Dur

Stebbing, A.R.D.. 1976. The Effects of Low Metal Levels on a
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15641

UEndp, Con

Stroemgren, T.. 1980. The Effect of Lead, Cadmium, and
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9902

UEndp, Con

Stromgren, T.. 1980. The Effect of Lead, Cadmium, and
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19931

UEndp, Dur, UChron

596

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Stromgren, T.. 1982. Effect of Heavy Metals (Zn, Hg, Cu, Cd,
Pb, Ni) on the Length Growth of Mytilus edulis. Mar.Biol.
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10899

UEndp

Sullivan, J.K.. 1977. Effects of Salinity and Temperature on
the Acute Toxicity of Cadmium to the Estuarine Crab
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8453

NonRes

Sunda, W.G., D.W. Engel, and R.M. Thuotte. 1978. Effect of
Chemical Speciation on Toxicity of Cadmium to Grass Shrimp,
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8454

UEndp

Sunila, I., and R. Lindstrom. 1985. The Structure of the
Interfilamentar Junction of the Mussel (Mytilus edulis L.) Gill
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11224

UEndp, Eff, Con

24hr only

Sunila, I. 1981. Toxicity of Copper and Cadmium to Mytilus
edulis L. (Bivalvia) in Brackish Water. Ann.Zool.Fenn. 18:213-
223.

15791

Dur, UEndp, Eff

ECOTOX provides one 96-h EC50 of 497.0
|jg/L for this study. Combined with the other
LC50s for Mytilus edulis, the SMAV would
have been 827.0 |jg/L. This SMAV is not
sensitive relative to other species. Note, this
test was not used in the 2001 cadmium WQC
doc

Syasina, I.G., and O.N. Lukyanova. 1993. Ultrastructural and
Biochemical Changes in Gonads of the Scallop Mizuhopecten
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16479

UEndp, Eff

Tedengren, M., M. Arner, and N. Kautsky. 1988.
Ecophysiology and Stress Response of Marine and Brackish
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13130

UEndp, Eff

Temara, A., G. Ledent, M. Warnau, H. Paucot, M. Jangoux,
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20122

Field, Eff

597

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Temara, A., M. Warneau, P. Dubois, and W.J. Langston.
1997. Quantification of Metallothioneins in the Common
Asteroid Asterias rubens (Echinodermata) Exposed
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34.

18402

UEndp, Eff

Thaker, A.A., and A.A. Haritos. 1989. Cadmium
Bioaccumulation and Effects on Soluble Peptides, Proteins
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UEndp, Eff

Thebault, M.T., A. Biegniewska, J.P. Raffin, and E.F.
Skorkowski. 1996. Short Term Cadmium Intoxication of the
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Comp.Biochem.Physiol.C 113(3):345-348.

16857

NonRes

Theede, H., N. Scholz, and H. Fischer. 1979. Temperature
and Salinity Effects on the Acute Toxicity of Cadmium to
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8457

Eff, Con

Thomas, P., and H.W. Wofford. 1993. Effects of Cadmium and
Aroclor 1254 on Lipid Peroxidation, Glutathione Peroxidase
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8235

UEndp, UChron

Thomas, P., and J.M. Neff. 1985. Plasma Corticosteroid and
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Advances :63-82.

4974

UEndp

598

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Thompson, K.A., D.A. Brown, P.M. Chapman, and R.O.
Brinkhurst. 1982. Histopathological Effects and Cadmium-
Binding Protein Synthesis in the Marine Oligochaete
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15442

UEndp, Eff, Con

Thongra-ar, W., and 0. Matsuda. 1995. Effects of Cadmium
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Joint Seminar on Marine Science, Dec.2-3, 1993,
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18912

UEndp

Thurberg, F.P., A. Calabrese, E. Gould, R.A. Greig, M.A.
Dawson, and R.K. Tucker. 1977. Response of the Lobster,
Homarus americanus, to Sublethal Levels of Cadmium and
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8458

UEndp, Eff

Thurberg, F.P., M.A. Dawson, and R.S. Collier. 1973. Effects
of Copper and Cadmium on Osmoregulation and Oxygen
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8732

UEndp, Con

Tort, L., and M. Rosell. 1989. Variations of Organ-Body
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56.

3370

UEndp, Dur, UChron

Tort, L., P. Torres, and J. Hidalgo. 1984. Short-Term Cadmium
Effects on Gill Tissue Metabolism. Mar.Pollut.Bull. 15(12):448-
450.

10769

UEndp, Dur, UChron

Triebskorn, R., H.R. Kohler, T. Zahn, G. Vogt, M. Ludwig, S.
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Z.Angew.Zool. 73(3):277-287.

16869

UEndp, Eff

599

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Udoidiong, O.M., and P.M. Akpan. 1991. Toxicity of Cadmium,
Lead and Lindane to Egeria radiata Lamarck (Lamellibranchia,
Donacidae). Rev.Hydrobiol.Trop. 24(2):111-117.

8515

AF, NonRes

Varanasi, U., and D. Markey. 1978. Uptake and Release of
Lead and Cadmium in Skin and Mucus of Coho Salmon
(Oncorhynchus kisutch). Comp.Biochem.Physiol.60C:187-191
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Communication Used).

15121

Eff, Con

Varanasi, U.. 1978. Biological Fate of Metals in Fish. In:
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5209

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Vashchenko, M.A., V.B. Durkina, and S.M. Gnezdilova. 1988.
The Influence of the Diesel Fuel Hydrocarbons and Cadmium
on the Development of Sea Urchin Progeny. Ontogensis
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298

UEndp, UChron

Vega, M.M., J.A. Marigomez, and E. Angulo. 1989.

Quantitative Alterations in the Structure of the Digestive Cell of
Littorina littorea on Exposure to Cadmium. Mar.Biol.
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712

UEndp, Eff

Veldhuizen-Tsoerkan, M.B., C.A. Van der Mast, and D.A.
Holwerda. 1992. Cadmium-Induced Changes in
Macromolecular Synthesis at Transcriptional and Translational
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6735

UEndp, Eff

Vernberg, W.B., P.J. De Coursey, and J. O'Hara. 1974.
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20409

UEndp

600

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Vernberg, W.B., P.J. Decoursey, M. Kelly, and D.M. Johns.
1977. Effects of Sublethal Concentrations of Cadmium on
Adult Palaemonetes pugio Under Static and Flow-Through
Conditions. Bull.Environ.Contam.Toxicol. 17(1): 16-24.

8466

UEndp, Eff

Verriopoulos, G., and M. Moraitou-Apostolopoulou. 1981.
Effects of Some Environmental Factors on the Toxicity of
Cadmium to the Copepod Tisbe holothuriae. Arch.Hydrobiol.
91 (3):287-293.

15444

UEndp, Con

Verriopoulos, G., and M. Moraitou-Apostolopoulou. 1982.
Differentiation of the Sensitivity to Copper and Cadmium in
Different Life Stages of a Copepod. Mar.Pollut.Bull. 13(4): 123-
125.

11097

Con, Dur

Viarengo, A., L. Canesi, M. Pertica, G. Poli, M.N. Moore, and
M. Orunesu. 1990. Heavy Metal Effects on Lipid Peroxidation
in the Tissues of Mytilus galloprovincialis Lam.

Com p. Biochem .Physiol. C 97(1 ):37-42.

UEndp, Eff

Visviki, I., and J.W. Rachlin. 1991. The Toxic Action and
Interactions of Copper and Cadmium to the Marine Alga
Dunaliella minuta, in Both Acute and Chronic Exposure.
Arch.Environ.Contam.Toxicol. 20(2):271-275.

Plants do not drive criteria, and therefore, are
not included in CWA review and approval of
ORWQS

Vitale, A.M., J.M. Monserrat, P. Castilho, and E.M. Rodriguez.
1999. Inhibitory Effects of Cadmium on Carbonic Anhydrase
Activity and Ionic Regulation of the Estuarine Crab
Chasmagnathus granulata (Decapoda, Grapsidae).

Com p. Biochem. Physiol .C 122(1): 121 -129.

19662

NonRes

96hr LC50 Crab

Von Westernhagen, H., and V. Dethlefsen. 1975. Combined
Effects of Cadmium and Salinity on Development and Survival
of Flounder Eggs. J.Mar.Biol.Assoc.U.K. 55(4):945-957.

15698

UEndp, Con

601

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Von Westernhagen, H., and V. Dethlefsen. 1982. Effect of the
Surfactant Corexit 7664 on Uptake of Cadmium by Organisms
and Biological Matter in a Closed Circulated Brackish-Water
System. Helgol.Meeresunters. 35(1):1 -12.

11054

UEndp, Eff, Con

Von Westernhagen, H., V. Dethlefsen, and H. Rosenthal.
1975. Combined Effects of Cadmium and Salinity on
Development and Survival of Garpike Eggs.
Helgol.Wiss.Meeresunters. 27(3):268-282.

15699

Eff, UChron

Von Westernhagen, H., V. Dethlefsen, and H. Rosenthal.
1980. Correlation Between Cadmium Concentration in the
Water and Tissue Residue Levels in Dab, Limanda limanda L.,
and Plaice, Pleuronectes platessa L. J.Mar.Biol.Assoc.U.K.
60(1):45-58.

9923

UEndp

Voogt, P.A., P.J. Den Besten, G.C.M. Kusters, and M.W.J.
Messing. 1987. Effects of Cadmium and Zinc on Steroid
Metabolism and Steroid Level in the Sea Star Asterias rubens
L. Comp.Biochem.Physiol.C 86(1):83-89.

12392

UEndp, Eff

Voyer, R.A., and D.G. McGovern. 1991. Influence of Constant
and Fluctuating Salinity on Responses of Mysidopsis bahia
Exposed to Cadmium in a Life-Cycle Test. Aquat.Toxicol.
19(3):215-230.

3612

UEndp

ECOTOX provides three 28-d CVs of 4.445
|jg/L for this study. Combined with the other
CVs for Americamysis bahia, the SMCV
would have been 5.661 |jg/L. This SMAV is
sensitive relative to other species and the
criteria, however Americamysis bahia was
already listed as sensitive. Note, this test was
not used in the 2001 cadmium WQC doc

Voyer, R.A., and G. Modica. 1990. Influence of Salinity and
Temperature on Acute Toxicity of Cadmium to Mysidopsis
bahia Molenock. Arch.Environ.Contam.Toxicol. 19(1): 124-131.

3008

Nom

ECOTOX provides twelve F,U and S,M 96-h
LC50s ranging from 11.03 |jg/L to 84.49 |jg/L
for this study. However, F,M tests exist for
Americamysis bahia, so these values would
not have been used. Note, this test was not
used in the 2001 cadmium WQC doc

Voyer, R.A., C.E. Wentworth Jr., E.P. Barry, and R.J.
Hennekey. 1977. Viability of Embryos of the Winter Flounder
Pseudopleuronectes americanus Exposed to Combinations of
Cadmium and Salinity at Selected Temperatures. Mar.Biol.
44(2): 117-124.

8468

602

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Voyer, R.A., J.A. Cardin, J.F. Heltshe, and G.L. Hoffman.
1982. Viability of Embryos of the Winter Flounder
Pseudopleuronectes americanus Exposed to Mixtures of
Cadmium and Silver in Combination with Selected Fixe.
Aquat.Toxicol. 2(4):223-233.

10500

UEndp, Dur

Voyer, R.A., J.F. Heltsche, and R.A. Kraus. 1979. Hatching
Success and Larval Mortality in an Estuarine Teleost, Menidia
menidia (Linnaeus), Exposed to Cadmium in Constant and
Fluctuating Salinity Re. Bull.Environ.Contam.Toxicol. 23(4-
5):475-481.

8467

Dur

Voyer, R.A.. 1975. Effect of Dissolved Oxygen Concentration
on the Acute Toxicity of Cadmium to the Mummichog,
Fundulus heteroclitus (L.), at Various Salinities.

Trans.Am. Fish.Soc. 104(1): 129-134.

6172

Nom

ECOTOX provides fourteen S,U 96-h LC50s
ranging from 28826 |jg/L to 113316 |jg/L for
this study. However, F,M tests exist for
Fundulus heteroclitus, so these values would
not have been used. Note, this test was not
used in the 2001 cadmium WQC doc

Vranken, G., R. Vandergaeghen, and C. Heip. 1991. Effects of
Pollutants on Life-History Parameters of the Marine Nematode
Monhystera disjuncta. ICES J Mar Sci 48:325-334.

7215

Con

Wang, J., M. Zhang, J. Xu, and Y. Wang. 1995. Reciprocal
Effect of Cu, Cd, Zn on a Kind of Marine Alga. Water Res.
29(1):209-214.

13720

UEndp

Ward, S.H. 1989. The Requirements for a Balanced Medium
in Toxicological Experiments Using Mysidopsis bahia with
Special Reference to Calcium Carbonate. In: U.M.Cowgill and
L.R.Williams (Eds.), Aquatic Toxicology and Hazard
Assessment, ASTM STP 1027, Philadelphia, PA 12:402-412.

13866

ECOTOX provides twelve R,U 96-h LC50s
ranging from 17.82 |jg/L to 33.60 |jg/L for this
study. However, F,M tests exist for
Americamysis bahia, so these values would
not have been used. Note, this test was not
used in the 2001 cadmium WQC doc

Warnau, M., J.L. Teyssie, and S.W. Fowler. 1995. Effect of
Feeding on Cadmium Bioaccumulation in the Echinoid
Paracentrotus lividus (Echinodermata). Mar.Ecol.Prog.Ser.
126(1-3):305-309.

18918

Eff

603

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Warnau, M., M. laccarino, A. De Biase, A. Temara, M.
Jangoux, P. Dubois, and G. Pagano. 1996. Spermiotoxicity
and Embryotoxicity of Heavy Metals in the Echinoid
Paracentrotus lividus. Environ.Toxicol.Chem. 15(11): 1931 -
1936.

17368

Dur

Waterman, A.J.. 1937. Effect of Salts of Heavy Metals on
Development of the Sea Urchin, Arbacia punctulata. Biol.Bull.
73(3):401-420.

17763

UEndp,Dur

Watling, H.R., and R.J. Watling. 1983. Sandy Beach Molluscs
As Possible Bioindicators of Metal Pollution 2. Laboratory
Studies. Bull.Environ.Contam.Toxicol. 31(3):339-343.

10862

UEndp, Eff

Watling, H.R.. 1978. Effect of Cadmium on Larvae and Spat of
the Oyster Crassostrea gigas (Thunberg). Trans.R.Soc.S.Afr.
43(2): 125-134.

10081

UEndp

Watling, H.R.. 1983. Accumulation of Seven Metals by
Crassostrea gigas, Crassostrea margaritacea, Perna perna,
and Choromytilus meridionalis. Bull.Environ.Contam.Toxicol.
30(3):317-322.

7374

UEndp, Eff

Watling, H.R.. 1983. Comparative Study of the Effects of
Metals on the Settlement of Crassostrea gigas.
Bull.Environ.Contam.Toxicol. 31(3):344-351.

11098

UEndp, Con

Weis, J.S., P. Weis, and J.L. Ricci. 1981. Effects of Cadmium,
Zinc, Salinity, and Temperature on the Teratogenicity of
Methylmercury to the Killifish (Fundulus heteroclitus).
Rapp.P.V.Reun.Comm.Int.Explor.Sci.Mer Mediterr. 178:64-70.

11419

UEndp

Weis, J.S.. 1976. Effects of Mercury, Cadmium, and Lead
Salts on Regeneration and Ecdysis in the Fiddler Crab, Uca
pugilator. Fish.Bull. 74(2):464-467.

8044

UEndp, UChron

604

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Weis, J.S.. 1980. Effect of Zinc on Regeneration in the Fiddler
Crab Ilea pugilator and its Interactions with Methyl-Mercury
and Cadmium. Mar.Environ.Res. 3(4):249-255.

9921

UEndp, Con

Weis, J.S.. 1985. Cadmium Acclimation and Limb
Regeneration in the Fiddler Crab, Ilea pugilator: Sex
Differences. Mar.Environ.Res. 16:199-214.

11417

UEndp

Weis, P., and J.S. Weis. 1978. Methylmercury Inhibition of Fin
Regeneration in Fishes and its Interaction with Salinity and
Cadmium. Estuar.Coast.Mar.Sci. 6(3):327-334.

7211

UEndp, Con

Weis, P., and J.S. Weis. 1986. Cadmium Acclimation and
Hormesis in Fundulus heteroclitus During Fin Regeneration.
Environ.Res. 39:356-363.

11420

UEndp, UChron

Westernhagen, H.V., V. Dethlefsen, H. Rosenthal, G.
Furstenberg, and J. Klinckmann. 1978. Fate and Effects of
Cadmium in an Experimental Marine Ecosystem.
Helgol.Wiss.Meeresunters. 31:471-484.

17305

UEndp, Eff

White, S.L., and P.S. Rainbow. 1982. Regulation and
Accumulation of Copper, Zinc and Cadmium by the Shrimp
Palaemon elegans. Mar.Ecol.Prog.Ser. 8(1 ):95-101.

9120

UEndp, UChron

White, S.L., and P.S. Rainbow. 1986. Accumulation of
Cadmium by Palaemon elegans (Crustacea: Decapoda).
Mar.Ecol.Prog.Ser. 32(1 ):17-25.

12244

UEndp, UChron

Wikfors, G.H., and R. Ukeles. 1982. Growth and Adaptation
Estuarine Unicellular Algae in Media with Excess Copper,
Cadmium or Zinc, and Effects of Metal-Contaminated Algal
Food on. Mar.Ecol.Prog.Ser. 7:191-206.

15508

UEndp, Con

605

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Wilkowska, 1., J. Kozuch, and J. Pempkowiak. 1994. The
Influence of Selected Abiotic Factors (Salinity, Temperature)
on the Accumulation of Cadmium from Sea Water by Blue
Mussel Mytilus edulis. Bull.Sea Fish.Inst.Gdynia
(Biul.Morsk.lnst.Ryback Gdynia) 131:61-65.

17103

UEndp, Eff

Wo, K.T., P.K.S. Lam, and R.S.S. Wu. 1999. A Comparison of
Growth Biomarkers for Assessing Sublethal Effects of
Cadmium on a Marine Gastropod, Nassarius festivus.
Mar.Pollut.Bull. 39(1-12):165-173.

20624

NonRes

Wood, A.M.. 1983. Available Copper Ligands and the
Apparent Bioavailability of Copper to Natural Phytoplankton
Assemblages. Sci.Total Environ. 28:51-64.

11038

Eff, Dur

Wright, D.A.. 1977. The Effect of Salinity on Cadmium Uptake
by the Tissues of the Shore Crab Carcinus maenas.
J.Exp.Biol. 67:137-146.

4146

Eff, UChron

Yang, M.S., and J.A.J. Thompson. 1996. Binding of
Endogenous Copper and Zinc to Cadmium-Induced Metal-
Binding Proteins in Various Tissues of Perna viridis.
Arch.Environ.Contam.Toxicol. 30(2):267-273.

16427

UEndp, Eff

Yih, W„ J.S. Yang, S.G. Jo, and E.Y. Chung. 1994. Effects of
Suspended Solid and Cadmium on the Shallow-Sea Foodweb
Ecosystem. 1. Reduction of Growth Rate and Biomass Yield of
Coastal Diatom Clones. Bull.Korean Fish.Soc.(Han'Guk Susan
Halchoiji) 27(4):373-379.

19358

Dur

Plants do not drive criteria, and therefore, are
not included in CWA review and approval of
ORWQS

Zanders, I.P., andW.E. Rojas. 1992. Cadmium Accumulation,
LC50 and Oxygen Consumption in the Tropical Marine
Amphipod Elasmopus rapax. Mar.Biol. 113(3):409-413.

6416

Con

606

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Zanders, I.P. and W.E. Rojas. 1996. Salinity Effects on
Cadmium Accumulation in Various Tissues of the Tropical
Fiddler Crab Ilea rapax. Environ.Pollut. 94(3):293-299.

18382

UEndp, Eff

ECOTOX provides one 96-h EC50 of 377.7
|jg/L for this study. This SMAV is not
sensitive relative to other species. Note, this
test was not used in the 2001 cadmium WQC
doc

Zaroogian, G.E., and S. Cheer. 1976. Accumulation of
Cadmium by the American Oyster, Crassostrea virginica.
Nature 261 (5559):408-410.

15703

UEndp, Eff

Zaroogian, G.E.. 1979. Studies on the Depuration of Cadmium
and Copper by the American Oyster Crassostrea virginica.
Bull.Environ.Contam.Toxicol. 23(1/2):117-122.

15552

UEndp, Eff

Zaroogian, G.E.. 1980. Crassostrea virginica as an Indicator of
Cadmium Pollution. Mar.Biol. 58(4):275-284.

9926

UEndp, Eff

Zauke, G.P., R. Von Lemm, H.G. Meurs, and W. Butte. 1995.
Validation of Estuarine Gammarid Collectives (Amphipoda:
Crustacea) as Biomonitors for Cadmium in Semi-Controlled
Toxicokinetic Flow-Through Experiments. Environ.Pollut.
90(2):209-219.

16960

Eff, Dur

7425

24hr only; No information about the paper,
just the reference number

Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

For the studies that were not utilized, but the most representative SMAV/2 or most representative SMCV fell below the
criterion, or, if the studies were for a species associated with one of the four most sensitive genera used to calculate the

FAV in the most recent national ambient water quality criteria dataset used to derive the CMC , EPA is providing a
transparent rationale as to why they were not utilized (see below).

92 U.S. EPA. 2001. 2001 Update of Ambient Water Quality Criteria for Cadmium. EPA-822-R-01-001.

607

-------
For the studies that were not utilized because they were not found to be pertinent to this determination (including
failing the QA/QC procedures listed in Appendix A) upon initial review of the download from ECOTOX, EPA is
providing the code that identifies why EPA determined that the results of the study were not reliable.

General QA/QC failure because non-resident species in Oregon

Tests with the following species were used in the EPA BE of OR WQS for cadmium in saltwater, but were not considered in the CWA
review and approval/disapproval action of the standards because these species do not have a breeding wild population in Oregon's
waters:

Nassarius

festivus

Snail

Woetal. 1999

Nucella

lapillus

Dog whelk,
Atlantic dogwinkle

Leung and Furness 1999

Americamysis

bahia

Opossum shrimp

Nimmo et al. 1977; Gentile et al. 1982;
Lussier et al. 1985; Voyer and Modica
1990; De Lisle and Roberts 1998

Americamysis

bigelowi

Shrimp

Gentile et al. 1982

608

-------
Appendix P Copper (Saltwater)
Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Aagaard, A., and M.H. Depledge. 1993. Inter-Individual
Variability in the Responses of Carcinus maenas to Copper
Exposure. In: J.C.AIdrich (Ed.), Proc.27th
Eur.Ma.Biol.Symp., Quantified Phenotypic Responses in
Morphology and Physiology, Sept.7-11, 1992, Dublin,
Ireland :275-280.

17945

UEndp

Abalde, J., A. Cid, S. Reiriz, E. Torres, and C. Herrero.
1995. Response of the Marine Microalga Dunaliella
tertiolecta (Chlorophyceae) to Copper Toxicity in Short
Time Experiments. Bull.Environ.Contam.Toxicol. 54(2):317-
324.

45175

UEndp

Abbasi, A.R., and S.E. Shackley. 1995. The Effect of
Copper on Developing Eggs of Herring, Clupea harengus
L. Sindh Univ.Res.J.Sci. 27(1):35-44.

18239

Dur, UChron

Abbasi, A.R., S.E. Shackley, and P.E. King. 1995. Effects
of Copper on the Ultrastructure of Muscle Cells of Herring,
Clupea harengus L. Pak.J.Zool. 27(1):83-87.

17605

UEndp

Abel, P.D.. 1976. Effects of Some Pollutants on the
Filtration Rate of Mytilus. Mar.Pollut.Bull. 7:228-231.

415

Con

Absil, M.C.P., J.J. Kroon, and H.T. Wolterbeek. 1994.
Availability of Copper from Phytoplankton and Water for the
Bivalve Macoma balthica. I. Separation of Uptake
Pathways Using the Radiotracer 64Cu. Mar.Biol.
118(1 ):123-127.

16336

UEndp

Absil, M.C.P., L.J.A. Gerringa, and B.T. Wolterbeek. 1993.
The Relation Between Salinity and Copper Complexing
Capacity of Natural Estuarine Waters and the Uptake of
Dissolved 64Cu by Macoma balthica. Chem.Spec.Bioavail.
5(4):119-128.

20704

UEndp

Absil, M.C.P., M. Berntssen, and L.J.A. Gerringa. 1996.
The Influence of Sediment, Food and Organic Ligands on
the Uptake of Copper by Sediment-Dwelling Bivalves.
Aquat.Toxicol. 34(1 ):13-29.

16133

Field, UEndp

609

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Adema, S.I. Deswaaf-Mooy, and P. Bais. 1972.
Laboratoriumonderzoek Over De Invloed Van Koper Op
Mosselen (Mytilus edilus). (Laboratory Investigations
Concerning the Influence of Copper on. Tno Nieuws
27(9):482-487.

8213

UEndp

Ahsanullah, M., and A.R. Williams. 1991. Sublethal Effects
and Bioaccumulation of Cadmium, Chromium, Copper, and
Zinc in the Marine Amphipod Allorchestes compressa.
Mar.Biol. 108:59-65.

331

Eff

Ahsanullah, M., and G.H. Arnott. 1978. Acute Toxicity of
Copper, Cadmium, and Zinc to Larvae of the Crab
Paragrapsus quadridentatus (H. Milne Edwards), and
Implications for Water. Aust.J.Mar.Freshwater Res. 29(1 ):1 -
8.

8296

NonRes

Ahsanullah, M., and T.M. Florence. 1984. Toxicity of
Copper to the Marine Amphipod Allorchestes compressa in
the Presence of Water-and Lipid-Soluble Ligands. Mar.Biol.
84(1):41-45.

10736

Con

Ahsanullah, M., and W. Ying. 1995. Toxic Effects of
Dissolved Copper on Penaeus merguiensis and Penaeus
monodon. Bull.Environ.Contam.Toxicol. 55(1):81-88.

14951

NonRes

Ahsanullah, M., D.S. Negilski, and M.C. Mobley. 1981.
Toxicity of Zinc, Cadmium and Copper to the Shrimp
Callianassa australiensis. I. Effects of Individual Metals.
Mar.Biol. 64(3):299-304(Author Communication Used).

15338

NonRes

Ahsanullah, M., D.S. Negilski, and M.C. Mobley. 1981.
Toxicity of Zinc, Cadmium and Copper to the Shrimp
Callianassa australiensis. III. Accumulation of Metals.
Mar.Biol.64(3):311-316 (Used Ref 15338) (Author
Communication Used).

15339

Eff, Dur

Ahsanullah, M., M.C. Mobley, and P. Rankin. 1988.
Individual and Combined Effects of Zinc, Cadmium and
Copper on the Marine Amphipod Allorchestes compressa.
Aust.J.Mar.Freshwater Res. 39(1):33-37.

13187

NonRes

Akberali, H.B., and J.E. Black. 1980. Behavioural
Responses of the Bivalve Scrobicularia plana (Dacosta)
Subjected to Short-Term Copper (Cu II) Concentrations.
Mar.Environ.Res. 4(2):97-107.

6095

NonRes

610

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Amiard-Triquet, C., J.C. Amiard, R. Ferrand, A.C.
Andersen, and M.P. Dubois. 1986. Disturbance of a Met-
Enkephalin-Like Hormone in the Hepatopancreas of Crabs
Contaminated by Metals. Ecotoxicol.Environ.Saf.
11 (2): 198-209.

12111

UEndp

Anderson, B.S., J.W. Hunt, H.R. McNulty, S.L. Turpen, and
M. Martin. 1994. Off-Season Spawning and Factors
Influencing Toxicity Test Development with Topsmelt
Atherinops affinis. Environ.Toxicol.Chem. 13(3):479-485.

4223

Con

Anderson, B.S., J.W. Hunt, W.J. Piekarski, B.M. Phillips,
M.A. Englund, R.S. Tjeerdema, and J.D. Goetzl. 1995.
Influence of Salinity on Copper and Azide Toxicity to Larval
Topsmelt Atherinops affinis (Ayres).
Arch.Environ.Contam.Toxicol. 29(3):366-372.

16025

UEndp, Uchron,
Dur

4 Lines of data have
LC50's (mort), 7 day
DUR

Anderson, D.M., and F.M.M. Morel. 1978. Copper
Sensitivity of Gonyaulax tamarensis. Limnol.Oceanogr.
23(2):283-295.

2848

UEndp, Eff, Con

Andersson, S., and L. Kautsky. 1996. Copper Effects On
Reproductive Stages Of Baltic Sea Fucus vesiculosus.
Mar.Biol. 125(1): 171-176.

19684

UEndp

16831

Dur

Arnott, G.H., and M. Ahsanullah. 1979. Acute Toxicity of
Copper, Cadmium and Zinc to Three Species of Marine
Copepod. Aust.J.Mar.Freshwater Res. 30(1):63-71.

5563

Dur

Arumugam, M., and M.H. Ravindranath. 1987. Copper
Toxicity in the Crab, Scylla serrata, Copper Levels in
Tissues and Regulation After Exposure to a Copper-Rich
Medium. Bull.Environ.Contam.Toxicol. 39:708-715.

727

UEndp, Con

Bailey, H.C., J.L. Miller, M.J. Miller, and B.S. Dhaliwal.
1995. Application of Toxicity Identification Procedures to
the Echinoderm Fertilization Assay to Identify Toxicity in a
Municipal Effluent. Environ.Toxicol.Chem. 14(12):2181 -
2186.

16375

Dur

611

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Baker, J.T.P.. 1969. Histological and Electron
Microscopical Observations on Copper Poisoning in the
Winter Flounder (Pseudopleuronectes americanus).
J.Fish.Res.Board Can. 26(11):2785-2793.

15553

UEndp

Ballan-Dufrancais, C., C. Marcaillou, and C. Amiard-
Triquet. 1991. Response of the Phytoplanktonic Alga
Tetraselmis suecica to Copper and Silver Exposure:
Vesicular Metal Bioaccumulation and Lack of Starch
Bodies. Biol.Cell 72(1/2):103-112.

7698

UEndp, Eff

Bambang, Y., P. Thuet, M. Charmantier-Daures, J.P.
Trilles, and G. Charmantier. 1995. Effect of Copper on
Survival and Osmoregulation of Various Developmental
Stages of the Shrimp Penaeus japonicus Bate (Crustacea,
Decapoda). Aquat.Toxicol. 33(2):125-139.

16111

NonRes

Bat, L.. 1997. Studies on the Uptake of Copper, Zinc and
Cadmium by the Amphipod Corophium volutator (Pallas) in
the Laboratory. Turk.J.Mar.Sci. 3(2):93-109.

19858

UEndp

Bay, S.M., P.S. Oshida, and K.D. Jenkins. 1983. A Simple
New Bioassay Based on Echinochrome Synthesis by
Larval Sea Urchins. Mar.Environ.Res. 8(1):29-39.

7919

UEndp

Beaumont, A.R., and J.E. Toro. 1996. Allozyme Genetics of
Mytilus edulis Subjected to Copper and Nutritive Stress.
J.Mar.Biol.Assoc.U.K. 76:1061 -1071.

18712

UEndp

Beaumont, A.R., G. Tserpes, and M.D. Budd. 1987. Some
Effects of Copper on the Veliger Larvae of the Mussel
Mytilus edulis and the Scallop Pecten maximus (Mollusca,
Bivalvia). Mar.Environ.Res. 21(4):299-309.

7975

Dur, Con

Bechmann . 1994. . .

NonRes

Bennett, R.O., and J.K. Dooley. 1982. Copper Uptake by
Two Sympatric Species of Killifish Fundulus heteroclitus
(L.)and F. majalis (Walbaum). J.Fish Biol. 21(4):381-398.

10491

UEndp, Eff

612

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Berail, G., P. Prudent, C. Massiani, and M. Pellegrini. 1992.
Isolation of Heavy Metal-Binding Proteins from a Brown
Seaweed Cystoseira barbata f. repens Cultivated in Copper
or Cadmium Enriched Seawater. In: E.Merian and
W.Haerdi (Eds.), Metal Compounds in Environment and
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2351

UEndp, Eff

Betzer, S.B., and M.E.Q. Pilson. 1975. Copper Uptake and
Excretion by Busycon canaliculatum L. Biol.Bull. 148(1): 1 -
15.

722

Con, Eff

Betzer, S.B., and P.P. Yevich. 1975. Copper Toxicity in
Busycon canaliculatum L. Biol.Bull. 148:16-25.

721

Con, UEndp, Eff

Bisbal, G.. 1987. Does Copper Affect the Mating Behavior
of Gammarus annulatus Smith, 1873 (Amphipoda:
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2417

UEndp, Con

Bjerregaard, P., and T. Vislie. 1986. Effect of Copper on
lon-and Osmoregulation in the Shore Crab Carcinus
maenas. Mar.Biol. 91(1):69-76.

11800

LT, Eff

Blasco, J., and J. Puppo. 1999. Effect of Heavy Metals (Cu,
Cd and Pb) on Aspartate and Alanine Aminotransferase in
Ruditapes phillippinarum (Mollusca: Bivalvia).

Com p. Biochem. Physiol .C 122(2):253-263.

20072

UEndp

Blust, R., L. Van Ginneken, and W. Decleir. 1994. Effect of
Temperature on the Uptake of Copper by the Brine Shrimp,
Artemia fraciscana. Aquat.Toxicol. 30(4):343-356.

17602

UEndp

Brine Shrimp

Bodammer, J.E.. 1985. Corneal Damage in Larvae of
Striped Bass Morone saxatilis Exposed to Copper.
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2479

UEndp, Con

Bodammer, J.E.. 1987. A Preliminary Study on the
Corneas of American San d Lance Larvae Exposed to
Copper. In: W.A.Vernberg, A.Calabrese, F.P.Thurberg, and
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4906

UEndp

Boitel, F., and J.P. Truchot. 1989. Effects of Sublethal and
Lethal Copper Levels on Hemolymph Acid-Base Balance
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715

UEndp, Eff

613

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Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Botton, M.L., K. Johnson, and L. Helleby. 1998. Effects of
Copper and Zinc on Embryos and Larvae of the Horseshoe
Crab, Limulus polyphemus. Arch.Environ.Contam.Toxicol.
35(1):25-32.

19307

Dur

ECOTOX provides
six 96-h LC50s of
1660-709650 (jg/L
for this study. These
values could have
been considered for
EPA's evaluation of
saltwater cadmium,
but the species is
relatively insensitive
to copper compared
to others.

Bougis, P., M.C. Corre, and M. Etienne. 1979. Sea-Urchin
Larvae As a Tool for Assessment of the Quality of Sea
Water. Ann.Inst.Oceanogr. 55(1):21-25.

5564

Con, NonRes

Brand, L.E., W.G. Sunda, and R.R.L. Guillard. 1986.
Reduction of Marine Phytoplankton Reproduction Rates by
Copper and Cadmium. J.Exp.Mar.BioI.Ecol. 96(3):225-250.

12014

UEndp

Bresler, V., and V. Yanko. 1995. Acute Toxicity of Heavy
Metals for Benthic Epiphytic Foraminifera Pararotalia
spinigera (Le Calvez) and Influence of Seaweed-Derived
DOC. Environ.Toxicol.Chem. 14(10):1687-1695.

15933

Dur

only 24 hrs

Brown, B., and M. Ahsanullah. 1971. Effect of Heavy
Metals on Mortality and Growth. Mar.Pollut.Bull. 2:182-187.

2467

LT, Con

Brown, C.L., and S.N. Luoma. 1995. Use of the Euryhaline
Bivalve Potamocorbula amurensis as a Biosentinel Species
to Assess Trace Metal Contamination in San Francisco
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18036

Eff

Browne, R.A.. 1980. Acute Response Versus Reproductive
Performance in Five Strains of Brine Shrimp Exposed to
Copper Sulphate. Mar.Environ.Res. 3(3):185-193.

5304

Con, LT

Brine Shrimp

Burdin, K.S., and K.T. Bird. 1994. Heavy Metal
Accumulation by Carrageenan and Agar Producing Algae.
Bot.Mar. 37:467-470.

45156

UEndp

614

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Burgess, R.M., B.A. Rogers, S.A. Rego, J.M. Corbin, and
G.E. Morrison. 1994. Sand Spiked with Copper as a
Reference Toxicant Material for Sediment Toxicity Testing:
A Preliminary Evaluation. Arch.Environ.Contam.Toxicol.
26(2): 163-168.

13674

UEndp

Burton, D.T., and D.J. Fisher. 1990. Acute Toxicity of
Cadmium, Copper, Zinc, Ammonia, 3,3'-Dichlorobenzidine,
2,6-Dichloro-4-nitroaniline, Methylene Chloride, and 2,4,6-
Trichlorophenol. Bull.Environ.Contam.Toxicol. 44(5):776-
783.

3163

Con, Dur

Calabrese et al. 1984.

UEndp

Bioaccumulation

Calabrese, A., J.R. Maclnnes, D.A. Nelson, and J.E. Miller.
1977. Survival and Growth of Bivalve Larvae Under Heavy-
Metal Stress. Mar.Biol. 41:179-184.

9064

Con

Calabrese, A., J.R. Maclnnes, D.A. Nelson, R.A. Greig, and
P.P. Yevich. 1984. Effects of Long-Term Exposure to Silver
or Copper on Growth, Bioaccumulation and Histopathology
in the Blue Mussel Mytilus edulis. Mar.Environ.Res.
11 (4):253-274.

10774

UEndp

Calabrese, A., R.S. Collier, D.A. Nelson, and J.R. Mac
Innes. 1973. The Toxicity of Heavy Metals to Embryos of
the American Oyster Crassostrea virginica. Mar.Biol.
18(3): 162-166.

2165

Con, Dur

Canesi, L., A. Viarengo, C. Leonzio, M. Filippelli, and G.
Gallo. 1999. Heavy Metals and Glutathione Metabolism in
Mussel Tissues. Aquat.Toxicol. 46(1):67-76.

20096

UEndp

Canli, M., and R.W. Furness. 1993. Toxicity of Heavy
Metals Dissolved in Sea Water and Influences of Sex and
Size on Metal Accumulation and Tissue Distribution in the
Norway Lobster. Mar.Environ.Res. 36(4):217-236.

4563

UEndp, Eff

Canterford, G.S., A.S. Buchanan, and S.C. Ducker. 1978.
Accumulation of Heavy Metals by the Marine Diatom
Ditylum brightwellii (West) Grunow. Aust.J.Mar.Freshwater
Res. 29(5):613-622.

15455

UEndp

Carmel, C.L.M., P.N.K. Nambisan, and R. Damodaran.
1983. Effect of Copper on Juvenile Penaeus indicus H.
Milne Edwards. Indian J.Mar.Sci. 12(2):128-130.

13964

NonRes

615

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Carter, R.J., and R.S. Eriksen. 1992. Investigation into the
Use of Zostera muelleri (Irmisch ex Aschers) as a Sentinel
Accumulator for Copper. Sci.Total Environ. 125:185-192.

7597

UEndp, Eff

Chan, H.M.. 1988. Accumulation and Tolerance to
Cadmium, Copper, Lead and Zinc by the Green Mussel
Perna viridis. Mar.Ecol.Prog.Ser. 48(3):295-303.

2970

NonRes

Chapman, H.F., J.M. Hughes, and R.L. Kitching. 1985.
Burying Response of an Intertidal Gastropod to Freshwater
and Copper Contamination. Mar.Pollut.Bull. 16(11 ):442-
445.

11461

NonRes

Chelomin, V.P., and N.N. Belcheva. 1992. The Effect of
Heavy Metals on Processes of Lipid Peroxidation in
Microsomal Membranes from the Hepatopancreas of the
Bivalve Mollusc Mizuhopecten. Comp.Biochem.Physiol.C
103(2):419-422.

6730

UEndp, Eff

Chen, C., L. Zhang, and Y. Wu. 1988. The Complexing
Capacity of Natural Organic Matters for Copper in
Estuarine Water and Its Effect on Growth of Diatom in
Xiamen Estuarine Harbor. China Environ.Sci.(Zhongguo
Huaniing Kexue) 8(1):29-35 (CHI) (ENG ABS).

3841

Dur, Con

Chen, I.M.. 1994. The Effects of Copper on the Respiration
of Oyster Crassotrea gigas (Thunberg). Fish.Sci. 60(6):683-
686.

16242

UEndp

Chen, J.C., and P.C. Liu. 1987. Accumulation of Heavy
Metals in the Nauplii of Artemia salina. J.World
Aquacult.Soc. 18(2):84-93.

2749

UEndp, Eff

Brine Shrimp

Cheung, S.G., and L.S. Wong. 1999. Effect of Copper on
Activity and Feeding in the Subtidal Prosobranch Babylonia
lutosa (Lamarck) (Gastropoda: Buccinidae). Mar.Pollut.Bull.
39(1 -12): 106-111.

20620

UEndp

Cid, A., C. Herrero, and J. Abalde. 1996. Functional
Analysis of Phytoplankton by Flow Cytometry: A Study of
the Effect of Copper on a Marine Diatom.
Sci.Mar.60(Suppl. 1):303-308.

3097

UEndp

616

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Coglianese, M.P., and M. Martin. 1981. Individual and
Interactive Effects of Environmental Stress on the
Embryonic Development of the Pacific Oyster, Crassostrea
gigas. I. The Toxicity of. Mar.Environ.Res. 5(1):13-27.

15740

UEndp

Coglianese, M.P.. 1982. The Effects of Salinity on Copper
and Silver Toxicity to Embryos of the Pacific Oyster.
Arch.Environ.Contam.Toxicol. 11(3):297-303.

15377

UEndp

Correia, A.D., and M.H. Costa. 2000. Effects of Sediment
Geochemical Properties on the Toxicity of Copper-Spiked
Sediments to the Marine Amphipod Gammarus locusta.
Sci.Total Environ. 247:99-106.

48393

UEndp

Courtois, L.A.. 1974. Physiological Responses of Striped
Bass, Roccus saxatilis (Walbaum), to Changes in Diet,
Salinity, Temperature, and Acute Copper Exposure.
Ph.D.Thesis, University of California, Davis, CA:118p.;
Diss.Abstr.lnt.B Sci.Eng.35(6):2976.

8522

UEndp, Eff

Cui, K., Y. Liu, and L. Hou. 1987. Effects of Six Heavy
Metals on Hatching Eggs and Survival of Larval of Marine
Fish. Oceanol.Limnol.Sin./Haiyang Yu Huzhao 18(2): 138-
144 (CHI) (ENGABS).

3222

NonRes

D'Agostino, A., and C. Finney. 1974. The Effect of Copper
and Cadmium on the Development of Tigriopus japonicus.
In: F.J.Vernberg and W.B.Vernberg (Eds.), Pollution and
Physiology of Mar.Organisms, Academic Press, NY :445-
463.

15558

UEndp

Davenport, J., and A. Manley. 1978. The Detection of
Heightened Sea-Water Copper Concentrations by the
Mussel Mytilus edulis. J.Mar.Biol.Assoc.U.K. 58(4):843-
850.

5598

Con

Denton, G.R.W., and C. Burdon-Jones. 1986.
Environmental Effects on Toxicity of Heavy Metals to Two
Species of Tropical Marine Fish from Northern Australia.
Chem.Ecol. 2(3):233-249.

4327

NonRes

Depledge, M.H.. 1984. Disruption of Circulatory and
Respiratory Activity in Shore Crabs (Carcinus maenas (L.))
Exposed to Heavy Metal Pollution.

Com p. Biochem. Physiol .C 78(2):445-459.

11384

UEndp, Eff

617

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Depledge, M.H.. 1987. Enhanced Copper Toxicity
Resulting From Environmental Stress Factor Synergies.
Com p. Biochem. Physiol .C 87(1): 15-19.

2589

UEndp, Eff, Con

2150

UEndp, Eff

Devi, V.U.. 1987. Heavy Metal Toxicity to Fiddler Crabs,
Ilea annulipes latreille and Ilea triangularis (Milne
Edwards): Tolerance to Copper, Mercury, Cadmium.
Bull.Environ.Contam.Toxicol. 39:1020-1027.

2602

NonRes

Devi, V.U.. 1997. Heavy Metal Toxicity to an Intertidal
Gastropod Morula granulata (Duclos): Tolerance to
Copper, Mercury, Cadmium and Zinc. J.Environ.Biol.
18(3):287-290.

19022

NonRes

Domouhtsidou, G.P., and V.K. Dimitriadis. 2000.
Ultrastructural Localization of Heavy Metals (Hg,Ag,Pb, and
Cu) in Gills and Digestive Gland of Mussels, Mytilus
galloprovincialis (L.). Arch.Environ.Contam.Toxicol.
38(4):472-478.

48771

UEndp

Durkina, V.B.. 1994. Development of Offspring of the Sea
Urchin Strongylocentrotus intermedius Exposed to Copper
and Zinc. Russ.J.Mar.Biol. 20(4):232-235.

17580

UEndp

Earnshaw, M.J., S. Wilson, H.B. Akberali, R.D. Butler, and
K.R.M. Marriott. 1986. The Action of Heavy Metals on the
Gametes of the Marine Mussel, Mytilus edulis(L.)-lll. The
Effect of Applied Copper and Zinc on Sperm Motility in.
Mar.Environ.Res. 20(4):261-278.

12324

UEndp

Edding, M., and F. Tala. 1996. Copper Transfer and

Influence on a Marine Food Chain.

Bull.Environ.Contam.Toxicol. 57(4):617-624.

17377

UEndp

Eisler, R., and G.R. Gardner. 1973. Acute Toxicology to an
Estuarine Teleost of Mixtures of Cadmium, Copper and
Zinc Salts. J.Fish Biol. 5(2): 131-142.

8342

UEndp, Eff, Con

Eklund, B.. 1993. A 7-Day Reproduction Test with the
Marine Red Alga Ceramium strictum. In: W.SIoof and H.De
Kruijf (Eds.), Proc.2nd European Conf.on Ecotoxicol.
Suppl.1/2:749-759.

16535

Dur

Plants do not drive
criteria, and
therefore, are not
included in CWA
review and approval
of ORWQS

618

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

El Nady, F.E.. 1989. Toxicity of Mercury to Mugil capito
Frys in Presence of EDTA and Copper Sulphate.

Bull. Natl. I nst. Oceanogr. Fish. 15(2): 163-169.

14377

NonRes

Eldon, J., M. Pekkarinen, and R. Kristoffersson. 1980.
Effects of Low Concentrations of Heavy Metals on the
Bivalve Macoma balthica. Ann.Zool.Fenn. 17:233-242.

17309

UEndp

Ellenberger, S.A., P.C. Baumann, and T.W. May. 1994.
Evaluation of Effects Caused by High Copper
Concentrations in Torch Lake, Michigan, on Reproduction
of Yellow Perch. J.Gt. Lakes Res. 20(3):531-536.

14630

UEndp

Elliott, N.G., R. Swain, and D.A. Ritz. 1985. The Influence
of Cyclic Exposure on the Accumulation of Heavy Metals
by Mytilus edulis planulatus (Lamarck). Mar.Environ.Res.
15(1): 17-30.

11669

UEndp

Elliott, N.G., R. Swain, and D.A. Ritz. 1986. Metal
Interaction During Accumulation by the Mussel Mytilus
edulis planulatus. Mar.Biol. 93(3):395-399.

12054

UEndp

Engel, D.W., and W.G. Sunda. 1979. Toxicity of Cupric Ion
to Eggs of the Spot Leiostomus xanthurus and the Atlantic
Silverside Menidia menidia. Mar.Biol. 50(2):121-126.

6826

Con

Engel, D.W., W.G. Sunda, and R.M. Thuotte. 1976. Effects
of Copper on Marine Fish Eggs and Larvae. Environ.Health
Perspect.Oct. :288-289 (ABS).

6443

Dur, UChron

Erickson, S.J.. 1972. Toxicity of Copper to Thalassiosira
pseudonana in Unenriched Inshore Seawater. J.Phycol.
8(4):318-323.

9078

NonRes

Erickson, S.J.. 1980. Unpublished Laboratory Data.
U.S.EPA, Gulf Breeze, FL :8.

3652

Eff, UEndp, Con

Erickson, S.J.. 1981. Inhibition of Photosynthesis in
Estuarine Phytoplankton by Mixtures of Copper and
Pentachlorophenol. Unpublished Manuscript, U.S.EPA,
Gulf Breeze, F L:11.

4802

Field, UEndp, Eff

Eriksson, S.P., and J.M. Weeks. 1994. Effects of Copper
and Hypoxia on Two Populations of the Benthic Amphipod
Corophium volutator (Pallas). Aquat.Toxicol. 29:73-81.

14069

UEndp

619

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

16031

Dur

Brine Shrimp

Esquivel, I. 1986. Short Term Copper Bioassay on the
Planula of the Reef Coral Pocillopora damicornis. In:
P.L.Jokiel, R.H.Richmond and R.A.Rogers (Eds.), Coral
Reef Population Biology, Hawaii Univ.Sea Grant
Coll.Program, Honolulu, HI :465-472.

4379

Ace

Fagotti, A., I. Di Rosa, R. Simoncelli, R.K. Pipe, F. Panara,
and R. Pascolini. 1996. The Effects of Copper on Actin and
Fibronectin Organization in Mytilus galloprovincialis
Haemocytes. Dev.Comp.Immunol. 20(6):383-391.

7315

UEndp, UChron

Fisher, N.S., and D. Frood. 1980. Heavy Metals and Marine
Diatoms: Influence of Dissolved Organic Compounds on
Toxicity and Selection for Metal Tolerance Among Four
Species. Mar.Biol. 59(2):85-93.

6470

UEndp

Fisher, N.S., and G.J. Jones. 1981. Heavy Metals and
Marine Phytoplankton: Correlation of Toxicity and
Sulfhydryl-Binding. J.Phycol. 17(1): 108-111.

14681

Dur

Plants do not drive
criteria, and
therefore, are not
included in CWA
review and approval
of ORWQS

Fitzwater, S.E., G.A. Knauer, and J.H. Martin. 1983. The
Effects of Cu on the Adenylate Energy Charge of Open
Ocean Phytoplankton. J.Plankton Res. 5(6):935-938.

11100

UEndp, Con

Florence, T.M., and J.L. Stauber. 1986. Toxicity of Copper
Complexes to the Marine Diatom Nitzschia closterium.
Aquat.Toxicol. 8(1 ):11-26.

11882

UEndp

Gainey, L.F.J., and J.R. Kenyon. 1990. The Effects of
Reserpine on Copper Induced Cardiac Inhibition in Mytilus
edulis. Comp.Biochem.Physiol.C 95(2): 177-179.

3462

Eff, Con

Gajbhiye, S.N., and R. Hirota. 1990. Toxicity of Heavy
Metals to Brine Shrimp Artemia. J.Indian Fish.Assoc.
20:43-50.

17792

UEndp, Dur

Brine Shrimp

Gao, S., Zou, and D.. 1994. Acute Toxicity of Copper,
Mercury and Chromium to Larvae of Penaeus penicillatus
Alcock. Mar.Sci.Bull./Haiyang Tongbao 13(2):28-32 (CHI)
(ENG ABS).

16613

NonRes

620

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Gardner, G.R., and G. Laroche. 1973. Copper Induced
Lesions in Estuarine Teleosts. J.Fish.Res.Board Can.
30(3):363-368.

8841

Con, UEndp

Gnassia-Barelli, M., M. Romeo, and S. Puiseux-Dao. 1995.
Effects of Cadmium and Copper Contamination on Calcium
Content of the Bivalve Ruditapes decussatus.
Mar.Environ.Res. 39(1-4):325-328.

16894

UEndp

Gotsis-Skretas, 0., and U. Christaki. 1992. Physiological
Responses of Two Marine Phytoplanktonic Species to
Copper and Mercury. In: G.P.Gabrielides (Ed.), Proc.ofthe
FAO/UNEP/IOC Workshop on the Biological Effects of
Pollutants on Marine Organisms, Malta, 10-14 Sept., 1991,
UNEP, Athens, Greece, MAP Tech.Rep.Ser.No.69 :151 -
164.

12989

UEndp

Gould, E., R.J. Thompson, L.J. Buckley, D. Rusanowsky,
and G.R. Sennefelder. 1988. Uptake and Effects of Copper
and Cadmium in the Gonad of the Scallop Placopecten
magellanicus: Concurrent Metal Exposure. Mar.Biol.
97(2):217-223.

2962

UEndp

Grace, A.L.Jr.. 1987. The Effects of Copper on the Heart
Rate and Filtration Rate of Mytilus edulis. Mar.Pollut.Bull.
18(2):87-91.

8271

UEndp, Eff

Gully, J.R., J.P. Bottomley, and R.B. Baird. 1999. Effects of
Sporophyll Storage on Giant Kelp Macrocystis pyrifera
(Agardh) Bioassay. Environ.Toxicol.Chem. 18(7):1474-
1481.

49798

Dur

26 lines of data with
EC50 info based on
POP effect(48hr)

Haglund, K., M. Bjorklund, S. Gunnare, A. Sandberg, U.
Olander, and M. Pedersen. 1996. New Method for Toxicity
Assessment in Marine and Brackish Environments Using
the Macroalga Gracilaria tenuistipitata (Gracilariales,
Rhodophyta). Hydrobiologia 326/327:317-325.

18453

NonRes

Hall, A.. 1981. Copper Accumulation in Copper-Tolerant
and Non-tolerant Populations of the Marine Fouling Alga,
Ectocarpus siliculosus (Dillw.) Lyngbye. Bot.Mar.
24(4):223-228.

9466

Eff, Con

Han and Hung. 1990.

UEndp

Bioaccumulation

621

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

18038

UEndp

Hansen, J.I., T. Mustafa, and M. Depledge. 1992.
Mechanisms of Copper Toxicity in Shore Crab, Carcinus
maenas II. Effects on Key Metabolic Enzymes, Metabolites
and Energy Charge Potential. Mar.Biol. 114(2):259-264.

20550

UEndp

Hansen, J.I., T. Mustafa, and M. Depledge. 1992.
Mechanisms of Copper Toxicity in the Shore Crab,
Carcinus maenas I. Effects on Na,K-ATPase Activity,
Haemolymph Electrolyte Concentrations and Tissue.
Mar.Biol. 114(2):253-257.

20551

UEndp

Haritonidis, S., H.J. Jager, and H.O. Schwantes. 1983.
Accumulation of Cadmium, Zinc, Copper and Lead by
Marine Macrophyceae Under Culture Conditions.
Angew.Bot. 57(5/6):311-330.

11369

UEndp

Haritonidis, S.. 1985. Uptake of Cd, Zn, Cu and Pb by
Marine Macrophyceae Under Culture Conditions.
Mar. Environ. Res. 17(2-4): 198-199.

6414

UEndp, Eff, Con

Harland, A.D., and N.R. Nganro. 1990. Copper Uptake by
the Sea Anemone Anemonia viridis and the Role of
Zooxanthellae in Metal Regulation. Mar.Biol. 104(2):297-
301.

20552

UEndp

Harrison, F.L., J.R. Lam, and R. Berger. 1983. Sublethal
Responses of Mytilus edulis to Increased Dissolved
Copper. Sci.Total Environ. 28:141-158.

13602

UEndp

Harrison, F.L.Jr.. 1978. Copper Sensitivity of Adult Pacific
Oysters. In: J.H.Thorp and J.W.Gibbons (Eds.),
Dep.Energy Symp.Ser., Energy and Environmental Stress
in Aquatic Systems, Augusta, GA 48:301-315.

5351

Con, Eff

Hattori, T., and Y. Shizuri. 1996. A Screening Method for
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10263

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Comment(s)

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3697

UEndp

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11370

UEndp, Eff

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15624

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17415

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16243

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16875

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10965

UEndp

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13460

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623

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Comment(s)

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5282

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5283

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16999

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8335

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2 lines of data with
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11496

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3215

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Comment(s)

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4043

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2882

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9700

See note

ECOTOX provides a
96-h LC50 of 2656
|jg/L for this study.
When combined with
other LC50s for
Fundulus
heteroclitus, the
SMAV would have
been 1470 |jg/L. This
value could have
been considered for
EPA's evaluation of
saltwater copper, but
the species is
relatively insensitive
to copper compared
to others. Note, this
test was not used in
the 1995 GLI for
copper.

625

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

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8590

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13009

UEndp

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14918

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17028

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15654

UEndp

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14966

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626

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Rejection Code(s)

Comment(s)

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an Antifouling Substance Isolated from an Octocoral
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16323

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Kirchin, M.A., M.N. Moore, R.T. Dean, and G.W. Winston.
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4392

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16686

UEndp

Kobayashi, N.. 1971. Fertilized Sea Urchin Eggs As an
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2963

UEndp, Dur

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6541

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19435

UEndp

Krishnakumar, P.K., P.K. Asokan, and V.K. Pillai. 1990.
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3553

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11014

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18886

NonRes

Kumaraguru, A.K., and K. Ramamoorthi. 1978. Toxicity of
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8381

NonRes

Kumaraguru, A.K., D. Selvi, and V.K. Venugopalan. 1980.
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Bull.Environ.Contam.Toxicol. 24(6):853-857.

9845

NonRes

627

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EcoRef #

Rejection Code(s)

Comment(s)

Lage, O.M., A.M. Parente, M.T.S.D. Vasconcelos, C.A.R.
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19194

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7077

UEndp

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Bioaccumulation and Depuration of Some Trace Metals in
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3240

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19990

Eff

20469

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18971

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10086

UEndp, Dur

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16218

UEndp

628

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Lin, W., M.A. Rice, and P.K. Chien. 1992. The Effects of
Copper, Cadmium and Zinc on Particle Filtration and
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6506

UEndp, Dur

Liu, P.C., and J.C. Chen. 1987. Effects of Heavy Metals on
the Hatching Rates of Brine Shrimp Artemia salina Cysts.
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4256

UEndp

Brine Shrimp

51641

NonRes

Lovegrove, T.. 1979. Anti-Fouling Paint in Farm Ponds.
Fish Farming Int. 6(2):13-15,39.

7563

UEndp

Lumsden, B.R., and T.M. Florence. 1983. A New Algal
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10266

UEndp, Con

Luoma, S.N., D.J. Cain, K. Ho, and A. Hutchinson. 1983.
Variable Tolerance to Copper in Two Species From San
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11399

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Lustigman, B., J.M. McCormick, G. Dale, and J.J.A.
McLaughlin. 1987. Effect of Increasing Copper and Salinity
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Bull. Environ.Contam .Toxicol. 38(2):359-362.

6017

UEndp

MacDonald, J.M., J.D. Shields, and R.K. Zimmer-Faust.
1988. Acute Toxicities of Eleven Metals to Early Life-
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12861

UEndp

Maclnnes, J.R., and A. Calabrese. 1979. Combined Effects
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15627

UEndp

Maclnnes, J.R., and F.P. Thurberg. 1973. Effects of Metals
on the Behavior and Oxygen Consumption of the Mud
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8902

UEndp, Eff

MacRae, T.H., and A.S. Pandey. 1991. Effects of Metals on
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Dur, UEndp

Brine Shrimp

629

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Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Madhupratap, M., C.T. Achuthankutty, and S.R.S. Nair.
1981. Toxicity of Some Heavy Metals to Copepods Acartia
spinicauda and Tortanus forcipatus. Indian J.Mar.Sci.
10:382-383.

15722

NonRes

Magni, P.. 1993. Effect of Oxygen Concentration on the
Bioavailability of Copper for the Bivalve 'Macoma balthica'.
Stage Report June 1992-Feb.1993, Inst.voor Oecologisch
Onderzoek, Heteren, Netherland s:27.

17396

UEndp

Malea, P., S. Haritonidis, and T. Kevrekidis. 1995. The
Short-Term Uptake of Copper by the Two Parts of the
Seagrass Halophila stipulacea (Forsk.) Aschers. and Leaf-
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15111

UEndp

Manley, A.R.. 1983. The Effects of Copper on the
Behaviour, Respiration, Filtration and Ventilation Activity of
Mytilus edulis. J.Mar.Biol.Assoc.U.K. 63:205-222.

10752

UEndp, Eff

Marcano, L., 0. Nusetti, J. Rodriguez-Grau, and J. Vilas.
1996. Uptake and Depuration of Copper and Zinc in
Relation to Metal-Binding Protein in the Polychaete
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18575

NonRes

Martin, J.L.M.. 1979. Schema of Lethal Action of Copper on
Mussels. Bull.Environ.Contam.Toxicol. 21(6):808-814.

8393

UEndp

Martincic et al. 1992.

Field, UEndp

Bioaccum

Mathew, R., and N.R. Menon. 1983. Effects of Heavy
Metals on Byssogenesis in Perna viridis (Linn.). Indian
J.Mar.Sci. 12(2): 125-127.

11120

NonRes

Mathew, R., and N.R. Menon. 1983. Oxygen Consumption
in Tropical Bivalves Perna viridis (Linn.) and Meretrix casta
(Chem.) Exposed to Heavy Metals. Indian J.Mar.Sci.
12(1 ):57-59.

11085

UEndp

McLeese, D.W.. 1975. Chemosensory Response of
American Lobsters (Homarus americanus) in the Presence
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8143

UEndp, Eff

McLusky and Phillips. 1975.

UEndp, Det

Bioaccum

630

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Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Menasria, R., and J.F. Pavilion. 1994. Toxic Effects of Two
Trace Metals, Copper and Silver, on a Crustacean
Harpacticoid Copepod Tigriopus brevicornis (Muller). Lethal
and Sublethal. J.Rech.Oceanogr.19(3/4):157-165 (Fre)
(Eng Abs).

18833

NonRes

Millward, R.N., and A. Grant. 1995. Assessing the Impact
of Copper on Nematode Communities from a Chronically
Metal-Enriched Estuary Using Pollution-Induced
Community Tolerance. Mar.Pollut.Bull. 30(11):701 -706.

18052

Minniti, F.. 1987. Effects of Copper Pollution on the
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574

UEndp, Eff, Con

Moore, M.N., J. Widdows, J.J. Cleary, R.K. Pipe, P.N.
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Responses of the Mussel Mytilus edulis to Copper and
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11537

UEndp

Moraitou-Apostolopoulou, M., and G. Verriopoulos. 1982.
Individual and Combined Toxicity of Three Heavy Metals,
Cu, Cd, and Cr, for the Marine Copepod Tisbe holothuriae.
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15726

NonRes

Moraitou-Apostolopoulou, M., M. Kiortsis, V. Verriopoulos,
and S. Platanistioti. 1983. Effects of Copper Sulphate on
Tisbe holothuriae Humes (Copepoda) and Development of
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15500

NonRes

Moreno Garrido, I., L.M. Lubian, and A.M.V.M. Soares.
1999. Oxygen Production Rate as a Test for Determining
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62(6):776-782.

20472

Eff

631

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Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Mortimer, M.R., and G.J. Miller. 1994. Susceptibility of
Larval and Juvenile Instars of the Sand Crab, Portunus
pelagicus (L.), to Sea Water Contaminated by Chromium,
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1121.

16331

UEndp, Dur

ECOTOX provides a
96-h LC50 of 41.50
|jg/L for this study.
When combined with
other LC50s for
Portunus pelagicus,
the SMAV would
have been 891.4
|jg/L. This value could
have been

considered for EPA's
evaluation of
saltwater copper, but
the species is
relatively insensitive
to copper compared
to others. Note, this
test was not used in
the 1995 GLI for
copper.

Murugadas, T.L., S.M. Phang, and S.L. Tong. 1995. Heavy
Metal Accumulation Patterns in Selected Seaweed Species
of Malaysia. Asia Pacific J.Mol.Biol.Biotechnol. 3(4):290-
310.

19239

UEndp

Myint, U.M., and P.A. Tyler. 1982. Effects of Temperature,
Nutritive and Metal Stressors on the Reproductive Biology
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12950

UEndp

Nacci, D., E. Jackim, and R.Walsh. 1986. Comparative
Evaluation of Three Rapid Marine Toxicity Tests: Sea
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Toxicity Test and Microtox. Environ.Toxicol.Chem. 5:521-
525.

17742

Dur

Nacci, D., P. Comeleo, E. Petrocelli, A. Kuhn-Hines, G.
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Sperm Cell Toxicity Test Using the Sea Urchin, Arbacia
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Toxicology and Risk Assessment, 14th Volume, ASTM STP
1124, Philadelphia, PA :324-336.

16722

Dur

632

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Nacci, D.E., and E. Jackim. 1985. Rapid Aquatic Toxicity
Assay Using Incorporation of Tritiated-Thymidine Into Sea
Urchin, Arbacia punctulata, Embryo: Evaluation of
Toxicant. In: R.C.Bahner and D.J.Hansen (Eds.), Aquatic
Toxicology and Hazard Assessment, 8th Symposium,
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9394

Con, Dur

Nagabhushanam, R., K.S. Rao, and R. Sarojini. 1986.
Acute Toxicity of Three Heavy Metals to Marine Edible
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12895

NonRes

Narayanan, K.R., S. Ajmalkhan, and S. Pechimuthu. 1994.
Histopathological Changes Due to Effects of Sublethal
Concentrations of Copper Sulphate on the Hepatopancreas
of Edible Crab, Scylla serrata (Forskal). J.Environ.Biol.
15(4):289-293.

13516

UEndp

19512

NonRes

Nasu, Y., and M. Kugimoto. 1981. Lemna (Duckweed) As
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9489

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Neiheisel, T.W., and M.E. Young. 1992. Use of Three
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3959

Dur

Nell, J.A., and R. Chvojka. 1992. The Effect of bis-
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4136

UEndp

Nelson, D.A., J.E. Miller, and A. Calabrese. 1988. Effect of
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15056

NonRes

633

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Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Nelson, W.G.. 1990. Use of the Blue Mussel, Mytilus edulis,
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18927

UEndp, Eff

Neuhoff, H.G.. 1983. Synergistic Physiological Effects of
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14336

Eff, UEndp

Nias, D.J., S.C. McKullup, and K.S. Edyvane. 1993.
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9714

UEndp,

Nicola Giudici, M., and S.M. Guarino. 1989. Effects of
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9979

UEndp

Niemi, A.. 1972. Effects of Toxicants on Brackish-Water
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9155

UEndp

Nonnotte, L., F. Boitel, and J.P. Truchot. 1993. Waterborne
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9229

UEndp

Nusetti, 0., R. Salazar-Lugo, J. Rodriguez-Grau, and J.
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19139

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Okamoto, O.K., L. Shao, J.W. Hastings, and P. Colepicolo.
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20347

UEndp

634

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Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Okazaki, R.K. 1976. Copper Toxicity in the Pacific Oyster
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8413

UEndp, See note

ECOTOX provides a
F,M 96-h LC50 of
464.8 |jg/L for this
study. Had this value
been use, the other
values, all from S,U
or S,M tests, would
have been rejected.
This value is less
sensitive to copper
than the original
SMAV, both of which
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Note, this test was
not used in the 1995
GLI for copper.

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15868

Eff

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5658

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Ozoh, P.T.E., and N.V. Jones. 1990. The Effects of Salinity
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3197

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Pablo, F., R.T. Buckney, and R.P. Lim. 1997. Toxicity of
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17482

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Pace, F., R. Ferrara, and G. Del Carratore. 1977. Effects of
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7612

UEndp

635

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Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

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18937

UEndp

Park, J.S., and H.G. Kim. 1978. Bioassays on Marine
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8418

Con, Eff, NonRes

ECOTOX provides a
96-h LC50 of 2108
|jg/L for this study.
When combined with
other LC50s for
Crassostrea gigas,
the SMAV is 20.69.
This value could have
been considered for
EPA's evaluation of
saltwater copper, but
the species is
relatively insensitive
to copper compared
to others.
Furthermore, this
LC50 is over 10x the
original SMAV and
can probably be
considered an outlier.
Note, this test was
not used in the 1995
GLI for copper.

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8419

NonRes

8420

NonRes

636

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Citation

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Rejection Code(s)

Comment(s)

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10890

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Patin, S.A., and V.N. Tkachenko. 1974. Effect of Metals on
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8669

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5344

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20564

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Persoone, G., and G. Uyttersprot. 1975. The Influence of
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5922

UEndp

Pesch and Morgan. 1978.

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19926

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15633

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Phinney, J.T., and K.W. .Bruland. 1994. Uptake of
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45097

UEndp

637

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Comment(s)

Phinney, J.T., and K.W. Bruland. 1997. Effects of
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20300

UEndp

Pipe, R.K., J.A. Coles, F.M.M. Carissan, and K.
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20089

UEndp

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5438

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Prabhudeva, K.N., and N.R. Menon. 1990. Metal
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14759

UEndp

Price, R.K.J., and R.F. Uglow. 1979. Some Effects of
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8423

Con, LT

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9879

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Pyefinch, K.A., and J.C. Mott. 1948. The Sensitivity of
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10199

Con, Dur

Rainbow, P.S., A.G. Scott, E.A. Wiggins, and R.W.
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6714

UEndp, Eff

Rainbow, P.S., and S.L.White. 1989. Comparative
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18778

UEndp

638

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ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Rainbow, P.S.. 1985. Accumulation of Zn, Cu and Cd by
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9713

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Ralph, P.J., and M.D. Burchett. 1998. Photosynthetic
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19866

UEndp

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17117

NonRes

Rao, V.N.R., and G.M. Latheef. 1989. Effect of Copper on
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9558

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Rao, Y.P., V.U. Devi, and D.G.V. Rao. 1986. Copper
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11765

UEndp

Raymont, J., E.G., and J. Shields. 1963. Toxicity of Copper
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20209

UEndp

Redpath, K.J.. 1985. Growth Inhibition and Recovery in
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10973

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Reed, R.H., and L. Moffat. 1983. Copper Toxicity and
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11161

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6045

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Reeve, M.R., M.A. Walter, K. Darcy, and T. Ikeda. 1977.
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6079

Con, UEndp

639

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Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Regoli, F., E. Orlando, M. Mauri, M. Nigra, and G.A.
Cognetti. 1991. Heavy Metal Accumulation and Calcium
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8705

UEndp, Eff

Reiriz, S., A. Cid, E. Torres, J. Abalde, and C. Herrero.
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16173

UEndp

Reish, D.J., and R.S. Carr. 1978. The Effect of Heavy
Metals on the Survival, Reproduction, Development and
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8428

UEndp

Reish, D.J., F. Piltz, J.M. Martin, and J.Q. Word. 1974.
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8635

UEndp, Con

Rihjstenbil, J.W., F. Dehairs, R. Ehrlich, and J.A. Wijnholds.
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19145

UEndp

Rijstenbil, J.W., A. Sandee, J. Van Drie, and J.A.
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14606

UEndp

Roesijadi, G.. 1980. Influence of Copper on the Clam
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9888

Rtal, A., and J.P. Truchot. 1996. Haemolymph Transport
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811.

19841

UEndp

Ruiz, J.M., G.W. Bryan, and P.E. Gibbs. 1994. Chronic
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14453

UEndp

640

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Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Ruiz, J.M., G.W. Bryan, G.D. Wigham, and P.E. Gibbs.
1996. Effects of Copper on the 48-H Embryonic
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9910

UEndp

Rumbold, D.G., and S.C. Snedaker. 1997. Evaluation of
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17830

Dur

Saifullah, S.M.. 1978. Inhibitory Effects of Copper on
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2260

NonRes

Saliba, L.J., and M. Ahsanullah. 1973. Acclimation and
Tolerance of Artemia salina and Ophryotrocha labronica to
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5168

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Sanders, B.M., L.S. Martin, S.R. Howe, W.G. Nelson, E.S.
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in Accumulation of Stress Proteins in Mytilus edulis
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4978

UEndp, Eff

Sanders, I.M.. 1984. Sublethal Effects of Copper on
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4249

UEndp

Sanders, J.G., and G.F. Riedel. 1993. Trace Element
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13354

Field, UEndp

Sarasquete, M.C., M.L. Gonzales de Canales, and S.
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9518

UEndp

Sasikumar, N., A.S. Clare, D.J. Gerhart, D. Stover, and D.
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53890

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Sathyanathan, B.. 1996. Kinetics and Mechanism of
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20158

Eff, UEndp

641

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Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Savant, K.B., and G.K. Amte. 1992. Respiratory Response
of Estuarine Crab llyoplax gangetica Exposed to Three
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17564

UEndp

Scott, D.M., and C.W. Major. 1972. The Effect of Copper
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15476

UEndp

Seeliger, U., and C. Cordazzo. 1982. Field and
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11220

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4125

UEndp, Eff

54052

UEndp

Selvakumar, S., S.A. Khan, and A.K. Kumaraguru. 1996.
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18580

NonRes

Shuster, C.N.Jr., and B.H. Pringle. 1969. Trace Metal
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19929

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Snell, T.W., and G. Persoone. 1989. Acute Toxicity
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3827

Dur

642

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ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Sobral, P., L. Castro, H. Costa, and 1. Peres. 1995. The
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19364

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Soria-Dengg, S., and D. Ochavillo. 1990. Comparative
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20706

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Soto, M., and I. Marigomez. 1997. BSD Extent, an Index for
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18327

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Soto, M., I. Quincoces, X. Lekube, and I. Marigomez. 1998.
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18951

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Spicer, J.I.. 1995. Effect ofWater-Borne Copper on
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19536

UEndp

Staples, L.S., P.F. Shacklock, and J.S. Craigie. 1995.

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19429

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Stauber, J.L., and T.M. Florence. 1987. Mechanism of
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12971

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Stauber, J.L.. 1995. Toxicity Testing Using Marine and
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19056

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3 lines of data with
72hr EC50 on green
algae and diatoms

Stebbing, A.R.D., and V.J.R. Santiago-Fandino. 1983. The
Combined and Separate Effects of Copper and Cadmium
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11562

UEndp

Stebbing, A.R.D.. 1976. The Effects of Low Metal Levels on
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15641

UEndp

643

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ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Stephenson, R.R., and D. Taylor. 1975. The Influence of
EDTAon the Mortality and Burrowing Activity of the Clam
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8223

UEndp

Stroemgren, T.. 1980. The Effect of Dissolved Copper on
the Increase in Length of Four Species of Intertidal Fucoid
Algae. Mar.Environ.Res. 3(1 ):5-13.

9901

UEndp, Con

Stromgren, T., and M.V. Nielsen. 1991. Spawning
Frequency, Growth and Mortality of Mytilus edulis Larvae,
Exposed to Copper and Diesel Oil. Aquat.Toxicol. 21:171-
180.

3857

UChron

1 line of data with a
30d EC50

Stromgren, T.. 1982. Effect of Heavy Metals (Zn, Hg, Cu,
Cd, Pb, Ni) on the Length Growth of Mytilus edulis.
Mar.Biol. 72(1):69-72.

10899

UEndp

Stromgren, T.. 1986. The Combined Effect of Copper and
Hydrocarbons on the Length Growth of Mytilus edulis.
Mar. Environ. Res. 19:251-258.

45177

UEndp

Subramanian, A., B.R. Subramanian, and V.K.
Venugopalan. 1980. Toxicity of Copper and Zinc on
Cultures of Skeletonema costatum (Grev.) Cleve and
Nitzschia longissima. Curr.Sci. 49(7):266-268.

9903

UEndp

Sullivan, B.K., and P.J. Ritacco. 1988. Effects of Nutrients
and Copper on Copepod Population Dynamics: A
Mesocosm Study. Adv.Environ.Sci.Technol. 21:335-357.

13124

Field, UEndp

11224

UEndp, Con

Sunila, I.. 1981. Toxicity of Copper and Cadmium to Mytilus
edulis L. (Bivalvia) in Brackish Water. Ann.Zool.Fenn.
18:213-223.

15791

Dur

Syasina, I.G., M.A. Vaschenko, and V.B. Durkina. 1992.
Histopathological Changes in the Gonads of Sea Urchins
Exposed to Heavy Metals. Russ.J.Mar.Biol.(Eng Transl) of
Biol.Morya (4):79-89 (Vladivostok) 17:244-251.

19065

UEndp

Tadros, M.G., P. Mbuthia, and W. Smith. 1990. Differential
Response of Marine Diatoms to Trace Metals.
Bull.Environ.Contam.Toxicol. 44(6):826-831.

18878

UEndp

644

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Targett, N.M., and W.R. Stochaj. 1994. Natural Antifoulants
and Their Analogs: Applying Nature's Defense Strategies to
Problems of Biofouling Control. In: M.F.Thompson,
R.Nagabhushanam, R.Sarojini, and M.Fingerman (Eds.),
Recent Developments in Biofouling Control, Oxford & IBH
Publ.Co., New Delhi, India :221-228.

16469

UEndp

Thomas, A.. 1915. Effects of Certain Metallic Salts upon
Fishes. Trans.Am.Fish.Soc. 44:120-124.

2865

UEndp, Dur

Thomsen, J.P.. 1980. A Study on the Possible Association
of Copper Pollution with Vibriosis in Eel. Nord.Vet.Med.
30:90-95.

10209

UEndp, Con

Thurberg, F.P., M.A. Dawson, and R.S. Collier. 1973.
Effects of Copper and Cadmium on Osmoregulation and
Oxygen Consumption in Two Species of Estuarine Crabs.
Mar.Biol. 23(3):171-175.

8732

UEndp,Con

Torres, P., L. Tort, and R. Flos. 1987. Acute Toxicity of
Copper to Mediterranean Dogfish.
Comp.Biochem.Physiol.C 86(1 ):169-171.

12386

Dur

1 line with 48hr LC50
data

Valente, R.M., E.M. Cosper, and C.F. Wurster. 1987.
Interactive Effects of Copper and Silicic Acid on Resting
Spore Formation and Viability in a Marine Diatom.
J.Phycol. 23(1): 156-163.

4380

UEndp

Vedel, G.R., and M.H. Depledge. 1995. Stress-70 Levels in
the Gills of Carcinus maenas Exposed to Copper.
Mar.Pollut.Bull. 31(1-3):84-86.

18722

UEndp

Verma, S.R., S.K. Bansal, and R.C. Dalela. 1978. Toxicity
of Selected Organic Pesticides to a Fresh Water Teleost
Fish, Saccrobranchus fossilis and its Application in
Controlling Water Pollution. Arch.Environ.Contam.Toxicol.
7(3):317-323.

661

UEndp

Verriopoulos, G., and M. Moraitou-Apostolopoulou. 1982.
Differentiation of the Sensitivity to Copper and Cadmium in
Different Life Stages of a Copepod. Mar.Pollut.Bull.
13(4): 123-125.

11097

NonRes

Verriopoulos, G., M. Moraitou-Apostolopoulou, and E.
Milliou. 1987. Combined Toxicity of Four Toxicants (Cu, Cr,
Oil, Oil Dispersant) to Artemia salina.

Bull. Environ.Contam .Toxicol. 38(3):483-490.

9336

Con

Brine Shrimp

645

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Verriopoulos, G.. 1992. Effects of Sublethal Concentrations
of Zinc, Chromium and Copper on the Marine Copepods
Tisbe holothuriae and Acartia clausi. In: G.P.Gabrielides
(Ed.), Proc.of the FAO/UNEP/IOC Workshop on the
Biological Effects of Pollutants on Marine Organisms,

Malta, 10-14 Sept., 1991, UNEP, Athens, Greece, MAP
Tech.Rep.Ser.No.69 :265-275.

4091

UEndp

Viarengo, A., G. Zanicchi, M.N. Moore, and M. Orunesu.
1981. Accumulation and Detoxication of Copper by the
Mussel Mytilus galloprovinicialis Lam.: A Study of the
Subcellular Distribution in the Digestive. Aquat.Toxicol.
1(3/4):147-157.

15415

UEndp

Viarengo, A., L. Canesi, M. Pertica, G. Poli, M.N. Moore,
and M. Orunesu. 1990. Heavy Metal Effects on Lipid
Peroxidation in the Tissues of Mytilus galloprovincialis Lam.
Com p. Biochem. Physiol .C 97(1 ):37-42.

UEndp, Eff

Viarengo, A., M. Pertica, G. Mancinelli, B. Burlando, L.
Canesi, and M. Orunesu. 1996. In Vivo Effects of Copper
on the Calcium Homeostasis Mechanisms of Mussel Gill
Cell Plasma Membranes. Comp.Biochem.Physiol.C
113(3):421-425.

16858

UEndp

Vogt, G., and E.T. Quinitio. 1994. Accumulation and
Excretion of Metal Granules in the Prawn, Penaeus
monodon, Exposed to Water-Borne Copper, Lead, Iron and
Calcium. Aquat.Toxicol. 28(3/4):223-241.

16561

UEndp

Vranken, G., C. Tire, and C. Heip. 1988. The Toxicity of
Paired Metal Mixtures to the Nematode Monhystera
disjuncta (Bastian, 1865). Mar.Environ.Res. 26(3):161-179.

2801

Eff

Wang, J., M. Zhang, J. Xu, and Y. Wang. 1995. Reciprocal
Effect of Cu, Cd, Zn on a Kind of Marine Alga. Water Res.
29(1):209-214.

13720

UEndp

17368

Dur

646

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Waterman, A.J.. 1937. Effect of Salts of Heavy Metals on
Development of the Sea Urchin, Arbacia punctulata.
Biol.Bull. 73(3):401-420.

17763

UEndp

Watling, H.R., and R.J. Watling. 1983. Sandy Beach
Molluscs As Possible Bioindicators of Metal Pollution 2.
Laboratory Studies. Bull.Environ.Contam.Toxicol.
31 (3):339-343.

10862

UEndp

Watling, H.R.. 1983. Accumulation of Seven Metals by
Crassostrea gigas, Crassostrea margaritacea, Perna
perna, and Choromytilus meridionalis.

Bull. Environ.Contam .Toxicol. 30(3):317-322.

7374

UEndp, Eff

Watling, H.R.. 1983. Comparative Study of the Effects of
Metals on the Settlement of Crassostrea gigas.
Bull.Environ.Contam.Toxicol. 31(3):344-351.

11098

UEndp, Con

Weber, R.E., A. De Zwaan, and A. Bang. 1992. Interactive
Effects of Ambient Copper and Anoxic, Temperature and
Salinity Stress on Survival and Hemolymph and Muscle
Tissue Osmotic Effectors in. J.Exp.Mar.BioI.Ecol.
159(2): 135-156.

7501

UChron, Dur

Weeks, J.M., and P.S. Rainbow. 1991. The Uptake and
Accumulation of Zinc and Copper from Solution by Two
Species of Talitrid Amphipods (Crustacea).

J. Mar. Biol .Assoc. U. K. 71 (4):811 -826.

3628

UEndp, Eff

Weis, P.. 1984. Metallothionein and Mercury Tolerance in
the Killifish, Fundulus heteroclitus. Mar.Environ.Res. 14(1 -
4): 153-166.

11357

UEndp

White, S.L., and P.S. Rainbow. 1982. Regulation and
Accumulation of Copper, Zinc and Cadmium by the Shrimp
Palaemon elegans. Mar.Ecol.Prog.Ser. 8(1 ):95-101.

9120

UEndp

15508

UEndp, Con

Wilson, R.W., and E.W. Taylor. 1993. Differential
Responses to Copper in Rainbow Trout (Oncorhynchus
mykiss) Acclimated to Sea Water and Brackish Water.
J.Comp.Physiol.B Biochem.Syst.Environ.Physiol.
163(3):239-246.

4741

UEndp

647

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Wilson, W.B., and L.R. Freeburg. 1980. Toxicity of Metals
to Marine Phytoplankton Cultures. EPA-600/3-80-025,
U.S.EPA, Narragansett, Rl :110 p.(U.S.NTIS PB80-
182843).

5557

Plants do not drive
criteria, and
therefore, are not
included in CWA
review and approval
of ORWQS

Wong, C.K., J.K.Y. Cheung, and K.H. Chu. 1995. Effects of
Copper on Survival, Development and Growth of
Metapenaeus ensis Larvae and Postlarvae (Decapoda:
Penaeidae). Mar.Pollut.Bull. 31(4-12):416-419.

18436

UEndp

Wong, C.K., K.H. Chu, K.W. Tang, T.W. Tam, and L.J.
Wong. 1993. Effects of Chromium, Copper and Nickel on
Survival and Feeding Behaviour of Metapenaeus ensis
Larvae and Postlarvae (Decapoda: Penaeidae).
Mar.Environ.Res. 36(2):63-78.

4127

NonRes

Wong, P.P.K., L.M. Chu, and C.K. Wong. 1999. Study of
Toxicity and Bioaccumulation of Copper in the Silver Sea
Bream Sparus sarba. Environ.Int. 25(4):417-422.

20630

NonRes

Wright, D.A., and C.D. Zamuda. 1987. Copper
Accumulation by Two Bivalve Molluscs: Salinity Effect is
Independent of Cupric Ion Activity. Mar.Environ.Res.
23(1): 1-14.

9147

UEndp

Wright, D.A., and C.D. Zamuda. 1991. Use of Oysters as
Indicators of Copper Contamination in the Patuxent River,
Maryland. Hydrobiologia 222:39-48.

5233

UEndp

Wright, D.A.. 1986. Trace Metal Uptake and Sodium
Regulation in Gammarus marinus From Metal Polluted
Estuaries in England. J.Mar.Biol.Assoc.U.K. 66(1):83-92.

5405

UEndp, Eff, Con

Wu, Z., and G. Chen. 1988. Studies of Acute Intoxication
by Some Harmful Substances on Penaeus orientalis K.
Mar.Sci./Haiyang Kexue (4):36-40 (CHI) (ENG ABS).

3232

NonRes

Young, J.S., R.L. Buschbom, J.M. Gurtisen, and S.P.
Joyce. 1979. Effects of Copper on the Sabellid Polychaete,
Eudistylia vancouveri: I. Concentration Limits for Copper
Accumulation. Arch.Environ.Contam.Toxicol. 8(1):97-106.

15581

UEndp

Bioaccum

648

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment(s)

Young, J.S., R.R. Adee, 1. Piscopo, and R.L. Buschbom.
1981. Effects of Copper on the Sabellid Polychaete,
Eduistylia vancouveri. II. Copper Accumulation and Tissue
Injury in the Brachil Crown. Arch.Environ.Contam.Toxicol.
10(1):87-104.

9510

UEndp

Yuan, Y.X., C.N. Gao, and D.X. Zhang. 1992. Egg
Hatching and Metamorphosis to Protozoea of Penaeus
chinensis (Osbeck) by Removal of Heavy Metals from
Rearing Systems with Polymeric Absorbent. Aquaculture
107:303-311.

7425

UEndp, Dur

Zaroogian, G.E., and M. Johnson. 1983. Copper
Accumulation in the Bay Scallop, Argopecten irradians.
Arch.Environ.Contam.Toxicol. 12(2):127-133.

12988

UEndp

Bioaccum

Zolotukhina, E.Y., E.E. Gavrilenko, and K.S. Burdin. 1987.
Effect of Zinc and Copper Ions on Photosynthesis and
Respiration of Marine Macroalgae. Soviet Plant
Physiol.(Eng.Trans.Fiziol.Rast.) 34(2):212-220.

6673

UEndp, Eff

C. Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

FAV in the most recent national ambient water quality criteria dataset used to derive the CMC , EPA is providing a
transparent rationale as to why they were not utilized (see below).

For the studies that were not utilized because they were not found to be pertinent to this determination (including failing
the QA/QC procedures listed in Appendix A) upon initial review of the download from ECOTOX, EPA is providing the
code that identifies why EPA determined that the results of the study were not reliable.

General QA/QC failure because non-resident species in Oregon

93 U.S. EPA. 1995. Ambient Water Quality Criteria - Saltwater Copper Addendum. U.S. EPA, Narragansett, RI.

649

-------
Tests with the following species were used in the EPA BE of OR WQS for copper in saltwater, but were not considered in the CWA
review and approval/disapproval action of the standards because these species do not have a breeding wild population in Oregon's
waters:

Isognomon

californicum

Purse oysters

Ringwood 1992

Crassostrea

virginica

Eastern oyster

Maclnnes and Calabrese 1978;
Calabarese et al. 1973

Crassostrea

rhizophorae

Mangrove oyster

Chung 1980

Crassostrea

madrasensis

Oyster

Kumaraguru and Ramamoorthi
1978

Crassostrea

cucullata

Oyster

Watling 1982

Mytilus

galloprovincialis

Mediterranean mussel

Taneeva 1973

Other Acute tests failins QA/QC by species
Mytilus spp. — Mussel

City of San Jose. 1998. Toxicities of ten metals to Crassostrea gigas and Mytilus edulis embryos and Cancer magister larvae.
Mar. Pollut. Bull. 12(9): 305-308 (Author Communication Used).

These values were determined to be for Mytilus edulis and used for that species.

Harrison, F.L. 1985. Effect of physicochemical form on copper availability to aquatic organisms. In: R.D. Cardwell, R. Purdy,
and R.C. Bahner (Eds.), Aquatic Toxicology and Hazard Assessment, 7th Symposium, ASTM STP 854, Philadelphia, PA: 469-
484.

This test was not used for determining the most representative SMAV in this CWA review and approval/disapproval action of these
standards because a more sensitive lifestage was available.

Mytilus edulis - Common bay mussel, blue mussel

Nelson, D.A., J.E. Miller and A. Calabrese. 1988. Effect of heavy metals on bay scallops, surf clams, and blue mussels in acute
and long-term exposures. Arch. Environ. Contam. Toxicol. 17(5): 595-600.

This test was not used for determining the most representative SMAV in this CWA review and approval/disapproval action of these
standards because a more sensitive lifestage was available.

650

-------
ToxScan. 1991a. Toxicities of ten metals to Crassostrea gigas and Mytilus edulis embryos and Cancer magister larvae. Mar.
Pollut. Bull. 12(9): 305-308 (Author Communication Used).

Listed as Mytilus edulis in the 1995 Saltwater Addendum and used to calculate ALC SMAV in the 1995 Saltwater Copper Addendum;
not used for WA 3-18 because this value was re-calculated as an IC50 using measured concentrations for low, med and high
concentrations, and interpolated concentrations in between. Some data from this study was used.

Paralichthys dentatus — Summer flounder

Cardin, J.A. 1985. Results of Acute Toxicity Tests Conducted with Copper at ERL, Narragansett. U.S. EPA, Narragansett, RI:
10 p.

This test was not used for determining the most representative SMAV in this CWA review and approval/disapproval action of these
standards because a more sensitive lifestage was available.

CH2M Hill 1999. Bioassay Report Acute Toxicity of Copper to Summer Flounder (Paralichthys dentatus). Prepared for U.S.
Navy, Norfolk, VA.

This test was not used for determining the most representative SMAV in this CWA review and approval/disapproval action of these
standards because a more sensitive lifestage was available.

Mulinia lateralis — Clam

Ho, M.S. and P.L. Zubkoff. 1982. The effects of mercury, copper, and zinc on calcium uptake by larvae of the clam, Mulinia
lateralis. Water Air Soil Pollut. 17(4): 409-414.

This test was not used for determining the most representative SMAV in this CWA review and approval/disapproval action of these
standards because of excessive control mortality.

Other Chronic tests failing QA/QC by species

Mytilus trossulus — Pacific mussel

Karaseva, E.M. and L.A. Medvedeva. 1993. Morphological and functional changes in the offspring of Mytilus trossulus and
Mizuhopecten yessoensis after parental exposure to copper and zinc. Russ. J. Mar. Biol. 19(4): 276-280; Biol. Morya
(Vladivost) (4): 83-89 (RUS).

651

-------
This test was not used in this CWA review and approval/disapproval action of these standards because it was not a life-cycle test.

652

-------
Appendix Q Lead (Saltwater)

Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comments

Alcutt, F., and J.T. Pinto. 1994. Glutathione Concentrations in the Hard Clam,
Mercenaria mercenaria, Following Laboratory Exposure to Lead (a Potential
Model System for Evaluating. Comp.Biochem.Physiol.C 107(3):347-352.

14073

UEndp

Almeida, M.J., G. Moura, T. Pinheiro, J. Machado, and J. Coimbra. 1998.
Modifications in Crassostrea gigas Shell Composition Exposed to High
Concentrations of Lead. Aquat.Toxicol. 40(4):323-334.

17349

UEndp

Benijts-Claus, C., and F. Benijts. 1975. The Effect of Low Lead and Zinc
Concentrations on the Larval Development of the Mud-Crab Rhithropanopeus
harrisii Gould. In: J.H.Koeman and J.J.T.W.A.Strik (Eds.), Sublethal Effects of
Toxic Chemicals on Aquat.Animals, Elsevier Sci.Publ., Amsterdam, NY :43-52.

15451

UEndp

Blasco, J., and J. Puppo. 1999. Effect of Heavy Metals (Cu, Cd and Pb) on
Aspartate and Alanine Aminotransferase in Ruditapes phillippinarum (Mollusca:
Bivalvia). Comp.Biochem.Physiol.C 122(2):253-263.

20072

Eff

Brown, B., and M. Ahsanullah. 1971. Effect of Heavy Metals on Mortality and
Growth. Mar.Pollut.Bull. 2:182-187.

2467

Burdin, K.S., and K.T. Bird. 1994. Heavy Metal Accumulation by Carrageenan
and Agar Producing Algae. Bot.Mar. 37:467-470.

45156

UEndp

653

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comments

Canli, M., and R.W. Furness. 1993. Toxicity of Heavy Metals Dissolved in Sea
Water and Influences of Sex and Size on Metal Accumulation and Tissue
Distribution in the Norway Lobster. Mar.Environ.Res. 36(4):217-236.

4563

UEndp

Canterford, G.S., A.S. Buchanan, and S.C. Ducker. 1978. Accumulation of
Heavy Metals by the Marine Diatom Ditylum brightwellii (West) Grunow.
Aust.J.Mar.Freshwater Res. 29(5):613-622.

15455

UEndp

Chinni, S., R.N. Khan, and P.R. Yallapragada. 2000. Oxygen Consumption,
Ammonia-N Excretion, and Metal Accumulation in Penaeus indicus Postlarvae
Exposed to Lead. Bull.Environ.Contam.Toxicol. 64(1): 144-151.

48202

UEndp

Congiu, A.M., E. Calendi, and G. Ugazio. 1984. Effects of Metal Ions and CCI4

on Sea Urchin Embryo (Paracentrotus lividus).

Res.Commun.Chem.Pathol.Pharmacol. 43(2):317-323.

625

UEndp

Cui, K„ Y. Liu, and L. Hou. 1987. . .

3222

NonRes

Denton, G.R.W., and C. Burdon-Jones. 1981. Influence of Temperature and
Salinity on the Uptake, Distribution and Depuration of Mercury, Cadmium and
Lead by the Black-Lip Oyster Saccostrea echinata. Mar.Biol. 64:317-326.

14335

UEndp

Denton, G.R.W., and C. Burdon-Jones. 1986. . .

4327

NonRes

Domouhtsidou, G.P., and V.K. Dimitriadis. 2000. Ultrastructural Localization of
Heavy Metals (Hg,Ag,Pb, and Cu) in Gills and Digestive Gland of Mussels,
Mytilus galloprovincialis (L.). Arch.Environ.Contam.Toxicol. 38(4):472-478.

48771

UEndp

Eldon, J., M. Pekkarinen, and R. Kristoffersson. 1980. Effects of Low
Concentrations of Heavy Metals on the Bivalve Macoma balthica.
Ann.Zool.Fenn. 17:233-242.

17309

UEndp

654

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comments

Elliott, N.G., R. Swain, and D.A. Ritz. 1985. The Influence of Cyclic Exposure on
the Accumulation of Heavy Metals by Mytilus edulis planulatus (Lamarck).
Mar. Environ. Res. 15(1 ):17-30.

11669

UEndp

Fernandez Leborans, G., Y.O. Herrero, and A. Novillo. 1998. Toxicity and
Bioaccumulation of Lead in Marine Protozoa Communities.
Ecotoxicol.Environ.Saf. 39(3): 172-178.

19269

UEndp

Fernandez-Leborans, G., and A. Novillo. 1992. Hazard Evaluation of Lead
Effects Using Marine Protozoan Communities. Aquat.Sci. 54(2): 128-140.

6208

UEndp

Fernandez-Leborans, G., and A. Novillo. 1994. Effects of Periodic Addition of
Lead on a Marine Protistan Community. Aquat.Sci. 56(3): 191-205.

14135

UEndp

Fisher, N.S., V.T. Breslin, and M. Levandowsky. 1995. Accumulation of Silver
and Lead in Estuarine Microzooplankton. Mar.Ecol.Prog.Ser. 116(1-3):207-215.

17381

Eff

Gould, E., and R.A. Greig. 1983. Short-Term Low-Salinity Response in Lead-
Exposed Lobsters, Homarus americanus (Milne Edwards). J.Exp.Mar.BioI.Ecol.
69:283-295.

14609

UEndp

Gray, J.S., and R.J. Ventilla. 1973. Growth Rates of Sediment-Living Marine
Protozoan as a Toxicity Indicator for Heavy Metals. Ambio 2(4): 118-121.

6355

UEndp

Gray, J.S.. 1974. Synergistic Effects of Three Heavy Metals on Growth Rates of
a Marine Ciliate Protozoan. In: F.J.Vernberg and W.B.Vernberg (Eds.), Pollution
and Physiology of Marine Organisms, Academic Press, NY :465-485.

8558

UEndp

Haglund, K., M. Bjorklund, S. Gunnare, A. Sandberg, U. Olander, and M.
Pedersen. 1996. . .

18453

NonRes

655

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comments

Haritonidis, S.. 1985. Uptake of Cd, Zn, Cu and Pb by Marine Macrophyceae
Under Culture Conditions. Mar.Environ.Res. 17(2-4):198-199.

6414

UEndp

Hessler, A.. 1975. The Effects of Lead on Algae. II. Mutagenesis Experiments on
Platymonas sabcordiformis (Chlorophyta: Volvocales). Mutat.Res. 31(1):43-47.

15840

UEndp

Hollibaugh, J.T., D.L.R. Seibert, and W.H. Thomas. 1980. A Comparison of the
Acute Toxicities of Ten Heavy Metals to Phytoplankton From Saanich Inlet, B.C.,
Canada. Estuar.Coast.Mar.Sci. 10(1):93-105.

5282

UEndp

Ikuta, K.. 1987. Localization of Heavy Metals in the Viscera and the Muscular
Tissues of Haliotis discus Exposed to Selected Metal Concentration Gradients.
Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan Gakkaishi) 53(12):2269-2274.

3215

UEndp

Ithack, E., and C.P. Gopinathan. 1995. The Effect of Heavy Metals on the
Physiological Changes of Microalgae. Cmfri Spec.Publ. 61:45-52.

19399

UEndp

Itow, T., R.E. Loveland, and M.L. Botton. 1998. Developmental Abnormalities in
Horseshoe Crab Embryos Caused by Exposure to Heavy Metals.
Arch.Environ.Contam.Toxicol. 35(1):33-40.

19470

UEndp

Itow, T., T. Igarashi, M.L. Botton, and R.E. Loveland. 1998. Heavy Metals Inhibit
Limb Regeneration in Horseshoe Crab Larvae. Arch.Environ.Contam.Toxicol.
35(3):457-463.

20180

UEndp

Karbe, L.. 1972. Marine Hydroids as Test Organisms for Assessing the Toxicity
of Water Pollutants. The Effect of Heavy Metals on Colonies of Eirene viridula.
Mar.Biol. 12(4):316-328 (GER) (ENG ABS).

15654

UEndp

Khan, I.A., and P. Thomas. 2000. Lead and Aroclor 1254 Disrupt Reproductive
Neuroendocrine Function in Atlantic Croaker. Mar.Environ.Res. 50:119-123.

56608

UEndp

656

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comments

Lakshmanan, P.T., and P.N.K. Nambisan. 1989. Bioaccumulation and
Depuration of Some Trace Metals in the Mussel, Perna viridis (Linnaeus).
Bull.Environ.Contam.Toxicol. 43(1 ):131-138.

3240

Eff

Lorenzon, S., M. Francese, and E.A. Ferrero. 2000. . .

51641

NonRes

Lussier, S.M., W.S. Boothman, S. Poucher, D. Champlin, and A. Helmstetten.
1999. Comparison of Dissolved and Total Metals Concentrations from Acute
Tests with Saltwater Organisms. Environ.Toxicol.Chem. 18(5):889-898.

51695

UEndp

Mathew, R., and N.R. Menon. 1983. Oxygen Consumption in Tropical Bivalves
Perna viridis (Linn.) and Meretrix casta (Chem.) Exposed to Heavy Metals.
Indian J.Mar.Sci. 12(1):57-59.

11085

UEndp

Odzak, N., and T. Zvonaric. 1995. Cadmium and Lead Uptake from Food by the
Fish Dicentrarchus labrax. Water Sci.Technol. 32(9/10):49-55.

18263

UEndp

Odzak, N., D. Martincic, T. Zvonaric, and M. Branica. 1994. Bioaccumulation
Rate of Cd and Pb in Mytilus galloprovincialis Foot and Gills. Mar.Chem.
46(1 /2): 119-131.

16644

UEndp

Okamoto, O.K., L. Shao, J.W. Hastings, and P. Colepicolo. 1999. Acute and
Chronic Effects of Toxic Metals on Viability, Encystment and Bioluminescence in
the Dinoflagellate Gonyaulax polyedra. Comp.Biochem.Physiol.C 123(1):75-83.

20347

UEndp

Parker, J.G.. 1984. The Effects of Selected Chemicals and Water Quality on the
Marine Polychaete Ophryotrocha diadema. Water Res. 18(7):865-868.

10890

Dur

A 48hr LC50 for a Polychaete

5922

UEndp

657

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comments

Phillips, D.J.H.. 1976. The Common Mussel Mytilus edulis As an Indicator of
Pollution by Zinc, Cadmium, Lead and Copper. I. Effects of Environmental
Variables on Uptake of. Mar.Biol. 38(1):59-69.

15633

UEndp

Phinney, J.T., and K.W. .Bruland. 1994. Uptake of Lipophilic Organic Cu, Cd,
and Pb Complexes in the Coastal Diatom Thalassiosira weissflogii.
Environ.Sci.Technol. 28(11): 1781-1790.

45097

UEndp

Prakash, N.T., and K.S.J. Rao. 1995. Modulations in Antioxidant Enzymes in
Different Tissues of Marine Bivalve Perna viridis During Heavy Metal Exposure.
Mol.Cell.Biochem. 146(2): 107-113.

17902

UEndp

Pringle, B.H., D.E. Hissong, E.L. Katz, and S.T. Mulawka. 1968. Trace Metal
Accumulation by Estuarine Mollusks. J.Sanit.Eng.Div.Proc.Am.Soc.Civ.Eng.
94:455-475.

58894

UEndp

Ralph, P.J., and M.D. Burchett. 1998. Photosynthetic Response of Halophila
ovalis to Heavy Metal Stress. Environ.Pollut. 103(1 ):91 -101.

19866

UEndp

Reish, D.J., and R.S. Carr. 1978. The Effect of Heavy Metals on the Survival,
Reproduction, Development and Life Cycles for Two Species of Polychaetous
Annelids. Mar.Pollut.Bull. 9(1):24-27.

8428

UEndp

Rivkin, R.B.. 1979. Effects of Lead on Growth of the Marine Diatom
Skeletonema costatum. Mar.Biol. 50:239-247.

58891

Dur, UChron

Schulz-Baldes, M., and R.A. Lewin. 1976. Lead Uptake in Two Marine
Phytoplankton Organisms. Biol.Bull. 150(1 ):118-127.

2244

UEndp

Schulz-Baldes, M.. 1974. Lead Uptake From Sea Water and Food, and Lead
Loss in the Common Mussel Mytilus edulis. Mar.Biol. 25(3):177-193.

8707

UEndp

658

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comments

Soria-Dengg, S., and D. Ochavillo. 1990. Comparative Toxicities of Trace Metals
on Embryos of the Giant Clam, Tridacna derasa. Asian Mar.Biol. 7:161-166.

20706

UEndp

Stroemgren, T.. 1980. The Effect of Lead, Cadmium, and Mercury on the
Increase in Length of Five Intertidal Fucales. J.Exp.Mar.Biol.Ecol. 43(2): 107-119.

9902

UEndp

Stromgren, T.. 1980. The Effect of Lead, Cadmium, and Mercury on the Increase
in Length of Five Intertidal Fucales. J.Exp.Mar.Biol.Ecol. 43:107-119.

19931

UEndp

Stromgren, T.. 1982. Effect of Heavy Metals (Zn, Hg, Cu, Cd, Pb, Ni) on the
Length Growth of Mytilus edulis. Mar.Biol. 72(1):69-72.

10899

UEndp

Sun, Y., and C. Chen. 1988. Effects of Hg, Zn, Pb on Embryonic Development of
Black Progy, Sparus macrocephalus Basilewsky. Mar.Sci./Haiyang Kexue
(3):54-57 (CHI) (ENG ABS).

3371

UEndp

Tan, W.H., and L.H. Lim. 1984. The Tolerance to and Uptake of Lead in the
Green Mussel, Perna viridis (L.). Aquaculture 42(3-4):317-332.

10857

Eff, Dur

Has two 7d LC50's for green mussels

Thomas, P.. 1988. Reproductive Endocrine Function in Female Atlantic Croaker
Exposed to Pollutants. Mar.Environ.Res. 24(1-4): 179-183.

13127

UEndp

Thomas, P.. 1990. Teleost Model for Studying the Effects of Chemicals on
Female Reproductive Endocrine Function. J.Exp.Zool.(Suppl. 4):126-128.

8682

UEndp

Tolba, M.R., A.E. Hagras, and A. Hilmy. 1995. Effect of Some Heavy Metals on
the Growth of Sphaeroma serratum (Crustacea: Isopoda). J.Environ.Sci.
10(1 ):219-231.

45118

UEndp

Udoidiong, O.M., and P.M. Akpan. 1991. . .

8515

NonRes

659

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comments

Varanasi, U., and D. Markey. 1978. Uptake and Release of Lead and Cadmium
in Skin and Mucus of Coho Salmon (Oncorhynchus kisutch).

Com p. Biochem. Physiol. 60C: 187-191 (1978) / Fed.Proc. 36(3):772 (ABS) (1977)
(Author Communication Used).

15121

Eff

Varanasi, U.. 1978. Biological Fate of Metals in Fish. In: D.A.Wolfe (Ed.), Marine
Biological Effects of OCS Petroleum Development, NOAA ERL, Boulder, CO
:41-53.

5209

Eff, UEndp

Vogt, G., and E.T. Quinitio. 1994. Accumulation and Excretion of Metal Granules
in the Prawn, Penaeus monodon, Exposed to Water-Borne Copper, Lead, Iron
and Calcium. Aquat.Toxicol. 28(3/4):223-241.

16561

UEndp

Watling, H.R., and R.J. Watling. 1983. Sandy Beach Molluscs As Possible
Bioindicators of Metal Pollution 2. Laboratory Studies.
Bull.Environ.Contam.Toxicol. 31(3):339-343.

10862

UEndp

Watling, H.R.. 1983. Accumulation of Seven Metals by Crassostrea gigas,
Crassostrea margaritacea, Perna perna, and Choromytilus meridionalis.
Bull.Environ.Contam.Toxicol. 30(3):317-322.

7374

UEndp

Watling, H.R.. 1983. Comparative Study of the Effects of Metals on the
Settlement of Crassostrea gigas. Bull.Environ.Contam.Toxicol. 31 (3):344-351.

11098

UEndp

Weis, J.S.. 1976. Effects of Mercury, Cadmium, and Lead Salts on Regeneration
and Ecdysis in the Fiddler Crab, Uca pugilator. Fish.Bull. 74(2):464-467.

8044

UEndp

Weis, P., and J.S. Weis. 1982. Toxicity of Methylmercury, Mercuric Chloride, and
Lead in Killifish (Fundulus heteroclitus) From Southampton, New York.
Environ.Res. 28(2):364-374.

15614

UEndp

660

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comments

Woolery, M.L., and R.A. Lewin. 1976. The Effects of Lead on Algae IV . Effects
of Pb on Respiration and Photosynthesis of Phaeodactylum tricornutum
(Bacillariophyceae). Water Air Soil Pollut. 6(1):25-31.

15972

UEndp

Wu, Z„ and G. Chen. 1988. . .

3232

NonRes

Yan, T., L.H. Teo, and Y.M. Sin. 1997. Effects of Mercury and Lead on Tissue
Glutathione of the Green Mussel, Perna viridis L. Bull.Environ.Contam.Toxicol.
58:845-850.

17980

UEndp

Yuan, Y.X., C.N. Gao, and D.X. Zhang. 1992. Egg Hatching and Metamorphosis
to Protozoea of Penaeus chinensis (Osbeck) by Removal of Heavy Metals from
Rearing Systems with Polymeric Absorbent. Aquaculture 107:303-311.

7425

UEndp

24hr only

Zaroogian, G.E., G. Morrison, and J.F. Heltshe. 1979. Crassostrea virginica as
an Indicator of Lead Pollution. Mar.Biol. 52(2): 189-196.

15704

UEndp

Zimmermann, S., B. Sures, and H. Taraschewski. 1999. Experimental Studies
on Lead Accumulation in the Eel-Specific Endoparasites Anguillicola crassus
(Nematoda) and Paratenuisentis ambiguus (Acanthocephala) as Compared with
Their Host, Anguilla anguilla. Arch.Environ.Contam.Toxicol. 37(2): 190-195.

20449

UEndp

Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

661

-------
in the most recent national ambient water quality criteria dataset used to derive the CMC94, EPA is providing a transparent
rationale as to why they were not utilized (see below).

For the studies that were not utilized because they were not found to be pertinent to this determination (including failing the
QA/QC procedures listed in Appendix A) upon initial review of the download from ECOTOX, EPA is providing the code
that identifies why EPA determined that the results of the study were not reliable.

General QA/QC failure because non-resident species in Oregon

Tests with the following species were used in the EPA BE of OR WQS for lead in saltwater, but were not considered in the CWA
review and approval/disapproval action of the standards because these species do not have a breeding wild population in Oregon's
waters:

Fundulus

heteroclitus

Mummichog

Dorfman 1977; Jackim et al. 1970

Cancer

anthonyi

Yellow rock crab

MacDonald et al. 1988

Mytilus

galloprovincialis

Mediterranean mussel

Taneeva1973

Ampelisca

abdita

Amphipod

Scott et al. 1982

94 U.S. EPA. 1984. Ambient Water Quality Criteria Documents for Lead. EPA-440/5-84-027.

662

-------
Appendix R Nickel (Saltwater)
Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Ahsanullah, M.. 1982. Acute Toxicity of Chromium, Mercury, Molybdenum and Nickel
to the Amphipod Allorchestes compressa. Aust.J.Mar.Freshwater Res. 33(3):465-
474.

10628

NonRes

Calabrese, A., J.R. Maclnnes, D.A. Nelson, and J.E. Miller. 1977. Survival and
Growth of Bivalve Larvae Under Heavy-Metal Stress. Mar.Biol. 41:179-184.

9064

Con, UChron

Cardin, J.A.. 1985. Results of Acute Toxicity Tests Conducted with Nickel at ERL,
Narragansett. U.S.EPA, Narragansett, Rl :1.

3755

See Note

Duplicate data to Gentile and Cardin 1982

Darmono, G.R.W.D., and R.S.F. Campbell. 1990. The Pathology of Cadmium and
Nickel Toxicity in the Banana Shrimp (Penaeus merguiensis de Man). Asian Fish.Sci.
3(3):287-297.

9711

UEndp

Denton, G.R.W., and C. Burdon-Jones. 1986. Environmental Effects on Toxicity of
Heavy Metals to Two Species of Tropical Marine Fish from Northern Australia.
Chem.Ecol. 2(3):233-249.

4327

NonRes

Eisler, R.. 1977. Acute Toxicities of Selected Heavy Metals to the Softshell Clam,
Mya arenaria. Bull.Environ.Contam.Toxicol. 17(2):137-145.

2166

Con, UChron

Eldon, J., M. Pekkarinen, and R. Kristoffersson. 1980. Effects of Low Concentrations
of Heavy Metals on the Bivalve Macoma balthica. Ann.Zool.Fenn. 17:233-242.

17309

Con

Haglund, K., M. Bjorklund, S. Gunnare, A. Sandberg, U. Olander, and M. Pedersen.
1996. New Method for Toxicity Assessment in Marine and Brackish Environments
Using the Macroalga Gracilaria tenuistipitata (Gracilariales, Rhodophyta).
Hydrobiologia 326/327:317-325.

18453

NonRes

Haley, M.V., and C.W. Kurnas. 1993. Aquatic Toxicity and Fate of Nickel Coated
Graphite Fibers, with Comparisons to Iron and Aluminum Coated Glass Fibers.
Rep.No.ERDEC-TR-090, Edgewood Res.Dev.Eng.Center, Aberdeen Proving
Ground, MD:19 p.(U.S.NTIS AD-A270/411/2).

4939

See Note

ECOTOX provides one 96-h LC50 of 5346 |jg/L for
this study. These values could have been considered
for EPA's evaluation of saltwater nickel, but the
species is relatively insensitive to nickel compared to
others.

663

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Krishnakumari, L.P.K.V., S.N. Gajbhiye, K. Govindan, and V.R. Nair. 1983. Toxicity of
Some Metals on the Fish Therapon jarbua (Forsskal, 1775). Indian J.Mar.Sci.
12(1):64-66.

11014

NonRes

Lee, H.H., and C.H. Xu. 1984. Effects of Metals on Sea Urchin Development: A Rapid
Bioassay. Mar.Pollut.Bull. 15(1 ):18-21.

10086

Dur, UEndp

Lussier, S.M., and J. Walker. 1985. Results of Acute Toxicity Tests Conducted with
Nickel at ERL, Narragansett. U.S.EPA, Narragansett, Rl :2.

3828

UEndp

Duplicate data to Gentile and Cardin 1982

Mortimer, M.R., and G.J. Miller. 1994. Susceptibility of Larval and Juvenile Instars of
the Sand Crab, Portunus pelagicus (L.), to Sea Water Contaminated by Chromium,
Nickel or Copper. Aust.J.Mar.Freshwater Res. 45(7): 1107-1121.

16331

NonRes

Pesch, C.E., D.J. Hansen, W.S. Boothman, W.J. Berry, and J.D. Mahony. 1995. The
Role of Acid-Volatile Sulfide and Interstitial Water Metal Concentrations in
Determining Bioavailability of Cadmium and Nickel from Contaminated.
Environ.Toxicol.Chem. 14(1): 129-141.

18028

Dur

Stromgren, T.. 1982. Effect of Heavy Metals (Zn, Hg, Cu, Cd, Pb, Ni) on the Length
Growth of Mytilus edulis. Mar.Biol. 72(1):69-72.

10899

UEndp

Taylor, D., B.G. Maddock, and G. Mance. 1985. The Acute Toxicity of Nine "Grey
List" Metals (Arsenic, Boron, Chromium, Copper, Lead, Nickel, Tin, Vanadium and
Zinc) to Two Marine Fish Species:. Aquat.Toxicol. 7(3):135-144.

11451

NonRes

Verriopoulos, G., and S. Dimas. 1988. Combined Toxicity of Copper, Cadmium, Zinc,
Lead, Nickel, and Chrome to the Copepod Tisbe holothuriae.
Bull.Environ.Contam.Toxicol. 41 (3):378-384.

13179

NonRes

Wilson, W.B., and L.R. Freeburg. 1980. Toxicity of Metals to Marine Phytoplankton
Cultures. EPA-600/3-80-025, U.S.EPA, Narragansett, Rl :110 p.(U.S.NTIS PB80-
182843).

5557

NonRes

Wong, C.K., K.H. Chu, K.W. Tang, T.W. Tam, and L.J. Wong. 1993. Effects of
Chromium, Copper and Nickel on Survival and Feeding Behaviour of Metapenaeus
ensis Larvae and Postlarvae (Decapoda: Penaeidae). Mar.Environ.Res. 36(2):63-78.

4127

NonRes

Studies That EPA Considered But Did Not Utilize In This Determination

664

-------
EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

3) For the studies that were not utilized, but the most representative SMAV/2 or most representative SMCV fell below the
criterion, or, if the studies were for a species associated with one of the four most sensitive genera used to calculate the
FAV in the most recent national ambient water quality criteria dataset used to derive the CMC95, EPA is providing a
transparent rationale as to why they were not utilized (see below).

4) For the studies that were not utilized because they were not found to be pertinent to this determination (including failing
the QA/QC procedures listed in Appendix A) upon initial review of the download from ECOTOX, EPA is providing the
code that identifies why EPA determined that the results of the study were not reliable (see Appendix R).

General QA/QC failure because non-resident species in Oregon

Tests with the following species were used in the EPA BE of OR WQS for nickel in saltwater, but were not considered in the CWA
review and approval/disapproval action of the standards because these species do not have a breeding wild population in Oregon's
waters:

Mysidopsis

intii

Shrimp

Hunt et al. 2002

Heteromysis

formosa

Opossom shrimp

Gentile and Cardin 1982

Mercenaria

mercenaria

Northern quahog or hard clam

Calabrese and Nelson 1974

Americamysis

bahia

Opossom shrimp

Gentile and Cardin 1982; Ho et al. 1999

Americamysis

bigelowi

Shrimp

Gentile and Cardin 1982

Crassostrea

virginica

Eastern oyster

Calabrese et al. 1973

95 U.S. EPA. 1986. Ambient Water Quality Criteria for Nickel - 1986. EPA 440-5-86-004.

665

-------
Appendix S Pentachlorophenol (Saltwater)

Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

"Anderson, B.S., and J.W. Hunt". 1988. "Bioassay Methods for
Evaluating the Toxicity of Heavy Metals, Biocides and Sewage
Effluent Using Microscopic Stages of Giant Kelp Macrocystis
pyrifera". Mar.Environ.Res. 26(2):113-134.

2349

UEndp

Has a 48hr NOEC for Giant Kelp

"Anderson, R.S., C.S. Giam, and L.E. Ray". 1984. Effects of
Hexachlorobenzene and Pentachlorophenol on Cellular and
Humoral Immune Parameters in Glycera dibranchiata.
Mar. Environ. Res. 14(1 -4):317-326.

11040

UEndp, Eff

"Anderson, R.S., C.S. Giam, L.E. Ray, and M.R. Tripp". 1981.
Effects of Environmental Pollutants on Immunological
Competency of the Clam Mercenaria mercenaria: Impaired
Bacterial Clearance. Aquat.Toxicol. 1:187-195.

15061

UEndp, Eff

"Benner, D.B., and R.S. Tjeerdema". 1993. Toxicokinetics and
Biotransformation of Pentachlorophenol in the Topsmelt
(Atherinops affinis). J.Biochem.Toxicol. 8(3):111-117.

4100

Eff, Dur

24hr only

"Brannon, A.C., and P.J. Conklin". 1978. "Effect of Sodium
Pentachlorophenate on Exoskeletal Calcium in the Grass
Shrimp, Palaemonetes pugio". "In: K.R.Rao (Ed.),
Pentachlorophenol: Chemistry, Pharmacology and Environmental
Toxicology, Plenum Press, NY :205-211".

45291

UEndp, Eff, Dur

"Cantelmo, A.C., P.J. Conklin, F.R. Fox, and K.R. Rao". 1978.
"Effects of Sodium Pentachlorophenate and 2,4-Dinitrophenol on
Respiration in Crustaceans". "In: K.R.Rao (Ed.),
Pentachlorophenol: Chemistry, Pharmacology and Environmental
Toxicology, Plenum Press, New York, NY :251-263".

7018

UEndp, Eff, Dur

666

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

"Cantelmo, F.R., and K.R. Rao". 1978. Effect of
Pentachlorophenol (PCP) on Meiobenthic Communities
Established in an Experimental System. Mar.Biol. 46(1):17-22.

7020

UEndp

"Cantelmo, F.R., and K.R. Rao". 1978. Effects of
Pentachlorophenol on the Meiobenthic Nematodes in an
Experimental System. "In: K.R.Rao (Ed.), Pentachlorophenol:
Chemistry, Pharmacology, and Environmental Toxicology,
Plenum Press, New York, NY :165-174".

7021

UEndp

"Carr, R.S., and J.M. Neff. 1981. Biochemical Indices of Stress
in the Sandworm Neanthes virens (Sars). I. Responses to
Pentachlorophenol. Aquat.Toxicol. 1:313-327.

13867

UEndp, Eff, Dur

"Carr, R.S., M.D. Curran, and M. Mazurkiewicz". 1986.
Evaluation of the Archiannelid Dinophilus gyrociliatus for Use in
Short-Term Life-Cycle Toxicity Tests. Environ.Toxicol.Chem.
5(7):703-712.

11940

NonRes, UEndp, Dur

"Conklin, P.J., and K.R. Rao". 1977. "Toxicity of Sodium
Pentachlorophenate to the Grass Shrimp, Palaemonetes pugio,
in Relation to the Molt Cycle". "In: K.R.Rao (Ed.),
Pentachlorophenol: Chemistry, Pharmacology, and
Environmental Toxicology, Plenum Press, New York, NY : 181 -
192".

6674

UEndp

"Cook, W.L., D. Fielder, and A.W. Bourquin". 1980. "Succession
of Microfungi in Estuarine Microcosms Perturbed by Carbaryl,
Methyl Parathion and Pentachlorophenol". Bot.Mar. 23:129-131.

15421

UEndp

"Crawford, R.B., and A.M. Guarino". 1976. Sand Dollar Embryos
as Monitors of Environmental Pollutants. Bull.Mt.Desert
Isl.Biol.Lab. 16:17.

13938

UEndp, Dur

"Crawford, R.B., and A.M. Guarino". 1985. Effects of
Environmental Toxicants on Development of a Teleost Embryo.
J.Environ.Pathol.Toxicol. 6:185-194.

14348

UEndp

667

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

"Dimick, R.E., and W.P. Breese". 1965. Bay Mussel Embryo
Bioassay. "Proc.12th Pacific Northwest Ind.Waste Conf.,
University of Washington, Seattle, W A: 165-175".

3758

UEndp, Dur

"Doughtie, D.G., and K.R. Rao". 1978. "Ultrastructural Changes
Induced by Sodium Pentachlorophenate in the Grass Shrimp,
Palaemonetes pugio, in Relation to the Molt Cycle". "In: K.R.Rao
(Ed.), Pentachlorophenol: Chemistry, Pharmacology and
Environmental Toxicology, Plenum Press, NY :213-250".

45293

UEndp, Eff, Dur

"Erickson, S.J.". 1980. Unpublished Laboratory Data. "U.S.EPA,
Gulf Breeze, FL :8".

3652

UEndp, Eff, Dur

"Erickson, S.J.". 1981. Inhibition of Photosynthesis in Estuarine
Phytoplankton by Mixtures of Copper and Pentachlorophenol.
"Unpublished Manuscript, U.S.EPA, Gulf Breeze, F L:11".

4802

UEndp, Eff, Dur

"Erickson, S.J., and A.E. Freeman". 1978. Toxicity Screening of
Fifteen Chlorinated and Brominated Compounds Using Four
Species of Marine Phytoplankton. "In: R.L.Jolley, H.Gorchev, and
D.H.Hamilton (Eds.), Water Chlorination: Environmental Impact
and Health Effects, Ann Arbor Sci.Publ., Ann Arbor, Ml 2:307-
310".

13851

UEndp, Eff, Dur

"Ernst, W.". 1979. Factors Affecting the Evaluation of Chemicals
in Laboratory Experiments Using Marine Organisms.
Ecotoxicol.Environ.Saf. 3:90-93.

3709

Eff

"Faas, L.F., and J.C. Moore". 1979. Determination of
Pentachlorophenol in Marine Biota and Sea Water by Gas-Liquid
Chromatography and High-Pressure Liquid Chromatography.
J.Agric.Food Chem. 27(3):554-557.

13807

UEndp, Eff

"Folke, J., J. Birklund, A.K. Sorensen, and U. Lund". 1983. The
Impact on the Ecology of Polychlorinated Phenols and Other
Organics Dumped at the Bank of a Small Marine Inlet.
Chemosphere 12(9/10): 1169-1181.

14232

Field, UEndp, Eff

668

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

"Gates, V.L., and R.S. Tjeerdema". 1993. Disposition and
Biotransformation of Pentachlorophenol in the Striped Bass
(Morone saxatilis). Pestic.Biochem.Physiol. 46(2): 161-170.

9658

Eff, Dur

"Goerke, H.". 1984. Testing the Fate of Xenobiotics in Nereis
diversicolor and Nereis virens (Polychaeta). "In: Persoone,G.,
E.Jaspers, and C.CIaus (Eds.), Ecotoxicol.Testing for the
Mar.Environ., State Univ.Ghent and Inst.Mar.Sci.Res., Bredene,
Belgium 2:53-66".

4027

UEndp.Eff

"Hansen, D.J., and M.E. Tagatz". 1980. A Laboratory Test for
Assessing Impacts of Substances on Developing Communities of
Benthic Estuarine Organisms. "In: J.G.Eaton, P.R.Parrish, and
A.C.Hendricks (Eds.), Aquatic Toxicology, ASTM STP 707,
Philadelphia, PA :40-57".

14007

UEndp

"Helmstetter, M.F., and lii". 1995. Passive Trans-Chorionic
Transport of Toxicants in Topically Treated Japanese Medaka
(Oryzias latipes) Eggs. Aquat.Toxicol. 32(1): 1 -13.

14875

UEndp, Eff, Dur

"Helmstetter, M.F., and lii". 1995. Toxic Responses of Japanese
Medaka (Oryzias latipes) Eggs Following Topical and Immersion
Exposures to Pentachlorophenol. Aquat.Toxicol. 32(1):15-29.

14876

RouExp, Dur

One or two values look okay

"Hiatt, R.W., J.J. Naughton, and D.C. Matthews". 1953. "Effects
of Chemicals on a Schooling Fish, Kuhlia sandvicensis". Biol.Bull.
104:28-44.

10010

UEndp, Eff, Dur

"Hori, H., M. Tateishi, K. Takayanagi, and H. Yamada". 1996.
Applicability of Artificial Seawater as a Rearing Seawater for
Toxicity Tests of Hazardous Chemicals by Marine Fish Species.
Nippon Suisan Gakkaishi /Bull.Jpn.Soc.Sci.Fish.(4):614-622
(JPN) (ENG ABS).

16999

NonRes, Dur

669

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

"Kaitala, S., and V.N. Maximov". 1986. The Desirability Function
in Evaluation of the Response of Phytoplankton Communities to
Toxicants. Toxic.Assess. 1 (1 ):85-101.

11846

Field, UEndp

"Kobayashi, K., H. Akitake, and T. Tomiyama". 1969. "Studies on
the Metabolism of Pentachlorophenate, a Herbicide in Aquatic
Organisms I. Turnover of Absorbed PCP in Tapes philippinarum".
Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan Gakkaishi) 35(12):1179-
1183 (JPN) (ENGABS).

3667

UEndp, Eff, Dur

"Kobayashi, K., Y. Oshima, S. Hamada, and C. Taguchi". 1987.
Induction of Phenol-Sulfate Conjugating Activity by Exposure to
Phenols and Duration of Its Induced Activity in Short-Necked
Clam. Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan Gakkaishi)
53(11):2073-2076.

3216

UEndp, Eff, Dur

"Krajnovic-Ozretic, M., and B. Ozretic". 1987. Specific Alteration
of Transaminases in Marine Organisms Under Pollution Impact.
"In: W.B.Vernberg, A.Calabrese, F.P.Thurberg, and F.J.Vernberg
(Eds.), Pollution Physiology of Estuarine Organisms :207-230".

13582

UEndp, Eff, Dur

"Kusk, K.O., and N. Nyholm". 1991. Evaluation of a
Phytoplankton Toxicity Test for Water Pollution Assessment and
Control. Arch.Environ.Contam.Toxicol. 20(3):375-379.

163

Eff, Dur

"Linden, E., B.E. Bengtsson, 0. Svanberg, and G. Sundstrom".
1979. "The Acute Toxicity of 78 Chemicals and Pesticide
Formulations Against Two Brackish Water Organisms, the Bleak
(Alburnus alburnus) and the Harpacticoid". Chemosphere
8(11/12):843-851 (Author Communication Used) (OECDG Data
File).

5185

NonRes

Has a 96hr LC50 for Harpacticoid copepod

670

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

"Martello, L.B., R.S. Tjeerdema, W.S. Smith, R.J. Kauten, and
D.G. Crosby". 1998. Influence of Salinity on the Actions of
Pentachlorophenol in Haliotis as Measured by In Vivo 31P NMR
Spectroscopy. Aquat.Toxicol. 41(3):229-250.

9361

UEndp, Eff, Dur

"McCulloch, W.L., and W.J. Rue". 1989. Evaluation of Seven-Day
Chronic Toxicity Estimation Test Using Cyprinodon variegatus.
"In: U.M.Cowgill and L.R.Williams (Eds.), Aquatic Toxicology and
Hazard Assessment, ASTM STP 1027, Philadelphia, PA 12:355-
364".

13864

UEndp, Det

Has six 7d NOEC's

"Missimer, C.L., D.P. Lemarie, and W.L. Rue". 1989. Evaluation
of a Chronic Estimation Toxicity Test Using Skeletonema
costatum. "In: U.M.Cowgill and L.R.Williams (Eds.), Aquatic
Toxicology and Hazard Assessment, 12th Volume, ASTM STP
1027, Philadelphia, PA :345-354".

2057

Eff

"North, W.J., and M.B. Schaefer". 1964. An Investigation of the
Effects of Discharged Wastes on Kelp. "Calif.State Water Control
Board, Publ No.26 :124 p.".

58038

UEndp, Eff

"Ozretic, B., and M. Krajnovic-Ozretic". 1985. Morphological and
Biochemical Evidence of the Toxic Effect of Pentachlorophenol
on the Developing Embryos of the Sea Urchin. Aquat.Toxicol.
7(4):255-263.

12957

Eff, Dur

"Ozretic, B., and M. Krajnovic-Ozretic". 1986. Sea Urchin
Gametes and Their Developing Embryos in Marine Toxicology
Studies. "In: Papers Presented at the FAO/UNEP Meeting on the
Toxicity and Bioaccumulation of Selected Substances in Marine
Organisms, Rovinj, Yugoslavia, 5-9 Nov., 1984, FAO
Fish.Rep.No.334(Suppl.) :111-121".

4047

UEndp, Eff, Dur

671

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

"Rao, K.R., P.J. Conklin, and A.C. Brannon". 1978. "Inhibition of
Limb Regeneration in the Grass Shrimp, Palaemonetes pugio, by
Sodium Pentachlorophenate". "In: K.R.Rao (Ed.),
Pentachlorophenol: Chemistry, Pharmacology and Environmental
Toxicology, Plenum Press, New York, NY :193-203".

6904

UEndp

Has two 22d EC50's and two 66d EC50's

"Roszell, L.E., and R.S. Anderson". 1996. Effect of Chronic In
Vivo Exposure to Pentachlorophenol on Non-Specific Immune
Functions in Fundulus heteroclitus. Mar.Environ.Res. 42(1-
4): 191-194.

19446

UEndp, Eff

"Roszell, L.E., and R.S. Anderson". 1996. Effect of In Vivo
Pentachlorophenol Exposure on Fundulus heteroclitus
Phagocytes: Modulation of Bactericidal Activity. Dis.Aquat.Org.
26(3):205-211.

19517

UEndp, Eff

"Schimmel, S.C., and R.L. Garnas". 1985. Interlaboratory
Comparison of the ASTM Bioconcentration Test Method Using
the Eastern Oyster. "In: R.C.Bahner and D.J.Hansen (Eds.),
Aquatic Toxicology and Hazard Assessment, 8th Symposium,
ASTM STP 891, Philadelphia, PA :227-287".

5310

Eff, Dur

"Shofer, S.L., and R.S. Tjeerdema". 1993. Comparative
Disposition and Biotransformation of Pentachlorophenol in the
Oyster (Crassostrea gigas) and Abalone (Haliotis fulgens).
Pestic.Biochem.Physiol. 46(2):85-95.

16471

Eff, Dur

5h only

"Shofer, S.L., and R.S. Tjeerdema". 1998. Effects of Hypoxia and
Toxicant Exposure on Adenylate Energy Charge and Cytosolic
ADP Concentrations in Abalone. Comp.Biochem.Physiol.C
119(1 ):51 -57.

18958

UEndp, Eff, Dur

2h only

"Shofer, S.L., J.A. Willis, and R.S. Tjeerdema". 1996. Sublethal
Effects of Pentachlorophenol and Hypoxia on Rates of Arginine
Kinase Flux in Red Abalone (Haliotis rufescens) as Measured by
31 P. Mar.Environ.Res. 42(1-4):363-367.

15533

UEndp, Eff, Dur

2h only

672

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

"Soto, E., A. Larrain, and E. Bay-Schmith". 2000. Sensitivity of
Ampelisca araucana Juveniles (Crustacea: Amphipoda) to
Organic and Inorganic Toxicants in Tests of Acute Toxicity.
Bull.Environ.Contam.Toxicol. 64(4):574-578.

54390

NonRes, Dur

"Tachikawa, M., A. Hasegawa, R. Sawamura, A. Takeda, S.
Okada, and M. Nara". 1987. Difference between Fresh- and
Seawater Fishes in the Accumulation and Effect of
Environmental Chemical Pollutants. I. Intakes of Chlordane.
J.Hyg.Chem./Eisei Kagaku 33(2):98-105 (JPN) (ENG ABS).

12737

UEndp, Dur

24hr only

"Tachikawa, M., and R. Sawamura". 1994. The Effects of Salinity
on Pentachlorophenol Accumulation and Elimination by Killifish
(Oryzias latipes). Arch.Environ.Contam.Toxicol. 26(3):304-308.

13665

UEndp, Eff, Dur

"Tagatz, M.E., C.H. Deans, G.R. Plaia, and J.D. Pool". 1983.
Impact on and Recovery of Experimental Macrobenthic
Communities Exposed to Pentachlorophenol. Northeast Gulf Sci.
6(2): 131 -136.

4808

UEndp

"Tagatz, M.E., J.M. Ivey, and M. Tobia". 1978. Effects of
Dowicide (Trade Name) G-ST on Development of Experimental
Estuarine Macrobenthic Communities. "In: K.R.Rao (Ed.),
Pentachlorophenol, Plenum Publ.Corp., New York, NY, EPA-
600/J-78-077, Environ.Res.Lab., U.S.EPA :9 p.(U.S.NTIS PB-
290037)".

7189

UEndp

"Tagatz, M.E., J.M. Ivey, J.C. Moore, and M. Tobia". 1977.
Effects of Pentachlorophenol on the Development of Estuarine
Communities. J.Toxicol.Environ.Health 3(3):501-506.

7497

UEndp

673

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

"Tagatz, M.E., J.M. Ivey, N.R. Gregory, and J.L. Oglesby". 1981.
Effects of Pentachlorophenol on Field- and Laboratory-
Developed Estuarine Benthic Communities.
Bull.Environ.Contam.Toxicol. 26(1 ):137-143.

6384

UEndp

"Thomas, P., and H.W. Wofford". 1984. "Effects of Metals and
Organic Compounds on Hepatic Glutathione, Cysteine, and Acid-
Soluble Thiol Levels in Mullet (Mugil cephalus L.)".
Toxicol.Appl.Pharmacol. 76:172-182.

13632

UEndp, Eff

"Thomas, P., R.S. Carr, and J.M. Neff'. 1981. Biochemical Stress
Responses of Mullet Mugil cephalus and Polychaete Worms
Neanthes virens to Pentachlorophenol. "In: F.J.Vernberg,
A.Calabrese, F.P.Thurberg, and W.B.Vernberg (Eds.), Biological
Monitoring of Marine Pollutants, Academic Press, New York :73-
103".

4835

UEndp, Eff, Dur

"Tjeerdema, R.S., and D.G. Crosby". 1992. Disposition and
Biotransformation of Pentachlorophenol in the Red Abalone
(Haliotis rufescens). Xenobiotica 22(6):681-690.

7440

Eff, Dur

"Tjeerdema, R.S., K.L. Lukrich, and E.M. Stevens". 1994.
Toxicokinetics and Biotransformation of Pentachlorophenol in the
Sea Urchin (Strongylocentrotus purpuratus). Xenobiotica
24(8):749-757.

10618

Eff, Dur

24hr only. Has a 24hr NOEC for the purple sea
urchin

"Tjeerdema, R.S., R.J. Kauten, and D.G. Crosby". 1991.
Interactive Effects of Pentachlorophenol and Hypoxia in the
Abalone (Haliotis rufescens) as Measured by In Vivo 31P NMR
Spectroscopy. Aquat.Toxicol. 21:279-294.

3861

UEndp, Eff, Dur

6hr only

674

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

"Tjeerdema, R.S., R.J. Kauten, and D.G. Crosby". 1993.
Interactive Effects of Pentachlorophenol and Temperature in the
Abalone (Haliotis rufescens) as Measured by In Vivo 31P-NMR
Spectroscopy. Aquat.Toxicol. 26(1/2): 117-132.

8264

UEndp, Eff, Dur

"Tjeerdema, R.S., T.W.M. Fan, R.M. Higashi, and D.G. Crosby".
1991. Sublethal Effects of Pentachlorophenol in the Abalone
(Haliotis rufescens) as Measured by In Vivo 31P NMR
Spectroscopy. J.Biochem.Toxicol. 6(1):45-56.

3798

UEndp, Eff, Dur

6hr and 5hr durations

"Tjeerdema, R.S.,W.S. Smith, L.B. Martello, R.J. Kauten, and
D.G. Crosby". 1996. Interactions of Chemical and Natural
Stresses in the Abalone (Haliotis rufescens) as Measured by
Surface-Probe Localized 31P NMR. Mar.Environ.Res. 42(1-
4):369-374.

14745

UEndp, Eff, Dur

"Tomiyama, T., and K. Kawabe". 1962. "The Toxic Effect of
Pentachlorophenate, a Herbicide, on Fishery Organisms in
Coastal Waters-I. The Effect on Certain Fishes and a Shrimp".
Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan Gakkaishi) 28(3):379-382
(JPN) (ENG ABS).

5832

NonRes, UEndp, Eff, Dur

"Tomiyama, T., K. Kobayashi, and K. Kawabe". 1962. "The Toxic
Effect of Pentachlorophenate, a Herbicide, on Fishery Organisms
in Coastal Waters-Ill. The Effect on Venerupis philippinarum".
Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan Gakkaishi) 28(4):417-421
(JPN) (ENG ABS).

13528

UEndp, Eff, Dur

"Trujillo, D.A., L.E. Ray, H.E. Murray, and C.S. Giam". 1982.
Bioaccumulation of Pentachlorophenol by Killifish (Fundulus
similus). Chemosphere 11(1 ):25-31.

10451

Eff, Dur

675

-------
Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

"Walsh, G.E.". 1981. Effects of Pesticides and Industrial Wastes
on Unicellular Algae and Seagrass. "In: Research and
Development: Experimental Environments Branch, Progress
Report for Fiscal Year 1981, Unpublished Laboratory Data,
U.S.EPA, ERL-Gulf Breeze, FL :3-26".

4803

Eff, Dur

"Walsh, G.E., D.L. Hansen, and D.A. Lawrence". 1982. A Flow-
Through System for Exposure of Seagrass to Pollutants.
Mar.Environ.Res. 7(1):1-12.

11630

Eff, Dur

"Wang, W.X., and J. Widdows". 1993. "Interactive Effects of
Pentachlorophenol (PCP) and Hypoxia on the Energy
Metabolism of the Mussel, Mytilus edulis". Mar.Environ.Res.
35:109-113.

14206

UEndp, Eff, Dur

"Woelke, C.E.". 1965. Development of a Bioassay Method Using
the Marine Algae - Monochrysis lutheri. "Progress Report -
Shellfish Research, Washington Dep.of Fisheries and Shellfish,
Seattle, WA:9".

3757

UEndp, Eff, UChron

"Yoshida, T., T. Maruyama, H.I. Kojima, I. Allahpichay, and S.
Mori". 1986. "Evaluation of the Effect of Chemicals on Aquatic
Ecosystem by Observing the Photosynthetic Activity of a
Macrophyte, Porphyra yezoensis". Aquat.Toxicol. 9(4-5):207-214.

12512

Eff, Dur

C. Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

1) For the studies that were not utilized, but the most representative SMAV/2 or most representative SMCV fell below the
criterion, or, if the studies were for a species associated with one of the four most sensitive genera used to calculate the
FAV in the most recent national ambient water quality criteria dataset used to derive the CMC96, EPA is providing a
transparent rationale as to why they were not utilized (see below).

96 U.S. EPA. 1986. Ambient Water Quality Criteria for Pentachlorophenol - 1986. EPA-440-5-86-009.

676

-------
2) For the studies that were not utilized because they were not found to be pertinent to this determination (including failing
the QA/QC procedures listed in Appendix A) upon initial review of the download from ECOTOX, EPA is providing the
code that identifies why EPA determined that the results of the study were not reliable (see Appendix S).

General QA/QC failure because non-resident species in Oregon

The test with the following species was used in the EPA BE of OR WQS for pentachlorophenol in saltwater, but was not considered in
the CWA review and approval/disapproval action of the standards because this species does not have a breeding wild population in
Oregon's waters:

Lagodon

rhomboides

Pinfish

Schimmel et al. 1978; Borthwick and
Schimmel 1978

Pseudodiaptomus

coronatus

Calanoid copepod

Hauch et al. 1980

Crassostrea

virginica

Eastern oyster

Borthwick and Schimmel 1978; Office of
Pesticide Programs 2000; Zaroogian 1981;
Davis and Hidu 1969

Other Acute tests failins QA/QC by species
Clupea pallasii - Pacific herring

Vigers, G.A., J.B. Marliave, R.G. Janssen and P. Borgmann. 1978. Use of larval herring in bioassays. In: J.C. Davis, G.L.
Greer and I.K. Birtwell (Eds.), Proc. 4th Annual Aquatic Toxicol. Workshop, Nov. 8-10,1977, Vancouver, B.C., Can. Fish.
Mar. Serv. Tech. Rep. No. 818: 31-52.

Two values from this study were rejected for use in calculating the SMAV in the 1986 ALC document because data for a more
sensitive lifestage was available. Other data from this study was used to calculate the SMAV for this species.

677

-------
Appendix T Silver (Saltwater)
Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Article Number and Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Abbe, G.R., and J.G. Sanders. 1990. Pathways of Silver Uptake and
Accumulation by the American Oyster (Crassostrea virginica) in Chesapeake
Bay. Estuar.Coast.Shelf Sci. 31:113-123.

20201

UEndp

Abbe, G.R., J.G. Sanders, and J.M. Bianchi. 1988. Pathways of Silver
Accumulation by the American Oyster (Crassostrea virginica Gmelin) in
Chesapeake Bay. J.Shellfish Res.7(1):107 (ABS).

3126

UEndp, Con

Amiard, J.C.. 1976. Phototactic Variations in Crustacean Larvae Due to Diverse
Metallic Pollutants Demonstrated by a Sublethal Toxicity Test.
Mar.Biol,34(3):239-245 (Fre) (Eng Abs).

5628

Con

Bailey, H.C., J.L. Miller, M.J. Miller, and B.S. Dhaliwal. 1995. Application of
Toxicity Identification Procedures to the Echinoderm Fertilization Assay to Identify
Toxicity in a Municipal Effluent. Environ.Toxicol.Chem. 14(12):2181 -2186.

16375

Dur

Ballan-Dufrancais, C., C. Marcaillou, and C. Amiard-Triquet. 1991. Response of
the Phytoplanktonic Alga Tetraselmis suecica to Copper and Silver Exposure:
Vesicular Metal Bioaccumulation and Lack of Starch Bodies. Biol.Cell
72(1 /2): 103-112.

7698

UEndp

Berry, W.J., M.G. Cantwell, P.A. Edwards, J.R. Serbst, and D.J. Hansen. 1999.
Predicting Toxicity of Sediments Spiked with Silver. Environ.Toxicol.Chem.
18(1):40-48.

19382

Dur, UChron

Berthet, B.. 1990. Effect of the Contamination Vector on the Physico-Chemical
Forms of Silver in Crassostrea gigas Thunberg. Oceanis 16(5):349-357 (FRE)
(ENG ABS).

20592

UEndp, Eff

Berthet, B., J.C. Amiard, C. Amiard-Triquet, M. Martoja, and A.Y. Jeantet. 1992.
Bioaccumulation, Toxicity and Physico-Chemical Speciation of Silver in Bivalve
Molluscs: Ecotoxicological and Health Consequences. Sci.Total Environ. 125:97-
122.

6930

UEndp

678

-------
Article Number and Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Brown, C.L., and S.N. Luoma. 1995. Use of the Euryhaline Bivalve
Potamocorbula amurensis as a Biosentinel Species to Assess Trace Metal
Contamination in San Francisco Bay. Mar.Ecol.Prog.Ser. 124(1-3):129-142.

18036

Eff

Calabrese, A., F.P. Thurberg, and E. Gould. 1977. Effects of Cadmium, Mercury
and Silver on Marine Animals. MFR Paper 1244, Mar Fish Rev 39:5-11.

12206

Eff, Dur

Calabrese, A., J.R. Maclnnes, D.A. Nelson, and J.E. Miller. 1977. Survival and
Growth of Bivalve Larvae Under Heavy-Metal Stress. Mar.Biol. 41:179-184.

9064

Con, Dur

Calabrese, A., J.R. Maclnnes, D.A. Nelson, R.A. Greig, and P.P. Yevich. 1984.
Effects of Long-Term Exposure to Silver or Copper on Growth, Bioaccumulation
and Histopathology in the Blue Mussel Mytilus edulis. Mar.Environ.Res.
11 (4):253-274.

10774

Eff, UEndp

Canterford, G.S., A.S. Buchanan, and S.C. Ducker. 1978. Accumulation of Heavy
Metals by the Marine Diatom Ditylum brightwellii (West) Grunow.
Aust.J.Mar.Freshwater Res. 29(5):613-622.

15455

UEndp, Eff

Carvalho, R.A., M.C. Benfield, and P.H. Santschi. 1999. Comparative
Bioaccumulation Studies of Colloidally Complexed and Free-Ionic Heavy Metals
in Juvenile Brown Shrimp Penaeus aztecus (Crustacea: Decapoda: Penaeidae).
Limnol.Oceanogr. 44(2):403-414.

48059

Eff, UEndp

Clarke, G.L.. 1947. Poisoning and Recovery in Barnacles and Mussels. Biol.Bull.
92:73-91.

14811

UEndp

Connell, D.B., J.G. Sanders, G.F. Riedel, and G.R. Abbe. 1991. Pathways of
Silver Uptake and Trophic Transfer in Estuarine Organisms. Environ.Sci.Technol.
25(5):921-924.

11561

UEndp

Dinnel, P.A., J.M. Link, and Q.J. Stober. 1987. Improved Methodology for a Sea
Urchin Sperm Cell Bioassay for Marine Waters. Arch.Environ.Contam.Toxicol.
16:23-32.

2610

Con, Dur

679

-------
Article Number and Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Domouhtsidou, G.P., and V.K. Dimitriadis. 2000. Ultrastructural Localization of
Heavy Metals (Hg,Ag,Pfc>, and Cu) in Gills and Digestive Gland of Mussels,
Mytilus galloprovincialis (L.). Arch.Environ.Contam.Toxicol. 38(4):472-478.

48771

UEndp

Fisher, N.S., M. Bohe, and J.L. Teyssie. 1984. Accumulation and Toxicity of Cd,
Zn, Ag, and Hg in Four Marine Phytoplankters. Mar.Ecol.Prog.Ser. 18(3):201-
213.

11805

UEndp, Eff

Fisher, N.S., V.T. Breslin, and M. Levandowsky. 1995. Accumulation of Silver and
Lead in Estuarine Microzooplankton. Mar.Ecol.Prog.Ser. 116(1-3):207-215.

17381

Eff, Ace

Gould, E., and J.R. Maclnnes. 1977. Short-Term Effects of Two Silver Salts on
Tissue Respiration and Enzyme Activity in the Cunner (Tautogolabrus
adspersus). Bull.Environ.Contam.Toxicol. 18(4):401-408.

6125

UEndp

Grosell, M., G. DeBoeck, 0. Johannsson, and C.M. Wood. 1999. The Effects of
Silver on Intestinal Ion and Acid-Base Regulation in the Marine Teleost Fish,
Parophrys vetulus. Comp.Biochem.Physiol. 124c(3):259-270.

49761

UEndp, Dur

Hannan, P.J., and C. Patouillet. 1972. Effects of Pollutants on Growth of Algae.
Rep.NRL (Nav.Res.Lab.) Prog.:1-8 (Author Communication Used).

9095

UEndp, Dur

Heitmuller, P.T., T.A. Hollister, and P.R. Parrish. 1981. Acute Toxicity of 54
Industrial Chemicals to Sheepshead Minnows (Cyprinodon variegatus).
Bull.Environ.Contam.Toxicol. 27(5):596-604 (OECDG Data File).

10366

Dur, UChron

Hogstrand, C., and C.M. Wood. 1996. The Toxicity of Silver to Marine Fish. In:
4th Int.Conf.Proc.: Transport, Fate and Effects of Silver in the Environment,
Aug.25-28, 1996, Madison, Wl :109-112.

20143

UEndp

Maclnnes, J.R., and F.P. Thurberg. 1973. Effects of Metals on the Behavior and
Oxygen Consumption of the Mud Snail. Mar.Pollut.Bull. 4(12):185-186.

8902

UEndp, Eff

Mathew, R., and N.R. Menon. 1983. Oxygen Consumption in Tropical Bivalves
Perna viridis (Linn.) and Meretrix casta (Chem.) Exposed to Heavy Metals. Indian
J.Mar.Sci. 12(1):57-59.

11085

UEndp, Eff, Con

680

-------
Article Number and Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Metayer, C., C. Amiard-Triquet, and J.P. Baud. 1990. Species-Related Variations
of Silver Bioaccumulation and Toxicity to Three Marine Bivalves. Water Res.
24(8):995-1001 (FRE) (ENG ABS).

10496

UEndp, Eff, Con

Nacci, D., E. Jackim, and R. Walsh. 1986. Comparative Evaluation of Three
Rapid Marine Toxicity Tests: Sea Urchin Early Embryo Growth Test, Sea Urchin
Sperm Cell Toxicity Test and Microtox. Environ.Toxicol.Chem. 5:521-525.

17742

Dur

Nolan, C., and H. Dahlgaard. 1991. Accumulation of Metal Radiotracers by
Mytilus edulis. Mar.Ecol.Prog.Ser. 70(2):165-174.

20303

Eff

Office of Pesticide Programs. 2000. Pesticide Ecotoxicity Database (Formerly:
Environmental Effects Database (EEDB)). Environmental Fate and Effects
Division, U.S.EPA, Washington, D.C..

344

ECOTOX provides one 96-h LC50 of 93.50
|jg/L for this study. This is similar to the
data used in the analysis. These values
could have been considered for EPA's
evaluation of saltwater silver, but the
species is relatively insensitive to silver
compared to others.

Pentreath, R.J.. 1977. The Accumulation of 110m Ag by the Plaice, Pleuronectes
platessa L. and the Thornback Ray, Raja clavata L. J.Exp.Mar.BioI.Ecol.
29(3):315-325.

7141

Con, Eff

Pereira, J.J., and K. Kanungo. 1981. Effects of Silver on Respiration and on Ion
and Water Balance in Neanthes virens. In: F.J.Vernberg, A.Calabrese,
F.P.Thurberg, and W.B.Vernberg (Eds.), Biological Monitoring of Marine
Pollutants, Academic Press, Inc., NY :107-125.

13465

UEndp, Eff

Shaw, J.R., W.J. Birge, and C. Hostrand. 1996. Parameters that Influence Silver
Toxicity: Ammonia and Salinity. In: 4th Int.Conf.Proc.: Transport, Fate and Effects
of Silver in the Environment, Aug.25-28, 1996, Madison, Wl : 155-159.

20142

Eff

ECOTOX provides one 96-h LC50 of 564.4
|jg/L for this study. This is similar to the
data used in the analysis. These values
could have been considered for EPA's
evaluation of saltwater silver, but the
species is relatively insensitive to silver
compared to others.

Thurberg, F.P., A. Calabrese, and M.A. Dawson. 1974. Effects of Silver on
Oxygen Consumption of Bivalves at Various Salinities. In: F.J.Vernberg and
W.B.Vernberg (Eds.), Pollution and Physiology of Mar.Organisms, Academic
Press, NY :67-78.

8733

UEndp, Eff, Con

Thursby, G.B., and R.L. Steele. 1986. Comparison of Short-and Long-Term
Sexual Reproduction Tests with the Marine Red Alga Champia parvula.
Environ.Toxicol.Chem. 5(11): 1013-1018.

12976

UEndp, Con

681

-------
Article Number and Citation

ECOTOX
EcoRef #

Rejection Code(s)

Comment

Voyer, R.A., J.A. Cardin, J.F. Heltshe, and G.L. Hoffman. 1982. Viability of
Embryos of the Winter Flounder Pseudopleuronectes americanus Exposed to
Mixtures of Cadmium and Silver in Combination with Selected Fixe.
Aquat.Toxicol. 2(4):223-233.

10500

UEndp, Dur

Warnau, M., M. laccarino, A. De Biase, A. Temara, M. Jangoux, P. Dubois, and
G. Pagano. 1996. Spermiotoxicity and Embryotoxicity of Heavy Metals in the
Echinoid Paracentrotus lividus. Environ.Toxicol.Chem. 15(11): 1931-1936.

17368

Dur

Wilson, W.B., and L.R. Freeburg. 1980. Toxicity of Metals to Marine
Phytoplankton Cultures. EPA-600/3-80-025, U.S.EPA, Narragansett, Rl :110
p.(U.S.NTIS PB80-182843).

5557

Dur

Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

the most recent national ambient water quality criteria dataset used to derive the CMC , EPA is providing a transparent
rationale as to why they were not utilized (see below).

For the studies that were not utilized because they were not found to be pertinent to this determination (including failing the
QA/QC procedures listed in Appendix A) upon initial review of the download from ECOTOX, EPA is providing the code that
identifies why EPA determined that the results of the study were not reliable.

General QA/QC failure because non-resident species in Oregon

Tests with the following several species were used in the EPA BE of OR WQS for silver in saltwater, but were not considered in the
CWA review and approval/disapproval action of the standards because these species do not have a breeding wild population in
Oregon's waters:

97 U.S. EPA. 1980. Ambient Water Quality Criteria Document for Silver. EPA-440/5-80-071.

682

-------
Paralichthys

dentatus

Opossum shrimp

Cardin 1980; Shaw et al. 1997

Crassostrea

virginica

Eastern oyster

Calabrese et al. 1973; Maclnnes
and Calabrese 1978; Zaroogian
Manuscript

Mercenaria

mercenaria

Northern quahog or hard
clam

Calabrese and Nelson 1974

Argopecten

Irradians

Bay scallop

Nelson et al. 1976

Other Acute tests failins QA/QC by species
Crassostrea gigas — Pacific oyster

The following test was included in EPA's BE of the OR WQS for silver in saltwater, but was not used in this CWA review and
approval/disapproval action of these standards because it was a greater than value and more definitive data was available for this
species.

Coglianese, M.P. 1982. The effects of salinity on copper and silver toxicity to embryos of the Pacific oyster. Arch. Environ.
Contam. Toxicol. 11:297-303.

683

-------
Appendix U Tributyltin (Saltwater)
Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Anderson, R.S., E.M. Burreson, and M.A. linger. 1995. The Effects of
Environmental Contaminants on the Progression of Perkinsus marinus
Infection in the Eastern Oyster [R/CBT-22], In: E.J.OImi III, B.Hens, P.Hill,
and J.G.Sanders (Eds.), Chesapeake Bay Environmental Effects Studies,
Toxics Research Program, 1994 Workshop Report, Solomons, MD :150-155.

19555

UEndp, Eff, Dur

Axiak, V., M. Sammut, P. Chircop, A. Vella, and B. Mintoff. 1995. Laboratory
and Field Investigations on the Effects of Organotin (Tributyltin) on the
Oyster, Ostrea edulis. Sci.Total Environ. 171 (1-3): 117-120.

18725

UEndp

Bauer, B., P. Fioroni, U. Schulte-Oehlmann, J. Oehlmann, and W. Kalbfus.
1997. The Use of Littorina littorea for Tributyltin (TBT) Effect Monitoring -
Results from the German TBT Survey 1994/1995 and Laboratory
Experiments. Environ.Pollut. 96(3):299-309.

18345

UEndp, Eff, UChron

Beaumont, A.R., and M.D. Budd. 1984. High Mortality of the Larvae of the
Common Mussel at Low Concentrations of Tributyltin. Mar.Pollut.Bull.
15(11):402-405.

10800

UEndp, Dur

Beaumont, A.R., and P.B. Newman. 1986. Low Levels of Tributyl Tin Reduce
Growth of Marine Micro-Algae. Mar.Pollut.Bull. 17(10):457-461.

12011

UEndp, Dur

Bettin, C., J. Oehlmann, and E. Stroben. 1996. TBT-lnduced Imposex in
Marine Neogastropods is Mediated by an Increasing Androgen Level.
Helgol.Meeresunters. 50:299-317.

17946

UEndp

Blanck, H., and B. Dahl. 1996. Pollution-Induced Community Tolerance
(PICT) in Marine Periphyton in a Gradient of Tri-n-butyltin (TBT)
Contamination. Aquat.Toxicol. 35(1):59-77.

17783

UEndp, Det

Bryan, G.W., D.A. Bright, L.G. Hummerstone, and G.R. Burt. 1993. Uptake,
Tissue Distribution and Metabolism of 14C-Labelled Tributyltin (TBT) in the
Dog-Whelk, Nucella lapillus. J.Mar.Biol.Assoc.U.K. 73(4):889-912.

4159

UEndp, Eff

684

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Bryan, G.W., P.E. Gibbs, G.R. Burt, and L.G. Hummerstone. 1987. The
Effects of Tributyltin (TBT) Accumulation on Adult Dog-Whelks, Nucella
lapillus: Long-Term Field and Laboratory Experiments. J.Mar.Biol.Assoc.U.K.
67(3):525-544.

9998

UENdp, Eff, Field

Bryan, G.W., P.E. Gibbs, L.G. Hummerstone, and G.R. Burt. 1986. The
Decline of the Gastropod Nucella lapillus Around South-West England:
Evidence for the Effect of Tributyltin from Antifouling Paints.
J.Mar.Biol.Assoc.U.K. 66:611-640.

4420

UEndp, Eff, UChron

Bryan, G.W., P.E. Gibbs, L.G. Hummerstone, and G.R. Burt. 1989. Uptake
and Transformation of 14C-Labelled Tributyltin Chloride by the Dog-Whelk,
Nucella lapillus: Importance of Absorption from the Diet. Mar.Environ.Res.
28:241-245.

18308

UEndp, Eff, UChron

Buccafusco, R.. 1976. Acute Toxicity of Tri-N-Butyltin oxide to Channel
Catfish (Ictalurus punctatus), the Fresh Water Clam (Elliptio complanatus),
the Common Mummichog. U.S.EPA-OPP Registration Standard.

12995

Dur, No Cone, AF

possile LC50 (18 ug/L) for mummichog but no
salinity

Burridge, T.R., T. Lavery, and P.K.S. Lam. 1995. Acute Toxicity Tests Using
Phyllospora comosa (Labillardiere) C. Agardh (Phaeophyta: Fucales) and
Allorchestes compressa Dana (Crustacea: Amphipoda).
Bull.Environ.Contam.Toxicol. 55(4):621-628.

14985

UEndp, Dur, NonRes

Burridge, T.R., T. Lavery, and P.K.S. Lam. 1995. Effects of Tributyltin and
Formaldehyde on the Germination and Growth of Phyllospora comosa
(Labillardiere) C. Agardh (Phaeophyta: Fucales).

Bull. Environ.Contam .Toxicol. 55(4):525-532.

14987

UEndp, Eff, Dur,
NonRes

Bushong, S.J., M.C. Ziegenfuss, M.A. Unger, and L.W. Hall Jr.. 1990. Chronic
Tributyltin Toxicity Experiments With the Chesapeake Bay Copepod, Acartia
tonsa. Environ.Toxicol.Chem. 9(3):359-366.

3199

Dur

Chiles, T.C., P.D. Pendoley, and R.B. Laughlin Jr.. 1989. Mechanisms of Tri-
N-Butyltin Bioaccumulation by Marine Phytoplankton. Can.J.Fish.Aquat.Sci.
46(5):859-862.

19095

UEndp, Eff, Dur

685

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Cima, F., L. Ballarin, G. Bressa, G. Martinucci, and P. Burighel. 1996. Toxicity
of Organotin Compounds on Embryos of a Marine Invertebrate (Styela
plicata; Tunicata). Ecotoxicol.Environ.Saf. 35(2):174-182.

18435

UEndp, Dur

Cima, F., L. Ballarin, G. Bressa, G.B. Martinucci, and P. Burighel. 1996.
Embryotoxic Effects of Organotin Compounds on Styela plicata (Tunicata;
Ascidiacea). Fresenius Environ.Bull. 5(11/12):718-722.

20235

UEndp, Eff, Dur

Cramm, G.. 1979. Acute and Chronic Toxicity of Tributyltin oxide (TBTO) to
Sheepshead Minnows (Cyprinodon variegatus). U.S.EPA-OPP Registration
Standard.

12998

UEndp, Dur

Dahl, B., and H. Blanck. 1996. Pollution-Induced Community Tolerance
(PICT) in Periphyton Communities Established Under Tri-n-butyltin (TBT)
Stress in Marine Microcosms. Aquat.Toxicol. 34(4):305-325.

17785

UEndp, Eff, Dur,
UChron, No Org

Dahl, B., and H. Blanck. 1996. Use of Sand-Living Microalgal Communities
(Epipsammon) in Ecotoxicological Testing. Mar.Ecol.Prog.Ser. 144(1-3):163-
173.

19988

Eff, Dur, No Org

Davies, I.M., and J.C. McKie. 1987. Accumulation of Total Tin and Tributyltin
in Muscle Tissue of Farmed Atlantic Salmon. Mar.Pollut.Bull. 18(7):405-407.

2489

UEndp, Eff, Con, Dur

Deutsch, U., and P. Fioroni. 1996. Effects of Tributyltin (TBT) and
Testosterone on the Female Genital System in the Mesogastropod Littorina
littorea (Prosobranchia). Helgol.Meeresunters. 50:105-115.

18847

UEndp, UChron

Deutsch, U., J. Oehlmann, and E. Stroben. 1993. Morphological Effects of
Tributyltin (TBT) In Vitro on the Genital System of the Mesogastropod
Littorina littorea (L.) (Prosobranchia). In: J.C.AIdrich (Ed.), Proc.27th
Eur.Mar.Biol.Symp., Quantified Phenotypic Responses in Morphology and
Physiology, Sept.7-11, 1992, Dublin, Ireland :297-300.

17524

UEndp, UChron

Dimitriou, P., J. Castritsi-Catharios, and H. Miliou. 2003. Acute Toxicity
Effects of Tributyltin Chloride and Triphenyltin Chloride on Gilthead
Seabream, Sparus aurata L., Embryos. Ecotoxicol.Environ.Saf. 54(1):30-35.

68277

UEndp, Dur

686

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Dixon, D.R., and H. Prosser. 1986. An Investigation of the Genotoxic Effects
of an Organotin Antifouling Compound(Bis(Tributyltin) oxide) on the
Chromosomes of the Edible Mussel,. Aquat.Toxicol. 8(3):185-195.

11949

UEndp

Ebdon, L., K. Evans, and S. Hill. 1989. The Accumulation of Organotins in
Adult and Seed Oysters from Selected Estuaries Prior to the Introduction of
U.K. Regulations Governing the Use of. Sci.Total Environ. 83(1/2):63-84.

3345

UEndp, Eff, Field

Fisher, W.S., L.M. Oliver, W.W. Walker, C.S. Manning, and T.F. Lytle. 1999.
Decreased Resistance of Eastern Oysters (Crassostrea virginica) to a
Protozoan Pathogen (Perkinsus marinus) After Sublethal Exposure to
Tributyltin. Mar.Environ.Res. 47:185-201.

20625

UEndp, Eff

Franchet, C., M. Goudeau, and H. Goudeau. 1999. Tributyltin Impedes Early
Sperm-Egg Interactions at the Egg Coat Level in the Ascidian Phallusia
mammillata but Does not Prevent Sperm-Egg Fusion in Naked Eggs.
Aquat.Toxicol. 44(3):213-228.

20099

UEndp, Eff, Dur, Con

Francois, R., F.T. Short, and J.H. Weber. 1989. Accumulation and
Persistence of Tributyltin in Eelgrass (Zostera marina L.) Tissue.
Environ.Sci.Technol. 23(2):191 -196.

2580

UEndp, UChron, Con

Gibbs, P.E., P.L. Pascoe, and G.R. Burt. 1988. Sex Change in the Female
Dog-Whelk, Nucella lapillus, Induced by Tributyltin from Antifouling Paints.
J. Mar. Biol .Assoc. U. K. 68(3):715-731.

9997

Field, UEndp, Eff,

Girard, J.P., C. Ferrua, and D. Pesando. 1997. Effects of Tributyltin on Ca2+
Homeostasis and Mechanisms Controlling Cell Cycling in Sea Urchin Eggs.
Aquat.Toxicol. 38:225-239.

18400

UEndp, Eff, Dur

Gomez-Ariza, J.L., E. Morales, and I. Giraldez. 1999. Uptake and Elimination
of Tributyltin in Clams, Venerupis decussata. Mar. Environ. Res. 47:399-413.

20627

Eff, UChron

Gomez-Ariza, J.L., I. Giraldez, and E. Morales. 2000. Temporal Fluctuations
of Tributyltin in the Bivalve Venerupis decussata at Five Stations in Southwest
Spain. Environ.Pollut. 108(2):279-290.

49630

UEndp, Eff, Dur,
UChron

Guolan, H., and W. Yong. 1995. Effects of Tributyltin Chloride on Marine
Bivalve Mussels. Water Res. 29(8): 1877-1884.

15027

UEndp, Eff

687

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Hall, L.W.Jr., S.J. Bushong, M.C. Ziegenfuss, W.E. Johnson, R.L. Herman,
and D.A. Wright. 1988. Chronic Toxicity of Tributyltin to Chesapeake Bay
Biota. Water Air Soil Pollut. 39(3-4):365-376.

13209

UEndp

Hattori, T., and Y. Shizuri. 1996. A Screening Method for Antifouling
Substances Using Spores of the Fouling Macroalga Ulva conglobata
Kiellman. Fish.Sci. 62(7):955-958.

10263

UEndp

Heitmuller, T. 1977. Toxicity of Tri-N-Butyltin oxide (TBTO) to Pink Shrimp
(Penaeus duorarum). U.S.EPA-OPP Registration Standard.

12991

Dur

ECOTOX provides one 96-h LC50 of 11.00 |jg/L
for this study. These values could have been
considered for EPA's evaluation of saltwater
TBT, but the species is relatively insensitive to
TBT compared to others. Note, this test was not
used in the 2003 TBT WQC doc.

Hollister, T.. 1977. Toxicity of Tri-N-Butyltin oxide (TBTO) to Embryos of
Eastern Oysters (Crassostrea virginica). U.S.EPA-OPP Registration
Standard.

12993

Dur

Holm, G., L. Norrgren, and 0. Linden. 1991. Reproductive and
Histopathological Effects of Long-Term Experimental Exposure to
bis(Tributyltin)oxide(TBTO) on the Three-Spined Stickleback. J.Fish Biol.
38(3):373-386.

3541

UEndp, Eff, Tox

Itow, T., R.E. Loveland, and M.L. Botton. 1998. Developmental Abnormalities
in Horseshoe Crab Embryos Caused by Exposure to Heavy Metals.
Arch.Environ.Contam.Toxicol. 35(1):33-40.

19470

UEndp, Dur

Itow, T., T. Igarashi, M.L. Botton, and R.E. Loveland. 1998. Heavy Metals
Inhibit Limb Regeneration in Horseshoe Crab Larvae.
Arch.Environ.Contam.Toxicol. 35(3):457-463.

20180

UEndp, UChron

Jak, R.G., M. Ceulemans, M.C.T. Scholten, and N.M. Van Straalen. 1998.
Effects of Tributyltin on a Coastal North Sea Plankton Community in
Enclosures. Environ.Toxicol.Chem. 17(9):1840-1847.

19460

UEndp, Dur, Field

Johansen, K., and F. Mohlenberg. 1987. Impairment of Egg Production in
Acartia tonsa Exposed to Tributyltin Oxide. Ophelia 27(2):137-141.

4236

UEndp, Dur

688

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Karande, A.A., and S.S. Ganti. 1994. Laboratory Assays of Tributyltin Toxicity
to Some Common Marine Organisms. In: M.F.Thompson,

R.Nagabhushanam, R.Sarojini, and M.Fingerman (Eds.), Recent
Developments in Biofouling Control, Oxford and IBH, New Delhi, India :115-
123 (Publ in Part As 13603).

17675

UEndp, UChron

Karande, A.A., S.S. Ganti, and M. Udhayakumar. 1993. Toxicity of Tributyltin
to Some Bivalve Species. Indian J.Mar.Sci. 22(2): 153-154.

13603

UChron, Eff, NonRes

Kawamata, M., K. Kon-Ya, and W. Miki. 1994. Trigonelline, an Antifouling
Substance Isolated from an Octocoral Dendronephthya sp. Fish.Sci.
60(4):485-486.

16323

Dur

Kelly, J.R., D.T. Rudnick, R.D. Morton, L.A. Buttel, and S.N. Levine. 1990.
Tributyltin and Invertebrates of a Seagrass Ecosystem: Exposure and
Response of Different Species. Mar.Environ.Res. 29(4):245-276.

8002

UEndp, Eff

Kelly, J.R., S.N. Levine, L.A. Buttel, K.A. Carr, D.T. Rudnick, and R.D.
Morton. 1990. The Effects of Tributyltin Within a Thalassia Seagrass
Ecosystem. Estuaries 13(3):301-310.

7816

UEndp, Eff

Kusk, K.O., and S. Petersen. 1997. Acute and Chronic Toxicity of Tributyltin
and Linear Alkylbenzene Sulfonate to the Marine Copepod Acartia tonsa.
Envi ron .Toxicol. Chem. 16(8): 1629-1633.

18078

Dur

Langston, W.J., and G.R. Burt. 1991. Bioavailability and Effects of Sediment-
Bound TBT in Deposit-Feeding Clams, Scrobicularia plana. Mar.Environ.Res.
32(1-4):61-77.

3214

Eff

Lapota, D., D.E. Rosenberger, and D. Duckworth. 1996. A Bioluminescent
Dinoflagellate Assay for Detecting Toxicity in Coastal Waters. In:
A.K.Campbell, L.J.Kricka, and P.E.Stanley (Eds.), Bioluminescence and
Chemiluminescence, Fundamentals and Applied Aspects, John Wiley &
Sons, NY : 156-159.

19990

Eff, Dur

Lapota, D., D.E. Rosenberger, M.F. Platter-Rieger, and P.F. Seligman. 1993.
Growth and Survival of Mytilus edulis Larvae Exposed to Low Levels of
Dibutyltin and Tributyltin. Mar.Biol. 115:413-419.

6982

UEndp, AF

689

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Laughlin, R.B.J., and W. French. 1988. Concentration Dependence of
Bis(Tributyl)tin Oxide Accumulation in the Mussel, Mytilus edulis.
Environ.Toxicol.Chem. 7(12): 1021-1026.

8015

Eff, UChron, Con

Laughlin, R.B.J., and W. French. 1989. Population-Related Toxicity
Responses to Two Butyltin Compounds by Zoeae of the Mud Crab
Rhithropanopeus harrisii. Mar.Biol. 102(3):397-401.

19081

UEndp, Dur, Con

Laughlin, R.B.J., R. Gustafson, and P. Pendoley. 1988. Chronic Embryo-
Larval Toxicity of Tributyltin (TBT) to the Hard Shell Clam Mercenaria
mercenaria. Mar.Ecol.Prog.Ser. 48(1):29-36.

2971

UEndp, Dur

Laughlin, R.B.J., R.G. Gustafson, and P. Pendoley. 1989. Acute Toxicity of
Tributyltin (TBT) to Early Life History Stages of the Hard Shell Clam,
Mercenaria mercenaria. Bull.Environ.Contam.Toxicol. 42(3):352-358.

2859

Con, UChron

Laughlin, R.B.J., W. French, and H.E. Guard. 1986. Accumulation of
Bis(Tributyltin) Oxide by the Marine Mussel Mytilus edulis.

Envi ron. Sci .Technol. 20(9) :884-890.

11905

Eff, Con

Laughlin, R.B.J., W. French, R.B. Johannesen, H.E. Guard, and F.E.
Brinckman. 1984. Predicting Toxicity Using Computed Molecular Topologies:
The Example of Triorganotin Compounds. Chemosphere 13(4):575-584.

10187

Con, UChron, Dur

Lawler, I.F., and J.C. Aldrich. 1987. Sublethal Effects of Bis(Tri-n-
Butyltin)Oxide on Crassostrea gigas Spat. Mar.Pollut.Bull. 18(6):274-278.

UEndp, Eff, UChron

Lee, R.F., A.O. Valkirs, and P.F. Seligman. 1989. Importance of Microalgae in
the Biodegradation of Tributyltin in Estuarine Waters. Environ.Sci.Technol.
23:1515-1518.

18429

UEndp, Dur, No Org

Li, Q., M. Osada, K. Takahashi, T. Matsutani, and K. Mori. 1997.
Accumulation and Depuration of Tributyltin Oxide and Its Effect on the
Fertilization and Embryonic Development in the Pacific Oyster, Crassostrea
gigas. Bull.Environ.Contam.Toxicol. 58(3):489-496.

18005

Eff

Liberatore, G.L., D.K. Christian, and J.M. Raines. 1977. Standard Bioassay
Using the Barnacle Larva. David W.Taylor Naval Ship Res.Dev.Ctr.,
Annapolis, MD :12 p.(U.S.NTIS AD-A036562).

6019

Dur

690

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Lignot, J.H., F. Pannier, J.P. Trilles, and G. Charmantier. 1998. Effects of
Tributyltin Oxide on Survival and Osmoregulation of the Shrimp Penaeus
japonicus (Crustacea, Decapoda). Aquat.Toxicol. 41(4):277-299.

19156

NonRes, UEndp, Eff,
Dur

Manning, C.S., T.F. Lytle, W.W. Walker, and J.S. Lytle. 1999. Life-Cycle
Toxicity of Bis(Tributyltin) Oxide to the Sheepshead Minnow (Cyprinodon
variegatus). Arch.Environ.Contam.Toxicol. 37(2):258-266.

20452

UEndp

Maruyama, T., D. Sun, S. Hashimoto, and A. Miura. 1991. Toxic Effects of
Triorganotins on the Adhesion and Germination - Growth of Conchospores of
Porphyra yezoensis, Red Arga. Mar.Pollut.Bull. 23:729-731.

7937

Con, Dur

Matthiessen, P., R. Waldock, J.E. Thain, M.E. Waite, and S. Scrope-Howe.
1995. Changes in Periwinkle (Littorina littorea) Populations Following the Ban
on TBT-Based Antifoulings on Small Boats in the United Kingdom.

Ecotoxicol. Environ. Saf. 30(2): 180-194.

15325

UEndp, Eff, Dur, Tox

Meador, J.P.. 1993. The Effect of Laboratory Holding on the Toxicity
Response of Marine Infaunal Amphipods to Cadmium and Tributyltin.
J. Exp. Mar. Biol. Ecol. 174(2):227-242.

4114

Con

Same data reported in another study, used for
SMAV calculation

Meador, J.P.. 1997. Differential Sensitivity of Marine Infaunal Amphipods to
Tributyltin. Mar.Biol. 116(2):231-239.

8519

Dur

Mercier, A., E. Pelletier, and J.F. Hamel. 1996. Toxicological Response of the
Symbiotic Sea Anemone Aiptasia pallida to Butyltin Contamination.
Mar.Ecol.Prog.Ser. 144(1-3): 133-146.

6838

UEndp, Eff, Dur

Mercier, A., E. Pelletier, and J.F. Hamel. 1998. Response of Temperate Sea
Anemones to Butyltin Contamination. Can.J.Fish.Aquat.Sci. 55(1):239-245.

18651

UEndp, Eff, Dur

Molander, S., B. Dahl, H. Blanck, J. Jonsson, and M. Sjostrom. 1992.
Combined Effects of Tri-n-butyl Tin (TBT) and Diuron on Marine Periphyton
Communities Detected as Pollution-Induced Community Tolerance.
Arch.Environ.Contam.Toxicol. 22(4):419-427.

6117

Eff, Dur, Con, No Org

691

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Morcillo, Y., and C. Porte. 2000. Evidence of Endocrine Disruption in Clams -
Ruditapes decussata - Transplanted to a Tributyltin-Polluted Environment.
Environ.Pollut. 107(1):47-52.

52364

Field, Eff

Morcillo, Y., M.J.J. Ronis, and C. Porte. 1998. Effects of Tributyltin on the
Phase I Testosterone Metabolism and Steroid Titres of the Clam Ruditapes
decussata. Aquat.Toxicol. 42(1 ):1 -13.

19153

Eff

Nell, J.A., and R. Chvojka. 1992. The Effect of bis-Tributyltin Oxide (TBTO)
and Copper on the Growth of Juvenile Sydney Rock Oysters Saccostrea
commercialis (Iredale and Roughley) and. Sci.Total Environ. 125:193-201.

4136

UEndp, UChron

Nias, D.J., S.C. McKullup, and K.S. Edyvane. 1993. Imposex in Lepsiella
vinosa from Southern Australia. Mar.Pollut.Bull. 26(7):380-384.

9714

UEndp, UChron, Pur

Oehlmann, J., and C. Bettin. 1996. Tributyltin-lnduced Imposex and the Role
of Steroids in Marine Snails. Malacol.Rev.(Suppl. 6):157-161.

17953

UEndp, UChron

Pickwell, G.V., and S.A. Steinert. 1988. Uptake and Accumulation of
Organotin Compounds by Oyster and Mussel Hemocytes: Correlation with
Serum Biochemical and Cytological Factors and. Aquat.Toxicol. 11 (3/4):419-
420 (ABS).

9646

UEndp, UChron, Con

Pinkney, A.E.. 1989. Biochemical, Histological, and Physiological Effects of
Tributyltin Compounds in Estuarine Fish. Diss.Abstr.lnt.B Sci.Eng.49(8):3080
/ Ph.D.Thesis, University of Maryland, College Park, MD :109 p..

3128

UEndp, Eff, UChron,
Con

Reader, S., and E. Pelletier. 1992. Biosorption and Degradation of Butyltin
Compounds by the Marine Diatom Skeletonema costatum and the Associated
Bacterial Community at Low Temperature. Bull.Environ.Contam.Toxicol.
48(4):599-607.

14967

UEndp, Eff

Ringwood, A.H.. 1992. Comparative Sensitivity of Gametes and Early
Developmental Stages of a Sea Urchin Species (Echinometra mathaei) and a
Bivalve Species (Isognomon. Arch.Environ.Contam.Toxicol. 22:288-295.

3886

Dur, UChron

692

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Roman, G., A. Rudolph, J. Morillas, and R. Ahumada. 1992. Observations on
Sublethal and Acute Toxicity on Choromytilus chorus (Molina, 1782),
Produced by Tributyltin (TBT). Bol.Soc.Biol.Concepcion 63:175-184 (SPA)
(ENG ABS).

16522

UEndp, Eff, NonRes

Ruiz, J.M., G.W. Bryan, and P.E. Gibbs. 1994. Bioassaying the Toxicity of
Tributyltin-(TBT)-Polluted Sediment to Spat of the Bivalve Scrobicularia plana.
Mar. Ecol. Prog. Ser. 113:119-130.

14426

UEndp, UChron,
NonRes

Ruiz, J.M., G.W. Bryan, and P.E. Gibbs. 1994. Chronic Toxicity of Water
Tributyltin (TBT) and Copper to Spat of the Bivalve Scrobicularia plana:
Ecological Implications. Mar.Ecol.Prog.Ser. 113:105-117.

14453

UEndp, UChron,
NonRes

Ruiz, J.M., G.W. Bryan, and P.E. Gibbs. 1995. Effects of Tributyltin (TBT)
Exposure on the Veliger Larvae Development of the Bivalve Scrobicularia
plana (da Costa). J.Exp.Mar.BioI.Ecol. 186(1):53-63.

16564

UEndp, Dur, NonRes

Ruiz, J.M., G.W. Bryan, and P.E. Gibbs. 1995. Acute and Chronic Toxicity of
Tributyltin (TBT) to Pediveliger Larvae of the Bivalve Scrobicularia plana.
Mar.Biol. 124(1): 119-126.

19051

UEndp, Eff, UChron,
NonRes

Ruiz, J.M., G.W. Bryan, G.D. Wigham, and P.E. Gibbs. 1995. Effects of
Tributyltin (TBT) Exposure on the Reproduction and Embryonic Development
of the Bivalve Scrobicularia plana. Mar. Environ.Res. 40(4):363-379.

18221

UEndp, Dur, NonRes

Salazar, M.H., and S. Salazar. 1993. Mussles as Bioindicators: Effects of TBT
on Survival, Bioaccumulation and Growth Under Natural Conditions. In:
M.A.Champ and P.F.Seligman (Eds.), Organotins: Environmental Fate and
Effects, Elsevier, NY :43 p..

9682

Field, UEndp, Eff

Salazar, M.H., and S.M. Salazar. 1987. Tributyltin Effects on Juvenile Mussel
Growth. In: Proc.Oceans, 1987, Halifax, Nova Scotia, Canada, Sept.28-Oct.1,
1987, Organotin Symposium 4:1504-1510.

9685

Field, UEndp, Eff, Tox

Salazar, M.H., and S.M. Salazar. 1988. Tributyltin and Mussel Growth in San
Diego Bay. In: Proc.Oceans, 1988, Baltimore, MD, Oct.31-Nov.2, 1988,
Organotin Symposium 4 :1188-1197.

9683

Field, UEndp, Eff

693

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Sasikumar, N., A.S. Clare, D.J. Gerhart, D. Stover, and D. Rittschof. 1995.
Comparative Toxicities of Selected Compounds to Nauplii of Balanus
amphitrite amphitrite Darwin and Artemia sp.. Bull.Environ.Contam.Toxicol.
54:289-296.

53890

Dur

Scammell, M.S., G.E. Batley, and C.I. Brockbank. 1991. A Field Study of the
Impact on Oysters of Tributyltin Introduction and Removal in a Pristine Lake.
Arch.Environ.Contam.Toxicol. 20(2):276-281.

68549

Field, UEndp, Eff

Smith, B.S.. 1981. Tributyltin Compounds Induce Male Characteristics on
Female Mud Snails Nassarius obsoletus = llyanassa obsoleta. J.Appl.Toxicol.
1 (3): 141 -144.

2503

UChron, Con

Snell, T.W., B.D. Moffat, C. Janssen, and G. Persoone. 1991. Acute Toxicity
Tests Using Rotifers. III. Effects of Temperature, Strain, and Exposure Time
on the Sensitivity of Brachionus plicatilis. Environ.Toxicol.Water Qual. 6:63-
75.

16539

Dur

Spooner, N., P.E. Gibbs, G.W. Bryan, and L.J. Goad. 1991. The Effect of
Tributyltin upon Steroid Titres in the Female Dogwhelk, Nuclella lapillus, and
the Development of Imposex. Mar.Environ.Res. 32(1-4):37-49.

3655

UEndp, Tox

Stenalt, E., B. Johansen, S.V. Lillienskjold, and B.W. Hansen. 1998.
Mesocosm Study of Mytilus edulis Larvae and Postlarvae, Including the
Settlement Phase, Exposed to a Gradient of Tributyltin.

Ecotoxicol. Environ. Saf. 40(3):212-225.

19280

Field, UEndp, Eff, Dur

Stephenson, M.. 1991. A Field Bioassay Approach to Determining Tributyltin
Toxicity to Oysters in California. Mar.Environ.Res. 32(1-4):51-59.

5682

Field, UEndp, Eff

Stroben, E., J. Oehlmann, and P. Fioroni. 1992. Hinia reticulata and Nucella
lapillus. Comparison of Two Gastropod Tributyltin Bioindicators. Mar. Biol.
114(2):289-296.

18430

UEndp, Eff, UChron

Stroemgren, T., and T. Bongard. 1987. The Effect of Tributyltin Oxide on
Growth of Mytilus edulis. Mar.Pollut.Bull. 18(1 ):30-31.

8946

UEndp, Con

Stromgren, T., and T. Bongard. 1987. The Effect of Tributyltin Oxide on
Growth of Mytilus edulis. Mar.Pollut.Bull. 18(1 ):30-31.

3449

UEndp, Con

694

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Sujatha, C.H., S.M. Nair, and J. Chacko. 1996. Tributyltin Oxide Induced
Physiological and Biochemical Changes in a Tropical Estuarine Clam.
Bull.Environ.Contam.Toxicol. 56(2):303-310.

16439

UEndp, Eff

Tsuda, T., S. Aoki, M. Kojima, and H. Harada. 1990. Differences Between
Freshwater and Seawater-Acclimated Guppies in the Accumulation and
Excretion of Tri-N-Butyltin Chloride and Triphenyltin Chloride. Water Res.
24(11):1373-1376.

3486

UEndp, Eff, Con

Valkirs, A.O., B.M. Davidson, and P.F. Seligman. 1987. Sublethal Growth
Effects and Mortality to Marine Bivalves From Long-Term Exposure to
Tributyltin. Chemosphere 16(1):201-220.

12445

UEndp, Con, AF

Van Slooten, K.B., and J. Tarradellas. 1994. Accumulation, Depuration and
Growth Effects of Tributyltin in the Freshwater Bivalve Dreissena polymorpha
Under Field Conditions. Environ.Toxicol.Chem. 13(5):755-762.

4194

Field, UEndp, Eff

Walsh, G.E., L.L. McLaughlan, E.M. Lores, M.K. Louie, and C.H. Deans.
1985. Effects of Organotins on Growth and Survival of Two Marine Diatoms,
Skeletonema costatum and Thalassiosira pseudonana. Chemosphere 14(3-
4):383-392.

11353

Dur, Con

Walsh, G.E., L.L. McLaughlin, M.K. Louie, C.H. Deans, and E.M. Lores. 1986.
Inhibition of ARM Regeneration by Ophioderma brevispina (Echinodermata,
Ophiuroidea) by Tributyltin oxide and Triphenyltin oxide.

Ecot oxi col. E nvi ro n. Chem. 12(1):95-100.

12007

UEndp

Weis, J.S., and K. Kim. 1988. Tributyltin is a Teratogen in Producing
Deformities in Limbs of the Fiddler Crab, Uca pugilator.
Arch.Environ.Contam.Toxicol. 17(5):583-587.

2352

UEndp

Weis, J.S., J. Gottlieb, and J. Kwiatkowski. 1987. Tributyltin Retards
Regeneration and Produces Deformities of Limbs in the Fiddler Crab, Uca
pugilator. Arch.Environ.Contam.Toxicol. 16:321-326.

15091

UEndp

Weis, J.S., P. Weis, and F. Wang. 1987. Developmental Effects of Tributyltin
on the Fiddler Crab, Uca pugilator, and the Killifish, Fundulus heteroclitus. In:
Proc.Oceans, 1987, Halifax, Nova Scotia, Canada, Sept.28-Oct.1, 1987,
Organotin Symposium 4:1456-1460.

4851

UEndp

695

-------
Citation

ECOTOX
EcoRef#

Rejection Code(s)

Comment

Widdows, J., and D.S. Page. 1993. Effects of Tributyltin and Dibutyltin on the
Physiological Energetics of the Mussel, Mytilus edulis. Mar.Environ. Res.
35(3):233-249.

7000

UEndp, Eff

Yamada, H., and K. Takayanagi. 1992. Bioconcentration and Elimination of
Bis(Tributyltin)Oxide (TBTO) and Triphenyltin Chloride (TPTC) in Several
Marine Fish Species. Water Res. 26(12): 1589-1595.

6077

Eff, Dur

Yamada, H., M. Tateishi, and K. Takayanagi. 1994. Bioaccumulation of
Organotin Compounds in the Red Sea Bream (Pagrus major) by Two Uptake
Pathways: Dietary Uptake and Direct Uptake from Water.
Environ.Toxicol.Chem. 13(9): 1415-1422.

13509

UEndp, Eff

Yla-Mononen, L.. 1989. The Effects of Tri-n-Butyltin Chloride (TBTC) on the
Early Life Stages of Perch (Perca fluviatilis L.) in Brackish Water. Aqua Fenn.
19(2): 129-133.

UEndp

Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

the most recent national ambient water quality criteria dataset used to derive the CMC , EPA is providing a transparent
rationale as to why they were not utilized (see below).

For the studies that were not utilized because they were not found to be pertinent to this determination (including failing the
QA/QC procedures listed in Appendix A) upon initial review of the download from ECOTOX, EPA is providing the code that
identifies why EPA determined that the results of the study were not reliable.

General QA/QC failure because non-resident species in Oregon

98 U.S. EPA. 2003. Ambient Water Quality Criteria for Tributyltin (TBT) - Final. EPA-882-R-03-031.

696

-------
Tests with the following species were used in the EPA BE of OR WQS for tributyltin in saltwater, but were not considered in the
CWA review and approval/disapproval action of the standards because these species do not have a breeding wild population in
Oregon's waters:

Crassostrea

virginica

Eastern oyster

U.S. EPA 2000; Roberts 1987

Mercenaria

mercenaria

Hard clam

Roberts 1987

Nucella

lapillus

Atlantic dogwhinkle

Harding et al. 1996

Other Acute tests failins QA/QC by species

Holmesimysis sculpta — Mysid

Davidson, B.M., A.O. Valkirs and P.F. Seligman. 1986a. Acute and Chronic Effects of Tributyltin on the Mysid Acanthomysis
sculpta (Crustacea, Mysidacea). NOSC-TR-1116 or AD-A175-294-8. National Technical Information Service, Springfield, VA.

One LC50 value from an R,M test of 0.42 |ig/L. This test was not used for determining the most representative SMAV in this CWA
review and approval/disapproval action of these standards because the test was not based on the preferred flow-through measured test
conditions; however, other flow-through measured test concentrations were available for these species.

Davidson, B.M., A.O. Valkirs and P.F. Seligman. 1986b. Acute and chronic effects of tributyltin on the mysid Acanthomysis
sculpta (Crustacea, Mysidacea). In: Oceans 86, Vol. 4. Proceeding International Organotin Symposium. Marine Technology
Society, Washington, DC.: 1219-1225.

The LC50 value from an R,M test of 0.42 |ig/L reported in this study is a repeat of the LC50 reported in Davidson et al. (1986a)
above. This test was not used for determining the most representative SMAV in this CWA review and approval/disapproval action of
these standards because the test was not based on the preferred flow-through measured test conditions; however, other flow-through
measured test concentrations were available for these species.

Valkirs, A., B. Davidson and P. Seligman. 1985. Sublethal growth effects and mortality to marine bivalves and fish from long-
term exposure to tributyltin. NOSC-TR-1042 or AD-A162-629-0. National Technical Information Service, Springfield, VA.

One test in this study was not used in this CWA review and approval/disapproval action of these standards because a more sensitive
lifestage was available for this species from this study.

Acartia tonsa - Copepod

U'ren, S.C. 1983. Acute toxicity of bis(tributyltin) oxide to a marine copepod. Mar. Pollut. Bull. 14: 303-306.

697

-------
One LC50 value from an R,U test of 0.6326 |ig/L. This test was not used in this CWA review and approval/disapproval action of
these standards because the test was not based on the preferred flow-through measured test conditions; however, other flow-through
measured test concentrations were available for these species.

Kusk, K.O. and S. Petersen. 1997. Acute and chronic toxicity of tributyltin and linear alkylbenzene sulfonate to the marine
copepod Acartia tonsa. Environ. Toxicol. Chem. 16: 1629-1633.

Two LC50 values from S,U tests ranging from 0.24 to 0.47 |ig/L. These values were not used in this CWA review and
approval/disapproval action of these standards because the test was not based on the preferred flow-through measured test conditions;
however, other flow-through measured test concentrations were available for these species.

Crassostrea gigas — Pacific oyster

Thain, J.E. 1983. The acute toxicity of bis(tributyltin) oxide to the adults and larvae of some marine organisms. Int. Counc.
Explor. Sea, Mariculture Committee E: 13. 5 pp.

One test in this study was not used in this CWA review and approval/disapproval action of these standards because a more sensitive
lifestage was available for this species from this study.

698

-------
Appendix V Zinc (Saltwater)

Studies Not Pertinent to this Determination
(Note: Codes Described in Attachment 3 of Appendix B)

Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Abel, P.D.. 1976. Effects of Some Pollutants on the Filtration Rate of
Mytilus. Mar.Pollut.Bull. 7:228-231.

415

Con

More sensitive endpoint exists

Ahsanullah, M., and A.R. Williams. 1991. Sublethal Effects and
Bioaccumulation of Cadmium, Chromium, Copper, and Zinc in the Marine
Amphipod Allorchestes compressa. Mar.Biol. 108:59-65.

331

Eff

Ahsanullah, M., and G.H. Arnott. 1978. Acute Toxicity of Copper, Cadmium,
and Zinc to Larvae of the Crab Paragrapsus quadridentatus (H. Milne
Edwards), and Implications for Water. Aust.J.Mar.Freshwater Res. 29(1): 1 -
8.

8296

Eff

Ahsanullah, M., D.S. Negilski, and M.C. Mobley. 1981. Toxicity of Zinc,
Cadmium and Copper to the Shrimp Callianassa australiensis. I. Effects of
Individual Metals. Mar.Biol. 64(3):299-304(Author Communication Used).

15338

Eff

Ahsanullah, M., D.S. Negilski, and M.C. Mobley. 1981. Toxicity of Zinc,
Cadmium and Copper to the Shrimp Callianassa australiensis. III.
Accumulation of Metals. Mar.Biol.64(3):311-316 (Used Ref 15338) (Author
Communication Used).

15339

Eff

Ahsanullah, M., M.C. Mobley, and P. Rankin. 1988. Individual and
Combined Effects of Zinc, Cadmium and Copper on the Marine Amphipod
Allorchestes compressa. Aust.J.Mar.Freshwater Res. 39(1):33-37.

13187

NonRes

Ahsanullah, M.. 1976. Acute Toxicity of Cadmium and Zinc to Seven
Invertebrate Species From Western Port, Victoria. Aust.J.Mar.Freshwater
Res. 27(2):187-196.

2445

NonRes

699

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Ajmalkhan, S., K. Rajendran, and R. Natarajan. 1986. Effect of Zinc on
Zoeal Development of the Estuarine Hermit Crab Clibanarius olivaceus
(Henderson). Proc.lndian Acad.Sci.Anim.Sci. 95(5):515-524.

3985

UEndp

Amado Filho, G.M., C.S. Karez, L.R. Andrade, Y. Yoneshigue-Valentin, and
W.C. Pfeiffer. 1997. Effects on Growth and Accumulation of Zinc in Six
Seaweed Species. Ecotoxicol.Environ.Saf. 37:223-228.

18321

UEndp

Amado Filho, G.M., C.S. Karez, W.C. Pfeiffer, Y. Yoneshigue-Valentin, and
M. Farina. 1996. Accumulation, Effects on Growth, and Localization of Zinc
in Padina gymnospora (Dictyotales, Phaeophyceae). Hydrobiologia
326/327:451-456.

17512

UEndp, Eff

Amiard, J.C., C. Amiard-Triquet, B. Berthet, and C. Metayer. 1987.
Comparative Study of the Patterns of Bioaccumulation of Essential (Cu, Zn)
and Non-Essential (Cd, Pb) Trace Metals in Various Estuarine and Coastal
Organ. J.Exp.Mar.BioI.Ecol. 106(1):73-89.

7913

UEndp, Eff, Con

Amiard-Triquet, C., J.C. Amiard, R. Ferrand, A.C. Andersen, and M.P.
Dubois. 1986. Disturbance of a Met-Enkephalin-Like Hormone in the
Hepatopancreas of Crabs Contaminated by Metals. Ecotoxicol.Environ.Saf.
11 (2): 198-209.

12111

UEndp, Eff

Anderson, B.S., and J.W. Hunt. 1988. Bioassay Methods for Evaluating the
Toxicity of Heavy Metals, Biocides and Sewage Effluent Using Microscopic
Stages of Giant Kelp Macrocystis pyrifera. Mar.Environ. Res. 26(2): 113-134.

2349

Dur

Six 48hr NOEC's

Andrade, L., S.M.F. Azevedo, and W.C. Pfeiffer. 1994. Effects of High Zinc
Concentrations in Phytoplankton Species from Sepetiba Bay (Brazil).
Arq.Biol.Tecnol. 37(3):655-666.

19200

UEndp

700

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Andryushchenko, V.V., and G.G. Polikarpov. 1974. An Experimental Study
of Uptake of Zn65 and DDT by Ulva rigida From Seawater Polluted with
Both Agents. Hydrobiol.J.10(4):41-46 / Gidrobiol Zh. 10(4):56-62 (RUS).

7588

Eff, Con

Arnott, G.H., and M. Ahsanullah. 1979. Acute Toxicity of Copper, Cadmium
and Zinc to Three Species of Marine Copepod. Aust.J.Mar.Freshwater Res.
30(1):63-71.

5563

Dur, Con

24hr only

Aunaas, T., S. Einarson, T.E. Southon, and K.E. Zachariassen. 1991. The
Effects of Organic and Inorganic Pollutants on Intracellular Phosphate
Compounds in Blue Mussels (Mytilus edulis). Comp.Biochem.Physiol.C
100(1/2):89-93.

3968

UEndp, Eff

Baby, K.V., and N.R. Menon. 1986. Oxygen Uptake in the Brown Mussel,
Perna indica (Kuriakose & Nair) Under Sublethal Stress of Hg, Cd & Zn.
Indian J.Mar.Sci. 15(2): 127-128.

12318

UEndp, AF, NonRes

Bat, L.. 1997. Studies on the Uptake of Copper, Zinc and Cadmium by the
Amphipod Corophium volutator (Pallas) in the Laboratory. Turk.J.Mar.Sci.
3(2):93-109.

19858

UEndp

Benijts-Claus, C., and F. Benijts. 1975. The Effect of Low Lead and Zinc
Concentrations on the Larval Development of the Mud-Crab
Rhithropanopeus harrisii Gould. In: J.H.Koeman and J.J.T.W.A.Strik (Eds.),
Sublethal Effects of Toxic Chemicals on Aquat.Animals, Elsevier Sci.Publ.,
Amsterdam, NY :43-52.

15451

UEndp

Bervoets, L., R. Blust, and R. Verheyen. 1996. Uptake of Zinc by the Midge
Larvae Chironomus riparius at Different Salinities: Role of Speciation,
Acclimation, and Calcium. Environ.Toxicol.Chem. 15(8):1423-1428.

17236

UEndp

Boikova, E.E.. 1978. Effect of Zinc Acetate on Paramecium putrinum.
Protozoologiya 3:105-111 (RUS) (ENGABS).

6998

UEndp, Dur, Con

701

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Bologa, A.S.. 1984. Uptake of 59Fe, 65Zn and 85Sr by Mytilus
galloprovincialis and Mya arenaria from the Romanian Black Sea Shore.
Cercet. Mar.(Rech. Mar.) 17:285-295.

4090

Eff, Con

Botton, M.L., K. Johnson, and L. Helleby. 1998. Effects of Copper and Zinc
on Embryos and Larvae of the Horseshoe Crab, Limulus polyphemus.
Arch.Environ.Contam.Toxicol. 35(1):25-32.

19307

Dur

ECOTOX provides six 48- and 72-h LC50s
of <94.6->946000 |jg/L for this study. This
value could have been considered for
EPA's evaluation of saltwater zinc, but the
species is relatively insensitive to zinc
compared to others. Some LC50s for this
species were entered into ECOTOX as
approximate values or ranges.

Boyden, C.R., H. Watling, and I. Thornton. 1975. Effect of Zinc on the
Settlement of the Oyster Crassostrea gigas. Mar.Biol. 31(3):227-234.

15885

UEndp

Braek, G.S., D. Malnes, and A. Jensen. 1980. Heavy Metal Tolerance of
Marine Phytoplankton. IV. Combined Effect of Zinc and Cadmium on Growth
and Uptake in Some Marine Diatoms. J.Exp.Mar.Biol.Ecol. 42:39-54.

9761

UEndp, Con

Brereton, A., H. Lord, I. Thornton, and J.S. Webb. 1973. Effect of Zinc on
Growth and Development of Larvae of the Pacific Oyster Crassostrea gigas.
Mar.Biol. 19(2):96-101.

8776

UEndp

Brown, B., and M. Ahsanullah. 1971. Effect of Heavy Metals on Mortality
and Growth. Mar.Pollut.Bull. 2:182-187.

2467

LT, Con

Brown, C.L., and S.N. Luoma. 1995. Use of the Euryhaline Bivalve
Potamocorbula amurensis as a Biosentinel Species to Assess Trace Metal
Contamination in San Francisco Bay. Mar.Ecol.Prog.Ser. 124(1-3):129-142.

18036

UEndp, Eff

Bryan, G.W.. 1969. The Absorption of Zinc and Other Metals by the Brown
Seaweed Laminaria digitata. J.Mar.Biol.Assoc.U.K. 49(1):225-243.

2268

UEndp, Con

Bryan, G.W.. 1969. The absorption of zinc and other metals by the brown
seaweed, Laminaria digitata.. J. Mar. Biol. Assoc. U.K. 49: 225-243..

Eff

702

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Bryant, V., D.M. Newbery, D.S. McKlusky and R. Campbell. 1985. Effect of
temperature and salinity on the toxicity of nickel and zinc to two estuarine
invertebrates (Corophium volutator, Macoma balthica). Mar. Ecol. Prog. Ser.
24: 139-153..

NonRes

Bryant, V., D.M. Newbery, D.S. McLusky, and R. Campbell. 1985. Effect of
Temperature and Salinity on the Toxicity of Nickel and Zinc to Two
Estuarine Invertebrates (Corophium volutator, Macoma balthica).

Mar. Ecol. Prog. Ser. 24(1 -2): 139-153.

11875

NonRes

Burbidge, F.J., D.J. Macey, J. Webb, and V. Talbot. 1994. A Comparison
Between Particulate (Elemental) Zinc and Soluble Zinc (ZnCI2) Uptake and
Effects in the Mussel, Mytilus edulis. Arch.Environ.Contam.Toxicol.
26(4):466-472.

13661

UEndp

Burdin, K.S., and K.T. Bird. 1994. Heavy Metal Accumulation by
Carrageenan and Agar Producing Algae. Bot.Mar. 37:467-470.

45156

UEndp, Eff

24hr only

Burton, D.T., and D.J. Fisher. 1990. Acute Toxicity of Cadmium, Copper,
Zinc, Ammonia, 3,3'-Dichlorobenzidine, 2,6-Dichloro-4-nitroaniline,
Methylene Chloride, and 2,4,6-Trichlorophenol.

Bull. Environ.Contam .Toxicol. 44(5):776-783.

3163

Con, Dur

Calabrese, A., J.R. Maclnnes, D.A. Nelson, and J.E. Miller. 1977. Survival
and Growth of Bivalve Larvae Under Heavy-Metal Stress. Mar.Biol. 41:179-
184.

9064

Con, UEndp

Calapaj, G.G.. 1974. Ricerche Di Laboratorio SuN'Inquinamento Chimico Dei
Mitili Nota II: Cadmio, Zinco. (Chemical Pollution of Mytilus. II. Cadmium and
Zinc). Ig.Mod. 67(2):136-145 (ITA) (ENG ABS).

8508

UEndp, Eff

703

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Canli, M., and R.W. Furness. 1993. Toxicity of Heavy Metals Dissolved in
Sea Water and Influences of Sex and Size on Metal Accumulation and
Tissue Distribution in the Norway Lobster. Mar.Environ.Res. 36(4):217-236.

4563

UEndp, Eff

Canterford, G.S., A.S. Buchanan, and S.C. Ducker. 1978. Accumulation of
Heavy Metals by the Marine Diatom Ditylum brightwellii (West) Grunow.
Aust.J.Mar.Freshwater Res. 29(5):613-622.

15455

UEndp, Con

Canterford, G.S., and D.R. Canterford. 1980. Toxicity of Heavy Metals to the
Marine Diatom Ditylum brightwellii (West) Grunow: Correlation between
Toxicity and Metal Speciation. J. Mar. Biol .Assoc. U.K. 60(1):227-242.

6405

UEndp

5d EC50 for a Diatom

Carvalho, R.A., M.C. Benfield, and P.H. Santschi. 1999. Comparative
Bioaccumulation Studies of Colloidally Complexed and Free-Ionic Heavy
Metals in Juvenile Brown Shrimp Penaeus aztecus (Crustacea: Decapoda:
Penaeidae). Limnol.Oceanogr. 44(2):403-414.

48059

Eff

Chan, H.M., and P.S. Rainbow. 1993. On the Excretion of Zinc by the Shore
Crab Carcinus maenas (L.). Ophelia 38(1):31-45.

17027

UEndp, Eff

Chan, H.M., and P.S. Rainbow. 1993. The Accumulation of Dissolved Zinc
by the Shore Crab Carcinus maenas (L.). Ophelia 38(1): 13-30.

17026

Eff

Chan, H.M., P. Bjerregaard, P.S. Rainbow, and M.H. Depledge. 1992.
Uptake of Zinc and Cadmium by Two Populations of Shore Crabs Carcinus
maenas at Different Salinities. Mar.Ecol.Prog.Ser. 86(1):91-97.

7546

UEndp, Eff

Chan, H.M. 1988. Accumulation and Tolerance to Cadmium, Copper, Lead
and Zinc by the Green Mussel Perna viridis. Mar.Ecol.Prog.Ser. 48(3):295-
303.

2970

UEndp, Eff

ECOTOX provides a 96-h LC50 of 5761
|jg/L for this study. This value could have
been considered for EPA's evaluation of
saltwater zinc, but the species is relatively
insensitive to zinc compared to others.

704

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Chapman, P.M., and C. McPherson. 1993. Comparative Zinc and Lead
Toxicity Tests with Arctic Marine Invertebrates and Implications for Toxicant
Discharges. Polar Rec.29(168):45-54; In: E.G.Baddaloo, S.Ramamoorthy
and J.W.Moore (Eds.), Proc.19th Annual Aquatic Toxicity Workshop, Oct.4-
7, 1992, Edmondton, Alberta, Can.Tech.Rep.Fish.Aquat.Sci.No.1942:7-22.

4092

UEndp, Dur

Chen, J.C., and P.C. Liu. 1987. Accumulation of Heavy Metals in the Nauplii
of Artemia salina. J.World Aquacult.Soc. 18(2):84-93.

2749

UEndp, Eff

Chung, K.S.. 1980. Acute Toxicity of Selected Heavy Metals to Mangrove
Oyster Crassostrea rhizophorae. Bull.Jpn.Soc.Sci.Fish.(Nippon Suisan
Gakkaishi) 46(6):777-780.

5308

Con

Clarke, G.L.. 1947. Poisoning and Recovery in Barnacles and Mussels.
Biol.Bull. 92:73-91.

14811

UENdp

Conroy, P.T., J.W. Hunt, and B.S. Anderson. 1996. Validation of a Short-
Term Toxicity Test Endpoint by Comparison with Longer-Term Effects on
Larval Red Abalone Haliotis rufescens. Environ.Toxicol.Chem. 15(7): 1245-
1250.

17224

Dur, UChron

Cotter, A.J.R., D.J.H. Phillips, and M. Ahsanullah. 1982. The Significance of
Temperature, Salinity and Zinc as Lethal Factors for the Mussel Mytilus
edulis in a Polluted Estuary. Mar.Biol. 68(2): 135-141.

15528

UEndp

Crespo, S., and J. Balasch. 1980. Mortality, Accumulation, and Distribution
of Zinc in the Gill System of the Dogfish Following Zinc Treatment.
Bull.Environ.Contam.Toxicol. 24(6):940-944.

2844

Con, Dur

Crespo, S., and R. Sala. 1986. Ultrastructural Alterations of the Dogfish
(Scyliorhinus canicula) Gill Filament Related to Experimental Aquatic Zinc
Pollution. Dis.Aquat.Org. 1(2):99-104.

12525

UEndp, Eff

705

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Crespo, S., E. Soriano, C. Sampera, and J. Balasch. 1981. Zinc and Copper
Distribution in Excretory Organs of the Dogfish Scyliorhinus canicula and
Chloride Cell Response Following Treatment with Zinc Sulphate. Mar.Biol.
65(2): 117-123.

15350

UEndp, Con

Cui, K., Y. Liu, and L. Hou. 1987. Effects of Six Heavy Metals on Hatching
Eggs and Survival of Larval of Marine Fish. Oceanol.Limnol.Sin./Haiyang Yu
Huzhao 18(2): 138-144 (CHI) (ENG ABS).

3222

Con

Davies, N.A., and K. Simkiss. 1996. The Uptake of Zinc from Artificial
Sediments by Mytilus edulis. J.Mar.Biol.Assoc.U.K. 76:1073-1079.

18668

UEndp, Eff

Davies, N.A., M.G. Taylor, and K. Simkiss. 1997. The Influence of Particle
Surface Characteristics on Pollutant Metal Uptake by Cells. Environ.Pollut.
96(2): 179-184.

18661

UEndp, Eff

Denton, G.R.W., and C. Burdon-Jones. 1986. Environmental Effects on
Toxicity of Heavy Metals to Two Species of Tropical Marine Fish from
Northern Australia. Chem.Ecol. 2(3):233-249.

4327

See note

ECOTOX provides two 96-h LC50s of
17501 |jg/L and 11825 |jg/L for this study.
These values could have been considered
for EPA's evaluation of saltwater zinc, but
the species is relatively insensitive to zinc
compared to others.

Deutch, B., B. Borg, L. Kloster, H. Meyer, and M.M. Moller. 1980. The
Accumulation of 65Zn by Various Marine Organisms. Ophelia (Suppl 1):235-
240.

9785

Eff

Devi, V.U., and Y.P. Rao. 1989. Heavy Metal Toxicity to Fiddler Crabs, Uca
annulipes Latreille and Uca triangularis (Milne Edwards): Respiration on
Exposure to Copper, Mercury,. Bull.Environ.Contam.Toxicol. 43(1):165-172.

2150

UEndp, Eff

Devi, V.U., and Y.P. Rao. 1989. Zinc Accumulation in Fiddler Crabs Uca
annulipes Latreille and Uca triangularis (Milne Edwards).

Ecotoxicol. Environ. Saf. 18(2):129-140.

2385

UEndp, Eff, Con

706

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Devi, V.U.. 1987. Heavy Metal Toxicity to Fiddler Crabs, Ilea annulipes
latreille and Ilea triangularis (Milne Edwards): Tolerance to Copper,
Mercury, Cadmium. Bull.Environ.Contam.Toxicol. 39:1020-1027.

2602

NonRes

Devineau, J., and C.A. Triquet. 1985. Patterns of Bioaccumulation of an
Essential Trace Element (Zinc) and a Pollutant Metal (Cadmium) in Larvae
of the Prawn Palaemon serratus. Mar.Biol. 86(2):139-143.

10835

UEndp

Drifmeyer, J.E.. 1980. Uptake of 65Zn by Eelgrass, Zostera marina, L.
Sci.Total Environ. 16(3):263-265.

9789

UEndp, Eff, Con

Durkina, V.B.. 1994. Development of Offspring of the Sea Urchin
Strongylocentrotus intermedius Exposed to Copper and Zinc.
Russ.J.Mar.Biol. 20(4):232-235.

17580

UEndp

Earnshaw, M.J., S. Wilson, H.B. Akberali, R.D. Butler, and K.R.M. Marriott.
1986. The Action of Heavy Metals on the Gametes of the Marine Mussel,
Mytilus edulis(L.)-lll. The Effect of Applied Copper and Zinc on Sperm
Motility in. Mar.Environ.Res. 20(4):261-278.

12324

UEndp

Eisler, R., and G.R. Gardner. 1973. Acute Toxicology to an Estuarine
Teleost of Mixtures of Cadmium, Copper and Zinc Salts. J.Fish Biol.
5(2):131-142.

8342

UEndp, Eff

Eldon, J., M. Pekkarinen, and R. Kristoffersson. 1980. Effects of Low
Concentrations of Heavy Metals on the Bivalve Macoma balthica.
Ann.Zool.Fenn. 17:233-242.

17309

UEndp, Eff

Elliott, N.G., R. Swain, and D.A. Ritz. 1985. The Influence of Cyclic
Exposure on the Accumulation of Heavy Metals by Mytilus edulis planulatus
(Lamarck). Mar.Environ.Res. 15(1):17-30.

11669

UEndp, Eff, Con

Elliott, N.G., R. Swain, and D.A. Ritz. 1986. Metal Interaction During
Accumulation by the Mussel Mytilus edulis planulatus. Mar.Biol. 93(3):395-
399.

12054

UEndp, Eff

707

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Fernandez, T.V., and N.V. Jones. 1990. Studies on the Toxicity of Zinc and
Copper Applied Singly and Jointly to Nereis diversicolor at Different
Salinities and Temperatures. Trop.Ecol. 31(1):47-55.

7744

Con, UEndp, LT

Fisher, N.S., and D. Frood. 1980. Heavy Metals and Marine Diatoms:
Influence of Dissolved Organic Compounds on Toxicity and Selection for
Metal Tolerance Among Four Species. Mar.Biol. 59(2):85-93.

6470

UEndp

Fisher, N.S., and G.J. Jones. 1981. Heavy Metals and Marine
Phytoplankton: Correlation of Toxicity and Sulfhydryl-Binding. J.Phycol.
17(1): 108-111.

14681

Dur

Has 24-72hr EC50 for a diatom

Fisher, N.S., M. Bohe, and J.L. Teyssie. 1984. Accumulation and Toxicity of
Cd, Zn, Ag, and Hg in Four Marine Phytoplankters. Mar.Ecol.Prog.Ser.
18(3):201-213.

11805

UEndp, Eff

Foster, P.. 1976. Concentrations and concentration factors of heavy metals
in brown algae. Environ. Pollut. 10: 45-53.

Eff, Det

Fowler, S.W., and L.F. Small. 1970. Distribution of Ingested Zinc-65 in the
Tissues of Some Marine Crustaceans. J.Fish.Res.Board Can. 27(6):1051-
1058.

9563

UEndp, Eff, Con

Gajbhiye, S.N., and R. Hirota. 1990. Toxicity of Heavy Metals to Brine
Shrimp Artemia. J.Indian Fish.Assoc. 20:43-50.

17792

UEndp

Brine Shrimp

Garnham, G.W., G.A. Codd, and G.M. Gadd. 1992. Kinetics of Uptake and
Intracellular Location of Cobalt, Manganese and Zinc in the Estuarine Green
Alga Chlorella salina. Appl.Microbiol.Biotechnol. 37(2):270-276.

6220

UEndp, Eff

Gnassia-Barelli, M., and M. Romeo. 1987. Uptake of Zinc by Cultured
Phytoplankters Hymenomonas elongata. Dis.Aquat.Org. 3(1):45-49.

4242

UEndp, Eff

708

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Goh, B.P.L., and L.M. Chou. 1997. Effects of the Heavy Metals Copper and
Zinc on Zooxanthellae Cells in Culture. Environ.Monit.Assess. 44:11-19.

45184

UEndp

Gray, J.S., and R.J. Ventilla. 1973. Growth Rates of Sediment-Living Marine
Protozoan as a Toxicity Indicator for Heavy Metals. Ambio 2(4): 118-121.

6355

UEndp

Gray, J.S.. 1974. Synergistic Effects of Three Heavy Metals on Growth
Rates of a Marine Ciliate Protozoan. In: F.J.Vernberg and W.B.Vernberg
(Eds.), Pollution and Physiology of Marine Organisms, Academic Press, NY
:465-485.

8558

UEndp

Greenwood, J.G., and D.R. Fielder. 1983. Acute Toxicity of Zinc and
Cadmium to Zoeae of Three Species of Portunid Crabs (Crustacea:
Brachyura). Comp.Biochem.Physiol.C 75(1):141 -144.

10063

Dur, NonRes

Hansen, I.V., J.M. Weeks, and M.H. Depledge. 1995. Accumulation of
Copper, Zinc, Cadmium and Chromium by the Marine Sponge Halichondria
panicea Pallas and the Implications for Biomonitoring. Mar.Pollut.Bull. 31(1-
3): 133-138.

18038

UEndp, Eff

Haritonidis, S., H.J. Jager, and H.O. Schwantes. 1983. Accumulation of
Cadmium, Zinc, Copper and Lead by Marine Macrophyceae Under Culture
Conditions. Angew.Bot. 57(5/6):311-330.

11369

UEndp, Eff

Haritonidis, S.. 1985. Uptake of Cd, Zn, Cu and Pb by Marine
Macrophyceae Under Culture Conditions. Mar.Environ.Res. 17(2-4):198-
199.

6414

UEndp, Eff, Con

Harland, A.D., G.W. Bryan, and B.E. Brown. 1990. Zinc and Cadmium
Absorption in the Symbiotic Anemone Anemonia viridis and the Non-
Symbiotic Anemone Actinia equina. J.Mar.Biol.Assoc.U.K. 70(4):789-802.

7819

UEndp, Eff

709

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Harmon, V.L., and C.J. Langdon. 1996. A 7-D Toxicity Test for Marine
Pollutants Using the Pacific Mysid Mysidopsis intii. 2. Protocol Evaluation.
Environ.Toxicol.Chem. 15(10):1824-1830.

17251

UChron?

Has Seven values made up of 7d LC50's
and 7d NOEC's for Opossum shrimp and
mysids

Haya, K., B.A. Waiwood, and D.W. Johnston. 1983. Adenylate Energy
Charge and ATPase Activity of Lobster (Homarus americanus) During
Sublethal Exposure to Zinc. Aquat.Toxicol./

Can.Tech.Rep.Fish.Aquat.Sci.No.1151.(1987) p.87-188 (ABS) 3(2):115-126.

5632

UEndp, Eff

Herbert, D.W.M., and A.C. Wakeford. 1964. The Susceptibility of Salmonid
Fish to Poisons Under Estuarine Conditions -1. Zinc Sulphate. Int.J.Air
Water Pollut. 8(3/4):251-256.

14398

Dur

has two 48hr LC50's for rainbow trout

Heyward, A.J.. 1988. Inhibitory Effects of Copper and Zinc Sulphates on
Fertilization in Corals. In: Proc.6th Int.Coral Reef.Symp., Aug.8-12, 1988,
Australia 2:299-303.

4735

UEndp

Hietanen, B., I. Sunila, and R. Kristoffersson. 1988. Toxic Effects of Zinc on
the Common Mussel Mytilus edulis L. (Bivalvia) in Brackish Water. I.
Physiological and Histopathological Studies. Ann.Zool.Fenn. 25(4):341-347.

2361

Dur, UEndp

24hr only

Hietanen, B., I. Sunila, and R. Kristoffersson. 1988. Toxic Effects of Zinc on
the Common Mussel Mytilus edulis L. (Bivalvia) in Brackish Water. II.
Accumulation Studies. Ann.Zool.Fenn. 25(4):349-352.

3685

UEndp, Eff

Hilmy, A.M., N.F. Abdel-Hamid, and K.S. Ghazaly. 1985. Toxic Effects of
Both Zinc and Copper on Size and Sex of Portunus pelagicus (L)
(Crustacea: Decapoda). Bull.Inst.Oceanogr.Fish.(Cairo) 11:207-215.

17415

NonRes

Has four 96hr LC50's for crab

710

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Ho, M.S., and P.L. Zubkoff. 1982. The Effects of Mercury, Copper, and Zinc
on Calcium Uptake by Larvae of the Clam, Mulinia lateralis. Water Air Soil
Pollut. 17(4):409-414.

15513

UEndp, Eff

Hollibaugh, J.T., D.L.R. Seibert, and W.H. Thomas. 1980. A Comparison of
the Acute Toxicities of Ten Heavy Metals to Phytoplankton From Saanich
Inlet, B.C., Canada. Estuar.Coast.Mar.Sci. 10(1):93-105.

5282

UEndp, Con

Hopkins, R., and J.M. Kain. 1971. The Effect of Marine Pollutants on
Laminarea hyperboria. Mar.Pollut.Bull. 2(5):75-77.

9356

UEndp, Con

Howell, R.. 1983. Heavy Metals in Marine Nematodes: Uptake, Tissue
Distribution and Loss of Copper and Zinc. Mar.Pollut.Bull. 14(7):263-268.

11121

UEndp, Eff, Con

Hunt, J.W., B.S. Anderson, S.L. Turpen, A.R. Coulon, M. Martin, F.H.
Palmer, and J.J. Janik. 1989. Marine Bioassay Project. 4th Report.
Experimental Evaluation of Effluent Toxicity Testing Protocols with Giant
Kelp, Mysids, Red Abalone. No.89-5WQ, State Water Resources Control
Board, State of California, Sacramento, CA :144.

19130

Dur

Ismail, P.. 1988. Influence of Salinity on the Toxicity of Zinc and Copper to
Guppy. Malays.Appl.Biol. 17(1 ):31 -38.

2882

Con

Ithack, E., and C.P. Gopinathan. 1995. The Effect of Heavy Metals on the
Physiological Changes of Microalgae. Cmfri Spec.Publ. 61:45-52.

19399

UEndp

Itow, T., R.E. Loveland, and M.L. Botton. 1998. Developmental
Abnormalities in Horseshoe Crab Embryos Caused by Exposure to Heavy
Metals. Arch.Environ.Contam.Toxicol. 35(1):33-40.

19470

UEndp

711

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Itow, T., T. Igarashi, M.L. Botton, and R.E. Loveland. 1998. Heavy Metals
Inhibit Limb Regeneration in Horseshoe Crab Larvae.
Arch.Environ.Contam.Toxicol. 35(3):457-463.

20180

UEndp

Jayaseeli, A.C., and J. Azariah. 1993. Accumulation and Distribution of Zinc
in Green Mussel Perna viridis (Linnaeus). Pollut.Res. 12(3): 127-133.

14820

Eff, Dur

Appears to be one or two values for perna
viridis

Jensen, A., B. Rystad, and S. Melsom. 1974. Heavy Metal Tolerance of
Marine Phytoplankton. I. The Tolerance of Three Algal Species to Zinc in
Coastal Sea Water. J.Exp.Mar.BioI.Ecol. 15(2):145-157.

2269

UEndp, Eff

Johnson, I.T., and M.B. Jones. 1990. Effects of Zinc on Osmoregulation of
Gammarus duebeni (Crustacea: Amphipoda) from the Estuary and the
Sewage Treatment Works at Looe, Cornwall. Ophelia 31 (3): 187-196.

18866

UEndp

Kaitala.S.. 1988. Multiple Toxicity and Accumulation of Heavy Metals in Two
Bivalve Mollusc Species. Water Sci.Technol. 20(6/7):23-32.

905

UEndp, Eff

Kaland, T., T. Andersen, and K. Hylland. 1993. Accumulation and
Subcellular Distribution of Metals in the Marine Gastropod Nassarius
reticulatus L. In: R.Dallinger and P.S.Rainbow (Eds.), Ecotoxicology of
Metals in Invertebrates, Lewis Publ. :37-53.

13829

UEndp, Eff

Karaseva, E.M., and L.A. Medvedeva. 1993. Morphological and Functional
Changes in the Offspring of Mytilus trossulus and Mizuhopecten yessoensis
After Parental Exposure to Copper and Zinc. Russ.J.Mar.Biol.19(4):276-280;
Biol.Morya (Vladivost) (4):83-89 (RUS).

17028

UEndp

Karaseva, E.M.. 1993. Accumulation of Heavy Metals in Gonads and
Somatic Organs of Bivalve Molluscs. Biol.Morya (Vladivost.) 2:66-76 (ENG
TRANSL, RUS Paper Attached).

4644

UEndp, Eff

712

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Karbe, L.. 1972. Marine Hydroids as Test Organisms for Assessing the
Toxicity of Water Pollutants. The Effect of Heavy Metals on Colonies of
Eirene viridula. Mar.Biol. 12(4):316-328 (GER) (ENG ABS).

15654

UEndp, Con

Karez, C.S., G.M. Amado, R.P. Luoro, and M. Farina. 1996. Accumulation of
Zinc by the Brown Alga Padina gymnospora. Bull.Inst.Oceanogr.Monaco
14(4):233-238.

20401

UEndp

Karez, C.S., M. Romeo, and M. Gnassia-Barelli. 1988. Uptake of Zn and Cd
by Coastal Phytoplankton Species in Culture. In: U.Seeliger, L.D.De
Lacerda, and S.R.Patchineelam (Eds.) Metals in Coastal Environments of
Latin America, Springer-Verlag New York, Inc., Secaucus, NJ :130-139.

13214

UEndp

Kobayashi, N., T.K. Naidenko, and M.A. Vashchenko. 1994. Standardization
of a Bioassay Using Sea-Urchin Embryos. Russ.J.Mar.Biol. 20(6):351-357.

16686

UEndp

Kobayashi, N.. 1971. Fertilized Sea Urchin Eggs As an Indicatory Material
for Marine Pollution Bioassay, Preliminary Experiments. Mar.Biol.Lab
18(6):379-406.

2963

UEndp

Kobayashi, N.. 1990. Marine Pollution Bioassay by Sea Urchin Eggs, an
Attempt to Enhance Sensitivity. Publ.Seto Mar.Biol.Lab. 34(4-6):225-237.

9717

UEndp, Dur

Krishnakumari, L.P.K.V., S.N. Gajbhiye, K. Govindan, and V.R. Nair. 1983.
Toxicity of Some Metals on the Fish Therapon jarbua (Forsskal, 1775).
Indian J.Mar.Sci. 12(1):64-66.

11014

Con

Kumar, K.P., and V.U. Devi. 1995. Effect of Heavy Metals on Toxicity and
Oxygen Consumption of Intertidal Gastrodpods nerita albicilla and Nerita
chamaeleon. J.Ecotoxicol.Environ.Monit. 5(1 ):1 -5.

18886

NonRes

Lakshmanan, P.T., and P.N.K. Nambisan. 1989. Bioaccumulation and
Depuration of Some Trace Metals in the Mussel, Perna viridis (Linnaeus).
Bull.Environ.Contam.Toxicol. 43(1 ):131-138.

3240

Eff

713

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

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14402

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5185

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51695

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715

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Martin, M., K.E. Osborn, P. Billig, and N. Glickstein. 1981. Toxicities of Ten
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716

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McKenney, C.L.Jr., and J.M. Neff. 1981. The Ontogeny of Resistance
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17414

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Mizrahi, L., L. Newberger-Cywiak, and Y. Achituv. 1993. Effect of Heavy
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12895

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52573

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6225

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Nelson, D.A., J.E. Miller, and A. Calabrese. 1988. Effect of Heavy Metals on
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Nott, J.A., and W.J. Langston. 1993. Effects of Cadmium and Zinc on the
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Nugegoda, D., and P.S. Rainbow. 1988. Zinc Uptake and Regulation by the
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15868

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Pagano, G., M. Cipollaro, G. Corsale, A. Esposito, E. Ragucci, G.G.
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Pagliarani, A., V. Ventrella, F. Trombetti, M. Pirini, G. Trigari, and A.R.
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Rejection Code(s)

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Persoone, G., and G. Uyttersprot. 1975. The Influence of Inorganic and
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Price, R.K.J., and R.F. Uglow. 1980. Cardiac and Ventilatory Responses of
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Rejection Code(s)

Comment

Rainbow, P.S., A.G. Scott, E.A. Wiggins, and R.W. Jackson. 1980. Effect of
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Rainbow, P.S.. 1985. Accumulation of Zn, Cu and Cd by Crabs and
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Rejection Code(s)

Comment

Reish, D.J., and T.V. Gerlinger. 1984. The Effects of Cadmium, Lead, and
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4007

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Sanpera, C., M. Vallribera, and S. Crespo. 1983. Zn, Cu, and Mn Levels in
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Rejection Code(s)

Comment

Sauer, G.R., and N. Watabe. 1989. Temporal and Metal-Specific Patterns in
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ECOTOX
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Rejection Code(s)

Comment

Shuster, C.N.Jr., and B.H. Pringle. 1969. Trace Metal Accumulation by the
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Assoc. 59:91-103.

Eff

Sivadasan, C.R., P.N.K. Nambisan, and R. Damodaran. 1986. Toxicity of
Mercury, Copper and Zinc to the Prawn Metapenaeus dobsoni (Mier).
Curr.Sci. 55(7):337-340.

11853

Con

Smith, M.A.. 1983. The Effect of Heavy Metals on the Cytoplasmic Fine
Structure of Skeletonema costatum (Bacillariophyta). Protoplasma
116(1 ):14-23.

11036

Con, Eff, UEndp

Sobral, P., L. Castro, H. Costa, and I. Peres. 1995. The Influence of Diet on
the Accumulation of Copper and Zinc in the Clam Ruditapes decussatus.
Physiological Assessment. In: D.Bellan, G.Bonin, and C.Emig (Eds.),
Functioning and Dynamics of Natural and Perturbed Ecosystems, Lavoisier
Intercept Ltd., Paris, France :583-591.

19364

UEndp, Eff

Somasundaram, B., P.E. King, and S.E. Shackley. 1984. Some
Morphological Effects of Zinc upon the Yolk-Sac Larvae of Clupea harengus
L. J.Fish Biol. 25(3):333-343.

11169

UEndp

Somasundaram, B., P.E. King, and S.E. Shackley. 1984. The Effect of Zinc
on the Ultrastructure of the Trunk Muscle of the Larva of Clupea harengus L.
Com p. Biochem. Physiol .C 79(2):311-315.

11222

UEndp

726

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Soto, M., 1. Quincoces, X. Lekube, and 1. Marigomez. 1998.
Automethallographed Metal Content in Digestive Cells of Winkles: ACost-
Effecive Screening Tool for Monitoring Cu and Zn Pollution. Aquat.Toxicol.
40(2/3): 123-140.

18951

UEndp, Eff

Stauber, J.L., and T.M. Florence. 1990. Mechanism of Toxicity of Zinc to the
Marine Diatom Nitzschia closterium. Mar.Biol. 105(3):519-524.

3256

UEndp

Has an IC50 for a diatom

Stromgren, T.. 1982. Effect of Heavy Metals (Zn, Hg, Cu, Cd, Pb, Ni) on the
Length Growth of Mytilus edulis. Mar.Biol. 72(1):69-72.

10899

UEndp

Subramanian, A., B.R. Subramanian, and V.K. Venugopalan. 1980. Toxicity
of Copper and Zinc on Cultures of Skeletonema costatum (Grev.) Cleve and
Nitzschia longissima. Curr.Sci. 49(7):266-268.

9903

UEndp

Sun, Y., and C. Chen. 1988. Effects of Hg, Zn, Pb on Embryonic
Development of Black Progy, Sparus macrocephalus Basilewsky.
Mar.Sci./Haiyang Kexue (3):54-57 (CHI) (ENG ABS).

3371

UEndp

Swedmark, M., and A. Granmo. 1981. Effects of Mixtures of Heavy Metals
and a Surfactant on the Development of Cod (Gadus morhua L.). Rapp.P.-
V. Reun. Cons. Int. Explor. Mer. 178:95-103.

195

UEndp

Syasina, I.G., M.A. Vaschenko, and V.B. Durkina. 1992. Histopathological
Changes in the Gonads of Sea Urchins Exposed to Heavy Metals.
Russ.J.Mar.Biol.(Eng Transl) of Biol.Morya (4):79-89 (Vladivostok) 17:244-
251.

19065

UEndp, Eff

Tadros, M.G., P. Mbuthia, and W. Smith. 1990. Differential Response of
Marine Diatoms to Trace Metals. Bull.Environ.Contam.Toxicol. 44(6):826-
831.

18878

UEndp

727

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Taneeva, A.I.. 1973. Toxicity of Some Heavy Metals for Hydrobionts. In:
V.N.Greze (Ed.), Proc.Mater.Vses.Simp.lzuch.Chern.Sredizemnogo Morei,
Ispol'Z Okhr.Ikh.Resur.Kiev, USSR Ser.4 :114-117 (RUS).

9001

Con, Dur

Taylor, D., B.G. Maddock, and G. Mance. 1985. The Acute Toxicity of Nine
"Grey List" Metals (Arsenic, Boron, Chromium, Copper, Lead, Nickel, Tin,
Vanadium and Zinc) to Two Marine Fish Species:. Aquat.Toxicol. 7(3):135-
144.

11451

Con

Thongra-ar, W., and 0. Matsuda. 1995. Effects of Cadmium and Zinc on
Growth of Thalassiosira weissflogii and Heterosigma akashiwo. In:
A.Snidvongs, W.Utoomprukporn, and M.Hungspreugs (Eds.), Proceedings
of the NRCT-JSPS Joint Seminar on Marine Science, Dec.2-3, 1993,
Chulalongkorn University, Thailand, Bangkok :90-96.

18912

UEndp

Thorpe, G.J.. 1988. A Toxicological Assessment of Cadmium Toxicity to the
Larvae of Two Estuarine Crustaceans, Rhithropanopeus harrisii and
Palaemonetes pugio. Ph.D.Thesis, Duke University, Durham, NC:120 p.;
Diss.Abstr.lnt.B Sci.Eng.50(6):2306 (1989).

3035

UEndp, Eff

Tolba, M.R., A.E. Hagras, and A. Hilmy. 1995. Effect of Some Heavy Metals
on the Growth of Sphaeroma serratum (Crustacea: Isopoda). J.Environ.Sci.
10(1 ):219-231.

45118

UEndp

Tort, L., R. Flos, and J. Balasch. 1984. Dogfish Liver and Kidney Tissue
Respiration After Zinc Treatment. Comp.Biochem.Physiol.C 77(2):381-384.

10979

Con, UEndp, Eff

Tort, L., S. Crespo, and J. Balasch. 1982. Oxygen Consumption of the
Dogfish Gill Tissue Following Zinc Treatment. Comp.Biochem.Physiol.C
72(1): 145-148.

15580

Con, UEndp, Eff

728

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Tsukidate, J.. 1974. Tracer Experiments on the Effect of Micronutrients on
the Growth of Porphyra Plants-ll Manganese-54 and Zinc-65 Assimilation in
Relation to. Bull.Nansei.Reg.Fish.Res.Lab. (7):9-18.

8741

UEndp, Eff

Verriopoulos, G., and D. Hardouvelis. 1988. Effects of Sublethal
Concentration of Zinc on Survival and Fertility in Four Successive
Generations of Tisbe. Mar.Pollut.Bull. 19(4):162-166.

7569

UEndp

Verriopoulos, G., and M. Moraitou-Apostolopoulou. 1989. Toxicity of Zinc to
the Marine Copepod Tisbe holothuriae; the Importance of the Food Factor.
Arch.Hydrobiol. 114(3):457-463.

2084

Dur

Has five 48hr LC50 for Harpacticoid

Verriopoulos, G.. 1992. Effects of Sublethal Concentrations of Zinc,
Chromium and Copper on the Marine Copepods Tisbe holothuriae and
Acartia clausi. In: G.P.Gabrielides (Ed.), Proc.of the FAO/UNEP/IOC
Workshop on the Biological Effects of Pollutants on Marine Organisms,
Malta, 10-14 Sept., 1991, UNEP, Athens, Greece, MAP
Tech.Rep.Ser.No.69 :265-275.

4091

UEndp

Viarengo, A., L. Canesi, M. Pertica, G. Poli, M.N. Moore, and M. Orunesu.
1990. Heavy Metal Effects on Lipid Peroxidation in the Tissues of Mytilus
galloprovincialis Lam. Comp.Biochem.Physiol.C 97(1):37-42.

UEndp, Eff

Viswanathan, S., and M.K. Manisseri. 1995. Histopathological Studies on
Zinc Toxicity in Penaeus indicus H. Milne Edwards. Cmfri Spec.Publ. 61:25-
29.

19405

NonRes, UEndp

Voogt, P.A., P.J. Den Besten, G.C.M. Kusters, and M.W.J. Messing. 1987.
Effects of Cadmium and Zinc on Steroid Metabolism and Steroid Level in the
Sea Star Asterias rubens L. Comp.Biochem.Physiol.C 86(1):83-89.

12392

UEndp, Eff

729

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Vranken, G., C. Tire, and C. Heip. 1988. The Toxicity of Paired Metal
Mixtures to the Nematode Monhystera disjuncta (Bastian, 1865).
Mar.Environ.Res. 26(3):161-179.

2801

Eff

Vranken, G., R. Vandergaeghen, and C. Heip. 1991. Effects of Pollutants on
Life-History Parameters of the Marine Nematode Monhystera disjuncta.

ICES J Mar Sci 48:325-334.

7215

Con

Wang, J., M. Zhang, J. Xu, and Y. Wang. 1995. Reciprocal Effect of Cu, Cd,
Zn on a Kind of Marine Alga. Water Res. 29(1):209-214.

13720

UEndp

Waterman, A.J.. 1937. Effect of Salts of Heavy Metals on Development of
the Sea Urchin, Arbacia punctulata. Biol.Bull. 73(3):401-420.

17763

UEndp

Watling, H.R., and R.J. Watling. 1983. Sandy Beach Molluscs As Possible
Bioindicators of Metal Pollution 2. Laboratory Studies.
Bull.Environ.Contam.Toxicol. 31(3):339-343.

10862

UEndp, Eff

Watling, H.R.. 1983. Accumulation of Seven Metals by Crassostrea gigas,
Crassostrea margaritacea, Perna perna, and Choromytilus meridionalis.
Bull.Environ.Contam.Toxicol. 30(3):317-322.

7374

UEndp, Eff

Watling, H.R.. 1983. Comparative Study of the Effects of Metals on the
Settlement of Crassostrea gigas. Bull.Environ.Contam.Toxicol. 31(3):344-
351.

11098

UEndp

Weeks, J.M., and P.S. Rainbow. 1991. The Uptake and Accumulation of
Zinc and Copper from Solution by Two Species of Talitrid Amphipods
(Crustacea). J.Mar.Biol.Assoc.U.K. 71 (4):811-826.

3628

UEndp, Eff

Weeks, J.M., and P.S. Rainbow. 1993. The Relative Importance of Food
and Seawater as Sources of Copper and Zinc to Talitrid Amphipods
(Crustacea; Amphipoda; Talitridae). J.AppI.Ecol. 30(4):722-735.

13607

UEndp, Eff

730

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Weis, J.S., P. Weis, and J.L. Ricci. 1981. Effects of Cadmium, Zinc, Salinity,
and Temperature on the Teratogenicity of Methylmercury to the Killifish
(Fundulus heteroclitus). Rapp.P.V.Reun.Comm.Int.Explor.Sci.Mer Mediterr.
178:64-70.

11419

UEndp

Weis, J.S.. 1980. Effect of Zinc on Regeneration in the Fiddler Crab Ilea
pugilator and its Interactions with Methyl-Mercury and Cadmium.
Mar.Environ.Res. 3(4):249-255.

9921

UEndp, Con

Weis, P., and J.S. Weis. 1980. Effect of Zinc on Fin Regeneration in the
Mummichog Fundulus heteroclitus, and its Interaction with Methylmercury.
Fish.Bull. 78(1):163-166.

9922

UEndp, Con

White, K.N., and G. Walker. 1981. Uptake, Accumulation, and Excretion of
Zinc by the Barnacle, Balanus balanoides (L.). J.Exp.Mar.BioI.Ecol. 51(2-
3):285-298.

9506

UEndp, Eff

White, S.L., and P.S. Rainbow. 1982. Regulation and Accumulation of
Copper, Zinc and Cadmium by the Shrimp Palaemon elegans.
Mar.Ecol.Prog.Ser. 8(1):95-101.

9120

UEndp

Wikfors, G.H., and R. Ukeles. 1982. Growth and Adaptation Estuarine
Unicellular Algae in Media with Excess Copper, Cadmium or Zinc, and
Effects of Metal-Contaminated Algal Food on. Mar.Ecol.Prog.Ser. 7:191-
206.

15508

UEndp, Con

Willis, J.N., and W.G. Sunda. 1984. Relative Contributions of Food and
Water in the Accumulation of Zinc by Two Species of Marine Fish. Mar.Biol.
80(3):273-279.

10673

UEndp, Eff, Con

731

-------
Citation

ECOTOX
EcoRef 3

Rejection Code(s)

Comment

Wilson, W.B., and L.R. Freeburg. 1980. Toxicity of Metals to Marine
Phytoplankton Cultures. EPA-600/3-80-025, U.S.EPA, Narragansett, Rl :110
p.(U.S.NTIS PB80-182843).

5557

Dur

Plants do not drive criteria, and therefore,
are not included in CWA review and
approval of OR WQS

Wright, D.A.. 1986. Trace Metal Uptake and Sodium Regulation in
Gammarus marinus From Metal Polluted Estuaries in England.
J. Mar. Biol .Assoc. U. K. 66(1):83-92.

5405

UEdp, Eff, Con

Wu, Z., and G. Chen. 1988. Studies of Acute Intoxication by Some Harmful
Substances on Penaeus orientalis K. Mar.Sci./Haiyang Kexue (4):36-40
(CHI) (ENG ABS).

3232

Con

Young, M.L.. 1975. The Transfer of Zn65 and Fe59 Along a Fucus serratus
(L.)-Littorina obtusata (L.) Food Chain. J.Mar.Biol.Assoc.U.K. 55(3):583-610.

2272

Eff

Young, M.L.. 1977. The Roles of Food and Direct Uptake From Water in the
Accumulation of Zinc and Iron in the Tissues of the Dogwhelk, Nucella
lapillus (L.). J.Exp.Mar.BioI.Ecol. 30:315-325.

2731

Eff, Con

Yuan, Y.X., C.N. Gao, and D.X. Zhang. 1992. Egg Hatching and
Metamorphosis to Protozoea of Penaeus chinensis (Osbeck) by Removal of
Heavy Metals from Rearing Systems with Polymeric Absorbent. Aquaculture
107:303-311.

7425

UEndp, Dur

Zolotukhina, E.Y., E.E. Gavrilenko, and K.S. Burdin. 1987. Effect of Zinc and
Copper Ions on Photosynthesis and Respiration of Marine Macroalgae.
Soviet Plant Physiol.(Eng.Trans.Fiziol.Rast.) 34(2):212-220.

6673

UEndp, Eff

Studies That EPA Considered But Did Not Utilize In This Determination

EPA evaluated these studies and determined that the results were not reliable for use in this determination, either because they
were not pertinent to this determination or they failed the QA/QC procedures listed in Appendix A.

732

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3) For the studies that were not utilized, but the most representative SMAV/2 or most representative SMCV fell below the
criterion, or, if the studies were for a species associated with one of the four most sensitive genera used to calculate the
FAV in the most recent national ambient water quality criteria dataset used to derive the CMC99, EPA is providing a
transparent rationale as to why they were not utilized (see below).

4) For the studies that were not utilized because they were not found to be pertinent to this determination (including failing
the QA/QC procedures listed in Appendix A) upon initial review of the download from ECOTOX, EPA is providing the
code that identifies why EPA determined that the results of the study were not reliable (see Appendix V).

General QA/QC failure because non-resident species in Oregon

Tests with the following species were used in the EPA BE of OR WQS for zinc in saltwater, but were not considered in the CWA
review and approval/disapproval action of the standards because these species do not have a breeding wild population in Oregon's
waters:

Nanosesarma

sp.

Crab

Selvakumar et al. 1996

Mercenaria

mercenaria

Northern quahog or hard clam

Calabrese and Nelson 1974

Crassostrea

virginica

Eastern oyster

Maclnnes and Calabrese 1978;
Calabrese et al. 1973

Other Acute tests failins QA/QC by species
Crassostrea cucullata - Oyster

The following test was included in EPA's BE of the OR WQS for zinc in saltwater, but was not used in this CWA review and
approval/disapproval action of these standards because it is not a North American resident.

Watling, H.R. 1982. Comparative study of the effects of zinc, cadmium, and copper on the larval growth of three oyster
species. Bull. Environ. Contam. Toxicol. 28: 195-201.

"U.S. EPA. 1987. Ambient Water Criteria for Zinc - 1987. EPA-440-5-87-003.

733

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Crassostrea rhizophorae - Mangrove oyster

Chung, k.S. 1980. Acute toxicity of selected heavy metals to mangrove oyster Crassostrea rhizophorae. Bull. Jpn. Soc. Sci. Fish.
(Nippon Suisan Gakkaishi) 46(6): 777-780.

Crassostrea gigas — Pacific oyster

The following test was included in EPA's BE of the OR WQS for zinc in saltwater, but was not used in this CWA review and
approval/disapproval action of these standards because the values were greater than values and were based on mortality, rather than
shell development and mortality which is a preferred endpoint.

Watling, H.R. 1982. Comparative study of the effects of zinc, cadmium, and copper on the larval growth of three oyster
species. Bull. Environ. Contam. Toxicol. 28: 195-201.

Acanthomysis costata - Mysid

Hunt, J.W., B.S. Anderson, S.L. Turpen, A.R. Coulon, M. Martin, F.H. Palmer and J.J. Janik. 1989. Marine Bioassay Project.
4th Report. Experimental Evaluation of Effluent Toxicity Testing Protocols with Giant Kelp, Mysids, Red Abalone. No. 89-
5WQ, State Water Resources Control Board, State of California, Sacramento, CA: 144.

This was a less than value. Other data from this study was used.

The following test was included in EPA's BE of the OR WQS for zinc in saltwater, but was not used in this CWA review and
approval/disapproval action of these standards because a more sensitive lifestage was available.

Martin, M., J.W. Hunt, B.S. Anderson and S.L. Turpen. 1989. Experimental evaluation of the mysid Holmesimysis costata as a
test organism for effluent toxicity testing. Environ. Toxicol. Chem. 8(11): 1003-1012.

This was a greater than value. Other data from this study was used.

Other Chronic tests failing QA/QC by species

734

-------
Haliotis rufescens - Red abalone

The following tests were included in EPA's BE of the OR WQS for zinc in saltwater, but were not used in this CWA review and
approval/disapproval action of these standards because of duration.

Hunt, J.W. and B.S. Anderson. 1989. Sublethal effects of zinc and municipal effluents on larvae of the red abalone Haliotis
rufescens. Mar. Biol. 101(4): 545-552.

9-day chronic test.

Anderson, B.S., J.W. Hunt, M. Martin, S.L. Turpen and F.H. Palmer. 1988. Marine Bioassay Project. 3rd Report. Protocol
Development: Reference Toxicant and Initial Complex Effluent Testing. No. 88-7WQ, State Water Resources Control Board,
State of California, Sacramento, CA: 154.

9-day chronic test.

Conroy, P.T., J.W. Hunt and B.S. Anderson. 1996. Validation of a short-term toxicity test endpoint by comparison with
longer-term effects on larval red abalone Haliotis rufescens. Environ. Toxicol. Chem. 15(7): 1245-1250.

10-day chronic test. The concentrations were also unmeasured for this test.

735

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ENCLOSURE 3

Responses to Supplemental

Comments

Submitted by Pacific Environmental
Advocacy Center to U.S. EPA Region 10
Concerning Oregon's New and Revised
Aquatic Life Criteria

January 29, 2013

U.S. ENVIRONMENTAL PROTECTION AGENCY - REGION 10

-------
The State of Oregon held public hearings in July 2003 regarding its proposed water quality standards.
The State responded to the comments delivered at the public hearing as well as those mailed, faxed, and
electronically delivered during the public comment period. On July 8, 2004, the State submitted its new
and revised water quality standards,1 including some modifications based on public comments, to U.S.
EPA. On October 6, 2005, U.S. EPA Region 10 received a letter dated September 30, 2005 from the
Pacific Environmental Advocacy Center on behalf of the Northwest Environmental Advocates which
containing supplemental comments regarding the State's new and revised water quality standards. The
supplemental comments were in the following two sections of the letter.

SECTION IV. OREGON'S PROPOSED WATER QUALITY STANDARDS FOR TOXIC
POLLUTANTS FAIL TO MEET THE REQUIREMENTS OF THE CLEAN
WATER ACT
SECTION V. SPECIFIC POLLUTANT CONCERNS

This memorandum responds to the supplemental comments in Sections IV and V. This memorandum
gives several General Responses and then reproduces the comments given in Sections IV and V of the
supplemental comments and gives a response to each comment.

GENERAL RESPONSES

1. The commenter cites many scientific documents throughout the letter to support issues raised about
the protectiveness of Oregon's aquatic life criteria. Some of the documents cited are based on
toxicity tests that do not meet EPA's threshold for consideration in developing water quality criteria.
In order to provide the necessary degree of reliability, EPA derives aquatic life criteria using a
standard methodology and only uses toxicity test results that meet certain criteria based on a review
for relevance and quality (see Appendix 1 for a description of the review process).

EPA uses the Ecotoxicological database (ECOTOX) that is maintained by EPA's Office of Research
and Development (ORD). ECOTOX is a comprehensive database that contains toxicity test results
for aquatic life, terrestrial plants, and wildlife obtained predominately from peer-reviewed literature.
Test results that do not satisfy ECOTOX's acceptability requirements are excluded from the
database. The review of a test result for inclusion in ECOTOX concerns whether sufficient
information is available concerning the test result. For example, whether test concentrations are
reported, if the tests is on a whole, live organism, if there is an explicitly identified exposure
duration, etc. When EPA searches for all available test results for the derivation of an aquatic life
criterion, EPA searches both ECOTOX and the broader ECOTOX holdings that are not available on
the internet (those studies identified, but not yet vetted through the process, see appendix B of the
technical support document), as well as several bibliographic databases of available scientific
information.

1 This action addresses Oregon's water quality standards submission of July 8, 2004. However, Oregon subsequently revised
that submission. In April, 2007 and July, 2011, Oregon corrected a number of errors in the 2004 submission, such as
incorrect descriptions of the criteria and erroneous cross-references to tables that had been deleted or renamed. In addition,
Oregon's 2007 and 2011 revisions deleted certain criteria for arsenic and chromium; even though the deletions appear to be
inadvertent, they reflect the current version of Oregon's standards upon which EPA must act. Accordingly, throughout this
response-to-comment document, references to the "July 8, 2004 submission" (or textual variants thereof) should be
understood to refer to the July 8, 2004 submission, as submitted by the State of Oregon on July 8, 2004, as amended by
Oregon submissions in April 2007 and July 2011.

-------
In developing water quality criteria, EPA uses only those toxicity tests that both meet the
acceptability review for inclusion ECOTOX, and are also acceptable in terms of relevance and
quality. Test results that are in ECOTOX might not be acceptable for use in the derivation of an
aquatic life criterion for such reasons as (i) temperature varied too much during the toxicity test, (ii)
the concentration of dissolved oxygen was too low during the toxicity test, (iii) the test organisms
were obtained from an unacceptable source, (iv) the dilution water was unacceptable, (v) the toxicity
test was too short or too long, and (vi) the concentration of test material varied too much during the
toxicity test. Tests obtained from sources other than ECOTOX are also subjected to the tests
acceptability and relevance review. Some test results cited by the commenter were not included in
the derivation of Oregon's aquatic life criteria because they did not pass basic quality assurance, as
defined in Appendix 1.

2. EPA notes that many of the sources cited by the commenter do not directly discuss Oregon's
aquatic life criteria or their potential impacts on species within Oregon's waters. The sources
therefore do not directly address the validity of the commenter's concerns that Oregon's aquatic life
criteria might be insufficient to protect Oregon's designated uses. The commenter typically does not
supply sufficient contextual information to make appropriate inferences about how to apply the
cited sources to the review of Oregon's aquatic life criteria. More specific responses are supplied
later in this document.

3. The commenter repeatedly refers to comments made by the Services in the California Toxics Rule
(CTR) Biological Opinion to support claims concerning Oregon's criteria. However, EPA submitted
a Biological Evaluation (BE) to the Services concerning approval of Oregon's aquatic life criteria.
With regard to EPA's review of Oregon's aquatic life criteria, EPA consulted with the Services
regarding the Oregon BE, not the CTR BE, which was specific to species and their critical habitat in
California.

4. The commenter repeatedly refers to ESA listed threatened and endangered aquatic species in the
comments concerning whether EPA should approve Oregon's aquatic life criteria.

As required by the ESA, EPA has submitted a Biological Evaluation (BE) to the Services. The BE
contains EPA's analysis of possible beneficial, adverse, and insignificant effects of Oregon's
aquatic life criteria on ESA listed threatened and endangered aquatic species in Oregon. U.S. Fish
and Wildlife finalized its Biological Opinion on July 30, 2012 (Final Biological Opinion on U.S.
Environmental Protection Agency Proposed Approval of Oregon Water Quality Criteria for
Toxics). The National Marine Fisheries Service finalized its Biological Opinion on August 14,
2012 (Jeopardy and Adverse Modification of Critical Habitat Biological Opinion for the
Environmental Protection Agency's Proposed Approval of Certain Oregon Administrative Rules
Related to Revised Water Quality Criteria for Toxic Pollutants).

5. The commenter repeatedly refers to protection of wildlife, but the current action concerns aquatic
life criteria, not wildlife criteria. Wildlife criteria are derived using a different process in order to
account for toxicity by the different routes of exposure.

Aquatic life criteria are derived to protect aquatic life only; different criteria protect other
designated uses, such as wildlife. See 63 FR 36742, 36762 (1998) ("There are three principal
categories of water quality criteria: criteria to protect human health, criteria to protect aquatic life,
and criteria to protect wildlife.") Therefore, comments expressing concern that Oregon has not
actually adopted particular wildlife criteria are outside the scope of this action. EPA's CWA

-------
303(c)(3) review is limited to a review of the new and revised aquatic life criteria that Oregon
actually adopted and submitted to the Agency. It is not a venue for EPA to evaluate whether
Oregon should have adopted and submitted some other criteria to protect a different designated use,
and EPA therefore does not construe the absence of particular numeric wildlife criteria for a
pollutant as a defect in the submitted aquatic life criteria for the same pollutant.

SECTION IV. OREGON'S PROPOSED WATER QUALITY STANDARDS FOR TOXIC
POLLUTANTS FAIL TO MEET THE REQUIREMENTS OF THE CLEAN
WATER ACT

COMMENT A: The Criteria Fail to Account for Additive and Synergistic Effects Caused by Multiple
Pollutants

Both Oregon's proposed criteria and EPA's recommended numeric criteria for toxic pollutants
suffer from the same, overarching problem: they are based on the fiction that water bodies will
contain only a single pollutant and that designated uses will therefore be exposed to only a single
pollutant at any point in time. Criteria for toxic pollutants are typically established by placing
test organisms in a tank of static water to which a single pollutant is added. Acute and chronic
toxicity levels are then established based on the percentage of the test organisms that die at set
pollutant concentrations. The tests do not consider whether these toxicity levels may be affected
by varying temperatures, pH levels, or the presence of other pollutants. This omission is
significant, because several studies demonstrate that the presence of multiple pollutants in a
waterway results in significant harm to aquatic species. EPA must consider these studies when it
reviews Oregon's submitted criteria and, based on this review, disapprove the standards because
they fail to include criteria that protect beneficial uses.

1. The Oregon Criteria Do Not Consider the Interactions Between Conventional and Toxic
Pollutants.

Oregon's proposed criteria do not protect designated uses because the criteria do not protect
against the hazardous interactions among toxic and conventional pollutants. Oregon's
aquatic life criteria are based on the amount of a single pollutant that a species can tolerate
in an ideal laboratory setting. The real environment, of course, contains multiple pollutants,
both conventional and toxic, that may decrease a species' tolerance for a particular pollutant.
For example, low dissolved oxygen (DO) in a water body increases the acute toxicity of
many metals and ammonia. In addition, a recent study demonstrates that water temperature
significantly affects an organism's silver uptake. Scientists measured silver accumulation by
rainbow trout in warm water (16 degrees C) and cold water (4 degrees C). The trout in the
warm water "accumulated [silver] more quickly in all sampled compartments compared to
'cold' fish." The rate of silver uptake and accumulation in the liver was more than four times
faster in the trout exposed to warm water. The study's authors concluded that greater silver
accumulation in warmer water is the result of increased metabolic rates at higher
temperatures. Based on this study's conclusion, it is likely that exposure to warmer water
will result in increased uptake and concentration of other pollutants as aquatic species'
metabolic rates increase. The Oregon criteria, however, do not consider these effects.

Nor do Oregon's proposed criteria consider the way in which species' exposure to toxic
pollutants can reduce those species' ability to adapt to lower water quality. Studies show that

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toxic pollutants may increase an organism's sensitivity to conventional pollutants, such as
temperature and low DO. Selenium, for example, may damage the gills of fish and decrease
the efficiency of oxygen uptake. In waterways impaired due to low dissolved oxygen,
selenium exposure can therefore exacerbate the problems associated with oxygen
deprivation.

The harmful interaction among toxic pollutants, temperature, pH, and dissolved oxygen is
particularly dangerous in Oregon, where several thousand miles of rivers are 303(d)listed as
water quality limited for temperature, over one thousand miles of rivers are listed for low
dissolved oxygen, and 47 segments are listed for pH violations. Given the prevalence of
high temperatures in Oregon's waters and the absence of any indication that Oregon's waters
will meet temperature criteria any time in the upcoming decades, EPA must assume, in
reviewing Oregon's proposed criteria for toxic pollutants, that Oregon's waters exceed
temperature criteria. This has two-fold implications for toxic criteria. First, EPA must
consider the interaction between temperature and other pollutants in its review of these
criteria. Second, EPA must consider that many species are currently at risk due to elevated
temperatures in most of Oregon's waters. Oregon's criteria do not account for these factors.
They are therefore insufficient to protect designated uses in Oregon.

Indeed, the Services have previously recognized that EPA's method of developing criteria
through purified univariate laboratory analysis is simply not realistic and therefore not
protective of designated uses. For example, the Services concluded that EPA's
recommended criteria for PCP, which Oregon has proposed to adopt, do not consider the
"interactive effects of pH, dissolved oxygen or temperature on toxicity of PCP to fish. These
factors exacerbate the deleterious effect of PCP toxicity on salmonids at the proposed
concentrations." EPA must now consider the synergistic effects of conventional and toxic
pollutants to ensure that the proposed toxic criteria are protective.

As it currently stands, Oregon's proposed criteria, which roundly ignore the effects of
common conventional pollutants on toxicity, cannot be found to protect designated uses.
While scientists are continuing to explore the complex interactions between conventional
and toxic pollutants, EPA must, at a bare minimum, apply current scientific knowledge to
protect designated uses from the adverse effects of known pollutant interactions (e.g., DO
and metals, temperature and metals). EPA should also apply a precautionary approach to set
more protective standards for those pollutant interactions that likely exist but have not yet
been studied. EPA must therefore disapprove Oregon's proposed criteria because Oregon did
not consider the effects of conventional pollutants on toxicity.

2. The Oregon Criteria Do Not Consider the Additive and Synergistic Effects of Species'
Exposure to Multiple Toxic Pollutants in a Waterway.

Oregon's proposed numeric criteria do not protect designated uses because the criteria fail to
consider the additive and synergistic effects of pollutants that radically increase the toxicity
of a pollutant. It is rare for a pollutant to exist in the environment in isolation. Rather,
waterways typically contain a wide array of multiple pollutants at various locations. For
example, in Oregon, the United States Geological Survey (USGS) found 48 pesticides at 40
sample sites in the Willamette Basin. The median number of pesticides detected at each site
was 8. USGS detected 29 different pesticides at a single sample site on Johnson Creek near
Mt. Angel in the Willamette Basin. Non-pesticide contaminants, including heavy metals and

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organochloride compounds, are also abundant, especially near urban areas. Oregon's
waterways contain complex mixtures of multiple toxic pollutants, but Oregon's proposed
water quality standards are based on the myth that each pollutant can be isolated from the
others. As a result, Oregon's proposed criteria fail to protect designated uses.

The existence of complex additive, antagonistic, and synergistic relationships among
pollutants is well known. In one study, researchers measured the toxicity of several metals
(As, Cd, Cr, Cu, Hg, Pb, Ni, Zn) on daphnia and trout. At doses below or near Oregon's
criteria for individual metals, mixtures of the metals produced additive chronic toxicity for
individual survival of trout and daphnia. In addition, the mixture produced additive effects
on the population growth of daphnia. These results demonstrate that Oregon's criteria, which
are designed to protect aquatic life from a pollutant in isolation, do not protect against the
real-world problem of multiple pollutants with additive toxic effects.

Another study exposed daphnia, fathead minnows, and rainbow trout to a combination of
arsenic, cadmium, copper, mercury, and lead at pollutant levels established in EPA's
proposed 1984 water quality criteria. At the 1984 acute criteria levels, the combination of
five common metals killed ninety-five percent of the rainbow trout and one hundred percent
of the daphnias. In addition to this massive mortality, there were important sublethal effects.
After just seventy days, fathead minnows showed a thirty percent weight reduction
compared to controls. After seven days, the combination of pollutants caused an eighty
percent reduction of young production in daphnia. The dramatic mortality and sublethal
effects highlight the danger of metal combinations that are common in the aquatic
environment. Because the tests were conducted at pollutant levels similar to the Oregon
proposed criteria, the high rate of mortality and sublethal effects demonstrate conclusively
that the Oregon criteria do not protect aquatic life.

Yet another study documented the interaction of heavy metals (Cu, Cd, and Pb) on plant
growth. The researchers exposed Cucumis sativus to single metals, as well as binary and ternary
metal mixtures in the soil. The results demonstrate the unpredictability of multiple
contaminants on an organism. The mixtures produced antagonistic, additive, and synergistic
responses, depending on the combination. In addition, the researchers observed inhibited or
enhanced bioaccumulations of individual metals in the mixtures, varying due to metal
combinations. The authors stated that the combined effects of mixtures must be taken into
account for ecological risk assessment. In developing its proposed water quality criteria,

Oregon has not considered the effects of multiple heavy metals on designated uses. Oregon's
proposed criteria are therefore not protective of designated uses.

Moreover, complex interactions between pollutants are not limited to metals. One study
reported dramatic synergistic effects among PCBs and dioxins. Scientists conducting the study
fed rats a congener of PCB (PCB 153 or 156 and/or TCDD 2,3,7,8 (a dioxin)). Rats that
received only one of the pollutants experienced slight increases in hepatic porphyrin
accumulation (increased porphryin accumulation indicates disease), reaching maximum levels
of hepatic porphryin that were double the control values. When the PCBs and TCDD were
administered together, there was a strong synergistic effect, producing porphyrin accumulation
at eight hundred times control levels. This study is but one example of the way in which the
combination of only two pollutants can have overwhelmingly detrimental impacts on
designated uses. In Oregon's waterways, in which dozens of pollutants may regularly be found
at any single location, it likely that the synergistic effects of multiple pollutants are even more

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striking and harmful. Despite these acknowledged synergistic impacts, Oregon's proposed
criteria for toxic pollutants were developed based on the fiction that such pollutant interactions
do not exist. Moreover, Oregon has no method of interpreting and applying its narrative
criterion in order to fill this gap. Oregon's criteria are therefore patently inadequate and must be
disapproved.

The clear weight of scientific evidence shows that pollutants occur together and that additive
or synergistic toxic responses are common. Oregon's criteria do not consider additive or
synergistic effects and are therefore cannot and do not protect designated uses.

EPA's Response to Comment A:

EPA disagrees with the comment that Oregon's new and revised aquatic life criteria fail to protect
Oregon's Fish & Aquatic Life designated use, due to a failure to account for additive and
synergistic effects caused by multiple pollutants. EPA's rationale is explained in its responses to
the two specific issues raised by the commenter.

1. The Oregon Criteria Do Not Consider the Interactions Between Conventional and Toxic
Pollutants.

A number of Oregon's new and revised aquatic life criteria (e.g., ammonia, cadmium, copper,
lead, nickel, silver, etc) do account for water quality characteristics such as temperature, pH,
and/or hardness. In the case of these pollutants, the relationships between these water quality
characteristics and the toxicities of the pollutants have been adequately demonstrated. But EPA
does not assume that such interactions take place, in the absence of studies to document them.
When an effect on toxicity has been adequately demonstrated, EPA takes it into account when
deriving an aquatic life criterion. For example, when hardness (and/or water quality
characteristics that co-vary with hardness) has been adequately demonstrated to affect the
toxicity of a pollutant, such as in the case of the acute criterion for silver, the criterion is
expressed as an equation in which hardness is an independent variable.

The commenter cited a study concerning the uptake of silver by rainbow trout at 16 and 4
degrees C. The commenter suggested that it is likely that exposure to warmer water will result
in increased uptake and concentration of silver, ammonia, and other pollutants as the metabolic
rates of aquatic species increase. Rate of uptake is independent of temperature in many cases,
especially where active biochemical mechanisms are in play. In addition, changes in the rate of
uptake and rate of accumulation do not necessarily mean that the bioconcentration factor (BCF)
is higher or that there are increased effects. It is possible that an increased rate of uptake, if it
occurs, will show that the concentration in the organism at which equilibrium occurs will be
reached faster during the toxicity test, without increasing the toxic effect. The commenter is
making an unjustified extrapolation of the results of this uptake test. Additionally, ASTM
Standard E729 recommends that acute toxicity tests with rainbow trout be performed at 12
degrees C.

The commenter stated that selenium exposure can exacerbate the problems associated with
oxygen deprivation. EPA knows of no evidence in the scientific literature to support this
contention, and the comment does not offer such evidence.

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2. The Oregon Criteria Do Not Consider the Additive and Synergistic Effects of Species'
Exposure to Multiple Toxic Pollutants in a Waterway.

EPA considered such variables when designing the approach represented in the 1985
Guidelines. Available data suggest that in real world situations, additivity is generally not a
significant issue, because most of the toxic stress is attributable to a single pollutant, even in
systems receiving complex mixtures of discharges from large metropolitan areas.2

To illustrate this, EPA collected 50 samples throughout New York Harbor, a large area
extending from the Hudson River to New York Bight, which receives a large volume of
wastewater and runoff from a highly diverse set of discharges, representing a wide range of
municipal, industrial, and agricultural activities. Six metals (Ag, Cd, Cu, Ni, Pb, and Zn) were
measured using clean techniques. For each sample, the toxic equivalent of each metal was
calculated as the metal concentration divided by its criterion. Assuming perfect additivity of
toxicity, the toxic equivalents in each sample were added together to obtain the total toxic
equivalents. One metal consistently dominated the toxic equivalents in each sample. On
average, the combined toxic equivalent of all six metals was only 10 percent greater than the
toxic equivalent of the dominant single metal. Among the 50 samples, the maximum ratio of
the combined toxic equivalents to the dominant single toxic equivalent was only 19 percent
greater than the single dominant toxic equivalent. Consequently, even assuming perfect
additivity, the combined contribution of the other metals was minor compared to the
contribution of the dominant toxicant (Battelle Ocean Sciences. 1992. Evaluation of trace-
metal levels in ambient water and tributaries to New York/New Jersey Harbor for wasteload
allocation. U.S. Environmental Protection Agency, Office of Wetlands Oceans and
Watersheds, and Region 2. Contract 68-C8-0105. January 9, 1992). No specific examples of
additivity have been provided to indicate these experimental observations do not hold true
regarding Oregon's waters.

EPA has reviewed two publications cited by the commenter [Enserink et al. 1991; Spehar and
Fiandt. 1986], The studies gave different results with different mixtures of metals and species;
some tests showed additivity, some showed less than additivity, and some possibly showed
synergism. As the commenter acknowledged, some combinations of pollutants had
antagonistic effects, not additive effects. Antagonistic relationships occur when one
contaminant reduces the toxicity of another contaminant. Such relationships are common
among metals, as noted by Lloyd (1987).3 Aquatic life criteria do not address simultaneous
exposure to more than one pollutant because quantifying the significance of pollutant
interactions (conventional or toxic) is difficult, if not impossible. Few data are available, and
the data that are available do not support the development of useful principles because of the
many possible combinations of pollutants. The commenter does not offer a sound scientific
approach for addressing the issue of pollutant interactions.

The many possible combinations of pollutants present in a water body make assessing the
aquatic life effects resulting from exposure to pollutant mixtures a very site-specific analysis
that requires data regarding the presence and concentrations of chemicals present in the

2 CTR, Response to Comments, Response to CTR-026-002b, California Department of Fish and Game, Specific to concerns
over Synergistic/Additive Effects; http://www.epa.gov/waterscience/standards/ctr/responses.pdf.

3 Lloyd, R. 1987. Special Tests in Aquatic Toxicity for Chemical Mixtures: Interactions and Modification of Response by
Variation of Physicochemical Conditions. In Methods for Assessing the Effects of Mixtures of Chemicals. Edited by V. B.
Vouk, G. C. Butler, A. C. Upton, D. V. Parke and S. C. Asher.

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particular body of water, as well as data concerning interactions between all of the chemicals.
Oregon's current aquatic life criteria address 120 priority pollutants, of which none, some, or
all could occur in a given body of water. Additionally, Oregon has aquatic life criteria for such
water quality characteristics as pH, dissolved oxygen, and temperature and these criteria vary
from site to site depending on the particular water body characteristics. The effect that a given
mixture of chemicals would have on aquatic life is likely to vary from one body of water to
another.

The pertinent conditions affecting individual sites will vary significantly. Consequently,
determining ambient criteria for chemical and conventional pollutant mixtures would have to
be done on a site-specific basis and would require extensive data regarding each site. As stated
above, EPA allows derivation of site-specific criteria to provide for site-specific consideration
of factors such as temperature, level of protection, and multiple pollutants.

Respecting synergism, the commenter contends that "[t]he clear weight of scientific evidence
shows that pollutants occur together and that additive or synergistic toxic responses are
common." However, the particular studies cited by the commenter do not themselves constitute
a clear weight of scientific evidence to establish that synergistic effects are characteristically an
important factor in the toxicity of effluent. To the contrary, field studies of effluent toxicity
and laboratory tests with specific chemicals support the conclusion that synergism is a rare
phenomenon4 (see 57 FR 60877-60878). (Also see response to comments regarding the 1985
Guidelines, Comment #9, 45 FR 79358, November 28, 1980.)

With respect to the commenter's suggestion that mixtures of dioxins and PCBs may have
radical synergistic effects, the World Health Organization (WHO) concluded and reconfirmed
that the combined effects of dioxin and dioxin-like compounds (e.g., PCBs) generally are
consistent with dose additivity (not synergism) (van den Berg et al., 19985, 20066). In addition,
the National Academy of Sciences supported the use of an additivity assumption in its report on
EPA's NAS review draft dioxin reassessment, concluding that "Additivity in biochemical and toxic
responses by the indicated DLCs [dioxin-like compounds] has been supported by numerous
controlled mixture studies in vitro and in vivo and is scientifically justifiable" (NAS, 2006, p. 80)7.
The commenter cites four scientific studies regarding additive and synergistic effects, but two
of the cited studies concern tests with rats and terrestrial plants, not aquatic organisms. The
other two studies concern tests with daphnids, fathead minnows, and rainbow trout on
combinations of metals.

If there is an indication of increased risk from a particular combination of pollutants at a
particular site in Oregon, it might be desirable to derive a site-specific criterion for that site.
However, no information regarding the specific combinations of these chemicals at specific
sites in Oregon has been provided.

4 Technical Support Document for Water Quality-based Toxics Control; March 1991; Page 24
http ://www. epa. gov/npdes/pubs/owm0264.pdf

5 van den Berg, M; Birnbaum, L; Bosveld, AT; et al. (1998) Toxic equivalency factors (TEFs) for PCBs, PCDDs, PCDFs for
humans and wildlife. Environ Health Perspect 106(12):775-792.

6 van den Berg, M; Birnbaum, LS; Denison, M; et al. (2006) The 2005 World Health Organization re-evaluation of human
and mammalian toxic equivalency factors for dioxins and dioxin-like compounds. Toxicol Sci 93(2):223-241.

7 NAS (National Academy of Science). (2006) Health risks from dioxin and related compounds: evaluation of the EPA
reassessment. National Academies Press, Washington, DC. Available online at

http ://www. nap. edu/catalog.php?record_id= 11688.

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Comment B: Oregon's Proposed Criteria Will Be Less Protective Due to DEQ's Decision to Switch
From a "Total Recoverable" To a "Total Dissolved" Method For Assessing Pollutant
Concentrations.

Oregon has proposed to switch from using a "total recoverable" to a "total dissolved" method of
measuring pollutant concentrations in Oregon's waters. Under this proposal, pollutant
concentrations will be measured only after water samples have first been filtered out to remove
particulate matter and any pollutants attached to the particulates. This type of measurement
ignores the fact that designated uses are exposed to particulate matter in natural waterways and is
based on an erroneous assumption that the "total dissolved" method of analysis represents a
closer approximation of the amount of any given pollutant that is bioavailable for uptake by
designated uses. The underlying premise of the "total dissolved" method is not supported by
science and cannot therefore form the basis of Oregon's water quality standards. Oregon's
proposal to switch to the "total dissolved" method is thus scientifically flawed.

Perhaps recognizing that the "total dissolved" method of measuring pollutants is inadequate,
EPA has proposed mitigating factors that are designed to increase the protectiveness of the "total
dissolved" method. These mitigation measures include a "conversion factor" and "translators,"
both of which are employed in an attempt to compare pollutant levels based on the "total
recoverable" method with those established through the "total dissolved" method. As discussed
in detail below, these mitigation measures fail to account for the serious scientific problems
inherent in assuming that species present in a natural waterway will be exposed only to filtered
water. Oregon's proposed use of the "total dissolved" method is simply not based on scientific
realities and cannot be justified through conversion factors, translators, or any other mitigation
measures. EPA cannot legally approve the use of the "total dissolved" method.

1. The "total dissolved" method does not adequately account for particulates.

The Oregon proposed criteria do not protect designated uses because the "total dissolved"
method adopted by Oregon does not adequately regulate toxic particulate metals. Particulate
metals are single atoms or metal complexes absorbed to, or incorporated into, silt, clay,
algae, detritus, or plankton found in the water column. EPA and the states are required to
establish water quality criteria that regulate the concentration of these pollutants in the water
column. The "total dissolved" method, which allows states to base their toxic criteria on the
fiction that the water column is free of any sort of particulate matter or particulate metals,
fails to protect designated uses.

Although current EPA guidance allows states to measure the concentration of pollutants found
in waterways using one of two methods, only the "total recoverable" method is based on
conditions present in the natural environment. The "total recoverable" method analyzes an
unfiltered sample of water, which includes pollutants in the dissolved and particulate forms. In
contrast, the "total dissolved" method filters out the particulate matter so that only those
pollutants that have dissolved in the water column are analyzed and considered. This latter
methodology bears no resemblance to natural conditions and, as discussed below, cannot
legally form the basis for Oregon's water quality criteria for toxic pollutants.

The underlying premise by which EPA has promoted use of the "total dissolved" method has
been seriously criticized by the Services. Inexplicably, EPA has claimed that the "total
dissolved" method more closely approximates the bioavailable fraction of the pollutant in the

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water column than the "total recoverable" method. This claim appears to be premised on EPA's
unfounded belief that organisms will uptake only those pollutants that have dissolved into the
water column and not those that have bound themselves to particulate matter. The Services,
however, have made clear that particulate metals remain bioavailable to aquatic species. The
Services stated, "particulate metals have been removed from the [regulatory] equation even
though chemical, physical, and biological activity can cause these metals to become
bioavailable." In fact, the Services concluded that the CTR was not protective of aquatic life
because, in part, the criteria were based on the "total dissolved" method: "While the CTR
criteria proposed for metals are based on the dissolved fractions of these metals only, aquatic
organisms in natural waters are exposed to additional, waterborne, particulate metal forms."
EPA's continued use of the "total dissolved" method is troubling, at best, in light of the
Services' comments.

2. The "total dissolved" method allows for increased discharges of toxic pollutants.

Another overarching problem with the "total dissolved" method is that it allows for an
increased mass of toxic pollutants to be discharged into waterways that already have high
concentrations of particulate pollutants. The CTR BiOp compared discharges of total metal
concentrations under the National Toxics Rule (which measured "total recoverable" metals)
and the CTR (which measured "total dissolved" metals). The Services reported that the mass of
metals discharged pursuant to National Pollutant Discharge Elimination Systems (NPDES)
permits would increase dramatically under the CTR due to the switch to using the "total
dissolved" method for metal regulation. For a waterway that received twenty percent of its
pollutant load in the dissolved form, a situation not uncommon in California, the CTR "total
dissolved" method increases the total zinc discharge by four hundred seventy-six percent over
the National Toxics Rule. At twenty percent dissolved load, the "total dissolved" method
increases arsenic discharges by four hundred forty six percent and cadmium discharges by five
hundred twenty six percent. This massive increase in total discharge indicates that the "total
dissolved" method does not protect Oregon's designated uses. EPA's - and by extension,
Oregon's - continued use of the "total dissolved" method, in light of the Services' rejection of
this method in other contexts, cannot withstand either scientific or judicial scrutiny.

3. The conversion factors used to equate the "total recoverable" method to the "total dissolved"
method are not protective.

The conversion factor is a tool used by EPA in an effort to equate values established under the
"total recoverable" method with values established through the "total dissolved" method. Most
of studies on which EPA (and hence, Oregon) has relied in developing its water quality criteria
for toxic pollutants are based on the "total recoverable" method. To derive the final criterion,
the "total dissolved" criterion that is determined in the laboratory is multiplied by the
conversion factor. The conversion factor lowers the final criterion, in theory, to make up for the
particulate metals that are present in natural water, but are not measured in the "total dissolved"
test.

To accomplish this "lowering," a conversion factor is always less than one (1), except for
arsenic, which equals one (1). The conversion factor is meant to reflect the percentage of
pollutants that are dissolved in any given water body. For example, if the particulate fraction of
a metal in a water body were forty percent, the dissolved fraction would be sixty percent. The
conversion factor for this water body should be 0.6 (i.e. sixty percent). When applying the

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conversion factor to a water quality criterion established through the "total recoverable"
method, the "total dissolved" criterion would be reduced by forty percent. Thus, if, based on
the "total recoverable" method, EPA established a recommended criterion for lead of 10 mg/L,
the "total dissolved" criterion in that water body would be 6 mg/L (10 mg/L * 0.6 conversion
factor), or forty percent lower than the "total recoverable" factor.

While, on its face, the conversion factor seems to mitigate concerns created by shifting between
the "total recoverable" and "total dissolved" methods, the conversion factors in Oregon's
proposed water quality standards do not adequately reduce the criteria to account for the
particulates in natural water. The conversion factors used in Oregon's criteria are all close to
one. This assumes that the metal fraction in water bodies is nearly one hundred percent
dissolved metals. This assumption is not environmentally realistic, as evidenced by the fact that
California waters commonly contain an eighty percent particulate fraction. The California Fish
and Game noted that particulate fractions in natural waters in California are commonly in the
range of 80 percent, which should result in a conversion factor of 0.2. The Services, moreover,
believe that the conversion factors are unrealistic, stating, "[t]he [conversion factor] values
approach one hundred percent for several metals because they are ratios determined in
laboratory toxicity test solutions, not in natural waters where relative contributions of
waterborne particulate metals are much greater." Because the conversion factors proposed by
Oregon do not accurately depict the waterborne concentrations of particulates in natural waters,
Oregon's criteria are not protective of designated uses.

In addition, the Services noted that EPA developed the conversion factors with a limited
database. For example, the conversion factor values for chromium were based on only two
studies. The conversion factor for lead was based on three studies. The three studies were
small, each containing only three records. As a result of the limited database, the Services
concluded that "[although additional confirmatory studies were performed to develop the
conversion factors, the database available appears to be limited and calls into question the
defensibility of the conversion factors determined for these metals." The Services' skepticism
of the conversion factors demonstrates that the Oregon proposed criteria do not protect
designated uses.

4. The translators used to convert "total dissolved" metals to "total recoverable" metals are not
protective of designated uses.

In addition to using a conversion factor, Oregon has proposed to adopt EPA's proposed
"translators," which are numbers used to translate the now converted "total dissolved" criteria
back into "total recoverable" figures for use in permits, Total Maximum Daily Loads (TMDLs)
and other regulatory mechanisms. For example, to establish a water quality criterion for use in
a TMDL, the dissolved criterion must be translated back to a "total recoverable" value so that
the TMDL and other regulatory calculations can be performed. The translator is also important
to the regulatory community because translators are necessary to calculate discharge limits in
NPDES permits.

EPA's preferred translation method is to determine a site-specific translator by measuring site-
specific ratios of dissolved-to-total metals and dividing the dissolved criterion by the translator.
If there is a high fraction of the total metal in the receiving water, the translator allows for a
corresponding increase in the total amount of pollutants discharged. Thus, not only does the
"total dissolved" method neglect particulate metals, including those lodged in sediment

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(neglecting the physical, biological, and chemical means by which the metal becomes
bioavailable), but the translators actually allow an increase in the discharge of the total metals.
By no means is this protective, particularly in water bodies in which aquatic species and other
designated uses are already imperiled.

The State of California and EPA previously determined that using the recommended site-
specific translators would decrease dischargers' costs by almost fifty percent. "This reduction
in cost in [sic] directly related to the less stringent effluent limitations that result for the use of
site-specific translators." The Services noted this same large cost savings is directly related to
the discharge of more pollutants: "This implies a strong economic incentive for dischargers to
reduce costs by developing site-specific translators and ultimately being allowed to discharge
more total metals." The Services' conclusion is supported by documents they received from
EPA in which EPA performed a sensitivity analysis on the effect of the site-specific translator.
The study showed that use of a translator to calculate criteria would result in greater releases of
0.4 to 124 million "toxic weighted" pounds of metals discharged in California. These data
demonstrate that EPA's "total dissolved" method of establishing toxic criteria and the
associated translators result in benefits to polluters, but not to aquatic life or other designated
uses.

As in California, there is no doubt that the state of Oregon proposed the use of the "total
dissolved" method, along with the unprotective translators, to benefit industrial and municipal
polluters. Indeed, DEQ's director acknowledged as much: "[t]he Department initially proposed
'total recoverable' metal for public comment and received much comment from industries and
municipalities that the environmental benefit associated with 'total recoverable' metals criteria
did not justify the cost." The translators will result in increased discharges of total metals into
waterways, such as the Willamette River, that already suffer from the presence of too many
toxic pollutants in the sediment and the water column. EPA cannot lawfully approve criteria
that weaken protections for aquatic life, wildlife, and threatened and endangered species,
particularly when the only apparent justification for weakening the criteria is cost. EPA must
therefore reject Oregon's attempt to use "total dissolved" metals criteria and the translators as a
means to appease industry and sacrifice water quality.

5. Oregon's decision to propose a "total dissolved" method for assessing toxic pollutants was a
political decision that EPA must reject as scientifically indefensible.

Both EPA and Oregon have recognized the problems inherent in the "total dissolved" method.
While EPA stated that it "believed, and continues to believe, that when a state develops and
adopts its standards, the state, in making its risk management decision, may want to consider
sediment, food chain effects, and other fate-related issues and decide to adopt total recoverable
or dissolved metals criteria," EPA has never convincingly explained why the "total dissolved
method" is protective of existing and designated uses. Oregon's scientists (the TAC)
recognized this and advised the state to adopt the "total recoverable" method, because the "total
dissolved" method did not consider the toxicity resulting from suspended metals and because
most of the data used to calculate criteria came from studies using the "total recoverable"
method. As matter of science, both DEQ and EPA know that the "total recoverable" method
provides the necessary protections for designated uses in Oregon.

Unfortunately, DEQ allowed politics to trump science when DEQ decided to ignore its
scientific advisors and propose the "total dissolved" method. DEQ thus proposed to abandon

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the "total recoverable" method to appease industry's unspecified cost concerns. While it may
be true that there are costs associated with providing adequate levels of protection to imperiled
species, DEQ and EPA have no legal authority to weaken protections for designated uses based
on cost considerations. EPA regulations provide that "[sjtates must adopt those water quality
criteria that protect the designated use. Such criteria must be based on sound scientific rationale
and must contain sufficient parameters or constituents to protect the designated use." This rule
does not allow a state to consider economic costs when adopting criteria. Nor does the CWA,
which requires water quality standards to be "such as to protect the public health or welfare,
enhance the quality of water and serve the purposes of the this chapter." EPA must reject
DEQ's attempt to abandon species protections in favor of political expediency.

6. EPA must perform an anti degradation review of the proposed revisions to Oregon's water
quality standards for toxic pollutants.

By allowing Oregon to switch from a "total recoverable" to a "total dissolved" method for
establishing toxic criteria, EPA is allowing Oregon to revise - and indeed, lower - its water
quality criteria for toxic pollutants, without performing an anti degradation review. The CWA
makes clear that "any water quality standard established under this section, or any other
permitting standard may be revised only if such revision is subject to and consistent with the
anti degradation policy established under this section." 33 U.S.C. § 1313(d)(4)(B) EPA's
failure to require or perform an anti degradation review for the toxic criteria, and particularly for
the switch from a "total recoverable" to a "total dissolved" methodology violates the clear
requirements of the CWA.

EPA's Response to Comment B:

EPA disagrees with the comment that Oregon's new and revised aquatic life criteria for metals fail
to protect Oregon's Fish & Aquatic Life designated use, as a result of Oregon's change from
expressing its criteria for metals in terms of total recoverable metal to expressing its criteria for
metals in terms of dissolved metal. EPA's rationale is explained in its responses to the six specific
arguments made by the commenter.

1. The "total dissolved" method does not adequately account for particulates.

EPA derives its national aquatic life criteria so that they protect water-column organisms from
exposure to pollutants that are present in the water column. The primary mechanism for water
column toxicity is adsorption at the gill surface which requires metals to be in the dissolved
form.

The scientific evidence indicates that particulate-bound metals do not contribute toxicity when
suspended in the water column. Two expert workshops, one held in Annapolis in 1993 (58 FR
32131, June 8, 1993) and one held in Pensacola in 1996 (Bergman, H.L. and E.J. Dorward-
Kind (eds.), Reassessment of Metal Criteria for Aquatic Life Protection. SET AC Press.
Pensacola, FL. 1997) were sponsored to discuss this issue. Both workshops recommended that
EPA express its aquatic life criteria for metals in terms of dissolved metal. EPA agrees with
the recommendations of the expert workshops and with the supporting rationales. Therefore,
EPA now expresses its aquatic life criteria for metals in terms of dissolved metal instead of
total recoverable metal because dissolved metal more closely approximates toxic metal in the

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water column than does total recoverable metal.8 Toxicity testing is performed under
conditions which increase the toxic fraction of metal and as such, present data that compensates
for the raised concerns as addressed by the workgroups.

EPA disagrees with the statements that the dissolved method is based on "the fiction that the
water column is free of any sort of particulate matter or particulate metals" and that EPA has
assumed that "species present in a natural waterway will be exposed only to filtered water."
EPA has made no such assumptions. The scientific consensus (discussed later in this response)
is to apply criteria to the dissolved metal fraction because that is the bioavailable fraction.

Metal that is bound in particulate phases is essentially not bioavailable. But in no case is the
particulate phase assumed to be absent.

Toxicity tests on metals are performed by adding simple salts to relatively clean water, of
defined composition, in terms of factors such as total organic carbon content, an approach used
to ensure comparability across tests and chemicals, and which in effect makes the tests more
protective. Because of the likely presence of substantial concentrations of agents that bind
metals (especially suspended and dissolved organic matter) in discharges and ambient waters,
metals in toxicity tests would generally be expected to be more bioavailable (and hence more
toxic) than metals in discharges or in ambient waters.9

The commenter states that the Services "have made clear that particulate metals remain
bioavailable to aquatic species." This is an incorrect summation of the particulate metals issue.
In fact, the Services stated that particulate metals might become bioavailable due to some future
shift in the environment. However, neither the commenter nor the Services provided any
scientific evidence to support a premise that metals would desorb to yield a higher dissolved
concentration than was in equilibrium with the particles to begin with, and therefore could
cause the criterion to be exceeded.

The dissolved concentration allows accurate prediction of both the concentration of the
pollutant in the water column (|ig pollutant/L water), and the degree to which the particulates in
equilibrium with the water column is contaminated (|ig of pollutant/kg particles). Even when
particulates settle to bottom, the water trapped in the pore space will retain a dissolved pollutant
concentration similar to that of overlying water. This is because the pollutant dissolved in pore
water, like the pollutant dissolved in the overlying water, is in equilibrium with the pollutant
bound to the sediment particles.

By contrast, the total concentration measurement advocated by the comment is dependent not
only the degree of adsorption to particulate matter, but also on the amount of particulate matter
that happens to be suspended in the water column at a particular point in time. But only the
first value, the degree of contamination, is predictive of toxicity. The total concentration
measurement is a less accurate measure of toxicity to aquatic life because it is also affected by
the second factor - the degree to which particulate matter happens to be suspended in the water
column. This second factor is irrelevant to the partition equilibrium which exists between
particle-bound contaminant and dissolved contaminant, and has no effect on toxicity to aquatic
life. Gobas and Morrison (2000) explain the central importance of the dissolved concentration

8 ibid

9 EPA. 1993. Memorandum: Office of Water Policy and Technical Guidance on Interpretation and Implementation of
Aquatic Life Metals Criteria.

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in controlling the behavior of chemicals in the environment.10

Because of these issues, criteria based on total recoverable metals could be over-protective (if
most of the metals are in particulate form) or under-protective (if most of the metals are in
dissolved form). In order to protect aquatic life, the critical issue is the concentration of metals
dissolved in the water column, because that is the form in which the metals are toxic. Thus
establishing criteria based on the dissolved metals fraction is the most scientifically valid
approach to protecting the aquatic life.

2. The "total dissolved" method allows for increased discharges of toxic pollutants.

Switching from expressing aquatic life criteria for metals in terms of the total recoverable
method to expressing such criteria in terms of the dissolved method may result in allowing the
discharge of more total recoverable metal, when the characteristics of the discharge and the
receiving water are such that much of the metals discharged will be in non-toxic particulate
form; it could also result in the discharge of less total recoverable metal, if most of the metals
discharged are in the toxic dissolved form. In either case, the switch will not allow the
concentration of bioavailable (toxic) metal in the water column to increase. Oregon's use of
the dissolved method will protect the designated use because it limits the concentration of
dissolved metal, which more accurately reflects the concentration of bioavailable, and hence
potentially toxic, metal than the concentration of total recoverable metal.

3. The conversion factors used to equate the "total recoverable " method to the "total dissolved"
method are not protective.

The commenter's criticism of the conversion factors is invalid. The results of most toxicity
tests on metals have been expressed in terms of total recoverable metal. Conversion factors
were developed to account for the possible presence of particulate metal in the laboratory
toxicity tests (62 FR 42172) in order to obtain an accurate measure of the dissolved metal
concentration that is protective of aquatic life. For example, the commenter says "The
conversion factor is meant to reflect the percentage of pollutants that are dissolved in any given
body of water." This is incorrect. The conversion factor is not meant to reflect the percentage
of the metal that is dissolved in a body of water; the conversion factor is meant to reflect the
percentage of the metal that is dissolved in the toxicity tests on which the criterion is based.
This allows the derivation of a criterion on the basis of dissolved metal in toxicity tests rather
than on the basis of total recoverable metal in toxicity tests for the purposes of standardization.

The commenter states that the conversion factors do not accurately depict the waterborne
concentrations of particulates in natural waters, and states that conversion factors should take
into account the ratio of total recoverable metal to dissolved metal in the receiving water.
However, the purpose of a conversion factor is to take into account the ratio of total
recoverable metal to dissolved metal in the test solutions in the toxicity tests on which the
criterion is based. Conversion factors are not intended to reflect natural waters. They are
intended to reflect aspects of the dilution water used in the toxicity tests on which the criteria
are based. Conversion factors are used to convert results of toxicity tests expressed in terms of
total recoverable metal to results of toxicity tests expressed in terms of dissolved metal. If

10 Gobas, F. A.P.C., and H. A. Morrison. 2000. Bioconcentration and Biomagnification in the Aquatic Environment.
Handbook of Property Estimation Methods for Chemicals. CRC Press.

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dissolved metal had been measured in the test solutions used in the toxicity test, the result of
the test could have been calculated directly in terms of dissolved metal and there would be no
need to use conversion factors to convert a total recoverable test result to a dissolved test result.

EPA recognizes that many of the conversion factors published in the draft report are very close
to 1.0. EPA chose to use experimentally determined conversion factors rather than using
assumed conversion factors. Conversion factors are not related to protectiveness. The
conversion from total recoverable to dissolved metal does not alter the protectiveness of a
criterion. EPA believes that this approach is technically sound.

Results of most toxicity tests on metals have been expressed in terms of either total recoverable
metal or dissolved metal, but not both. In order to calculate a conversion factor, however, it is
necessary for both total recoverable metal and dissolved metal to be measured in the same
solution. Therefore, in order to derive conversion factors, special studies were performed to
allow careful measurement of both total recoverable metal and dissolved metal at
concentrations close to criteria concentration in solutions that were similar to those that
occurred in toxicity tests that were important in the derivation of the criteria. (Response to
Final Biological Opinion on California Toxics Rule, USEPA, p. 9; Derivation of Conversion
Factors for the Calculation of Dissolved Freshwater Aquatic Life Criteria for Metals, draft
dated 3-11-95, C. E. Stephan).

4. The translators used to convert "total dissolved" metals to "total recoverable " metals are not
protective of designated uses.

Oregon's new and revised criteria, submitted to EPA on July 8, 2004, can be found at OAR
340-041-0033 and in Tables 33A and 33B in the Water Quality Criteria Toxic Criteria
Summary. Although Oregon provided conversion factors to convert its aquatic life criteria for
some metals from "total recoverable" to "dissolved", it did not provide any "translators" to
convert the "total dissolved' criteria back into "total recoverable" concentrations for use in
permits or other regulatory mechanisms. Therefore, translators are not part of Oregon's
submission of new and revised standards and are therefore not a part of this regulatory action.

The commenter states "If there is a high fraction of the total metal in the receiving water, the
translator allows for a corresponding increase in the total amount of pollutants discharged..."
The translator is not based on the fraction of the total metal in the receiving water; the
translator is based on the percentage of the total recoverable metal in the effluent that becomes
dissolved in the downstream water. Regardless of whether aquatic life criteria are expressed in
terms of total recoverable metal or dissolved metal, permit limits are based on total recoverable
metal. Therefore, when an aquatic life criterion is expressed in terms of dissolved metal, an
effluent-specific translator is needed to take into account the fact that only a portion of the total
recoverable metal in the effluent becomes dissolved in the receiving water.

In order to provide permitting authorities and other authorities methods by which to convert
dissolved metals criteria to total recoverable permit limits, EPA has provided guidance in "The
Metals Translator: Guidance for Calculating a Total Recoverable Permit Limit From a
Dissolved Criterion" (EPA 823-B-96-007, June 1996). The Guidance provides that a translator
may take one of three forms: (1) it may be assumed to be equivalent to the criteria guidance
conversion factors, (2) it may be developed directly as the ratio of dissolved metal to total
recoverable metal in the receiving water; and (3) it may be developed through the use of a

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partition coefficient that is functionally related to the number of metal binding sites on the
binding agent in the water column (e.g. concentrations of total suspended solids or TSS). (62
FR 42173). In this way, Oregon's criteria can be applied and translated to reflect the site-
specific characteristics of the water body where a permit would apply.

The commenter states that any use of translators for NPDES permits and TMDLs would result
in an increase in metals within the waters of Oregon, and therefore would not sufficiently
protect the designated uses. The commenter cites the Services' criticisms of the CTR. EPA and
the Services have already resolved those criticisms and the CTR continues to express aquatic
life criteria for all metals except aluminum in terms of dissolved metal. The Services have not
objected to the use of dissolved metals criteria in connection with Oregon's aquatic life criteria,
which are at issue here.

5. Oregon's decision to propose a "total dissolved" method for assessing toxic pollutants was a
political decision that EPA must reject as scientifically indefensible.

When Oregon decided to express its aquatic life criteria for metals in terms of dissolved metal,
Oregon was adopting an approach that EPA recommends and has itself promulgated (in the
California Toxics Rule and in the Interim National Toxics Rule), and therefore an approach that
EPA concurs with, as long as it is implemented correctly in the calculation of permit limits. As
stated earlier, two expert workshops, one in Annapolis in 1993 (58 FR 32131, June 8, 1993)
and one in Pensacola in 1996 (Bergman, H.L. and E.J. Dorward-Kind (eds.), Reassessment of
Metal Criteria for Aquatic Life Protection. SET AC Press. Pensacola, FL. 1997) were held to
discuss this issue. Both workshops recommended that EPA express its aquatic life criteria for
metals in terms of dissolved metal. EPA agrees with the recommendations of the expert
workshops and the supporting rationales. Consequently, the Office of Water recommended use
of dissolved metal to set and measure compliance with water quality standards as scientifically
appropriate, because dissolved metal more closely approximates the bioavailable fraction of the
metal in the water column than does total recoverable metal (EPA 1993). EPA's decision to
express aquatic life criteria in terms of dissolved metal rather than total recoverable metal is
based on science; it is not based on cost and it is not based on political expediency.n,12

The commenter states that EPA must reject Oregon's aquatic life criteria for metals, arguing
that the decision to adopt the "total dissolved" method was based on impermissible
considerations. EPA notes that a state has the discretion to adopt standards based on either
dissolved metal or total recoverable metal. EPA recommends that State water quality standards
for aquatic life be based on dissolved metal. EPA will also approve a State decision to adopt
standards based on total recoverable metal, if those standards are otherwise approvable (EPA
1993), but in this case, Oregon opted to adopt EPA recommendations. For the reasons
described above, EPA believes there is a sound scientific basis to conclude that Oregon's
aquatic life criteria for metals, which were calculated using the total dissolved method, are
sufficient to protect Oregon's fish and aquatic life designated use.

11 Stephan, CE. 1995. Derivation of Conversion Factors for the Calculation of Dissolved Freshwater Aquatic Life Criteria
for Metals. U.S. EPA, Office of Research and Development, Environmental Research Laboratory, Duluth, MN.

12 Lussier, SM, WS Boothman, S Poucher, D Champlin, A Helmstetter. 1995. Derivation of Conversion Factors for
Dissolved Saltwater Aquatic Life Criteria for Metals. U.S. EPA, Office of Research and Development, Environmental
Research Laboratory, Narragansett, RI.

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6. EPA must perform an antidegradation review of the proposed revisions to Oregon's water
quality standards for toxic pollutants.

EPA's regulations instruct States to adopt antidegradation policies and identify antidegradation
implementation methods around three categories of water quality protection, commonly called
"tiers." 40 CFR 131.12. Antidegradation reviews occur, consistent with such policies, in the
context of a specific authorization to discharge, such as an NPDES authorization.

However, neither the CWA nor its implementing regulations require an antidegradation review
by a state prior to adopting a new or revised WQS, or by EPA prior to approving a new or
revised WQS.13

EPA does not read the phrase, "any water quality standard established under this section" in
CWA Section 303(d)(4)(B), to stand alone, as a separate trigger for antidegradation review.
Rather, that phrase serves as a modifier describing the antecedent clause "any effluent
limitation," such that revisions of "any effluent limitation based on . . . any water quality
standard . . . may be revised" only if consistent with a State's antidegradation policy. The
legislative history of the CWA confirms that the antidegradation review required under
303(d)(4)(B) must be construed in concert with the antibacksliding principles of Section
402(o)(l), and that it applies to revisions of water quality-based effluent limitations, and not to
revisions of water quality standards themselves. See., e.g., 133 Cong. Rec. 850 (1987).
Congress only required an antidegradation review in the context of revisions to effluent
limitations in an NPDES permit proceeding, where a particular activity responsible for
proposed increased discharges is known and can be properly assessed. EPA's guidance also
construes Section 303(d)(4)(B) to require a State antidegradation review for revisions of
effluent limitations based on water quality standards rather than for revisions to water quality
standards themselves. See, e.g., Attachment to Draft Interim Guidance on Implementation of
Section 402(o) Anti-backsliding Rules for Water Quality-Based Permits, at 6 & n.9 (Sept.
1989) (available at http://www.epa.gov/npdes/pubs/owm0354.pdf).

COMMENT C: The Water Effects Ratio Is Not Protective of Designated Uses.

Oregon's proposed criteria for certain metals also include a Water Effects Ratio (WER), which is a
number greater than or equal to one (1). The WER "purportedly accounts for the difference in
toxicity of a metal in a site water relative to the toxicity of the same metal in reconstituted
laboratory water," by raising the applicable criterion (i.e., making the criterion less protective) in an
effort to account for the binding effect of constituents in natural waters. The underlying premise
used to justify the use of a WER is that natural waters may contain constituents, such as dissolved
organic carbon (DOC), that are not present in pure laboratory water. These constituents may act to
bind metals and possibly reduce the bioavailability of the metals in certain circumstances. The WER
is therefore designed to account for the presence of the constituents in natural water, so as to allow
for greater concentrations of pollutants to be discharged into these natural waters.

Whatever their underlying purpose may be, the use of improper WERs developed by EPA and
proposed by Oregon will undermine the protectiveness of Oregon's criteria. In the CTR BiOp, the

13 EPA's interpretation of the law been subject to judicial review, and upheld. See Native Village of Point Hope v. U.S.
Environmental Protection Agency. No. ll-cv-00200, slip op. at 25 (D. Alaska Sept. 13, 2012).

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Services concluded that criteria derived from WERs do not protect aquatic life. Oregon's proposed
criteria, which include the same WERs that the Services criticized in the CTR BiOp, suffer from
three primary flaws.

First, the calcium-to-magnesium ratio used in laboratory water overestimates the proportion of
calcium in natural waters, which results in less protective standards. "The Services observed that
imbalances in the Ca-to-Mg ratios between site waters and dilution waters may result in WERs
which are overestimated because calcium ions are more protective of metals toxicity than are
magnesium ions." By basing its raw, laboratory-derived criteria on an underprotective and
unrealistic calcium-to-magnesium ratio, EPA has premised its use of the WERs on the unsupported
assumption that laboratory-developed criteria are more protective than necessary in the natural
environment. The harmful effects of that erroneous assumption are only amplified by the use of
WERs, which further weaken the criteria. The use of WERs is thus inappropriate and fails to protect
designated uses.

Second, EPA developed the WERs based on an inadequate number of test species and thus cannot
claim that its use of WERs is scientifically sound. Unlike EPA's metals criteria, which are based on
over nine hundred records of laboratory toxicity tests performed on many genera and trophic levels,
the WERs may be determined with only two or three test species that do not encompass multiple
genera or trophic levels. Two or three test species do not adequately represent the toxic sensitivity
of millions of species. Indeed, the use of the WERs has the perverse result of allowing two or three
tests to dramatically alter criteria that were established based on data from hundreds of species.
EPA's use of WERs is thus questionable at best.

Third, the bioassays upon which national and site-specific criteria and WERs are based may not
have used the most sensitive life stage of the organism tested. For example, most bioassays use the
asexual life stage of daphnia, a common test organism. Yet, researchers found that sexual
reproduction in daphnia is the most sensitive life stage. As a result, the Services concluded, "EPA
procedures for determining WERs for metals may result in criteria that are not protective of
threatened or endangered aquatic species. Thus, WERs of three or less are unacceptable because
they are likely within the variance of toxicity tests." These findings are equally applicable to the use
of WERs adopted by Oregon in its proposed numeric criteria for metals. The WERs proposed by
Oregon are thus insufficient to protect aquatic life, including threatened and endangered species.

Moreover, as discussed in detail below, the underlying premise of the WERs - that metals that bind
to other constituents are not bioavailable and thus present less risk to designated uses is flawed.
Any effort to weaken the otherwise applicable criteria must therefore be rejected.

EPA's Response to Comment C:

EPA disagrees with the comment that use of water-effect ratios (WERs)14 results in certain of
Oregon's new and revised aquatic life criteria failing to protect Oregon's Fish & Aquatic Life
designated use. Oregon's new and revised aquatic life criteria can be found at OAR 340-041-0033
and in Tables 33A and 33B in the Water Quality Criteria Toxic Criteria Summary. Oregon did not
use any WERs in the derivation of their submitted criteria for metals. Consequently, the use of the
water-effect ratio is not part of this action.

14 Interim Guidance on Determination and Use of Water-Effect Ratios for Metals (EPA-823-B-94-001, 1994)

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Comment D: The Proposed Oregon Criteria Do Not Protect Designated Uses, Because They Fail to
Address Exposure Pathways From Particulates and Contaminated Food.

The proposed Oregon criteria fail to protect designated and existing uses from dermal exposure and
dietary exposure to particulate metals and contaminated food sources. As noted above, Oregon's
proposed aquatic life criteria are based exclusively on exposure to dissolved metals in the water
column.

By basing the proposed criteria on the "total dissolved" method, DEQ has ignored the reality that
aquatic species, wildlife, and other designated uses are exposed to toxic metals via particulates in
the water column and the consumption of contaminated food. Unless the criteria protect species
from these exposure pathways, they cannot possibly be considered protective.

1. Oregon's proposed water quality standards for toxic pollutants do not adequately protect
species from exposure to sediments and particulates.

Aquatic species and wildlife are exposed to significant amounts of toxic pollutants through
sediments and particulate matter. A United States Army Corps of Engineers study summarized
these exposure pathways as follows:

Sediments may serve as sinks by binding and sequestering contaminants that are entering
aquatic systems where they can accumulate to much higher concentrations than in the
overlying water. Sediments may then serve as secondary sources for biotic exposure to the
materials, particularly when sediments are disturbed by physical perturbations such as
storm events, bioturbation, or dredging and aquatic placement of dredged material.
Sediment-sorbed contaminants may accumulate sufficiently in the tissues of prey
organisms to elicit direct adverse effects, and they may be transferred to consumers
through dietary intake or by increased concentration in the water column. Aquatic
organisms that bioaccumulate contaminants from water or sediment may transfer these
contaminants to predators that forage on them. The extent to which these sediment-
associated contaminants can move through aquatic food webs and thus potentially affect
organisms at higher trophic levels is a crucial issue for environmental decision-making.

The Services similarly note, "Dredging and disposal operations can result in substantial re-
suspension of particulates in the water column, including those contaminated with metals."
From its work on the Portland Harbor Superfund site, EPA is well aware that dredging, suction
dredging, and natural events disturb contaminated sediments in Oregon. Thus, there can be no
doubt that sediments and particulates expose designated and existing uses to significant levels
of bioavailable pollutants.

Despite the clear weight of evidence showing that contaminated sediments and particulates
present risks to designated uses, Oregon DEQ has insisted on using the "total dissolved" metals
method, which ignores these important exposure pathways. EPA cannot legally approve
Oregon's proposed criteria, in light of this significant omission.

2. Oregon's proposed water quality standards for toxic pollutants do not adequately protect
species from gill exposure to particulates.

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Oregon's criteria do not protect designated uses because the criteria fail to protect against
dermal exposure to toxic particulate metals via the gills. EPA developed (and Oregon adopted)
water quality criteria for metals based on the concentration of a pollutant in the water column.
This assumes that the only exposure pathway is via contact with dissolved metals across the
gills during respiration. However, as the Services have explained, gill contact with toxic
particulates also adversely affects fish: "Through respiratory uptake, aquatic organisms are
exposed to metals in addition to those measured in the dissolved fraction of ambient waters. As
fish ventilate, a nearly continuous flow of water pass across their gills and particulate metals
suspended in the water column may become entrapped. At the lowered pHs occurring near gill
surfaces entrapped particulate metals may release soluble metal ions, which are the forms EPA
considers most bioavailable and efficiently taken up by aquatic organisms." As a result, the
Services concluded that "the proposed EPA metals criteria in the CTR for aquatic life should
not exclude particulate forms of any metal, unless and until EPA demonstrates that exposures
of threatened or endangered species to these contaminants are unlikely to cause adverse effects
in natural waters." EPA has not demonstrated, in the five years since the Services released the
CTR BiOp, that the current EPA-recommended criteria protect species from gill exposure to
toxic particulates. Thus, the proposed Oregon criteria, which rely on the same unproven
assumptions regarding gill exposure to toxic pollutants, unlawfully exclude toxic pollutants and
thereby fail to protect aquatic uses.

3. Oregon's proposed water quality standards for toxic pollutants do not adequately protect
species from dietary exposure to particulates.

Although dietary exposure is a critical exposure pathway for toxic pollutants, EPA has largely
ignored the effects of dietary exposure on water quality and species protection. EPA did not
consider dietary exposure when it established its recommended criteria for toxic pollutants,
and, as a result, the EPA recommended criteria greatly underestimate an organism's exposure
to toxic pollutants. In March of 2000, the Services noted that "EPA has not assessed whether
the food base of aquatic organisms may accumulate excessive metal residues under CTR
proposed criteria." Likewise, neither EPA nor Oregon has assessed whether organisms may
accumulate heavy metals as a result of dietary exposure to toxic pollutants for which Oregon
has proposed water quality criteria. The failure of the agencies to consider this vital aspect of
toxic exposure undermines the protectiveness - and thus the legality - of the criteria overall.

Dietary exposure is an extremely important pathway for species exposure to toxic pollutants.
"The consensus of research studies is that most of the selenium in fish tissue results from
selenium in diet rather than the water (Cumbie and Van Horn 1978; Lemly 1982,1985a; Finley
1985, Hamilton et al. 1986; Woock et al. 1987; Besser et al. 1993; Coyle et al. 1993)" Studies
show that dietary exposure to toxic pollutants has adverse effects on aquatic life and wildlife.
For example, in a study comparing young rainbow trout that were fed contaminated
invertebrate prey with young rainbow trout that were fed clean prey, the trout that were fed the
contaminated prey showed reduced growth and survival, while the control group showed no
reductions in growth. Both study groups were placed in clean water, and the only variable at
issue was the level of contamination in the prey. This study demonstrates that contaminated
prey has adverse effects on trout, notwithstanding the presence of dissolved pollutants in the
water body. The presence of contaminated food sources is particularly important as the
contaminants work their way up the food chain. As an example, "[bjenthic organisms can
tolerate body burdens of selenium far greater than the dietary toxic level for fish and aquatic
birds without suffering ill effects. Thus, the most important aspect of selenium residues in

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sediments is not direct toxicity to benthic organisms themselves, but rather the dietary source of
selenium they provide to fish and wildlife species that feed on them." It is thus indisputable that
contaminated food may have a negative impact on designated and existing uses in Oregon's
waters.

Oregon's proposed water quality standards for toxic pollutants fail to consider dietary uptake of
pollutants via contaminated prey and contaminated benthic organisms. By failing to consider
this important exposure pathway, Oregon's criteria fail to protect designated and existing uses.
EPA must therefore disapprove these criteria as failing to meet the requirements of the CWA.

EPA's Response to Comment D:

EPA disagrees with the comment that Oregon's new and revised aquatic life criteria all fail to
protect Oregon's Fish & Aquatic Life designated use because of a failure to address exposure
pathways from particulates and contaminated food. EPA's rationale is explained in its responses to
the three specific claims made by the commenter.

1. Oregon's proposed water quality standards for toxic pollutants do not adequately protect
species from exposure to sediments and particulates.

In regards to exposure to particulates, EPA discussed many aspects of this issue in its response
to claim 1 in Comment B concerning the expression of aquatic life criteria for metals in terms
of dissolved metal rather than total recoverable metal.

A great deal of scientific evaluation has been invested in the issue of sediments and toxicity to
benthic organisms.15a6'17 However, the new and revised Oregon criteria before EPA for action
are aquatic life criteria, not sediment criteria. EPA derives its national aquatic life criteria,
which Oregon adopted, for metals to protect water column organisms from exposure to
pollutants present in the water column. Gobas and Morrison (2000) and Ankley et al. (1996)
discuss these concepts of partitioning between dissolved and solid phases.18,19

The fact that dissolved metal criteria limit not only equilibrium conditions but also to
nonequilibrium conditions, caused by time variability of water-column concentrations, provides
an additional margin of safety. The peak concentrations to which the water-column criteria
apply are greater than the average concentration in the water column, often by a wide margin.

15 Hansen, D.J., J.D. Mahony, W.J. Berry, S. Benyi, J. Corbin, S. Pratt and M.B. Able. 1996. Chronic
effect of cadmium in sediments on colonization by benthic marine organisms: An evaluation of the role
of interstitial cadmium and acid volatile sulfide in biological availability. Environ. Toxicol. Chem.

15:2136-2137.

16 Hare, L., R. Carignan and M.A. Huerta-Diaz. 1994. A field experimental study of metal toxicity and
accumulation by benthic invertebrates; implication for the acid volatile sulfide (AVS) model. Limnol.

Oceanogr. 39:1653-1668.

17 Lee, B.-G., H.-S. Jeon, S.N. Luoma, J.-S. Yi, C.-H. Koh. 1998. Effects of AVS (Acid Volatile Sulfide)
on the bioaccumulation of Cd, Ni, and Zn in bivalves and polychaetes. Abstract: 19th Annual Meeting of
the Society of Environmental Toxicology and Chemistry. Charlotte, NC.

18 Gobas, F. A.P.C., and H. A. Morrison. 2000. Bioconcentration and Biomagnification in the Aquatic Environment.
Handbook of Property Estimation Methods for Chemicals. CRC Press, http://research.rem.sfu.ca/downloads/rem-
610/readings/gobas.pdf accessed 2012-11-28.

19 Ankley, G.T., et al. 1996. Technical basis and proposal for deriving sediment quality criteria for metals. Environ. Toxicol.
Chem. 15(12): 2056-2066.

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Sediment concentrations, by contrast, reflect long-term average concentrations of the
contaminant on the settling particles.

See General Response 5 concerning wildlife.

2. Oregon's proposed water quality standards for toxic pollutants do not adequately protect
species from gill exposure to particulates.

As was noted in response to claim 1 in Comment B, EPA derives its national aquatic life
criteria so that they protect water column organisms from exposure to pollutants that are
present in the water column. The primary mechanism for water column toxicity is absorption
at the gill surface, which requires metals to be in the dissolved form and bioavailable.
Therefore, protection of aquatic life is provided using the quantification of dissolved metals as
proposed by Oregon.

The total dissolved method proposed in the CTR and NTR is consistent with the best available
scientific evidence for non-bioaccumulative metals.

Please see General Response 4 concerning ESA listed species and consultation with the
Services.

3. Oregon's proposed water quality standards for toxic pollutants do not adequately protect
species from dietary exposure to particulates.

Aquatic life criteria are derived to protect organisms from exposure to pollutants in the water
column. Studies of the importance of other routes of exposure, such as pollutant ingestion via
food, are much less common than water-only toxicity tests, and do not have well standardized
methods. Where there is strong experimental evidence that, for a particular metal, dietary
exposure is a primary source of exposure, EPA is able to take dietary exposure into account
(e.g., the 1987 selenium criterion and the draft revised selenium criteria under development).

The likelihood of exposure to particulate matter is very waterbody-specific because it depends
on the flow, hydrology, and geomorphology of the waterbody. These would need to be
modeled for each waterbody, because, for example, the flow and hydrology of rivers are much
different than the flow and hydrology of lakes, wetlands, and estuaries. Such considerations
are most appropriately taken into account in the derivation of site-specific criteria.

Although data clearly show that fish accumulate some specific metals through the diet, at
present it is not clear to what degree such metal accumulation produces negative effects or
ecological risk. Results of experiments performed using dietary metal introduced in different
forms conflict as to the degree of uptake and the existence of negative effects resulting from
those exposures (e.g., compare Woodward et al. 199420, Mount et al. 199421, and Julshamn et

20 Woodward, D.F., W.G. Brumbaugh, A.J. Delonay, E.E. Little, and C.E. Smith. 1994. Effects on rainbow trout fry of a

metals-contaminated diet of benthic invertebrates from the Clark Fork River, Montana. Trans. Amer. Fish. Soc. 123: 51-62.

Mount, D.R., A.K. Barth, T.D. Garrison, K.A. Barten, and J.R. Hockett. 1994. Dietary and waterborne exposure of
rainbow trout (Oncorhynchus mykiss) to copper, cadmium, lead and zinc using a live diet. Environ. Toxicol. Chem. 13:2031-
2041.

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al. 199822). Further, comparison of data from water-borne and dietary exposures of metals
shows no significant relationship between metal accumulated in tissue and the presence or
absence of biological effects (e.g. compare Marr et al. 199623 with Woodward et al. 199424 and
Mount et al. 199425). Differences among the results of these studies demonstrate why the
assessment of the ecological relevance of metals requires more than a demonstration of
accumulation, because the presence of contaminant in diet or tissue is not itself a biologically
meaningful effect.

The primary experiments suggesting the existence of risk from dietary metal exposure
(Woodward et al. 199426 and later studies from the same laboratory) used designs that preclude
unequivocal assignment of cause and effect to single metals, mixtures of metals, or other
factors. As a result, these experiments are useful for focusing attention on the need to further
examine the importance of dietary exposure, but they do not provide an approach for taking
such exposure into account in the derivation of aquatic life criteria.

As with many other scientific issues, EPA recognizes that additional studies are desirable to
better define the relative importance of dietary exposure to particulates. If such work were to
indicate that ingestion substantially adds to the adverse effects caused by dissolved metal, EPA
would include the new data in its review of new and revised aquatic life criteria to ensure that
they account for dietary exposure to particulates. But presently available evidence does not
support that conclusion.

EPA does not agree that EPA's recommended selenium criterion fails to account for
bioaccumulation. In fact, the National Ambient Water Quality chronic criterion for selenium,
which was adopted by Oregon, does account for bioaccumulation. It is a field-based criterion
that is based on data obtained at Belews Lake (in North Carolina), the food chain of which was
contaminated by selenium. Contamination of Belews Lake waters yielded elevated
concentrations in aquatic plants, which in turn yielded elevated concentrations in invertebrates
and fish - that is, bioaccumulation was occurring and accounted for the observed effects in
Belews Lake. Although the comment discusses the importance of dietary selenium exposure, it
provides no evidence or discussion to support its contention that EPA's selenium chronic
criterion fails to account for bioaccumulation.

The commenter stated that the Services noted that "EPA has not assessed whether the food base
of aquatic organisms may accumulate excessive metal residues under CTR proposed criteria."
As addressed above, the accumulation of metal in the diet is not a basis for criteria
development. In cases where dietary uptake has been scientifically demonstrated to occur and
is directly relevant to ecological risk, the EPA incorporates such data into criteria development.

See General Response 5 concerning wildlife.

Julshamn, K., K.J. Andersen, O. Ringdal and J. Brenna. 1988. Effect of dietary copper on the hepatic concentration and
subcellular distribution of copper and zinc in the rainbow trout (Salmo gairdneri). Aquaculture 73: 143-155.

23 Marr, J.C.A., J. Lipton, D. Cacela, J.A. Hansen, H.L. Bergman, J.S. Meyer and C. Hogstrand. 1996. Relationship between
copper exposure, duration, tissue copper concentration, and rainbow trout growth. Aqua. Toxicol. 36: 17-30.

24 Ibid.

25 Ibid.

26 Ibid.

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Comment E: Oregon's Proposed Criteria Do Not Protect Designated Uses, Because They Fail to
Address Bioaccumulation of Toxic Metals and Organic Pollutants

Oregon's proposed criteria fail to account for the bioaccumulative nature of toxic metals and other
toxic pollutants. The proposed criteria thus fail to consider the increased risks that bioaccumulation
presents to designated and existing uses. Moreover, Oregon's rules, which allow mixing zones for
bioaccumulative pollutants and which exempt known sources of bioaccumulative toxics from
compliance with water quality standards, exacerbate the harms presented by bioaccumulative
pollutants. Oregon's proposed criteria thus fail to protect designated uses and must be disapproved.

1. Oregon's criteria do not protect against bioaccumulation.

Oregon's proposed standards fail to regulate bioaccumulation of toxic pollutants. The proposed
criteria for toxic pollutants are based on the concentration of pollutants in the water column. As
such, the criteria do not account for bioaccumulation, which, by definition, is an increase in the
concentration of a pollutant above the ambient water concentration. This increased
concentration adversely affects the beneficial uses. By failing to account for bioaccumulation,
the Oregon criteria fail to protect designated and existing uses.

There are many pollutants that bioaccumulate, including arsenic, mercury, selenium, DDT,
PCBs, endrin, and toxaphene, and the bioaccumulative nature of these pollutants makes them
particularly harmful. Pollutants may be concentrated or magnified in successive trophic levels.
In a study of Lake Ontario, PCBs were magnified 2.8 million times in lake trout and 25 million
times in herring gulls. In aquatic ecosystems, bioaccumulation has the greatest adverse effect
on top predators, such as Oregon's ESA-listed salmonid species - Chinook, Coho, chum,
sockeye, and steelhead - because they eat prey from high trophic levels. Moreover, as EPA has
noted about Bioaccumulative Chemicals of Concern (BCCs): "[Human] exposure to BCCs can
result in decreased fertility, premature labor, spontaneous abortion, reproductive hormone
disorders, increased stillbirths, lack of mammary function, reduced libido, and delayed estrus.
Children may be at greater risk than adults... Risks to infants and children include central
nervous system effects, mortality, low IQ scores, cataracts, congestive heart failure, skin
disorders, cancers, immune system dysfunction and immunosuppression, skeletal disorders,
neurological/behavioral effects, and endocrinological disorders." BCCs also adversely affect
fish and wildlife.

EPA has recognized that bioaccumulation is important, and EPA guidelines indicate that tissue
residue studies should be used to assure that criteria protect against bioaccumulation. The
guidelines, however, have not been implemented. The Services noted, "criteria documents for
metals include the discussion of bioaccumulation studies but final criteria are based on acute
and chronic toxicity studies. EPA has not considered results of investigations which indicate
that exposures of salmonids to metals-contaminated invertebrate diets may result in adverse
effects." The Services conclude that "without due consideration of the bioaccumulation
potential of metals in aquatic ecosystems the proposed CTR criteria for metals are not
protective of threatened or endangered species." Because Oregon simply adopted EPA's
recommended criteria without considering the effects of bioaccumulation, the Services
comments apply equally to Oregon.

Oregon's proposed criteria for toxic pollutants are not protective of aquatic life or wildlife

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because they do not protect against bioaccumulation and instead regulate only the contaminant
levels in the water column. For example, EPA's - and thus Oregon's - recommended criteria for
metals were derived "solely on the results of aquatic toxicity tests where metal exposures occur
only across the gills or other respiratory surfaces. This is because toxicity tests used to develop
the criteria are performed with controlled laboratory water with little particulate metals and do
not include realistic dietary or other exposures." Toxicity to fish and wildlife, however, is
highly influenced by how much of the toxic pollutant is partitioned to the food chain, rather
than the water column concentration.

While Oregon's proposed criteria do consider the risk of elevated organic contaminants in fish
tissue eaten by humans, the criteria do not consider how contamination of fish tissue affects the
fish itself. Nor do the criteria consider the effects of bioaccumulation on aquatic invertebrates,
even though these animals are a designated use and form a critical component in the food
chain. Degradation of the aquatic invertebrates affects the larger predators, including threatened
and endangered salmon. Oregon's proposed criteria fail to protect designated uses because the
standards do not consider how bioaccumulation will adversely affect aquatic organisms
themselves. The criteria thus cannot be considered protective of designated and existing uses.

2. Oregon's rules and policies weaken any protections against bioaccumulative
pollutants that the criteria may provide.

In addition to failing to account for bioaccumulation in its proposed criteria, Oregon has
adopted rules and policies that further limit the protectiveness of its water quality standards.
Oregon's water quality program ignores bioaccumulation in several key policies that greatly
weaken the standards.

First, Oregon's rules, in effect, exempt forestry and agriculture from water quality standards.
Regarding agriculture and forestry on federal lands, the rules state, "water quality standards are
expected to be met through the development of water quality restoration plans, best
management practices and aquatic conservation strategies." Thus, under Oregon's proposed
rules, water quality standards will not apply to agricultural runoff. Instead, Oregon rules
exempt major sources of pollution and rely on vague "restoration plans" and "best management
practices" that do not adequately address or monitor water quality standards. No agricultural
water quality management plans expressly address bioaccumulative pollutants and agricultural
water quality management plans themselves are vague and unenforceable. As a result, known
sources of bioaccumulative pollutants will go unchecked. Selenium, for example, concentrates
in subsurface irrigation drainage and may discharge into surface waters. Thousands of fish and
waterfowl were poisoned in the Kesterson National Wildlife Refuge, CA because selenium
leached from the soil of adjacent agricultural areas. Oregon's water quality standards will not
prevent the same from happening in Oregon.

Second, Oregon rules do not require a sampling frequency that protects against
bioaccumulative pollutants, which may accumulate in the food chain after a rapid mass loading.
Even if the criteria were protective, mass loadings of pollutants could go unnoticed and have a
long-term effect on organisms.

Third, Oregon's standards do not protect designated uses because state rules allow the
discharge of toxic pollutants, including pollutants that bioaccumulate in the environment, into
mixing zones. Oregon's rules allow point sources to discharge BCCs into mixing zones at

-------
levels higher than the applicable numeric criteria. Oregon and EPA view a mixing zone as a
localized concentration of pollution that is diluted by the surrounding water such that the water
body as a whole still protects designated uses. BCCs and other toxic pollutants that bind to
sediment are not appropriate for mixing zones, however, because these pollutants do not dilute.
Because Oregon's rules allow mixing zones to apply to discharges that will not dilute, the rules
allow for increased discharges of bioaccumulative toxic pollutants and thus fail to protect
designated uses.

EPA has acknowledged that mixing zones are not appropriate for bioaccumulative toxic
pollutants. EPA promulgated a rule that prohibits mixing zones for BCCs in the Great Lakes
System (GLS), which includes Illinois, Indiana, Michigan, Minnesota, and Wisconsin. In this
rulemaking, EPA found that "BCCs, due to their persistent and bioaccumulative nature, are
incompatible with mixing zones. By definition, BCCs are chemicals that do not degrade over
time... Because the effects of these chemicals are not mitigated by dilution, using a mixing zone
to 'dilute' BCC discharges is not appropriate." EPA recognized that it is the mass, not just the
concentration, of these chemicals that poses a problem. As in the GLS, reproductive failure due
to BCCs occurs in Oregon rivers, such as the Columbia and the Willamette. Oregon industries
discharge many of the same chemicals, Oregon waters have similar designated uses, and
Oregon has heavily polluted, large bodies of water. Thus, as with the GLS, in Oregon, "using a
mixing zone to 'dilute' BCC discharges is not appropriate."

EPA's Response to Comment E:

EPA disagrees with the comment that Oregon's new and revised aquatic life criteria all fail to
protect Oregon's Fish & Aquatic Life designated use due to a failure to consider bioaccumulation.
EPA's rationale is explained in its responses to the three specific claims made by the commenter.

1. Oregon's criteria do not protect against bioaccumulation.

For water-column organisms, bioconcentration is uptake from water whereas bioaccumulation
is uptake from both water and food. Therefore, bioaccumulation is bioconcentration (i.e.,
uptake from water) plus dietary exposure (i.e., uptake from food). Bioconcentration can occur
during every toxicity test, depending on the specific chemical and species under study. Dietary
exposure via bioaccumulation on food after addition in chronic tests may occur to some degree,
particularly for a partially live food such as YCT, but no quantification of this phenomenon has
been performed and would likely be inconsequential in the scope of the test. The issue
concerning bioaccumulation is the same as issue 3 in Comment D concerning dietary exposure
and is addressed in the response to that response.

See General Response 4 concerning ESA listed species and General Response 5 concerning
wildlife.

2. Oregon's rules and policies weaken any protections against bioaccumulative pollutants that the
criteria may provide.

EPA's adjudicatory authority under CWA 303(c)(3) is limited to the State's particular
submission of new and revised water quality standards. In this case, EPA's action is limited to
approving or disapproving Oregon's new or revised water quality standards that were submitted

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to EPA on July 8, 2004, as updated by its 2007 and 2011 submissions. The forestry and
agricultural rules cited by the commenter are part of a set of water quality standards revisions
submitted to EPA in 2003, which are not the subject of this action. The 2003 submission is the
subject of a separate action, which is proceeding in accordance with a Stipulated Order on
Nonpoint Source and Endangered Species Act Remedies. Northwest Environmental Advocates
v. United States Environmental Protection Agency. No. 05-1876 (D. Or.) (order issued January
7, 2013).

Comment F: Oregon's Proposed Criteria Are Not Protective Because They Are Derived From LC50
Concentrations, Which Are Established Through A Flawed And Underprotective
Methodology.

Oregon's proposed criteria are established through a flawed methodology that does not assure
protection of designated and existing uses. Specifically, for many of the toxic pollutants for which
Oregon has submitted proposed criteria, Oregon has proposed to adopt EPA's recommended
criteria. EPA's recommended criteria are, in turn, derived from so-called LC50 tests, which are tests
that determine, on a pollutant-by-pollutant basis, the concentration of any given pollutant that will
kill fifty percent of the exposed species population that is being tested. Once EPA determines the
concentration that will result in death to half the test population, EPA then divides that number in
half to establish the applicable criterion. Although EPA believes that it is establishing a protective
criterion through this method, the LC50 method is, in fact, a crude methodology that does not protect
imperiled populations or account for sublethal effects of toxic pollutants.

By its very nature, the LC50 does not protect imperiled species, because it allows up to half of a
population to die and fails to protect against sublethal effects. The Services noted as much in the
CTR BiOp when they concluded that EPA's recommended criterion for PCP was not protective of
aquatic life based, in part, on the use of LCsoto derive the criterion. The Services stated, "[by]
definition the LC50 is the concentration at which half the organisms are expected to die, and cannot
be used to determine the concentration that would be lethal to low numbers of salmonid trout
exposed for a short period of time."

Furthermore, Oregon's criteria do not consider sublethal effects on populations. The LCso-based
criteria are designed only to keep some portion of a population alive, but not necessarily healthy or
viable. Oregon assumes the safety factor of two prevents toxicity to aquatic life. The safety factor,
however, does not prevent, or even consider, adverse effects that result in harm less than death.
These sublethal effects are especially dangerous for chronic exposures, which occur at a much
lower threshold. Sublethal effects are also dangerous to threatened and endangered species, which,
by definition, are on the brink of extinction and cannot handle any additional stress. EPA cannot
approve Oregon's criteria because the criteria do not consider sublethal effects.

Because Oregon has not shown what percentage of a population is protected by its criteria, EPA
cannot assume that the criteria are protective of designated uses. Failure to protect aquatic life is a
violation of 40 C.F.R § 131.11. In addition, the ESA prohibits a take of any threatened or
endangered species. Oregon's criteria violate the ESA because the criteria are not designed to
protect one hundred percent of the populations.

EPA's Response to Comment F:

EPA disagrees with the comment that Oregon's new and revised aquatic life criteria fail to protect

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Oregon's Fish & Aquatic Life designated use because the criteria are derived from LC50S.

The commenter's arguments are based on a misunderstanding of the methodology Oregon relied on
for the derivation of its aquatic life criteria. EPA derives water quality criteria for use by States and
Tribes based on a rigorous methodology that is set forth in the Guidelines for Deriving Numerical
National Water Quality Criteria for the Protection of Aquatic Organisms and their Uses (Stephan et
al. 1985, hereafter referred to as the Guidelines). These Guidelines provide a scientifically
defensible methodology for deriving both an acute criterion concentration (to protect against short-
term lethality and, in some cases, other short-term severe effects) and a chronic criterion
concentration (to protect from sublethal and long-term effects such as reduced survival, growth, or
reproduction).

The commenter's statement that "the LC50 does not protect imperiled species, because it allows up
to half of a population to die" is not valid. Although LC50S reported from toxicity tests are used
during the derivation of criterion, the criteria are not set at the level of the LC50, but rather at a level
that yields toxicity essentially un-differentiable from controls, a concentration of one-half the LC50
of the 5th percentile of all represented genera. An LC50 serves as the basis for defining the
sensitivity of a genera, which is then used in conjunction with all other available genera level data
to calculate a 51 percentile to derive acute and chronic criteria for the protection of the aquatic
environment via the following methodologies:

The acute criterion concentration is derived, based on the Guidelines, as follows:

The acute criterion concentration is based on acute toxicity tests, which are sometimes called
"LC50 tests". The Guidelines require that the acute criterion concentration be based on effects
that reflect the total adverse acute impact of the pollutant on the test organisms. For most
species, the acute test result is the 48 or 96 hour (depending on the species) LC50 or EC50 based
on a combination of the percentage of organisms exhibiting loss of equilibrium plus the
percentage of organisms immobilized plus the percentage of organisms killed. This is more
protective than simply considering the percentage killed (i.e., LC50). For early life stages of
bivalve mollusks, the acute effect is the 96-hour EC50 based on a combination of the percentage
with incompletely developed shells plus the percentage killed.

If the available data indicate that one or more life stages are at least a factor of two more
acutely sensitive than one or more other life stages of the same species, test results for the more
resistant life stages are not used in the calculation of the Species Mean Acute Value (SMAV)
because a species can be considered protected from acute toxicity only if the most sensitive life
stage is protected.

For each species for which at least one acceptable acute value (LC50 or EC50) is available, the
SMAV is calculated as the geometric mean of the acceptable results of flow-through tests in
which the concentrations of test material were measured. For a species for which no such test
result is available, the SMAV is calculated as the geometric mean of all acceptable acute
values, i.e., results of flow-through tests in which the concentrations were not measured and
results of static and renewal tests based on initial concentrations of test material. The genus
mean acute values (GMAV) are then calculated as the geometric mean of the SMAVs that are
available for each genus. EPA uses geometric means instead of arithmetic means because
acute values are more likely to be log normally distributed than normally distributed.

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When acceptable acute tests are available for species in eight specified families, all of the
GMAVs are ranked from the least to the most sensitive. A regression analysis is performed
using the four GMAVs whose cumulative probabilities are closest to 0.05 in order to calculate
an estimate of the concentration of the pollutant corresponding to a cumulative probability of
0.05, which is called the Final Acute Value. If the SMAV of a commercially or recreationally
important species is lower than the calculated Final Acute Value and that SMAV is based on
results of a flow-through test in which the concentrations of the test material were measured,
then that SMAV becomes the Final Acute Value in order to provide protection for that
important species. The Final Acute Value is then divided by 2 to derive the acute criterion
concentration that corresponds to a percent mortality in the range of 0 to 10% for a hypothetical
species whose SMAV equals the FAV, based on empirical data and analyses which indicate
that dividing the LC50 for a test by two generally lowers the value to a lethality level which is
nearly indistinguishable from the level of mortality observed in the control samples using clean
water.

The commenter also states that Oregon's new and revised aquatic life criteria do not protect against
sublethal effects. This is incorrect because the chronic criteria are derived from data on the
sublethal endpoints, such as growth and reproduction, as defined in the Guidelines:

Chronic criterion concentrations are calculated in the same manner as acute criterion
concentrations when acceptable chronic tests are available for species in eight specified
families. However, instead of LC50S and EC50S derived from acute tests, the calculations use no
observed effect concentration (NOEC) and the lowest observed effect concentration (LOEC),
which are based on chronic toxicity tests which, by nature, are measured affects on growth,
reproduction, and long-term survival. The NOEC is the highest tested concentration in which
survival, growth, and reproduction are not statistically significantly different from the control
treatment, whereas the LOEC is the lowest tested concentration in which survival, growth,
and/or reproduction is statistically significantly different from the control treatment. The
geometric mean of these two values is called the Maximum Acceptable Toxicant Concentration
(MATC). Another acceptable endpoints is the EC20, or concentration that effects 20 percent of
a test population.

EPA uses results of three types of chronic toxicity tests to derive the CCC.

a. Life-cycle toxicity tests take into account adverse effects on survival and growth of adults
and young, maturation of males and females, eggs spawned per female, embryo viability,
and hatchability.

b. Partial life-cycle chronic toxicity tests are used for fish species that require more than a
year to reach sexual maturity, and the effects taken into account are the same as full life-
cycle toxicity tests.

c. For fish, early life-stage toxicity test take into account survival and growth during 28 to
90-day exposures, depending on the species, that begin shortly after fertilization and go
through embryonic, larval, and early juvenile development of the fish species. For fish,
results of early life-stage toxicity tests are used because they have been shown to be useful
predictors of the results of life-cycle tests.

If sufficient acceptable chronic data are not available to derive a CCC directly, an alternative
method exists that uses fewer chronic data to estimate the CCC from the FAV using an acute-
chronic ratio (ACR) to extrapolate from acute to chronic effects based on measured
relationships between the two types of effects. This approach can be used if ACRs are

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available for species from at least three different families provided that one is a fish, one is an
invertebrate, and one is an acutely sensitive freshwater or saltwater species. For each chronic
value for which at least one corresponding acceptable acute value is available, an ACR is
calculated by dividing the acute value by the chronic value. For each species, the Species
Mean Acute-Chronic Ratio is calculated as the geometric mean of all acute-chronic ratios
available for that species.

If the Species Mean Chronic Value of a commercially or recreationally important species is
lower than the calculated Final Chronic Value, then that Species Mean Chronic Value replaces
the calculated Final Chronic Value in order to provide protection for that important species as
was the case with tributyltin.

The acute and chronic criterion concentrations that are derived as described are then implemented
with duration and frequency limits that prevent the unacceptable effects to species from
exceedances of the criterion concentration by ensuring compensating periods of time during which
the concentration is below the criterion concentration. For most pollutants the four-day average
concentration of the pollutant must not exceed the CCC more than once every three years on
average and the one-hour average concentration must not exceed the acute criterion concentration
more than once every three years on average.

The CCC sets an upper limit below which concentrations must remain a high percentage of the time
in order for the water body to attain standards. The attainment goal for the chronic criteria set forth
by Oregon is a 4-day average exceedance once in 3 years. Interpreted as remaining below the
criterion more than 99.5 percent of the time, this indicates that concentrations in attaining waters
would seldom rise to the level of the criterion. Given typical time variability of real-world ambient
waters, for example, a log standard deviation of 0.5, waters that remain below the criterion 99.5
percent of the time would have a median and geometric mean concentration nearly six-fold lower
than the criterion (as determined for a lognormal distribution by log geometric mean = log criterion
- z sigma, where z, the normal deviate (i.e., Excel's NORMSINV) corresponding to 0.995 is 2.58
and sigma is 0.5). If the median concentration were higher than this, the frequency of exceeding the
criterion concentration would higher than that specified for attainment.

For such a time-variable situation the aggregate level of effect for a species having an EC20 (or
MATC) equal to the criterion can be calculated as the summation of the each possible level of effect
(from 0% to 100% of individuals affected) multiplied the probability (over time) of that level of
effect occurring, as illustrated in Appendix D of Delos (2008). For the above situation where (a) the
concentration remains below the criterion 99.5 percent of the time, and where (b) the concentration-
response curve has a has a typical log-probit shape (which assumes a lognormal distribution of
sensitivity among individuals in the species) with a typical slope such that the EC20/EC50 is 0.625,
the aggregate effect on the sensitive species would be less than one percent, meaning that on
average less than one percent of individuals would be affected. Such a low level of effect is
indistinguishable from zero and is far below the threshold for detecting effects in the field or even in
the lab. The criteria thus provide a much higher level of protection than implied by a naive
assertion that the criteria allow 20 percent effect27.

The commenter states that Oregon's new and revised criteria are not protective because Oregon has

27 Delos, C.G. 2008. Modeling Framework Applied to Establishing the Aquatic Life Criteria Attainment Frequency, June
2008 Draft. Office of Water, U.S. Environmental Protection Agency, Washington, DC. 160 p.

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not shown a percentage of "a population" protected. EPA does not agree that these criteria are not
protective. The derivation of national ambient water quality criteria for the protection of aquatic
life, and thereby the protection of the aquatic life designated use as adopted in Oregon, aims to
protect the biological integrity of the waters of the United States. Calculating the percentages of a
population that may be affected by criterion concentrations is not performed as there is no robust
and vetted method to do so, however, as discussed in the Guidelines, the criteria are set at
concentrations that protect 95 percent of all genera (and by extension, species) based on existing
toxicity data.

The general protectiveness of water quality criteria has been summarized in EPA's Technical
Support Document for Water Quality-based Toxics Control (page 2) as indicated in 40 CFR 131.11.

See General Response 4 concerning ESA listed species.

Comment G: Oregon's Proposed Criteria Do Not Adequately Protect Designated Uses Because
They Are Based On Studies Performed On An Unrepresentative Population Of
Surrogate Species.

Oregon's proposed criteria suffer from a primary flaw underlying EPA's development of
recommended toxics criteria: they are established through testing toxicity on a narrow and
unrepresentative population of surrogate species. Rather than test a toxic chemical's impacts on
species found in a particular water body, EPA uses surrogate species to estimate the effects of toxic
pollutants on other untested species. The data derived from surrogate species tests, however, are not
precise enough to protect species found in natural waterways. While EPA must set criteria based on
available data, and while the use of surrogate species is generally appropriate, EPA's failure to
adjust the criteria to account for the lowered sensitivity of surrogate species results in criteria that
do not protect species found in Oregon's waters.

Surrogate species are often less sensitive to toxic pollutants than species for which the surrogates
are used. For example, EPA uses toxicity data that it developed for fish to assess the impacts of
toxics on amphibians, even though some amphibians are up to three orders of magnitude more
sensitive than the test fish. The chart below, from the EPA pesticide ecotoxicity database,
demonstrates the great differences in sensitivity to pesticides even between members of the same
genus.

Pesticide

Organism

LCsn(ua/L)

Diuron

Red-legged frog (Ranc aurora)

22,200

Diuron

Carp, (Carrassius)

63,000

Diazinon

Climbing Perch (Anabas scandens)

37,750

Diazinon

Green frog (Rana clamitans)

Diazinon

Bog frog (Rana limncharis)

7,977

Carbaryl

Walking catfish (Clarias batrachus)

71,350

Carbaryl

Western mosquitofish (Gambusla affinis)

20,377

Carbaryl

Toad (Bufo hufojaponicus)

7,200

Carbaryl

Gray tree frog (Hyla versieolor)

2,470

Carbaryl

Green frog (Rana clamitans)

20,372

Endosulfan

Snake-head catfish (Channa punctata)

4,586

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Endosulfan Zebra danio (Danio rerio)

Endosulfan Toad (Bufo vulgaris formosus)

Endosulfan Bog frog (Rana limnocharis)

Endosulfan Tiger frog (Rana tigrina)

750
2,075
12
2

As one example, the green frog (Rana clamitans) is two orders of magnitude more sensitive to
diazinon than the bog frog (Rana linrnockaris). The criteria do not account for these differences.

Similarly, studies show that toxic pollutants have different effects on different salmonid stocks. For
example, sockeye salmon are five times more sensitive to copper than Chinook salmon. In addition,
an organism's sensitivity to toxic pollutants varies according to the species' life stage. For example,
salmon eggs, juvenile fish, and juvenile mussels are much more sensitive than adults to certain
pollutants. EPA does not, however, lower its recommended criteria to protect the most sensitive
species or most sensitive life stages or to account for different tolerances to toxic pollutants among
surrogate species. Nor does Oregon account for these differences in its proposed criteria. The
criteria do not, as a result, adequately protect designated uses in these circumstances.

EPA's Response to Comment G:

EPA disagrees with the comment that Oregon's new and revised aquatic life criteria fail to protect
Oregon's Fish & Aquatic Life designated use, due to their use of toxicity data from tests performed
using surrogate species. The comment does not include any specific information supporting the
contention that the toxicity data underlying Oregon's aquatic life criteria are insufficiently
representative of the species present in Oregon waters.

On the contrary, the data provided in the comment supported the protectiveness of those criteria
magnitudes. For diazinon, the commenter presents 21 |ig/L as the most sensitive frog LCso-
However, the submitted acute criterion is 0.17 |ig/L, more than 100-fold lower. For endosulfan, the
comment presents 2 |ig/L as the most sensitive frog LC50, whereas the submitted criterion is 0.22
|ig/L, almost 10-fold lower.28 EPA recognizes that there is variation among species in their
sensitivity to various pollutants, as illustrated by the data presented in the comment, and uses this
information in its procedures. But the data supplied here actually support EPA's risk assessment
conclusion that the nationally recommended criteria are protective of sensitive species in Oregon.

While there are toxicity data for some of the species in Oregon waters, for most species those data
are not available and EPA must use toxicity for surrogate species to determine potential effects on
aquatic species from the criteria values. EPA criteria development relies on a variety of surrogate
species to ensure that the criteria are protective of the wide variety of aquatic species that may occur
in an ecosystem.

Criteria are derived using a data set that is sufficiently broad to encompass most ecosystems within
the State. They do in fact take into account all available relevant data regardless of the distribution
of sensitivities (see response to comment F). The 1985 Guidelines were applied to Oregon's
derivation of individual chemical criteria and require acceptable test results for a broad range of
species in order to ensure aquatic life criteria protect almost all aquatic ecosystems. EPA's
minimum data requirements for deriving a criterion for freshwater aquatic animals require results of

28 The comment also presents a sensitive frog LC50 of 22,500 |ig/L for diuron. However, as diuron is not included in the
Oregon standards package being reviewed, this information is not directly relevant to the current action.

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acceptable acute tests with at least one species of freshwater animal in at least eight specified
families.29 These families are:

1. the family Salmonidae in the class Osteichthyes

2. a second family in the class Osteichthyes, preferably a commercially or recreationally
important warmwater species (e.g., bluegill, channel catfish, etc.)

3. a third family in the phylum Chordata (may be in the class Osteichthyes or may be an
amphibian, etc.)

4. a planktonic crustacean (e.g., cladoceran, copepod, etc.)

5. a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)

6. an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)

7. a family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca,
etc.)

8. a family in any order of insect or any phylum not already represented.30

Similarly, the Guidelines require results of acceptable acute tests with at least one species of

saltwater animal in at least eight different families. These families are:

1. two families in the phylum Chordata

2. a family in a phylum other than Arthropoda or Chordata

3. either the Mysidae or Penaeidae family

4. three other families not in the phylum Chordata (may include Mysidae or Penaeidae, whichever
was not used above)

5. any other family.31

A method to derive Final Chronic Values using chronic data from at least 3 families (in
combination with acute data from at least 8 families) is presented in the 1985 Guidelines because
chronic toxicity test data are significantly less available. The minimum taxonomic data
requirements (MDRs) outlined in the 1985 Guidelines ensure that resulting criteria are reliable
estimates that protect the majority of species in the majority of aquatic ecosystems. Results of acute
and chronic toxicity tests with representative species of aquatic animals are necessary so that the
data available for tested species can be considered a useful indication of the sensitivities of untested
species. To ensure that national aquatic life criteria are appropriately protective, the required data
purposely include some species that are sensitive to many pollutants, specifically daphnids and
salmonids. The required breadth of families in criterion calculations serve as useful surrogate
species and are representative in these assessments. Additional data are desirable and uncertainty in
a criterion decreases as the amount of available quality data increases.

In development of the criterion, the toxicological data are rank ordered from least sensitive to most
sensitive. The calculation of the final acute value, and if sufficient data is available, the final
chronic value, are determined by using the fifth percentile value based on the four most sensitive
genus mean values. Therefore, criteria development is specifically designed to protect the most
sensitive species for which toxicological data that meet data quality objectives are available. The
final acute value is further divided by 2 as identified above to be below a calculable level of effect
for that fifth percentile genus.

It has not been demonstrated that surrogate species are less sensitive as the commenter claims.

29 Ibid. Reference 1. PB85-227049. Section III, Required Data.

30 Ibid.

31 Ibid.

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Rather, the available data demonstrate that the sensitivities of surrogate species are similar, on the
average, to the sensitivities of other species. For example, Dwyer et al. (2005) tested early life
stages of 17 species and found that the rainbow trout was equal to or more sensitive than listed
species 81% of the time and, therefore, criteria that protect rainbow trout would, in most cases,
protect listed fish species. In addition, previous studies comparing the sensitivities of ESA listed
species with the sensitivities of standard test species demonstrated that listed species generally are
not more sensitive and the use of surrogate species is appropriate for endangered species risk
assessment.32 Indeed, many scientists concur that, although no one species is consistently the most
sensitive, rainbow trout and other salmonids are generally more sensitive than other species and are
adequate surrogates for listed species.33'34'35

The commenter can readily find instances of substantial differences between species within the
same genus. The methods described above in response to comment F account for apparent
divergent sensitivities based on test acceptability (where the data may not be of sufficient quality to
be used in criteria development) and by using all available data in the calculation of species and
genus mean averages. If studies yield quality data, the results are used in the calculation of the
aquatic life criterion. In fact, per the Guidelines, EPA uses Genus Mean Acute Values (GMAVs)
that include all species within a genus for which acceptable data exist. Further, the commenter has
not demonstrated that, when there are differences between species, EPA uses data for the more
resistant species. In fact, this is contradictory to the 1985 Guidelines approach; the calculation of
the criteria uses the four most sensitive genera (including most sensitive life stages tested) based on
all available data.

It is incorrect that EPA uses data solely from fish studies to assess impacts on amphibians. When
data are available for amphibians, they are used. When data are not available for amphibians, all of
the other species for which data are available become surrogates for that missing family per the
Guidelines protocol listed above for the protection of the ecosystem.

Additionally and importantly, most of the toxicological data upon which EPA bases the water
quality criteria use the most sensitive life stages (i.e., juvenile fish, etc) when performing these tests.
Therefore, these more sensitive life stages are protected in the calculation of Oregon's water quality
criteria.

Comment H: Oregon's Proposed Criteria Do Not Protect Designated Uses, Because They Are
Based Primarily OnToxicity Studies Performed In Static Water.

Oregon's proposed criteria do not protect designated uses because the criteria are derived primarily
from toxicity studies performed in static water. Scientists have demonstrated that static studies
greatly underestimate the toxicity of a pollutant. Test organisms are most sensitive to a pollutant in

32 Raimondo, S, Vivian, DN, Delos, C, Barron, MG. 2008. Protectiveness of Species Sensitivity Distribution Hazard
Concentrations for Acute Toxicity Used in Endangered Species Risk Assessment. Environ. Toxicol. Chem. 27:12 2599-2607.

33 Mayer FL, and Ellersieck MR. 1986. Manual of acute toxicity: Interpretation and database for 410 chemicals and 66
species of freshwater animals. Resource Publication 160. U.S. Fish and Wildlife Service, Washington

34 Dwyer FJ, Mayer FL, Sappington LC, Buckler DR, Bridges CM, Greer IE, Hardesty DK, Henke CE, Ingersoll CG, Kunz
JL, Whites DW, Augspurger T, Mount DR, Hattala K, and Neuderfer GN. 2005. Assessing contaminant sensitivity of
endangered and threatened aquatic species: I. Acute toxicity of five chemicals. Arch. Environ. Contam. Toxicol. 48:143-154

35 Sappington LC, Mayer FL, Dwyer FJ, Buckler DR, Jones JR, and Ellersieck MR. 2001. Contaminant sensitivity of
threatened and endangered fishes compared to standard surrogate species. Environ. Toxicol. Chem. 20:2869-2876

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a tank that allows polluted water to flow continuously, rather than in a tank of static water. For
example, a study comparing the toxicity of silver on fathead minnows showed that toxicity rates
were two times higher in flow-through tanks than in the static tanks. Another study found that static
test results were twenty times less protective than flow-through tests for DDT. These data indicate
that tests performed in static water underestimate the toxicity of pollutants. It should go without
saying that flow-through tests more closely resemble the natural conditions of species exposure to
toxic pollutants in most Oregon waterways, which consist primarily of rivers, streams, and other
moving waterways. Oregon's proposed criteria, however, are based on tests performed in static
water unless such information is unavailable. The criteria thus fail to adequately assess the risks to,
and thus protect, Oregon's designated and existing uses.

EPA's Response to Comment H:

While EPA prefers the results of flow-through acute tests, then static-renewal tests, over results of
static acute tests (as stated in EPA's response to Comment F), EPA disagrees with the overall
premise of the comment—that Oregon's new and revised aquatic life criteria all fail to protect
Oregon's Fish & Aquatic Life designated use, due to reliance on data from static acute tests.

When flow-through or static-renewal acute test data are available, EPA does not use results of static
acute tests. Data for static tests is used only when no other relevant data is available and when there
are no concerns regarding volatility or other interference in the test, except in certain cases as
identified in ASTM or EPA toxicity testing standards. This is done to maximize the amount of
acute data for species used in the derivation of the FAV and to ensure protection of all species
tested by using the fullest quality data set available. EPA decided that it was better to use acute
values for more species rather than reject results of all static acute toxicity tests. Further, flow-
through tests do not necessarily yield lower, more protective values; chemicals that are stable in
water may not exhibit increased toxicity in flow-through tests.

More importantly, EPA does not use results of static chronic tests; acceptable chronic tests must be
flow-through or renewal tests in order to guarantee constant concentrations and water quality during
the timeframe in which the test is performed. The chronic criterion concentration of high BCF
chemicals is of much more regulatory significance than the acute criterion concentration due to their
bioaccumulative nature.

The commenter cited a study which found that static test results were twenty times less protective
than flow-through tests for DDT. As a practical matter, the acute tests for DDT have no regulatory
or environmental relevance, whether they are static or flow-through tests, because the chronic
criterion concentration for DDT was derived independently of the acute tests (see Appendix I) with
more robust direct chronic data. Consequently, it is not clear why this issue is raised for DDT. If the
commenter is implying that results of static acute toxicity tests are typically 20-fold higher than the
results of flow-through acute toxicity tests for other pollutants, such a conclusion is unfounded.
Organic pollutants with large bioconcentration factors (BCFs) are likely to show larger differences
between static and flow-through acute toxicity tests than other pollutants, but such pollutants are
also ones for which the CCC (based solely on non-static test data) is much more important than the
acute criterion concentration as discussed above.

Comment I: Oregon's Proposed Criteria Fail To Adequately Consider Impacts Of Water Hardness
And pH On Toxicity And Thus Fail To Protect Designated And Existing Uses.

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Oregon's proposed criteria use a hardness-dependant formula for metals that does not consider other
variables that affect the toxicity of a pollutant and, as a result, does not protect designated and
existing uses. In general, the toxicity of certain metals decreases as the hardness of the ambient
water increases. EPA measures hardness as a ratio of calcium to magnesium. The hardness-based
formula, however, is not protective of designated uses.

The hardness-based formula established by EPA does not consider other environmental variables,
such as dissolved organic carbon (DOC) and pH which affect the degree to which hardness
influences toxicity. Scientists have demonstrated repeatedly that hardness is just one of the
influences on toxicity. One study determined that pH values had a greater impact on toxicity than
hardness. As pH increased from 7.17 to 8.58, the level of toxicity necessary to cause death to half
the test population decreased nearly three-fold. The same results occurred as the alkalinity was
adjusted from 20 to 600 mg/L CaC03. Similar results occurred as the water hardness was adjusted.
Another test showed that the addition of small quantities of sodium chloride (common salt)
increased toxicity. In addition, researchers have demonstrated that both alterations in pH and DOC
affect copper toxicity to daphnia. Researchers have also found that DOC is important in controlling
toxicity of copper in fathead minnows. These studies provide convincing evidence that natural
variables, in addition to hardness, significantly affect the toxicity of contaminants. Despite this,
however, only hardness is considered in establishing criteria.

In the case of silver, scientists discovered that hardness is not the most important variable
influencing its toxicity. The Services noted that "recent science challenges the EPA concept of
hardness as having a large ameliorating effect on aquatic toxicity of silver." Researchers have found
that calcium, by itself, is not the most protective constituent for silver. Their work concluded that
DOC is more important than hardness for predicting the toxicity of ionic silver in natural waters to
rainbow trout, fathead minnows, and daphnia.

Scientists have also recently developed complex gill surface interaction models to account for
waters of different chemical compositions. A new model tests the additive or synergistic
relationship of various metals on gill toxicity and reports that a number of factors in addition to
calcium influence toxicity.

Research thus demonstrates that Oregon's hardness formula oversimplifies the interactions of
multiple chemicals, resulting in metals criteria that are underprotective of aquatic uses. The Services
interpreted this research by stating, "the use of hardness alone as a universal surrogate for all water
quality parameters that may modify toxicity, while perhaps convenient, will clearly leave gaps in
protection when hardness does not correlate with other water quality parameters such as DOC, pH,
CI- or alkalinity." Five years after the Services made this observation, EPA continues to rely on
outdated hardness data alone. Similarly, Oregon's failure to use more accurate science and its
reliance on an oversimplified and scientifically unsound model renders the proposed criteria
unprotective of designated and existing uses.

EPA's Response to Comment I:

EPA disagrees with the comment that Oregon's new and revised aquatic life criteria for metals fail
to protect Oregon's Fish & Aquatic Life beneficial use because they fail to adequately consider
impacts of hardness and pH on toxicity. The commenter provides some discussion of hardness-
based criteria and the biological opinion concerning the CTR, but the commenter presents no

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specific data demonstrating that Oregon's criteria fail to protect Oregon's designated use.

Additive and synergistic interactions have been addressed in EPA's response to Comment A.

Hardness is a variable that has been demonstrated to correlate with change in the toxicity of many
metals. For some metals the effect might be, wholly or partially, due to variables such as alkalinity
and pH that are usually correlated with hardness. In the derivation of criteria EPA does examine the
effects of pH, temperature, and other tested water chemistry variables on toxicity, where there are
sufficient data to determine such relationships (e.g., ammonia criteria).

The presence of dissolved organic carbon (DOC) decreases the toxicity of most metals. EPA
intentionally uses results of acute toxicity tests performed in dilution waters that have low
concentrations of DOC. Therefore, not taking DOC into account in the derivation of an aquatic life
criterion generally has the effect of preserving the protectiveness of criteria, not rendering the
criteria less protective. Very few surface waters would have DOC concentrations even lower than
the dilution waters used in acceptable laboratory toxicity tests contain. Thus, the metal and other
water quality criteria determined using tests waters with low DOC yield values that are generally
expected to be more protective, not less, than would be determined in natural waters.

Although it is true that speciation and site-water chemistry can affect toxicity and that the criteria do
not account for some of these factors, EPA does not agree that the criteria are underprotective of
designated and existing uses. There are inadequate data on enough species and conditions to adjust
for all important factors in the criteria, although current work is addressing these issues with
increasing specificity. However, this uncertainty is insufficient reason to refuse to adopt and
implement criteria based on the best science presently available; criteria are sufficiently protective
of most receiving waters without modification, and can be appropriately adjusted for other waters
through the development of site-specific criteria.

Comment J: Oregon's Proposed Criteria Do Not Protect Species From Sublethal Effects Of Toxic
Pollutants And Therefore Do Not Adequately Protect Designated And Existing Uses.

Oregon's proposed criteria do not protect designated and existing uses because the criteria do not
defend against sublethal effects, such as species' decreased ability to obtain food, escape predators,
or produce successful offspring due to functional impairment. Functional impairment includes
developmental, endocrinal, reproductive, neurological, or immuniologic impairment. Oregon's
proposed criteria neglect toxic pollutants' contribution to functional impairment in designated uses,
even though the CWA mandates the protection of the most sensitive designated uses and the
restoration of the physical, chemical, and biological integrity of the nation's waters. By not
considering the sublethal effects of toxic pollutants, Oregon has failed to protect the most
designated uses in the manner required by the CWA.

Studies demonstrate that Oregon's proposed criteria are not protective of designated uses, including
threatened and endangered species, because sublethal effects result from pollutant concentrations
that fall well below Oregon's proposed criteria. As an example, one study showed that very low
concentrations of endosulfan cause sublethal effects in salamanders. The study demonstrated that
0.5 |ig/L of endosulfan disrupted the pheromonal communication system of female red-spotted
newts. Pheromone disruption resulted in decreased mate selection and mating success for the
exposed newts. The sublethal effects manifested themselves, even though there were no outward
signs of toxicosis. In contrast to the low levels of endosulfan that caused these results, Oregon's

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proposed criteria do not protect aquatic life from endosulfan whatsoever, and the human health
criterion is 62 |ig/L, well above the concentration of endosulfan that caused sublethal effects in
newts. Oregon's proposed criteria simply do not protect designated uses because they fail to protect
species against sublethal effects, such as the ones demonstrated in the endosulfan tests.

Similarly, Oregon's proposed criteria do not consider, and thus do not protect against,
immunosuppression and lower disease resistance that result from exposure to toxic pollutants. A
study comparing the disease resistance of Chinook salmon in Oregon's polluted estuaries versus the
disease resistance of Chinook salmon in Oregon's less polluted waters demonstrated that "juvenile
fall chinook salmon from polluted estuaries are immunosuppressed and are more susceptible to
disease than those from less polluted waters." This field study corroborates a recent laboratory
experiment in which scientists administered sublethal doses of polycyclic aromatic hydrocarbons
(PAHs) and PCBs to juvenile chinook. The exposed fish exhibited suppression of their primary and
secondary plague-fighting cells' response to an antigen, as well as an increase in disease
susceptibility. The scientists concluded that, while disease is a natural occurrence, pollution "may
significantly shift the balance between salmon survival and mortality due to disease." Another study
compared fish responses to two stressors, a natural parasite and a PCB mixture. The results showed
that, in combination, the natural and anthropogenic stressors have a greater adverse effect on
salmon health than either stressor alone. Since natural waterways contain several natural parasites,
diseases, and other stressors, it must be concluded that the addition of anthropogenic pollutants will
lower species' natural resistance to these natural stressors. Oregon's proposed criteria, however,
were established through tests conducted in purified laboratory water and do not consider the
potential for pollutants to affect species' immunosuppression, disease resistance, or ability to fend
of parasites. As such, Oregon's proposed criteria fail to protect against demonstrated risks to
designated uses and thus fail to meet the requirements of the CWA.

Reduced physical performance is another sublethal effect that Oregon does not incorporate into its
proposed criteria. One study showed that low doses of ammonia affected the swimming
performance of coho salmon. At 0.04 mg/L of ammonia in water, the swimming velocity of coho
noticeably decreased. At 0.08 mg/L, there was a marked decrease in swimming efficiency. Very
low doses of ammonia, therefore, can induce the sublethal effects of reduced swimming
performance which, in turn, affects the species' survival. These concentrations of ammonia are two
orders of magnitude less than EPA's recommended criteria and Oregon's proposed criteria of 24
mg/L for salmonids. In failing to account for these sublethal effects, Oregon's proposed criteria
clearly do not protect designated uses, particularly threatened and endangered salmonids.

EPA's Response to Comment J:

EPA disagrees with the comment that Oregon's new and revised aquatic life criteria all fail to
protect Oregon's Fish & Aquatic Life beneficial use because they do not protect species from
sublethal effects of toxic pollutants. EPA's methodology for deriving aquatic life criteria considers
available data concerning "cumulative and delayed toxicity, flavor impairment, reduction in
survival, growth, or reproduction, or any other adverse effect that has been shown to be biologically
important."36 Such data can be used to lower the CCC if sublethal effects indicate that a lower
value should be used. Furthermore, chronic tests inherently include measures of sublethal effect
such as effects on growth and reproduction.

36 Reference 1. PB85-227049. Section X Other Data and Section XI Criterion.

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While it is possible that some sublethal effects may not be identified in standard toxicity tests, many
sublethal effects will have no bearing on the survival of organisms or maintenance of a population
due to the lack of a biological link to disruption of natural homeostatic function. The National
Academy of Sciences report "Toxicity Testing in the 21st Century" (NAS/NRC, 2007, p.6) notes
that "... at low doses, many biological systems may function normally within their homeostatic
limits."

Regarding the Park et al (2001) study of salamander reproductive disruption claimed by the
commenter to be relevant to this action regarding reproductive success: The commenter is incorrect
in stating that Oregon's "proposed criteria do not protect aquatic life from endosulfan whatsoever."
In fact, the magnitude of Oregon's chronic criterion for endosulfan (0.056 |ig/L) is almost an order
of magnitude lower than the 0.5 |ig/L referenced above.

The commenter alludes to data regarding the impacts of polluted waters on the immune system of
chinook salmon, but no specific chemical criteria are discussed in relation to the data presented,
other than for PAHs and PCBs. Oregon did not propose new or revised aquatic life criteria for
PAHs or PCBs. Because there are no revised aquatic life criteria for EPA to review for PAHs or
PCBs in this action, these comments are not pertinent to EPA's action.

The cited study by Wicks et al. (2002) is, in fact, included in EPA's analysis of the submitted
ammonia criteria. Also, the comment mentions information on the effect of ammonia on swimming
performance of coho salmon, but does not include sufficient information for EPA to use the
referenced information. From the magnitude of the effect concentrations, it is clear that the
comment refers to un-ionized ammonia concentrations, which are a small fraction of total ammonia,
and cannot be translated to the total ammonia nitrogen (the units of the criterion) without knowing
the pH and temperature of the study, for which the comment provides no reference information.
EPA has thus considered the comment but finds the information to be too incomplete to be used
scientifically. Please see the comment and response concerning ammonia in the Specific Pollutant
Concerns section at the end of this document. Consequently, EPA disagrees with the commenter's
comment that EPA is failing to consider sublethal effects of toxic pollutants.

See General Response 4 concerning ESA listed species and Response to Comment F regarding
chronic criteria.

Comment K: Oregon's Proposed Criteria Do Not Account For Hundreds Of Dioxins, Furans, And
PCBs, And Thus Fail To Protect Designated And Existing Uses.

EPA's Response to Comment K:

EPA responded to Comment K in its June 1, 2010 Supplemental Response to Comment Submitted
by Northwest Environmental Advocates [NWEA} as They Pertain to Oregon's New and Revised
Human Health Water Quality Criteria for Toxics Submitted on July 8, 2004. For the full comment
and EPA's response, please see pages 15-17 of the referenced document.

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Comment L: Oregon's Proposed Criteria Do Not Include Protections Against Endocrine

Disrupting Chemicals And Thus Fail To Protect Designated And Existing Uses.

Oregon's proposed criteria do not protect designated uses because the criteria fail to defend against
endocrine disrupting chemicals (EDC) that adversely affect organisms at concentrations well below
Oregon's criteria. The scientific community, including EPA, recognizes that many pollutants can
disrupt the hormonal balance controlled by the endocrine system. EDCs disrupt thyroid hormones,
androgens, estrogens, and other endocrine processes. Endocrine disruption may have profound
effects, including feminization of males, decreased offspring survival, alteration of the immune
system, and behavioral changes. Despite the known presence of EDCs in Oregon's waters and the
significant harm that EDCs cause, Oregon has failed to include in its water quality standards
protections against these chemicals. As a result, Oregon's proposed criteria do not protect
designated uses.

Federal agencies have long been aware of endocrine disruption. In its proposed statement of policy
for the long-term Endocrine Screening Program, EPA stated, "[t]aken collectively, the body of
scientific research on human epidemiology laboratory animals, and fish and wildlife provides a
plausible scientific hypothesis that environmental contaminants can disrupt the endocrine system
leading to adverse-health consequences." The National Toxicology Program, which consists of a
panel of academic, government, and industry scientists, similarly determined that there is "credible
evidence" that some hormone-like chemicals can affect test animals' bodily functions well below
the "no effect" levels determined by traditional testing and used as a basis for Oregon's new criteria.
The report stated, "[l]ow-dose effects, as defined for this review, were demonstrated in laboratory
animals exposed to certain endocrine active agents." Low dose effects were clearly demonstrated
for estradiol and several other estrogenic compounds, methozychlor (an insecticide), and
nonylphenol (an industrial compound identified in drinking water supplies).

Recent studies have shown disturbing effects of EDCs at very low concentrations. For example,
Professor Hayes at the University of California found that extremely low concentrations of atrazine
(0.1 ppb or |ig/L) cause hermaphradotism in male leopard frogs in the laboratory. Hayes also
conducted broad field studies across the Great Plains that corroborated the lab results.
Hermaphradotism in leopard frogs was widespread, but only in locations where atrazine was
present. Twenty-nine percent of the frogs exposed to 0.1 ppb of atrazine showed some degree of sex
reversal, whereas none of the frogs in the control group (in which no atrazine present in the water)
showed any sex reversal. Hayes' results show that extremely low concentrations of a pesticide can
disrupt hormonal processes of aquatic life.

Many of the pesticides contained in Oregon's water quality standards are EDCs. Oregon's criteria,
however, were developed using traditional toxicological parameters, omitting any inclusion of the
pollutants' effects on the endocrine system. For example, Oregon's water quality standards do not
address atrazine at all, even though it is one of the most widely used herbicides. For those pollutants
for which Oregon has proposed water quality criteria, Oregon has utterly ignored their endocrine
disrupting effects. Because Oregon's proposed criteria do not consider EDCs, they do not protect
designated uses and EPA should disapprove the standards.

EPA's Response to Comment L:

EPA disagrees with the comment that Oregon's new and revised aquatic life criteria all fail to
protect Oregon's Fish & Aquatic Life beneficial use because certain other criteria, relating to

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endocrine disrupting chemicals (EDCs), were not included in the submission upon which EPA is
acting. Specifically, Oregon did not submit new or revised aquatic life criteria for estradiol,
methoxychlor, nonylphenol, or atrazine. These substances are therefore not being reviewed in this
action. The commenter's contention that Oregon needs to adopt additional criteria (chosen based on
those additional pollutants' effects on the endocrine system) simply does not bear on the question
currently before EPA: whether or not to approve the particular new and revised criteria that Oregon
actually did adopt and submit to EPA's review.

In general, EDCs pose a challenge because of their complex nature and their potential effects on
aquatic life, humans, and wildlife. A major issue that must be addressed for endocrine disruption is
the need to define what constitutes an "adverse effect," especially considering that effects might be
observed from the molecular level to the community level. According to EPA's interim position, the
Agency does not consider endocrine disruption to be an adverse effect per sc\ but rather a mode of
action potentially related to other outcomes, such as carcinogenic, reproductive, or developmental
effects, that are routinely used in making regulatory decisions.37

In 2004, Oregon adopted new aquatic life criteria for tributyltin (TBT) which, in part, acts as an
EDC. TBT is a highly toxic biocide that has been used extensively in anti-fouling paint to protect
the hulls of large ocean-going ships. It is deemed a problem in the aquatic environment because it is
extremely toxic to non-target organisms and has been linked to imposex (i.e., the superimposition of
male anatomical characteristics on females) and to immuno-supression in snails and bivalves (U.S.
EPA 2003) in valid scientific studies. The low effect concentrations established for female
gastropods in the laboratory were subsequently corroborated in field studies. The saltwater CCC
was lowered based on the professional judgment that these effects were relevant for the risks of
TBT to gastropod reproduction.

Comment M: Oregon's Proposed Criteria Do Not Provide Adequate Protections For Endangered
And Threatened Species.

Studies demonstrate that Oregon's proposed criteria jeopardize several threatened and endangered
species. The Services found that the CTR criteria, which are very similar to Oregon's proposed
criteria, jeopardize several threatened and endangered species that occur in Oregon, including bald
eagle, California brown pelican, California least tern, marbled murrelet, western snowy plover, and
several salmonid species. The Services concluded, based on an extensive review of the literature,
that the criteria do not protect physiological needs of the species, mostly due to bioaccumulation. As
with the CTR criteria, Oregon's proposed criteria fail to protect imperiled species.

The criteria do not protect threatened or endangered populations that are inherently stressed due to
low numbers, decreased genetic diversity, reduced geographic range, or health and reproductive
problems. In adopting the EPA recommended criteria, Oregon noted that EPA's criteria arc
intended to protect "at least 95% of the species" because "aquatic ecosystems are tolerant of some
stress". This statement, however, does not begin to address the requirements of threatened and
endangered species. Oregon's threatened and endangered species cannot tolerate any additional
stress. The environmental baseline for these species is, by definition, bordering on extinction. For
example, the stresses on threatened or endangered salmon include habitat loss, dams, competition

37 EPA, 1997. Special Report on Environmental Endocrine Disruption: An Effects Assessment And Analysis. EPA/630/R-
96/012. http://oaspub.epa.gov/eims/eimscomm.getfile?p_download_id=36841

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and disease from hatchery fish, elevated temperature, and decreased dissolved oxygen. Even if the
proposed toxic criteria were accurate and protected species with a healthy population (Oregon's
criteria do not), the assumption that all species can tolerate additional stress is faulty and will result
in adverse effects on threatened and endangered species that are already overstressed.

In addition, criteria designed to protect ninety-five percent of the species present must, by
definition, sacrifice five percent. The ESA proscribes any unauthorized "take" of any listed species.
Therefore, the policy to protect ninety-five percent of the species is contrary to the ESA unless the
agency can demonstrate that the sacrificed five percent does not contain any listed species. This is
unlikely, however, because many threatened and endangered species, such as salmonids and the
California tern, are more likely than other species to be adversely affected by bioaccumulative toxic
pollutants because they eat at high trophic levels.

Listed species that use aquatic habitats or prey are in peril because the regulatory system is not
working to protect them. For example, chemicals such as atrazine are not regulated to protect
against detrimental impacts from their effects on aquatic and wildlife species, including threatened
and endangered species. It is unrealistic to design water quality standards to sacrifice five percent of
species, and then assume that none of the five percent sacrificed are threatened or endangered.
Oregon's criteria will cause further harm to already imperiled species and thus do not protect
designated uses that are also listed as threatened and endangered species.

EPA's Response to Comment M:

See General Response 4 concerning ESA listed species and General Response 5 concerning
wildlife. Specifics covering the percentile protections are addressed directly in the response to
Comment F.

Comment N: Oregon's Proposed Criteria Do Not Contain Wildlife Criteria And Thus Do Not
Protect All Designated Uses.

EPA rules require states to protect wildlife as a designated use. When classifying designated uses, a
state must consider "protection and propagation of fish, shellfish and wildlife." EPA's Water
Quality Standards Handbook provides, "[sjtates must provide water quality for the protection and
propagation offish, shellfish, and wildlife, and provide for recreation in and on the water where
attainable." The Handbook further provides, "[wjildlife protection should include waterfowl, shore
birds, and other water emigrated wildlife." As required by federal rule, wildlife is a designated use
in Oregon. Oregon's proposed water quality criteria, therefore, must protect the designated use of
wildlife.

Oregon's proposed criteria do not, however, protect wildlife. Oregon proposes to adopt EPA's
recommended criteria, which scientists have condemned as not protective of wildlife. (See, e.g.,
infra, for criticism of selenium, mercury, PCP, and cadmium criteria.) Oregon's proposed standards
contain criteria to protect only aquatic life and human health. The standards do not contemplate
aquatic-dependent wildlife, such as shorebirds, bald eagles, mink, and otter. Rather than establish
wildlife criteria, Oregon relies on chronic aquatic life criteria to serve as a proxy for wildlife-
specific criteria. However, aquatic criteria do not serve as an adequate proxy for wildlife-specific
criteria, as the chart below shows. This chart compares Oregon's proposed chronic aquatic life
criteria with the criteria developed by EPA to protect wildlife for in the Great Lakes Initiative

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(GLI). It makes clear that the GLI criteria are at least an order of magnitude more protective than
Oregon's proposed criteria.

Pollutant

GLI

Oregon Chronic Aquatic
Life

DDT

0.000011 |ig/L

0.001 |ig/L

Mercury

0.0013 |ig/L

0.012 |ig/L

PCBs

0.00012 |ig/L

0.014 |ig/L

2,3,7,8 TCDD

0.0000000031 |ig/L

None

Similarly, New Jersey's water quality standards for toxic pollutants demonstrate not only that states
and EPA are able to develop criteria for wildlife but that EPA has, in other states, made a
commitment to do so because toxic criteria for the protection of human health and aquatic life are
not sufficient to protect designated uses. In 2001, New Jersey completed an analysis on which to
base its criteria for the protection of wildlife for DDT and its metabolites, mercury, and PCBs. The
state and federal agencies involved used the same test doses, uncertainty factors, water and food
consumption rates, animal weights, and equation for deriving wildlife values as the Great Lakes
Water Quality Initiative. Proposed in 2002, values derived for Peregrine falcon were used to
establish the regulatory criteria because, of the species evaluated, falcon's consumption of
piscivorous birds, rather than fish, placed it at the highest risk. The proposed values were as
follows: 0.000004 for DDT and its metabolites; 0.00053 for mercury; and 0.000072 for PCBs |ig/L
(ppb). In addition, New Jersey prohibited mixing zones for new discharges of bioaccumulative
chemicals of concern with a bioaccumulation factor of greater than 1000 L/kg based on the need to
protect beneficial uses from bioaccumulative pollutants.

Moreover, the Services, in the CTR BiOp, have already concluded the 0.3 ug/g human health tissue
residue concentration (TRC) criterion for mercury does not protect several threatened or endangered
species present in Oregon. These examples demonstrate that Oregon's aquatic life criteria do not
protect wildlife. EPA must disapprove any criteria that do not protect wildlife and either direct
Oregon to establish protective criteria or use its own authority to establish criteria protective of
wildlife.

EPA's Response to Comment N:

See General Response 4 concerning ESA listed species and General Response 5 concerning
wildlife.

Comment O: EPA Must Review And Disapprove Any Unidentified, Substantive Revisions That
Oregon Made To Its Toxic Narrative Criteria

Oregon submitted new water quality standards to EPA on December 10, 2003. Most of the changes
regarded temperature, but there were also changes to the toxic narrative standards. EPA approved
these changes on March 2, 2004 without review. CWA section 303(c)(3) requires that the EPA
determine whether the revised or new standard submitted by the state meets the requirements of the
chapter. EPA overlooked the substantive changes to the revised standards, and, as a result, failed to
determine if the standards met the requirements of the chapter pursuant to section 303(c)(3). In
addition, EPA's approval of Oregon's standard is arbitrary and capricious under section 706 of the
Administrative Procedure Act because EPA approved Oregon's standards without considering these
substantive changes.

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EPA's Support Document states that the changes to Oregon's toxic standards are "non-substantive
editorial changes or corrections that do not alter the substance of the water quality standards that
EPA has previously approved." This statement is incorrect. DEQ substantively changed its rules
regarding toxic pollutants. DEQ changed the substantive requirements of its toxic standards by
replacing imperative terms, such as "shall," with permissive terms, such as "may." DEQ's previous
standards on toxic pollutants are ordained in OAR 340-041-0205(A), which provides, "[t]oxic
substances shall not be introduced above natural background levels . . " The new rule, OAR 340-
041-0033(1), changes "shall not" to "may not." In addition, OAR 340-041-0033(2) also, changes
"shall not" to "may not." These are substantive changes because "shall" indicates a mandatory term
whereas "may" is generally permissive. While "may not" could be seen as a prescriptive term, it
also could convey an element of discretion that did not exist in the previous rules. Since Oregon did
not identify the reason for these changes and did not indicate the meaning that it intends for "may
not" to now have, EPA must assume that the changes from "shall not" to "may not" were deliberate
and substantive changes. Therefore, the old narrative criteria prohibited toxic substances above
background levels whereas the new narrative criteria do not. No antidegradation review was
conducted on this change.

Another rule changes "shall" to "will." "Shall" provides a mandatory duty, whereas "will" may
indicate a future intent that is not a legally binding commitment enforceable under the APA. The
old rule provides, "[i]f toxicity occurs, the Department shall evaluate and implement necessary
measures to reduce toxicity on a case-by-case basis." The new rule provides, "[i]f toxicity occurs,
the Department will evaluate and implement necessary measures to reduce toxicity on a case-by-
case basis". By changing the language of the rules, particularly without providing any explanation
for the changes, DEQ must be assumed to have substantively altered the meaning of the rules. EPA
must therefore review the revised toxic standards pursuant to 33 U.S.C. § 1313(c)(3).

DEQ also revised OAR 340-041-0205(D), an important provision that requires the Department to
conduct bioassessment studies once the Department deems the studies necessary. The old rule
provided:

Bioassessment studies such as laboratory bioassays or instream measurements of indigenous
biological communities, shall be conducted, as the Department deems necessary, to monitor the
toxicity of complex effluents, other suspected discharges or chemical substances without
numeric criteria, to aquatic life. These studies, properly conducted in accordance with standard
testing procedures, may be considered scientifically valid data for, the purposes of paragraph
(c) of this subsection. If toxicity occurs, the Department shall evaluate and implement measures
necessary to reduce toxicity on a case-by-case basis.

The old rule required that a bioassessment be conducted if the Department deems it necessary. The
old rule, therefore, provides both a discretionary duty and a nondiscretionary duty. It gives the
Department the discretion to deem a study necessary. Once the Department deems, that a study is
necessary, the performance of the study is nondiscretionary (the "study shall be conducted").

In contrast, the new rule provides:

If the Department determines that it is necessary to monitor the toxicity of complex effluents,
other suspected discharges or chemical substances without numeric criteria to aquatic life, then
bio-assessment studies may be conducted. Laboratory bioassays or in-stream measurements of
indigenous biological communities, properly conducted in accordance with standards testing
procedures, may be considered as scientifically valid data for the purposes of section (3) of this
rule. If toxicity occurs, the Department will evaluate and implement necessary measures to

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reduce or eliminate the toxicity on a case-by-case basis.

The new rule states even if the Department satisfies the prerequisite and deems a study necessary,
the Department retains discretion to forego the study ("may be conducted").

The new rule substantively differs from the old rule. First, the new rule requires the Department to
deem a study necessary for one of the three listed purposes, whereas the old rule grants the
Department discretion to conduct a study "as [it] deems necessary." The new rule, therefore, limits
the Department's discretion to conduct important bioassessment studies and may require the
Department to make an affirmative finding of necessity for each study it wishes to conduct. Second,
the statement in the new rule that "bioassessment studies may be conducted" gives the Department
full discretion to refuse to conduct a bioassessment even if the study is deemed necessary. The old
rule ("shall be conducted") provides a nondiscretionary duty to conduct a study when the
Department deemed a study necessary. The new rule removes this duty.

EPA failed to identify any of DEQ's substantive changes discussed above as requiring EPA review.
NWEA informed EPA that DEQ substantively changed its rules without notifying the public or
EPA. NWEA specifically pointed out changes of "shall" to "may" in a letter to EPA and comments
forwarded to EPA. Inexplicably, however, in the EPA support document for approval of the rule,
EPA stated, "[a]ll underlined text indicates the actual change or revision to the rule unless otherwise
noted." The only underlined text in this section is the editorial change from "paragraph" to
"section" and "subsection" to "rule." DEQ underlined these same two changes in its submission to
EPA. Apparently, EPA relied on DEQ's misrepresentation that the changes it made to the narrative
criterion for toxics were simply editorial. However, as explained above, DEQ altered much more
than either DEQ or EPA identified. Because the new rule is subject to a different interpretation from
the old rule, EPA must consider the effects that these revisions will have on Oregon's water quality
standards.

DEQ's revisions of OAR 340-041-0033(1) and (4) weaken the narrative criteria. The narrative
criteria in OAR 340-041-033(1) and (4) are meant to fill the gaps left by inadequate numeric
standards. Subsection (1) provides the general narrative statement that "[t]oxic substances may not
be introduced above background levels... in amounts, concentrations, or combinations that may be
harmful..." Subsection 4 authorizes DEQ to conduct bioassessment studies to evaluate whether the
standards are protecting aquatic life and to implement protective measures if toxicity occurs. EPA
and DEQ recognize the importance of bioassessments for protection of aquatic life. This importance
is undermined by these unidentified changes.

Oregon's narrative criteria assume added importance because the state's numeric criteria are less
stringent than EPA requirements (which themselves are not adequately protective) for some toxic
pollutants. EPA is well aware of the essential gap-filling nature of the narrative criteria. Indeed, in
reviewing the CTR, EPA noted that it could justify the proposed numeric criteria only because the
narrative criteria would be heavily used to fill in the gaps left by the inadequate numeric criteria.
Due to the vital role of Oregon's narrative criteria, EPA must scrutinize any changes made to the
criteria.

EPA's failure to review Oregon's revised water quality standards for toxic pollutants is a violation
of CWA section 303(c)(3).

EPA's Response to Comment O:

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EPA provided its response to each of the issues raised in Comment O in its February 8, 2005 letter
to Holly Schroeder, Oregon Department of Environmental Quality (Re: Provisions in Oregon's
water quality standards submission that EPA did not act on.)

Comment P: Oregon's Proposed Criteria Do Not Protect Designated Uses Because Oregon's Water
Quality Standards Lack A Narrative Implementation Methodology.

EPA's Response to Comment P:

EPA responded to Comment P in its June 1, 2010 Supplemental Response to Comment Submitted by
Northwest Environmental Advocates [NWEA} as They Pertain to Oregon's New and Revised
Human Health Water Quality Criteria for Toxics Submitted on July 8, 2004. For the full comment
and EPA's response, please see pages 19-21 of the referenced document.

SECTION V. SPECIFIC POLLUTANT CONCERNS

A. Selenium

1. Oregon's proposed selenium criterion does not protect designated uses.

There is widespread scientific agreement that Oregon's proposed freshwater chronic criterion
for selenium, 5 |ig/L, does not protect designated uses because selenium is strongly
bioaccumulative. The Services stated, "nearly every major review of experimental and field
data conducted over the past decade has concluded that a chronic criterion of 5 |ig/L is not fully
protective of fish and wildlife resources." EPA's public notice of this recommended criterion
stated that the chronic criterion of 5 |ig/L, for selenium continues to be scientifically valid and
protective of aquatic life. This is not so. As the Services stated, "In the aggregate, the weight of
scientific evidence supporting a chronic criterion for selenium of <2 |ig/L is now
overwhelming."

In addition, Oregon's proposed freshwater aquatic life acute criterion for selenium does not
protect designated uses because selenium bioaccumulates quickly and affects designated uses at
concentrations below the proposed criterion. Oregon adopted the EPA recommended criterion,
which is a speciation-weighted criterion based on the relative concentrations of selenite,
selenate, and all other forms of selenium found in a water body. Based on the formula, the
range of potential criteria is 12.8 (if one hundred percent selenate) to 185.9 (if one hundred
percent selenite). The Services determined that "the promulgation of the proposed speciation
weighted acute criterion for selenium in the CTR would not afford adequate protection to listed
species." Selenium bioaccumulates rapidly in aquatic organisms and a single pulse of selenium
(>10 |ig/L) into aquatic ecosystems could have lasting effects, including elevated selenium
concentrations in aquatic food webs. In addition, Oregon's speciation-weighted criterion
assumes that selenate is more toxic than selenite, an assumption that runs opposite of the
findings of most studies.

The Services stated that the EPA recommended acute criterion "may fail to adequately protect
aquatic dependent fish and wildlife." because of the pulse-effect hypothesis. This was
demonstrated by a study that evaluated a pulse of 23 |ig/L selenium discharged into a wetland

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that usually had a selenium concentration of 2 to 3 |ig/L. Three months after the pulse, and
without any additional selenium pulses, twelve percent of avian eggs sampled at the site
contained greater than 6 |ig/L selenium, a level that exceeds the exbryotoxic risk threshold. The
pulse of 23 |ig/L selenium, which was well within the EPA recommended acute criterion,
created an unacceptable level of risk. The rapid uptake of this selenium pulse and the resultant
toxic effects demonstrate the need for a much lower acute criterion.

2. The proposed selenium criterion does not account for bioaccumulation and
harm caused by other stressors.

The proposed selenium criterion does not protect aquatic life and wildlife because selenium
bioaccumulates in aquatic organisms. Bioaccumulation results in a marked elevation of
residues in food-chain organisms as compared to waterborne concentrations. Therefore,
relatively low concentrations of selenium in the water can result in dangerous concentrations of
selenium in organisms. For example, laboratory studies show that organoselenium compounds
can be bioconcentrated over 200,000 times by zooplankton when water concentrations are 0.5
to 0.8 |ig/L, which is well under the Oregon proposed criteria of 5 |ig/L. The selenium
concentrations in the zooplankton of these were 100 jug/g, much higher than the dietary toxicity
threshold for fish (0.3 |ig/g).These results demonstrate that water concentrations of selenium
that are permissible under Oregon's proposed criteria result in extremely high tissue
concentrations in aquatic life.

Field studies similarly demonstrate selenium bioaccumulation factors of 500 to 35,000 in
contaminated aquatic habitats where the water concentration of selenium ranged from 2 to 16
|ig/L. Based on waters containing 1-5 |ig/L of total selenium, composite bioaccumulation
factors for aquatic food-chain items are typically between 1,000 and 10,000. Oregon's
proposed chronic criterion of 5 |ig/L, therefore, permits bioaccumulation factors of 1,000-
10,000.

Because selenium is highly bioaccumulative, the majority of scientists recommend a chronic
aquatic life criterion much lower than Oregon's proposed 5 |ig/L criterion. Lemly stated,

"based on risk from bioaccumulative dietary toxicity, a generic aquatic life criterion in the
range 0.2 to 2 would be justified." Lillebo concluded that a chronic criterion of 0.9 |ig/L for
total selenium is required to protect fish. Person and Nebeker stated that 1 |ig/L for wildlife is
warranted. Each of these recommendations is significantly lower than the 5 |ig/L chronic
criterion proposed by Oregon. In addition, Lemly synthesized the scientific literature on
selenium and concluded that a chronic criterion greater than 2 |ig/L will cause food chain
bioaccumulation and reproductive failure in fish and piscivorous birds. In sum, Oregon's new
criterion of 5 |ig/L is much less protective than the recommendations from USFWS and
academia. It is abundantly clear that Oregon's proposed 5 |ig/L criterion, therefore, does not
protect beneficial uses.

In addition, Oregon's proposed criterion does not protect aquatic life because natural stressors
reduce an organism's ability to survive toxic contamination. The purified laboratory tests, upon
which EPA and Oregon based the criterion, do not account for stressors. Any metabolic stressor
- including winter stress syndrome, migration, smoltification, and pathogen challenges - may
lower the toxicity threshold. Albers et al. concluded that the dietary toxicity threshold in the
presence of winter stress was only half the threshold level for selenium as a solitary stressor.
Accordingly, criteria based on single stressor data should be reduced by at least a factor of two.

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Furthermore, the Services provide additional reasons why Oregon's proposed selenium chronic
criterion of 5 |ig/L does not protect designated uses. First, EPA's criterion of 5 |ig/L is based,
in part, on inaccurate or misinterpreted field data from Belews Lake, North Carolina. EPA
claimed that aquatic life in the lake was unaffected at 5 |ig/L. Dr. Lemly reexamined the lake
and found multiple lines of evidence that indicated adverse effects of selenium on fish in the
lake at concentrations of 0.2 - 4 |ig/L. Second, wildlife exposed to elevated levels of selenium
are more susceptible to pathogens. Third, Oregon's criterion does not address the effects of
chemical synergism. Other contaminants act as stressors that make wildlife vulnerable to lower
levels of selenium. The Services cite a study of ninety-eight Swedish lakes that concluded that
1-2 |ig/L was the maximum safe criterion. Another study upon which the Services depended in
the CTR BiOp cites very strong synergistic effects between dietary organo-selenium and
organo-mercury with regard to reproductive impairment of mallards.

In 2000, the Services issued a draft jeopardy opinion for the CTR because the 5 |ig/L selenium
criterion would jeopardize fifteen ESA-listed species. Four years later Oregon has submitted
the same unprotective criterion to EPA. In those four years, scientists have further
demonstrated that 5 |ig/L is not protective of fish and birds due to selenium's highly
bioaccumulative properties. Therefore, EPA must disapprove Oregon's selenium criterion. In
fact, this criterion should be based on a tissue residue criterion that is protective of threatened
or endangered salmonids and aquatic-dependent wildlife. The Services took this position in the
CTRBiOp:

There is a strong need for developing a method to link criteria directly to food chain
contamination. In the absence of site-specific and species-specific data regarding the
sensitivity of particular species and for threatened and endangered species of fish and
wildlife, a general criterion of at least 2 |ig/L is required to assure adequate protection of
threatened and endangered fish and wildlife. This is especially warranted considering the
well-demonstrated potential for selenium facilitated pathogen susceptibility that can
rapidly extirpate entire populations of fish and wildlife via epizootic events.

3. Field data from Belews Lake show that Oregon's proposed selenium criterion will not protect
designated uses.

The Belews Lake, North Carolina selenium poisoning serves as an important case study to
demonstrate the hazards of selenium bioaccumulation. During ten years of heavy
contamination, the average selenium concentration in Belews Lake was 10 |ig/L. At this
concentration, selenium accumulated 514 to nearly 4000 times in the biota. As a result,
nineteen of the twenty fish species were rendered sterile and extirpated. It is interesting to note
that one of the worst selenium poisonings in the history of the United States occurred at 10
|ig/L, a level that is only twice Oregon's proposed criterion.

Prior to extirpation, fish in Belews Lake had damaged gills, blood, liver, kidneys, heart ovaries,
and eyes. The most insidious aspect of selenium poisoning occurred in the eggs, which received
selenium from their mother's diet and stored the toxin until hatching. This poisoning was
invisible because adult fish can survive and appear healthy despite the fact that massive
reproductive failure is occurring. A wealth of studies show that these insidious effects occur at
selenium water concentration levels below the 5 |ig/L criterion proposed by Oregon.

The extreme, yet invisible, nature of selenium poisoning requires Oregon to exercise caution in

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order to protect designated uses. Lemly stated, "once selenium contamination begins, a
cascade of events is set into motion that can result in major ecosystem disruption. Early
detection and action is key. Environmentally sound hazard assessment and water quality goals,
coupled with prudent risk management, can prevent significant biological impacts." Contrary to
this warning, Oregon's chronic criterion, which is significantly higher than what scientists
consider safe, will result in major ecosystem disruption.

4. The proposed selenium criterion fails to protect threatened and endangered species.

Oregon's selenium criterion does not protect threatened or endangered species, as demonstrated
by the examples presented below.

Bald Eagle:

Oregon's proposed selenium chronic criterion of 5 |ig/L does not protect the bald
eagle. Lillebo et al. demonstrated that 1.4 |ig/L is necessary to protect piscivorous
birds. This is greater than three times more protective than Oregon's proposed
standards. Likewise, Peterson and Nebeker calculated a chronic criterion specific to
bald eagles at 1.9 |ig/L. The Services concluded that "widespread expansion of aquatic
habitats containing >1.9 |ig/L selenium, as could occur with a criterion of 5 |ig/L,
could put substantial numbers of California's bald eagles at risk of toxic effects of
selenium. The Services' concerns regarding eagles apply equally in Oregon.

Therefore, Oregon's proposed criterion jeopardizes the threatened bald eagle.

Brown Pelican:

Oregon's proposed selenium chronic criterion does not protect the brown pelican. The
Services concluded that a criterion on the order of 1.4 |ig/L is needed to protect the
brown pelican from selenium poisoning. The Services suggest that a very unusual and
large case of botulism that killed more than 1400 brown pelicans may have resulted
from elevated selenium level in fish tissue, which left the fish immune-impaired and
hypersensitive to the bacterial attacks that facilitated the botulism outbreak. The
Services recommendation of 1.4 |ig/L applies equally to Oregon's brown pelicans.

California Least Tern:

Oregon's proposed selenium chronic criterion does not protect the California least
tern. Terns, like bald eagles and pelicans, are piscivorous. Since there are no data
specific to the California least tern, the Services determined that the studies related to
piscivorous birds applied to the tern. Oregon's 5 |ig/L criterion, therefore, is up to
three times less protective than necessary to support this piscivorus bird. In addition,
results from interior least tern studies suggest that California least tern eggs would
"substantially exceed the 6 ug/g threshold for embryotoxicity established for black
necked stilts if selenium concentrations were permitted to rise to 5 |ig/L water
concentration. In combination with elevated mercury concentrations already noted for
eggs of California least terns, significant reproductive impairment would be the
expected outcome."

Marbled Murrelet:

Oregon's proposed chronic selenium criterion does not protect marbled murrelets.
Marbled murrelets feed in Oregon's bays and estuaries on small fish and shrimp. As a
piscivorous bird, the 1.4 to 1.9 |ig/L threshold also applies to murrelets. The Services
concluded, "5 |ig/L must be viewed as unprotective of marbled murrelets foraging in
enclosed bays and estuaries in the State of California." This statement applies to
Oregon's murrelets because they have the same physiological needs as murrelets in
California.

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Salmonids:

Oregon's proposed selenium chronic criterion does not protect salmonids. The
agencies concluded that the most dangerous exposure pathway for salmonids is to
obtain selenium via dietary bioaccumulation. After citing numerous studies that refute
the alleged protectiveness of the 5 |ig/L criterion, the Services concluded that
"currently available data for salmonids do not support the CTR proposed selenium
criterion of 5 |ig/L as adequately protective of salmonids." The agencies were
referring to salmonid species present in Oregon as well as California, including the
Southern Oregon/Northern California Coast ESU, Chinook salmon, steelhead, and
Lahontan cutthroat trout. The Services concluded that "a criterion of 2 |ig/L or less
would be necessary for protection of these species, that the proposed speciation based
acute criterion should not be promulgated and that a selenium criteria revision that
considered the bioaccumulative nature and long term persistence of selenium in
aquatic sediments and food chains was necessary.

In sum, the Services concluded that the selenium criterion in the CTR BiOp does not protect each of
the endangered species above. This is directly relevant to Oregon because Oregon's proposed
criterion is identical to the CTR criterion roundly criticized by the Services and scientists.

Moreover, many of the species identified in the CTR BiOp are also found in Oregon. EPA must
reject Oregon's attempt to use this discredited criterion.

EPA's response to specific pollutant concerns regarding selenium

While EPA does not necessarily agree with all of the commenter's intermediate contentions regarding
the appropriate evaluation these criteria, the Agency agrees with the commenter's ultimate conclusion:
that the submitted criteria for selenium are not protective of Oregon's designated aquatic life use. EPA
has detailed its reasons for reaching this conclusion in the Technical Support Document associated with
this action.

B. Mercury

Oregon's proposed criterion for mercury is similarly flawed. Oregon has proposed to adopt an acute
criterion that exceeds EPA's recommended criterion, in direct contravention of the CWA. The
proposed criterion will not protect designated uses and must be disapproved.

1. Oregon failed to adopt a criterion at least as stringent as EPA's recommended criterion.

Oregon's proposed acute criterion for mercury of 2.4 |ig/L violates section 303(c)(2)(B) of the
CWA because Oregon's criterion is higher than the EPA recommended criterion of 1.4 |ig/L.
Section 303(c)(2)(B) provides that a state shall adopt the EPA recommended criteria for toxic
pollutants during each triennial review. EPA must disapprove Oregon's acute mercury criterion
because Oregon did not adopt the EPA recommended value.

Oregon's rationale for not following the requirements of the Clean CWA is not a legitimate
justification for allowing Oregon to avoid the requirements of federal law. In attempting to
justify its failure to adopt EPA's recommended criterion, Oregon stated:

DEQ believes that maintaining the current Oregon aquatic life criteria for mercury [2.4

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|ig/L] is prudent because of concerns existing in Oregon over mercury and the protection
of threatened and endangered salmonids. These criteria were "reserved" (i.e. withdrawn)
from the CTR because of the Services' objections to suspected adverse impact of the
proposed EPA criteria on Threatened and Endangered salmonids. Since Oregon has the
same species as those identified in the BO to the California Toxics Rule, DEQ believes this
is the most prudent action until such time that the mercury criteria can he reviewed in
depth.

This justification, however, is nonsensical. The Services criticized EPA's proposed criterion
because of concerns that the 1.4 |ig/L criterion would not provide adequate protection for
designated uses. No rational decision maker would conclude that Oregon's proposed criterion,
which is 1 |ig/L higher - and thus less protective - than the disputed EPA criterion, would
satisfy the state's obligation to adopt criteria that are protective of designated uses. Oregon's
failure to adopt EPA's recommended criterion, at a minimum, or a more stringent criterion,
plainly violates the requirements of section 303(c)(2)(B).

2. Oregon's proposed criterion for mercury does not protect designated uses.

Oregon's proposed acute criterion of 2.4 |ig/L also violates 40 C.F.R. § 131.11 because it does
not protect designated uses. Mercury is highly toxic, it bioaccumulates, and it biomagnifies.
Oregon failed to consider any of these facts when it proposed a criterion that is less protective
than the 1.4 |ig/L acute criterion rejected by the Services.

In their review of EPA's proposed criteria for mercury, the Services stated:

the aquatic life mercury criteria of [.770 (chronic) and 1.4 (acute)] are so high as to
effectively be without value for controlling mercury in even the most severely mercury-
impaired California water bodies. Concentrations above the CCC in the dissolved form are
virtually unmeasured in the California environment, even though those environments
contain numerous water bodies with direct mercury discharges.

The Services thus rejected EPA's proposed criterion of 1.4 |ig/L, because it would have no
beneficial effect. It necessarily follows that Oregon's proposed acute criterion of 2.4 |ig/L
certainly does not protect designated uses.

In addition, Oregon's proposed acute criterion of 2.4 |ig/L is significantly higher than the
mercury criterion recommended by the Mercury Report to Congress as necessary to protect
wildlife. In that report, EPA recommended a 0.05|ig/L methylmercury criterion and a
0.641 |ig/L "total dissolved" mercury criterion. Both of these recommendations clearly fall
below Oregon's outrageous 2.4 |ig/L proposal.

3. Oregon's tissue residue concentration of 0.3 mg/kg does not protect wildlife.

Oregon has also proposed a tissue residue concentration (TRC) criterion of 0.3 mg/kg for
mercury. However, this criterion will not protect wildlife and must therefore be rejected. Water
quality criteria must protect the most sensitive designated use, including wildlife. Oregon's
proposed TRC criterion was meant to protect human health, and was never established to
protect more sensitive wildlife uses.

During the consultation process for the CTR, EPA requested that USFWS determine if the TRC

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of 0.3 mg/kg would affect federally listed species in California. The Services created a risk
assessment methodology to assess the protectiveness of the criterion for threatened and
endangered wildlife using two different methodologies to create a more protective Highest
Trophic Level (HTL) and a less protective Average Trophic Level (ATL) approach. The
USFWS found that applying the TRC criterion with the estimated trophic level methylmercury
concentrations under the less protective ATL approach may be sufficiently protective for only
two of the seven species considered: the southern sea otter and Western snowy plover. It
concluded that the five other species examined (California least tern; bald eagle; California,
light-footed, and Yuma clapper rails) would likely have dietary exposures under this approach
that would place them at risk for adverse effects from methylmercury toxicity. Applying the
TRC under the more protective HTL approach yielded sufficient protection for four of the
seven species considered: the southern sea otter, California clapper rail, Western snowy plover,
and bald eagle. Two remaining species examined (California least tern and Yuma clapper rail)
would likely have dietary exposures under this approach that would place them at risk for
adverse effects from methylmercury toxicity.

Thus, the USFWS found that not all designated uses of wildlife are protected by the 0.3 mg/kg
TRC criterion even using the more protective approach. The California least tern, which is
found in Oregon and is listed as endangered under both the federal and state ESAs, would
likely have adverse effects from methylmercury toxicity under the TRC of 0.3 mg/kg. This
evaluation demonstrates that Oregon's proposed TRC of 0.3 mg/kg is not protective of wildlife
in violation of EPA regulations.

Further support that Oregon's 0.3 mg/kg TRC criterion for mercury does not protect wildlife
comes from the Services' comments on the Clear Lake TMDL in California. The Services
concluded that the proposed methylmercury concentrations of 0.13 and 0.30 mg/kg of wet
weight fish tissue for trophic levels three and four, respectively, are not sufficient to protect
wildlife resources at Clear Lake. The Services instead recommended criteria of 0.09 mg/kg and
0.19 mg/kg to protect wildlife. The Services' recommendation indicates that Oregon's
proposed criterion for mercury does not protect wildlife.

There is no support for Oregon's 0.3mg/kg TRC criterion. EPA must therefore disapprove
Oregon's recommended criterion and replace it with a criterion that will at long last protect
beneficial uses.

EPA's response to specific pollutant concerns regarding mercury

While the commenter characterizes Oregon's aquatic life criteria for mercury as "proposed," (apparently
on the grounds that Oregon stated reasons for not revising those criteria),38 a statement of reasons for not
altering a previously-adopted regulatory provision cannot be reasonably equated with a proposal to
adopt that provision in the first place. Oregon made clear that it was "not proposing to change aquatic
life criteria for mercury."39

EPA only reviews new or revised water quality standards under CWA § 303(c)(3). The aquatic life
criteria for mercury that are being commented upon here are neither new nor revised. Because there are

38 DEQ Issue Paper at H-65 (2004).

39 Summary of Public Comments and Agency Responses at B-17 (Attachment B to Agenda Item at the May 20-21, 2004
meeting of the Oregon Environmental Quality Commission).

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no new or revised aquatic life criteria for mercury for EPA to review in this action, these comments are
not pertinent to EPA's CWA § 303(c)(3) action.

Oregon's revised human health criteria for mercury have already been separately addressed.40

C. Ammonia

Oregon's proposed criterion for ammonia does not protect designated uses because the criterion was
developed with tests on fish resting in stagnant water. Tests in moving water indicate that exercising
fish are much more sensitive to ammonia. Fish excrete ammonia while exercising to regulate the
ammonia in their system. Ammonia concentrations that are above a waterbody's natural level
adversely affect the ammonia regulatory system of fish. Oregon's criterion is not protective of fish
because the criterion was developed using tests in static water, thus ignoring the importance of
exercise sensitivity.

Wicks et al. demonstrated that the Oregon proposed criterion does not protect salmonids because
even small doses of ammonia (0.04 mg/L) decrease coho swimming velocity. Comparing, the
results of these studies with the EPA recommended criteria for ammonia, Wicks concluded, "the
levels set forth by the US EPA will not protect swimming fish and may endanger annual migrations
of anadromous fishes."

Oregon's proposed criterion mirrors EPA's inadequate recommended criterion for ammonia. The
criterion will not protect beneficial uses, and EPA must disapprove it.

EPA's response to specific pollutant concerns regarding ammonia

EPA agrees that Oregon's 2004 submitted aquatic life criteria for ammonia do not protect Oregon's
Fish & Aquatic Life designated use based on currently available information. While EPA does not
necessarily agree with all of the commenter's intermediate contentions regarding the appropriate
evaluation these criteria, the Agency agrees with the commenter's ultimate conclusion: that the
submitted criteria for ammonia are not protective of Oregon's designated aquatic life uses. EPA has
detailed its reasons for reaching this conclusion in the Technical Support Document associated with
this action.

EPA published a draft criteria update in December 2009 and is poised to release final recommended
aquatic life criteria for ammonia that take into account new data since the 1999 criteria update.
Specifically, the new ammonia criterion includes acute data for sensitive species of freshwater
mussels, resulting in an adjustment to the 304(a) criteria.

D. Cadmium

Research indicates that Oregon's proposed cadmium criteria do not protect designated uses. EPA's
recommended criteria for cadmium are based on a hardness-dependent formula. At a hardness of
100 mg/L, the freshwater acute criterion is 2 |ig/L and the freshwater chronic criterion is 0.25 |ig/L.
Oregon's proposed standards adopt the EPA recommended criteria. The proposed criteria are

40 See EPA's letter to Neil Mullane, Oregon Department of Environmental Quality from Michael Bussell, EPA; October
17,2011; Re: Approval of New and Revised Human Health Water Quality Criteria for Toxics and Implementation Provisions
in Oregon's Water Quality Standards Submitted on July 12 and 21, 2011.

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significantly higher than the values recommended by the Services for the protection of threatened
and endangered species. The Services stated, "it appears that a [chronic] criterion for cadmium that
would be protective of salmonids and stickleback is somewhere between 0.096 and 0.180 |ig/L, but
probably would still not protect cladocerans." Oregon's proposed concentration of 0.25 |ig/L is
considerably less protective than even the high end of this recommendation.

Oregon's proposed cadmium criteria also do not protect rainbow trout (and more sensitive species)
because cadmium bioaccumulates in aquatic organisms at concentrations below Oregon's proposed
criteria. McGeer et al. demonstrated that bioaccumulation of cadmium occurs in rainbow trout
continuously because cadmium is not regulated by the trout. In addition, some aquatic invertebrates
are sensitive to an increased concentration of particulate cadmium in the water column. Canfield et
al. showed that some aquatic invertebrate communities change to more pollution tolerant species at
higher levels of cadmium. This reduces the biomass, which likely limits food availability for
predators, thereby affecting their survival.

These examples demonstrate demonstrates that Oregon's criteria do not protect the most
sensitive use in violation of 40 C.F.R. § 131.11 and that Oregon's proposed criterion would not
satisfy the 'no jeopardy' requirement of consultation under section 7 of the ESA. Therefore, EPA
cannot approve Oregon's proposed criteria for cadmium.

EPA's response to specific pollutant concerns regarding cadmium

EPA notes that the August 14, 2012 Biological Opinion of the National Marine Fisheries Service
(NMFS) and the July 30, 2012 Biological Opinion of the U.S. Fish and Wildlife Service (FWS)
supersede the commenter's reliance on the California Toxics Rule Biological Opinion (apparently
as a surrogate for the Services' views on this action).

Significantly, neither NMFS nor FWS were of the opinion that Oregon's revised chronic criterion
for cadmium would jeopardize any listed species in Oregon's waters.

With respect to Oregon's revised acute criterion for cadmium (2 ug/L), EPA acknowledges that
NMFS is of the opinion that certain ESA-listed species may be jeopardized by acute exposure to
cadmium at the revised criterion concentration. For the reasons described in decision document for
this action, EPA is disapproving the revised acute aquatic life criterion for cadmium. However, EPA
does not thereby assume the validity of the commenter's general contentions with respect to the
acute aquatic life criteria for cadmium.

In regards to the specific references brought forward by the commenter, EPA would like to address
specific scientific concerns. First, although McGreer et al. (2000) demonstrated uptake of cadmium
by rainbow trout, uptake by itself is not an adverse effect; it is necessary to demonstrate that
unacceptable adverse effects are caused by exposure (see response to comment H). The last
sentence in the abstract of McGreer et al. (2000) says "While the initial patterns of accumulation for
each metal were generally consistent with the damage, repair and accumulation pattern from
concurrent physiological measurements it was clear that tissue metal accumulation was not a good
indicator of either exposure [or] physiological impact." The EPA cannot ascribe specific
physiologic effects with any specific compound of concern from this study.

Canfield et al. (1994) found that metal-contaminated sediment affected benthic invertebrate
community structure. However, the sediment was contaminated by arsenic, cadmium, copper, lead,
manganese, and zinc and therefore this study does not provide information regarding cadmium as a

-------
contributor to water column based toxicity.

See General Response 4 concerning ESA listed species.

E. Pentachlorophenol

Oregon's proposed acute and chronic criteria for pentachlorophenol (PCP) also do not protect
salmonids. Oregon's PCP criterion is pH-dependent. At a pH of 7.8, the acute and chronic criteria
are 19 |ig/L and 15 |ig/L, respectively. The Services evaluated the protectiveness of these criteria on
threatened and endangered species in the CTR BiOp. The Services concluded that "the proposed
acute and chronic water quality criteria for PCP arc not protective of endangered and threatened
fish. Current literature indicates adverse effects of... PCP on reproduction, early life stage growth,
or behavior of salmonid species at concentrations at or below the proposed criteria."

Research demonstrates that Oregon's acute criterion for PCP is not protective of the most sensitive
stages of salmon life. Studies by VanLeeuwen et al. and Dominguez and Chapmen derived different
96-hour LC50 values for early life stage salmonids (18 |ig/L and 66 |ig/L, respectively). The
Services acknowledged that different study methods led to different results, but concluded that "the
essential point is that both studies indicate that PCP can cause significant lethality in early life stage
salmonids after exposures as short as 4 days.... Since the LC50 is the concentration at which half the
organisms die, both these studies suggest it is likely that some mortality would occur at PCP
concentrations at or below the proposed chronic criterion." Because the mortality of young
salmonids will likely occur at or below Oregon's proposed acute criterion, the standards do not
protect the designated uses of aquatic life and fish propagation.

Fish do not fare any better under the chronic criteria. One study by Dominguez and Chapman
exposed rainbow trout to EPA's recommended chronic criterion of purified PCP from the embryo
state through 72 days of development. The authors reported a 34 percent mortality after 72 days.
They also found a 32 percent reduction in weight, fin erosion, mild malformations, and lethargy
compared to controls. This demonstrates that Oregon's chronic criterion does not protect salmonids.
EPA must therefore disapprove the acute and chronic criteria for PCP.

EPA's response to specific pollutant concerns regarding pentachlorophenol

EPA disagrees with the comment that Oregon's aquatic life criteria for pentachlorophenol (PCP)
does not protect salmonids.

Significantly, neither NMFS nor FWS were of the opinion that Oregon's revised chronic criterion
for pentachlorophenol would jeopardize any listed species in Oregon's waters.

More recently, the EPA evaluated existing toxicity data for PCP. Only the exotic fish, Cyprinus
carpio, is sensitive at the current freshwater criteria. No tested species are sensitive at the saltwater
criteria. The PCP criteria, both acute and chronic, are protective of all tested salmonids. The 1988
study by Dominguez and Chapman mentioned by the comment is in the data table and was
considered with a value of 20ug/L which is above the criterion. The VanLeeuwan study was

-------
rejected due to quality failure (see Appendix K of the TSD).
See General Response 4 regarding ESA listed species.

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APPENDIX 1: TEST RESULT QUALITY REVIEW PROCEDURES

Sections II.B - F, IV.B - E, IV.H, and VI.B - E of the Guidelines give reasons why the results of some
toxicity tests should not be used, should be rejected, or should not be used in calculations, whereas
sections II.G, X, XI.C, XII. A. 14, and XII.B allow the use of "questionable data" and "other data" in
some situations. In other words, sections II.B - F, IV.B - E, IV.H, VI.B - E give reasons why the results
of some toxicity tests using aquatic animals should not be directly used in the derivation of a Final Acute
Value (FAV) or a Final Chronic Value (FCV), whereas sections II.G, X, XI.C, XII.A. 14, and XII.B
describe other possible uses of test results with aquatic animals that should not be directly used in the
derivation of a FAV or a FCV.

The Guidelines say the following concerning the use of results of toxicity tests using aquatic animals:

1. General guidance:

a. All data should be available in typed, dated, and signed hard copy (publication, manuscript,
letter, memorandum, etc.) with enough supporting information to indicate that acceptable test
procedures were used and that the results are probably reliable, (section II.B)

b. Information that is confidential or privileged or otherwise not available for distribution should
not be used, (section II.B)

c. Questionable data, whether published or unpublished, should not be used. For example, a test
result should usually be rejected if it is from:

i. a test that did not contain a control treatment.

ii. a test in which too many organisms in the control treatment died or showed signs of stress
or disease.

iii. a test in which distilled or deionized water was used as the dilution water without addition
of appropriate salts.

(section II.C)

d. A result of a test on technical-grade material may be used if appropriate, but a result of a test on
a formulated mixture or an emulsifiable concentrate of the test material should not be used,
(section II.D)

e. For some highly volatile, hydrolyzable, or degradable materials it is probably appropriate to use
only results of flow-through tests in which the concentrations of test material in the test
solutions were measured often enough using acceptable analytical methods, (section HE)

f. Data should be rejected if they were obtained using:

i. Brine shrimp.

ii. A species that does not have a reproducing wild population in North America.

iii. Organisms that were previously exposed to substantial concentrations of the test material
or other contaminants, (section II.F)

2. Guidance specifically regarding results of acute tests:

g. Acute toxicity tests should have been conducted using acceptable procedures, (section IV.B)
The following two American Society for Testing and Materials (ASTM) Standards are
referenced as examples of acceptable procedures:

i. ASTM Standard E 729, Practice for Conducting Acute Toxicity Tests with Fishes,

Macroinvertebrates, and Amphibians. (The title was later changed to "Standard Guide for
Conducting Acute Toxicity Tests on Test Materials with Fishes, Macroinvertebrates, and
Amphibians".)

Some of the most important items in Standard E 729 include:

(1) "The test material should be reagent-grade or better, unless a test on a formulation,
commercial product, or technical-grade or use-grade material is specifically needed."

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("Reagent-grade" is referenced to the American Chemical Society specifications.) (section
9.1)

(2) "If an organic solvent is used, it should be reagent-grade or better and its concentration in
any test solution must not exceed 0.5 mL/L. A surfactant must not be used in the
preparation of a stock solution because it might affect the form and toxicity of the test
material in the test solutions." (section 9.2.3)

(3) "For static tests the concentration of dissolved oxygen in each test chamber must be from
60 to 100 % of saturation during the first 48 h of the test and must be between 40 and 100
% of saturation after 48 h. For renewal and flow-through tests the concentration of
dissolved oxygen in each test chamber must be between 60 and 100 % of saturation at all
times during the test." (section 11.2.1)

ii. ASTM Standard E 724, Practice for Conducting Static Acute Toxicity Tests with Larvae of
Four Species of Bivalve Molluscs. (The title was later changed to "Standard Guide for
Conducting Static Acute Toxicity Tests Starting with Embryos of Four Species of
Saltwater Bivalve Molluscs".)

When water quality criteria for aquatic life are derived, EPA does not automatically accept all
toxicity tests that are performed according to an ASTM Standard or according to "Standard
Methods". EPA reviews results of all aquatic toxicity tests for acceptability using best
professional judgment. Although written methodologies are very useful, no such methodology
can appropriately address all aspects of toxicity tests, especially all organism-specific and all
chemical-specific aspects. In addition, written methodologies often do not keep up with the
newest information that is available.

h. Except for tests using saltwater annelids and mysids, results of acute tests during which the test
organisms were fed should not be used, unless data indicate that the food did not affect the
toxicity of the test material, (section II.C)

i. Results of acute tests conducted in unusual dilution water, e.g., dilution water in which total
organic carbon or particulate matter exceeded 5 mg/L, should not be used, unless a relationship
is developed between acute toxicity and organic carbon or particulate matter or unless data
show that organic carbon, particulate matter, etc., do not affect toxicity, (section IV.D)

j. Acute values should be based on endpoints which reflect the total severe acute adverse impact
of the test material on the organisms used in the test. Therefore, only the following kinds of
data on acute toxicity to aquatic animals should be used:

(1) Tests with daphnids and other cladocerans should be started with organisms less than 24
hours old and tests with midges should be started with second- or third-instar larvae. The
result should be the 48-hr EC50 based on the percentage of organisms immobilized plus
percentage of organisms killed. If such an EC50 is not available from a test, the 48-hr LC50
should be used in place of the desired 48-hr EC50. An EC50 or LC50 of longer than 48 hr
can be used as long as the animals were not fed and the control animals were acceptable at
the end of the test.

(2) The result of a test with embryos and larvae of barnacles, bivalve molluscs (clams,
mussels, oysters, and scallops), sea urchins, lobsters, crabs, shrimp, and abalones should be
the 96-hr EC50 based on the percentage of organisms with incompletely developed shells
plus the percentage of organisms killed. If such an EC50 is not available from a test, the
lower of the 96-hr EC50 based on the percentage of organisms with incompletely developed
shells and the 96-hr LC50 should be used in place of the desired 96-hr EC50. If the duration
of the test was between 48 and 96-hr, the EC50 or LC50 at the end of the test should be
used.

(3) The acute values from tests with all other freshwater and saltwater animal species and

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older life stages of barnacles, bivalve molluscs, sea urchins, lobsters, crabs, shrimps, and
abalones should be the 96-hr EC50 based on the percentage of organisms exhibiting loss of
equilibrium plus the percentage of organisms immobilized plus the percentage of
organisms killed. If such an EC50 is not available from a test, the 96-hr LC50 should be
used in place of the desired 96-hr EC50.

(4) Tests with single-celled organisms are not considered acute tests, even if the duration was
96 hours or less.

(5) If the tests were conducted properly, acute values reported as "greater than" values and
those which are above the solubility of the test material should be used, because rejection
of such acute values would unnecessarily lower the FAV by eliminating acute values for
resistant species.

(section IV.E)

k. The agreement of the data within and between species should be considered. Acute values that
appear to be questionable in comparison with other acute and chronic data for the same species
and for other species in the same genus probably should not be used in the calculation of a
Species Mean Acute Value (SMAV). For example, if the acute values available for a species or
genus differ by more than a factor of 10, some or all of the values probably should not be used
in calculations, (section IV.H)

3. Guidance specifically regarding results of chronic tests:

n. Results of chronic tests conducted in unusual dilution water, e.g., dilution water in which total
organic carbon or particulate matter exceeded 5 mg/L, should not be used, unless a relationship
is developed between chronic toxicity and organic carbon or particulate matter or unless data
show that organic carbon, particulate matter, etc., do not affect toxicity, (section VI.D)
o. Chronic values should be based on endpoints and lengths of exposure appropriate to the
species. Therefore, only data on chronic toxicity to aquatic animals that satisfy the species-
specific requirements given in sections VI.E.l, VI.E.2, and VI.E.3 should be used.

4. Guidance regarding other possible uses of results of toxicity tests using aquatic animals:

p. Questionable data, data on formulated mixtures and emulsifiable concentrates, and data
obtained with non-resident species or previously exposed organisms may be used to provide
auxiliary information but should not be used in the derivation of criteria, (section II.F)
q. Pertinent information that could not be used in earlier sections might be available concerning
adverse effects on aquatic organisms and their uses. The most important of these are data on
cumulative and delayed toxicity, flavor impairment, reduction in survival, growth, or
reproduction, or any other adverse effect that has been shown to be biologically important.
Especially important are data for species for which no other data are available. Data from
behavioral, biochemical, physiological, microcosm, and field studies might also be available.
Data might be available from tests conducted in unusual dilution water, from chronic tests in
which the concentrations were not measured, from tests with previously exposed organisms,
and from tests on formulated mixtures or emulsifiable concentrates. Such data might affect a
criterion if the data were obtained with an important species, the test concentrations were
measured, and the endpoint was biologically important, (section X)
r. The Criterion Continuous Concentration (CCC) is equal to the lowest of the Final Chronic

Value (FCV), Final Plant Value (FPV), and Final Residue Value (FRV), unless other data show

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that a lower value should be used, (section XI.C)
s. Are any of the other data important? (section XII. A. 14)

t. On the basis of all available pertinent laboratory and field information, determine if the
criterion is consistent with sound scientific information. If it is not, another criterion, either
higher or lower, should be derived using appropriate modifications of these Guidelines.

(section XII.B)

In addition, the following aquatic life criteria documents published by U.S. EPA in 1985, 1986, 1987,
and 1988 gave a variety of reasons for classifying specific test results as "unused":

U.S. EPA. 1985. Ambient Water Quality Criteria for Cadmium - 1984. EPA 440/5-84-032. U.S.
Environmental Protection Agency, Washington, DC.

U.S. EPA. 1985. Ambient Water Quality Criteria for Chlorine - 1984. EPA 440/5-84-030. U.S.
Environmental Protection Agency, Washington, DC.

U.S. EPA. 1985. Ambient Water Quality Criteria for Copper - 1984. EPA 440/5-84-031. U.S.
Environmental Protection Agency, Washington, DC.

U.S. EPA. 1985. Ambient Water Quality Criteria for Lead - 1984. EPA 440/5-84-027. U.S.
Environmental Protection Agency, Washington, DC.

U.S. EPA. 1985. Ambient Water Quality Criteria for Mercury - 1984. EPA 440/5-84-026. U.S.
Environmental Protection Agency, Washington, DC.

U.S. EPA. 1986. Ambient Water Quality Criteria for Chiorpyrifos - 1986. EPA 440/5-86-005.
U.S. Environmental Protection Agency, Washington, DC.

U.S. EPA. 1986. Ambient Water Quality Criteria for Parathion - 1986. EPA 440/5-86-007. U.S.
Environmental Protection Agency, Washington, DC.

U.S. EPA. 1986. Ambient Water Quality Criteria for Pentachlorophenol - 1986. EPA 440/5-86-
009. U.S. Environmental Protection Agency, Washington, DC.

U.S. EPA. 1986. Ambient Water Quality Criteria for Toxaphene - 1986. EPA 440/5-86-006. U.S.
Environmental Protection Agency, Washington, DC.

U.S. EPA. 1987. Ambient Water Quality Criteria for Selenium - 1987. EPA 440/5-87-006. U.S.
Environmental Protection Agency, Washington, DC.

U.S. EPA. 1987. Ambient Water Quality Criteria for Zinc- 1987. EPA 440/5-87-003. U.S.
Environmental Protection Agency, Washington, DC.

U.S. EPA. 1988. Ambient Water Quality Criteria for Chloride - 1988. EPA 440/5-88-001. U.S.
Environmental Protection Agency, Washington, DC.

The following is a list of common reasons why the results of some toxicity tests should not be used.
Most of these reasons can be considered to be based on items "a" through "o" listed above.

1. The document is a secondary publication of the test result.

2. The test procedures, test material, dilution water, and/or results were not adequately described.

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3. The test species is not resident in North America.

4. The test species was not obtained in North America and was not identified well enough to
determine whether it is resident in North America.

5. The test organisms were not identified specifically, for example, "crayfish" or "minnows."

6. There is reason to believe that the test organisms were possibly stressed by disease or parasites.

7. The test organisms were exposed to elevated concentrations of the test material before the test
and/or the control organisms contained high concentrations of the test material.

8. The test organisms were obtained from a sewage oxidation pond.

9. By the end of the test, the test organisms had not been fed for too long a period of time.

10. The water quality varied too much during the test.

11. The test was conducted with brine shrimp, which are from a unique saltwater environment.

12. The exposed biological material was an enzyme, excised or homogenized tissue, tissue extract,
plasma, or cell culture.

13. The test organisms were not acclimated to the dilution water for a sufficiently long time period.

14. The test organisms were exposed to the test material via gavage, injection, or food.

15. There is reason to believe that the test organisms were probably crowded during the test.

16. The test organisms reproduced during an acute test, and the new individuals could not be
distinguished from the original test individuals at the end of the test.

17. The test material was a component of a mixture, effluent, fly ash, sediment, drilling mud, sludge, or
formulation.

18. In a test on zinc, the dilution water contained a phosphate buffer.

19. The test material was chlorine and it was not measured acceptably during the test.

20. The test chamber contained sediment.

21. The test was conducted in plastic test chambers without measurement of the test material.

22. The test was a field study and the concentration of test material was not measured adequately.

23. A known volume of stock solution was placed on a wall of the test chamber and evaporated and
then dilution water was placed in the test chamber; the investigators assumed that all of the test
material dissolved in the dilution water, but the concentrations of the test material in the test
solutions were not measured.

24. The test only studied metabolism of the test material.

25. The only effects studied were biochemical, histological, and/or physiological.

26. The data concerned the selection, adaptation, or acclimation of organisms for increased resistance to
the test material.

27. The percent survival in the control treatment was too low.

28. The concentration of solvent in some or all of the test solutions was too high.

29. The study was a microcosm study.

30. The concentration of test material fluctuated too much during the exposure.

31. Too few test organisms were used in the test.

32. The dilution factor was ten.

33. There was no control treatment.

34. The pH was below 6.5.

35. The dilution water was chlorinated or "tap" water.

36. The dilution water contained an excessive amount of a chelating agent such as EDTA or other
organic matter.

37. The acceptability of the dilution water was questionable because of its origin or content.

38. The dilution water was distilled or deionized water without the addition of appropriate salts.

39. The measured test temperature fluctuated too much.

40. Neither raw data nor a clearly defined endpoint was reported.

41. The results were not adequately presented or could not be interpreted.

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42. The results were only presented graphically.

43. The test was a chronic test and the concentration of test material was not measured.

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ENCLOSURE 4

Aquatic Life Criteria
in Effect for
Clean Water Act Purposes

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TABLE 20

AQUATIC LIFE WATER QUALITY CRITERIA SUMMARY1

The concentration for each compound listed in this chart is a criteria or guidance value* not to be exceeded in waters of the state for the
protection of aquatic life and human health. Specific descriptions of each compound and an explanation of values are included in Quality
Criteria for Water (1986). Selecting values for regulatory purposes will depend on the most sensitive beneficial use to be protected, and what
level of protection is necessary for aquatic life and human health.

Compound Name (or Class)

Priority
Pollutant

Concentration in Micrograms Per Liter
for Protection of Aquatic Life

Fresh Acute
Criteria

Fresh Chronic
Criteria

Marine Acute
Criteria

Marine Chronic
Criteria

ACENAPTHENE

ACROLEIN

ACRYLONITRILE

ALDRIN

1.3

ALKALINITY

AMMONIA

CRITERIA ARE pH AND TEMPERATURE DEPENDENT—SEE DOCUMENT USEPA JANUARY 1985 (Fresh Water)

ANTIMONY

ARSENIC

ARSENIC (PENT)

ARSENIC (TRI)

360

190

ASBESTOS

BARIUM

BENZENE

BENZIDINE

BERYLLIUM

BHC

CADMIUM

3.9+

CARBON TETRACHLORIDE

CHLORDANE

2.4

0.0043

0.09

0.004

CHLORIDE

CHLORINATED BENZENES

CHLORINATED NAPHTHALENES

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Concentration in Micrograms Per Liter

for Protection of Aquatic Life

Priority

Fresh Acute

Fresh Chronic

Marine Acute

Marine Chronic

Compound Name (or Class)

Pollutant

Criteria

CHLORINE

CHLOROALKYL ETHERS

CHLOROETHYL ETHER (BIS-2)

CHLOROFORM

CHLOROISOPROPYL ETHER (BIS-2)

CHLOROMETHYL ETHER (BIS)

CHLOROPHENOL 2

CHLOROPHENOL 4

CHLOROPHENOXY HERBICIDES (2,4,5,-TP)

CHLOROPHENOXY HERBICIDES (2,4-D)

CHLORP YRIF 0 S

CHLORO-4 METHYL-3 PHENOL

CHROMIUM (HEX)

1,100

CHROMIUM (TRI)

COPPER

18.+

12.+

CYANIDE

DDT

1.1

0.001

0.13

0.001

(TDE) DDT METABOLITE

(DDE) DDT METABOLITE

DEMETON

DIBUTYLPHTHALATE

DICHLOROBENZENES

DICHLOROBENZIDINE

DICHLOROETHANE 1,2

DICHLOROETHYLENES

DICHLOROPHENOL 2,4

DICHLOROPROPANE

DICHLOROPROPENE

DIELDRIN

0.71

0.0019

DIETHYLPHTHALATE

DIMETHYL PHENOL 2,4

DIMETHYL PHTHALATE

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Compound Name (or Class)

Priority
Pollutant

Concentration in Micrograms Per Liter
for Protection of Aquatic Life

Fresh Acute
Criteria

Fresh Chronic
Criteria

Marine Acute
Criteria

Marine Chronic
Criteria

DINITROTOLUENE 2,4

DINITROTOLUENE

DINITRO-O-CRESOL 2,4

DIOXIN (2,3,7,8-TCDD)

DIPHENYLHYDRAZINE

DIPHENYLHYDRAZINE 1,2

DI-2-ETHYLHEXYL PHTHALATE

ENDOSULFAN

0.22

0.056

0.034

0.0087

ENDRIN

0.037

0.0023

ETHYLBENZENE

FLUORANTHENE

GUTHION

HALOETHERS

HALOMETHANES

HEPTACHLOR

0.52

0.0038

0.053

0.0036

HEXACHLOROETHANE

HEXACHLOROBENZENE

HEXACHLOROBUT ADIENE

HEXACHLOROCYCLOHEXANE (LINDANE)

0.08

0.16

HEXACHLOROCYCLOHEXANE-ALPHA

HEXACHLOROCYCLOHEXANE-BETA

HEXACHLOROCYCLOHEXANE-GAMA

HEXACHLOROCYCLOHEXANE-
TECHNICAL

HEXACHLOROCYCLOPENT ADIENE

IRON

ISOPHORONE

LEAD

MALATHION

MANGANESE

MERCURY

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Compound Name (or Class)

Priority
Pollutant

Concentration in Micrograms Per Liter
for Protection of Aquatic Life

Fresh Acute
Criteria

Fresh Chronic
Criteria

Marine Acute
Criteria

Marine Chronic
Criteria

METHOXYCHLOR

MIREX

MONOCHLOROBENZENE

NAPHTHALENE

NICKEL

NITRATES

NITROBENZENE

NITROPHENOLS

NITROSAMINES

NITROSODIBUTYL AMINE N

NITROSODIETHYLAMINE N

NITROSODIMETHYL AMINE N

NITROSODIPHENYL AMINE N

NITROSOPYRROLIDINE N

PARATHION

PCB's

PENTACHLORINATED ETHANES

PENTACHLOROBENZENE

PENTACHLOROPHENOL

PHENOL

PHOSPHORUS ELEMENTAL

PHTHALATE ESTERS

POLYNUCLEAR AROMATIC
HYDROCARBONS

SELENIUM

260

SILVER

SULFIDE HYDROGEN SULFIDE

TETRACHLORINATED ETHANES

TETRACHLOROBENZENE 1,2,4,5

TETRACHLOROETHANE 1,1,2,2

TETRACHLOROETHANES

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Concentration in Micrograms Per Liter

for Protection of Aquatic Life

Priority

Fresh Acute

Fresh Chronic

Marine Acute

Marine Chronic

Compound Name (or Class)

Pollutant

Criteria

TETRACHLOROETHYLENE

TETRACHLOROPHENOL 2,3,5,6

THALLIUM

TOLUENE

TOXAPHENE

TRICHLORINATED EtHANES

TRICHLOROETHANE 1,1,1

TRICHLOROETHANE 1,1,2

TRICHLOROETHYLENE

TRICHLOROPHENOL 2,4,5

TRICHLOROPHENOL 2,4,6

VINYL CHLORIDE

ZINC

MEANING OF SYMBOLS:

= grams

= milligrams

= micrograms

= nanograms

= picograms

= Yes

= No

1 =

Hardness Dependent Criteria (100 mg/L used).

Insufficient data to develop criteria; value presented is the L.O.E.L - Lower Observed Effect Level.

pH Dependent Criteria (7.8 pH used).

Values in Table 20 are applicable to all basins.

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Table 33A

Note: The environmental Quality Commission adopted the following criteria on May 20, 2004 to become effective February 15, 2005.
However, EPA has not yet acted (as of June 2006) approved the criteria. Thus, Table 33 A criteria may be used in NPDES permits, but not for
the section 303(d) list of impaired waters.

AQUATIC LIFE WATER QUALITY CRITERIA SUMMARY4

The concentration for each compound listed in Table 33 A is a criterion not to be exceeded in waters of the state in order to protect aquatic
life. All values are expressed as micrograms per liter (|i/L) except where noted. Compounds are listed in alphabetical order with the
corresponding EPA number (from National Recommended Water Quality Criteria:2002, EPA 8220R-02-047), the Chemical Abstract Service
(CAS) number, aquatic life freshwater acute and chronic criteria, aquatic life saltwater acute and chronic criteria. The acute criteria refer to
the average concentration for one (1) hour and the chronic criteria refer to the average concentration for 96 hours (4-days), and that these
criteria should not be exceeded more than once every three (3) years.

Freshwater

Saltwater

Acute (CMC)

Effective
Date

Chronic (CCC)

Effective
Date

Acute
(CMC)

Effective
Date

Chronic
(CCC)

Effective
Date

Acenaphthene

83329

Acenaphthylene

208968

Acrolein

107028

Acrylonitrile

107131

102

Aldrin

309002

Alkalinity

20,000 P

2 N

Aluminum (pH 6.5 - 9.0)

7429905

3 N

Ammonia

7664417

Anthracene

120127

Antimony

7440360

Arsenic

7440382

Asbestos

1332214

6 N

Barium

7440393

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19

~61

~63

103

104

106

105

7 N

~21

107

8 N

9 N

~~23

~65

"125

15 N

Freshwater

Acute (CMC)

-------
71

~45

ION

11N

12 N

108

109

110

14 N

~75

111

Freshwater

Acute (CMC)

Chronic (CCC)

-------
79

~81

27 N

~83

~85

112

113

114

115

116

~~33

17 N

117

118

~91

19 N

Freshwater

Acute (CMC)

£ A

Chronic (CCC)

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92

20 N

21 N

22 N

23 N

24 N

25 N

~51

26 N

28 N

29 N

30 N

32 N

33 N

Freshwater

Acute (CMC)

-------
119

34 N

~~53

36 N

100

40 N

43 N

120

44 N

101

~41

~43

45 N

~~55

Freshwater

Acute (CMC)

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Footnotes for Table 33A and 33B

M Freshwater aquatic life values for pentachlorophenol are expressed as a function of pH, and are calculated as follows: CMC=(exp(1.005(pH)-4.869);
CCC=exp( 1,005(pH)-5.134).

N This number was assigned to the list of non-priority pollutants in National Recommended Water Quality Criteria: 2002 (EPA-822-R-02-047).

P Criterion shown is the minimum (i.e. CCC in water should not be below this value in order to protect aquatic life).

S This criterion is expressed as |ig free cyanide (CN)/L.

U This criterion applies to total PCBs (e.g. the sum of all congener or all isomer or homolog or Arochlor analyses).

X The effective date for the criterion in the column immediately to the left is 1991.

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Table 33B

Note: The environmental Quality Commission adopted the following criteria on May 20, 2004 to become effective on EPA approval. EPA
has not yet (as of June 2006) approved the criteria. The Table 33B criteria may not be used until they are approved by EPA.

AQUATIC LIFE WATER QUALITY CRITERIA SUMMARY4

The concentration for each compound listed in Table 33 A is a criterion not to be exceeded in waters of the state in order to protect aquatic
life. All values are expressed as micrograms per liter (|i/L) except where noted. Compounds are listed in alphabetical order with the
corresponding EPA number (from National Recommended Water Quality Criteria: 2002, EPA 8220R-02-047), the Chemical Abstract Service
(CAS) number, aquatic life freshwater acute and chronic criteria, aquatic life saltwater acute and chronic criteria. The acute criteria refer to
the average concentration for one (1) hour and the chronic criteria refer to the average concentration for 96 hours (4-days), and that these
criteria should not be exceeded more than once every three (3) years.

Freshwater

Saltwater

Acute (CMC)

Effective

Chronic
(CCC)

Effective
Date

Acute (CMC)

Effective
Date

Chronic
(CCC)

Effective
Date

2 N

Aluminum (pH 6.5 - 9.0)

7429905

3 N

Ammonia

7664417

Arsenic

7440382

Asbestos

1332214

Benzene

71432

Beryllium

7440417

105

BHC gamma- (Lindane)

58899

Cadmium

7440439

E, F

40 E

8.8 E

107

Chlordane

57749

CHLORINATED BENZENES

Chloroform

67663

ChloroisopropylEther Bis2-

108601

15 N

ChloromethylEther, Bis

542881

Chromium (III)

E,F

Chromium (VI)

18540299

16 E

11 E

Copper

7440508

4.8 E

3.1 E

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Freshwater

Saltwater

Acute (CMC)

Effective

T^QtA

Chronic
(CCC)

Effective
Date

Acute (CMC)

Effective
Date

Chronic
(CCC)

Effective
Date

108

DDT 4,4'-

50293

DIBUTYLPHTHALATE

DICHLOROBENZENES

DICHLOROBENZIDINE

DICHLOROETHYLENES

DICHLOROPROPENE

111

Dieldrin

60571

0.056

DINITROTOLUENE

DIPHENYLHYDRAZINE

115

Endrin

72208

0.036

Fluoranthene

206440

HALOMETHANES

20 N

Iron

7439896

Lead

7439921

E,F

210 E

8.1 E

22 N

Manganese

7439965

Mercury

7439976

MONOCHLOROBENZENE

Nickel

7440020

E,F

74 E

8.2 E

Pentachlorophenol

87865

Phenol

108952

POLYNUCLEAR AROMATIC
HYRDOCARBONS

Selenium

7782492

290 E

71 E

Silver

7440224

E,F

0.10 E

1.9 E

44 N

Tributyltin (TBT)

688733

0.46

0.063

0.37

0.01

Trichloroethane 1,1,1-

71556

Trichlorophenol 2,4,6-

88062

Zinc

7440666

E,F

90 E

81 E

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Footnotes for Table 33A and 33B

E Freshwater and saltwater criteria for metals are expressed in terms of "dissolved" concentrations in the water column, except where otherwise noted (e.g.
aluminum).

F The freshwater criterion for this metal is expressed as a function of hardness (mg/L) in the water column. Criteria values for hardness may be calculated from
the following formulae (CMC refers to Acute Criteria; CCC refers to Chronic Criteria):

CMC= (exp(mA*[ln(hardness)] +bA))*CF
CCC= (exp(mc*[ln(hardness)] +bc))*CF

where CF is the conversion factor used for converting a metal criterion expressed as the total recoverable fraction in the water column to a criterion expressed
as the dissolved fraction in the water column.

Chemical

l>^

in,

1).

Cadmium

—

0.7409

-4.719

Chromium III

0.8190

3.7256

0.8190

0.6848

Copper

—

Lead

1.273

-1.460

1.273

-4.705

Nickel

0.8460

2.255

0.8460

0.0584

Silver

1.72

-6.59

Zinc

0.8473

0.884

0.8473

0.884

Conversion factors (CF) for dissolved metals (the values for total recoverable metals criteria were multiplied by the appropriate conversion factors shown
below to calculate the dissolved metals criteria):

Chemical

l-rcslmalcr

Sallwalcr

Acule

Chronic

Acule

Chronic

Arsenic

...

Cadmium

...

1.101672-[(ln hardness)(0.041838)]

0.994

Chromium III

0.316

0.860

Chromium VI

0.982

0.962

...

Copper

...

0.83

Lead

1.46203-[(lnhardness)(0.145712)]

1.46203-[(In hardness)(0.145712)]

0.951

Nickel

0.998

0.997

0.990

Selenium

...

0.998

Silver

0.85

...

Zinc

0.978

0.986

0.946

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M Freshwater aquatic life values for pentachlorophenol are expressed as a function of pH, and are calculated as follows: CMC=(exp(1.005(pH)-4.869);
CCC=exp(1.005(pH)-5.134).

N This number was assigned to the list of non-priority pollutants in National Recommended Water Quality Criteria: 2002 (EPA-822-R-02-047).

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