United States
Environmental Protection
Agency
Off ice of Water
Regulations and Standards
Criteria and Standards Divisor.
Washington DC 20460
October 1983
SCO// 0 '
Water
vvEPA
INITIAL EVALUATION OF ALTERNATIVES
FOR DEVELOPMENT OF SEDIMENT RELATED
CRITERIA FOR TOXIC CONTAMINANTS IN
MARINE WATERS (PUGET SOUND)
PHASE I: DEVELOPMENT OF CONCEPTUAL
FRAMEWORK
PHASE II. DEVELOPMENT AND TESTING OF
THE SEDIMENT-WATER EQUILIBRIUM
PARTITIONING APPROACH, /
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INITIAL EVALUATION OF ALTERNATIVES FOR
DEVELOPMENT OF SEDIMENT RELATED
CRITERIA FOR TOXIC CONTAMINANTS IN
MARINE WATERS (PUGET SOUND)
PHASE I: DEVELOPMENT OF CONCEPTUAL
FRAMEWORK
FINAL REPORT
October 28. 1983
by:
S.P. Pavlou and D.P. Weston
JRB Associates*
13400-B Northup Way, Suite 38
Bellevue, Washington 98005
Submitted to Water Quality Branch, EPA Region X, 1200 Sixth Avenue,
Seattle, Washington 98101, In response to tu requirements under
EPA Contract No. 68-01-6388, Work Assignment 62, JRB Project No.
2-813-03-852-42.
*A Company of Science Applications, Incorporated.
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PHASE I: DEVELOPMENT OF CONCEPTUAL
FRAMEWORK
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TABLE OF CONTENTS
Page
1.0 INTRODUCTION 1
1.1 Rationale and Objectives 1
1.2 Previous Work in Sediment Criteria Development 2
2.0 PROPOSED ALTERNATIVES FOR SEDIMENT CRITERIA ESTABLISHMENT 8
2.1 General Considerations 8
2.2 Establishment of Criteria on the Basis of Background
Levels 8
2.3 Establishment of Criteria Based on EPA Water Quality
Criteria 11
2.4 Establishment of Criteria on the Basis of Equilibrium
Partitioning 12
2.4.1 Basic Definitions 12
2.4.2 Application of Partitioning Constants to the
Development of Sediment Criteria 20
2.5 Establishment of Criteria on the Basis of Biological
Response 22
2.5.1 Bioassays 22
2.5.2 Biological Field Surveys 24
2.6 Environmental Degradation Assessment 26
2.6.1 NOAA Approach 26
2.6.2 Ecological Risk Index 27
2.6.3 Quality Degradation Factors 28
3.0 APPLICATION SCENARIOS 30
3.1 Issuance of CWA Section 301 (h) Waivers 30
3.2 Issuance of CWA Section 404 Dredge and Fill Permits
and Designation of Dredge Material Disposal Sites 31
3.3 Selection of Remedial Alternatives at Superfund Sites 32
3.4 Issuance of NPDES Permits 33
4.0 SUMMARY AND CONCLUSIONS 34
5.0 REFERENCES 38
APPENDIX A - INTERVIEW RESULTS 4?
APPENDIX B - COMPUTATION OF ECOLOGICAL RISK INDEX 52
APPENDIX C - QUALITY DEGRADATION FACTORS 54
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1.0 INTRODUCTION
1.1 RATIONALE AND OBJECTIVES
The Environmental Protection Agency has focused historically on the develop-
ment of water quality criteria which are supported by a broad base of toxico-
logical studies. Implementation and enforcement of these criteria provides
some degree of assurance that contaminant concentrations will be within accept-
able limits for the protection of aquatic life and human health. However,
there is disturbing evidence of environmental degradation in many of the
heavily urbanized of Puget Sound even though water quality criteria are not
exceeded. The majority of adverse biological impacts recently observed are
not among organisms living in the water column but those that live in or on
the sediments. Macrobenthic communities in the vicinity of point source
discharges have demonstrated significant changes in species composition and
i
abundance (Armstrong, et al., 1978; Malins et al., 1982; Comiskey et al.,
1983), sediments from urbanized areas have been shown to induce mortality in
sensitive benthic species (Swartz et al., 1982) and demersal fishes from
heavily polluted areas have been shown to have a higher incidence of hlsto-
pathological abnormalities than those from reference areas (Malins et al.,
1980; 1982). These observations raise some questions as to whether existing
water quality criteria alone are adequate to protect the environmental
resources of Puget Sound.
It is becoming increasingly evident that some sort of sediment criteria are
needed to supplement existing water quality criteria in judging the signifi-
cance of contaminant concentrations and to provide a basis for remedial
action. There are a number of reasons why sediment criteria deserve considera-
tion:
• Most toxic compounds are highly insoluble so the majority of the
contaminant is not dissolved in the water but is associated with
the organic matrix on sediment particles. For example, sediments
in Elliott Bay contain 60,000 times more PCBs than overlying
water (Pavlou and Dexter, 1979).
i
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• Sediments serve to integrate contaminant concentrations over
time, eliminating the high degree of temporal variability which
plagues sampling of toxicants in the water column.
• Sediments serve as a sink for most toxic materials, thus a long-
tern low level discharge of a contaminant may result in a
dangerous build up in the sediment even though water quality.
criteria are not violated at any given time.
• Sediments can serve as a reservoir (source) of contaminants which
could be reincroduced Co unpolluted overlying water.
• A large number of organisms, Including many of commercial impor-
tance, spend most of their lives in or on the sediments. For
these species, contaminant levels in the sediments may be of
greater concern than those in the overlying water and may be the
controlling factor with regards to bioaccumulation potential.
The goal of this project is to evaluate selected approaches to developing sedi-
ment criteria for Puget Sound. Emphasis will be placed on establishment of
methodologies and techniques though tentative criteria may be proposed for
selected approaches if the data base is adequate. This report details the
results of Phase 1, Development of Conceptual Framework. Included are a brief
«
discussion of past efforts to establish sediment criteria, an evaluation of
numerous approaches and a discussion of application scenarios. Also presented
as an appendix is the results froa interviews with a number of investigators
and representatives of local agencies currently involved in projects address-
ing sediment quality in Puget Sound.
1.2 PREVIOUS WORK IN SEDIMENT CRITERIA DEVELOPMENT
•
Much of the impetus for earlier work in sediment criteria development has come
from the need to evaluate the toxicity of dredge spoils in determining the
most prudent disposal alternative. Since the late 1950s, several attempts
have been made to determine the level of pollutants in sediment which consti-
tute an ecological threat. These previous attempts to establish "safe" levels
of contamination have all been adopted to varying degrees though none have met
with broad acceptance. _A brief summary of these approaches follows with the
recommended guidelines presented in Tables 1 and 2.
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Table 1
FWPCA CHICAGO GUIDELINES FOR THE DEGREE OF
POLLUTION OF HARBOR SEDIMENTS (AUGUST, 1968)*
Extent of Pollution
Parameter
Armenia N
COD
Total Iron
i
Lead
Oil & Grease
Phenol
Total Phosphorus
Sulphide
Zinc
Volatile Solids (%)
Light
0-25
0-40,000
0-8,000
0-40
0-1,000
0-0.26
0-100
0-20
0-90
0-5
Moderate
25-75
40,000-120,000
8,000-13,000
40-60
1,000-2,000
0.26-0.60
100-300
20-60
90-200
5-8
Heavy
over 75
over 120,000
over 13,000
over 60
over 2,000
over 0.60
over 300
over 60
over 200
over 8
*Units are in mg/kg dry weight
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Table 2
PREVIOUSLY ESTABLISHED SEDIMENT QUALITY GUIDELINES
Jeaeen
Criteria.
EPA. 1971
D>A teflon V *
Culdellnea
for Pollution*! DSCS
Claeelflcatlon fedlawnl
of Sedtaenta Alert Level*
(at/k*> (a«/k«l
Afitlavny
Araealc
•arli*
t*T7llli»
CadMiaa
20
IV
total
Copper
Iron
Lead
Hanganeee
Hercury
nickel
Seltnlu*)
Silver
line •
Aldrtn
Chlordaae
2.4-0
2.4.3-TP
DOT
Dteldrtn
DioBln
Endoaulfen
Endrln
Heptachlor
Heptachlor
EpOBld*
llndaae
Malachloa
Hethoxychlor
Hire*
Parathlon
Toaaphene
KB
Phenol
Hltrata aa H
JO
JO
23
17,000
40
100
1
20
.fO
0.26
Fboapbonia
NO; * HO]
MO] aa N
Cyanldo
Volatile Solid*
COO
KJtldaM
Hltroiaa
Oil 6 Craaaa
60.000
SO. 000
I.000
1.300
I.10
73
420
O.I
30.000
40.000
1.000
1.000
200
2.000
200
20
200
2.000
300
20
2.000
20
1.000
3.000
0.02
0.02
0.02
0.02
0.02
0.02
0.02
0.02
0.02
0.02
0.02
0.02
0.02
0.0]
0.0]
0.0]
Ontario ETA lesion VI
Nlnlatry of the Fropoied
Environment Guideline*
Dredge Spoil for Sedlaeat
Guideline* Dlapoaal
(an/kc) (at/kt)
300
a 3
23
23
10.000
so
0.1
23
100
100
30
SO
I
30
7)
100
O.OS
100
1.000
0.1
60.000
30.000
2.000
1.300
ETA legion VI
lediaeat Quality
Indicator*
laitratitla] or
Uutrlair w*ter
(llC/l)
440
1.03ia(H) -6.31
1.08tn(H) +3.48
0.2*
3.6
2.131n(l) -9.41
0.00037
0.76la(M) +1.06
33 (laoriaalc)
l.721a(H) -6.32
47
3.0
0.0041
0.0010
0.001*
-0-
0.036
0.0021
0.0031
0.003
0.011
0.014
1.0
10.000
23 (lake*)
10.000
1.000
3.3
*U«ala anon vara raiardad aa the cut-off valua txtvm noo-pollutad and •odtracaly polluiad tadlawnt*.
bS*dlarata with KB concentrailaaa batvoan 1 and 10 wra conaidarad on a caa* by cat* baali. Sadlacnt*
vlth graatar than 10 ppa Kl 'era conaldtrcd iroialy. polluted.
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In 1968 the Chicago office of the Federal Water Pollution Control Administra-
tion (FWPCA) released guidelines to be used in establishing the degree of
pollution in harbor sediments. The ranking was somewhat arbitrary but was
primarily based on correlations between sediment pollutant burden and the
benthic community. Sediments were considered heavily polluted in areas where
benthic organisms were absent or sharply reduced in number. A predominance of
pollution tolerant species was considered indicative of moderate pollution.
Sediments were considered lightly polluted in areas in which benthic organisms
showed little or no evidence of pollution-induced alteration.
The Cleveland office of the FWPCA performed a similar assessment in 1969
which, together with the Chicago FWPCA guidelines, eventually became the
Jensen criteria which were adopted by EPA in 1971. EPA promulgated these
criteria for national use in determining the suitability of open water spoils
disposal. When one or more parameters exceeded criteria, the sediments were
considered unacceptable for open water disposal.
In 1977 EPA Region V released interim guidelines for the classification of
polluted sediments in harbors of the Great Lakes. Recognizing that the guide-
lines were somewhat arbitrary and that a strong scientific basis for criceria
were lacking, Region V recommended use of the guidelines only as a tool in
making a subjective Judgement as to suitability of dredge material for open
water disposal. Additional factors such as elutriate test results, source of
contamination, particle size distribution, benthic populations, sediment color
and odor were also considered. Only in the case of mercury and PCB were
violations of guidelines considered irrefutable evidence of severe pollution,
thus making sediments unsuitable for open water disposal.
The U. S. Geological Survey employs a system of alert levels for in-house
usage in evaluating the extent of sediment pollution. These alert levels were
arbitrarily established to flag 15 to 20 percent of the samples analyzed
nationwide. Since much of the ir.ormation available at the time of alert
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level establishment was from heavily polluted areas, alert levels established
in this manner are artificially inflated (B. Malo, USGS, personal communica-
tion). Use of USGS alert levels have been limited to a flagging mechanism to
identify potential sites of concern. They were never intended, nor have they
been used, as rigid criteria for management decisions.
The Ontario Ministry of the Environment released a document in January, 1976
entitled "Evaluating Construction Activities Impacting on Water Resources"
which was amended in 1978. These documents provided guidelines for the evalua-
tion of the suitability of dredge spoil for open water disposal which were
based on the Jensen criteria of EPA but modified to reflect data from Canadian
harbors on the Great Lakes. For example, guidelines for mercury were made
stricter than those originally employed by EPA because of correlations
observed between sediment mercury concentrations and tissue burdens of mercury
in fish which exceeded guidelines for human consumption. The sediment pollu-
tion guidelines proposed by the Ontario Ministry of the Environment have been
used subjectively in evaluating dredge spoils but flexibility was allowed in
assessing the potential danger o.f dredge disposal operations.
EPA Region VI has proposed two alternative guidelines for evaluating the
degree of pollution in sediments. The region has released guidelines for
assessing the extent of metal contamination in dredge material intended for
open water disposal. However, of greater significance is a recent attempt by
the region to establish sediment criteria for metals, organics and other
pollutants of concern based on a modification of existing EPA water quality
criteria. The apprdach employed made the assumption that interstitial waters
are an extension of the overlying water column and in need of the same level
of protection. Existing EPA water quality criteria for the 24 hour average
concentration for the protection of freshwater aquatic life were directly
applied as sediment quality Indicators for both interstitial and elutriate
water. In the absence of 24 hour average criteria che maximum permissible
concentration In water were used. The sediment quail*y indicators derived in
this manner were suggested for use as a screeening tool rather than for use in
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regulatory or enforcement actions. They are unique among previous attempts to
establish sediment criteria in that they depend upon analysis of interstitial
and elutriate water rather than bulk sediments and that they draw upon the
broad toxlcological data incorporated by existing water quality criteria.
Criteria for PCB concentrations in the sediments of Puget Sound have pre-
viously been proposed by Pavlou, et al. (1977). These authors recommended
that the total PCB concentration in sediments not exceed 0.5 ng/kg dry weight,
and that the individual components not exceed 0.025 mg/kg dry weight. These
limits were those necessary to maintain ambient water quality within accept-
able standards, based on an estimated sedinent-water partition coefficient.
The only sediment criteria currently approved for national usage by EPA is a
bioassay to provide an assessment of the toxicity of dredged material intended
for ocean dumping (U.S. EPA/COE, 1977). To meet requirements of Section 103
of Public Law 92-532 (Marine Protection, Research and Sanctuaries Act of
1972), any proposed dumping of dredged material into ocean waters must either
meet several exclusionary criteria or be evaluated by a solid phase bioassay.
Organisms to be employed in the bioassay must include one filter-feeder, one
deposit-feeder and one burrowing species. Any statistically significant
increase in mortality relative to controls Is considered potentially undesir-
able.
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in those sediments corresponding to pre-industrial depositional periods can
then be established as the true background concentrations for the region prior
to anthropogenic enrichment. Attempts to establish background levels by this
method for Puget Sound have already been made (Riley, et al., 1981; Pavlou et
al., 1983) and some previously established background levels are presented in
Table 3.
An alternative means to establish concentrations representative of unpolluted
sediments is to determine the concentration of pollutants in surficial sedi-
ments from areas distant from all known pollution point sources. This method
has an important advantage over background concentrations derived from deep
cores. Since synthetic organics are virtually absent from pre-industrial
sediments, except for small amounts incorporated from more recent sediments by
bioturbation. background concentrations of synthetic organics established by
deep coring' would be essentially zero which may be an unrealistically
restrictive criteria.
Establishment of background concentrations should take into consideration the
fact that the concentration of most pollutants in the sediments is strongly
dependent upon the organic carbon content of that sediment or covariates such
as percent fines or total volatile solids. This consideration could be
addressed by establishing several criteria for a given pollutant, each of
which would be applicable within a specified range of organic carbon content.
However, it may be more appropriate to derive a regression equation in which
the criteria is a function of the organic carbon content. This approach is
directly comparable to EPA water quality criteria for metals in freshwater for
which the criteria is a function of water hardness.
Given the above considerations the optimal approach to establishment of
sediment criteria on the basis of background concentrations is as follows:
1. Determine the concentration of the pollutant in surficial sedi-
ments from relatively pristine areas, ensuring that a wide
range of sediment textures are included.
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Table 3
PRE-INDUSTRIAL (PRIOR TO 1900) CONCENTRATION
OF TRACE ORGAN1CS IN PUGET SOUND SEDIMENTS
Concentration
6.0
0.04
0.04
25
6.0
80
13
378
337
175
-0-
given are mean of five measure-
ments made at depths greater than 150
cm in sediment cores from Elliott Bay,
Brown's Point, and Meadow Point (from
Pavlou, et al.. 1983).
bMetal concentrations expressed in vg/g
dry weight, organic concentrations
expressed in ng/g dry weight.
Compounds
Pb
Hg
»
Ag
Cu
As
Zn
PCBs
Phchalaces
CPNAs
PNAs
DDTs
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2. Develop a regression equation for the relationship between
organic carbon content (or a covariate) and pollutant burden.
3. Determine the extent of departure from this regression line,
based on the variability of the data, which would Indicate
contributions from a local discharge and constitute a criteria
violation.
Unlike all other approaches considered in this report, this approach is unique
in that it is not necesary to assess the toxicity of a pollutant since any
increase in concentration above background is considered undesirable. How-
ever, for many compounds this may be unnecessarily restrictive, for the
environment may be capable of assimilating additional inputs above background
levels with no adverse effects. The optimal approach may eventually involve
use of information on toxicity of specific compounds to establish the
permissable degree of enrichment above background for these compounds.
i
Enough data is presently available on levels of pollutants in relatively.clean
areas of Puget Sound to establish tentative background levels though addi-
tional sampling may be necessary before final criteria can be adopted. It is
important to note that criteria established on the basis of background
concentrations would probably be valid for only site specific usage since
natural variability in background concentrations can be substantial due to
geochemical differences.
2.3 ESTABLISHMENT OF CRITERIA BASED ON EPA WATER QUALITY CRITERIA
The attempt by EPA Region VI to develop Sediment Quality Indicators was
discussed in Section 1.2. The approach used was simply to employ EPA water
quality criteria, without adjustment, to Interstitial and elutriate waters.
An advantage of this approach, and all others based on EPA water quality
criteria, is that they are able to make use of the large toxicologlcal data
base incorporated In the establishment of the water quality criteria. These
criteria incorporate the results of a great number of bioassays in which a
variety of water column organisms were exposed to dissolved pollutants. If
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bloassays with water column organisms are equally valid for infaunal biota,
Chen Che Region VI approach eliminates Che need for a costly and time-
consuming redevelopment of a new sediment-oriented Coxlcological data base.
The applicability of water quality criteria to benthic organisms is a question
that will require extensive verification prior to general acceptance. The EPA
Region VI approach neglects the potential for direct biota-sediment pollutant
transfer without the mediation of interstitial water. The importance of
direct biota-sediment transfer processes cannot be adequately evaluated on the
basis of existing information, but its potential contribution may be substan-
tial. For example, ingestion of sediment and an associated toxicant by a
deposit-feeding organism may result in a greater biological uptake of toxicant
than would occur simply by exposure to the comparatively low concentrations of
the toxicant in interstitial water.
i
A second difficulty of the EPA Region VI approach lies in the sampling and
analytical difficulties encountered in attempting to quantify pollutant con-
centration in interstitial water. The concentrations of most pollutants in
interstitial water are so low that it is difficult to obtain a sufficient
volume of interstitial water to permit accurate quantitation of pollutant
levels. The very act of extracting interstitial water from the bulk sediment
can substantially alter the chemical content of Che water so obtained.
2.4 ESTABLISHMENT OF CRITERIA ON THE BASIS OF EQUILIBRIUM PARTITIONING
2.4.1 Basic Definitions
The concept of equilibrim partitioning has been used extensively in past
studies to predict the accumulation of contaminants in the aquatic environment
(Pavlou, 1980; Pavlou and Dexter, 1979; Dexter and Pavlou, 1978; Pavlou and
Dexter, 1977; Clayton et al., 1977; Neuhold and Ruggerio, 1977; Chiou et al.,
1977; Issacs, 1975; Metcalf et al., 1975; Neely et al., 1974; Hamelink, 1971;
Grzenda et al., 1970; Gakstatter aru Weiss, 1967; Ferguson et al., 1966).
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The pathways of contaminant transport among sediment, biota, and water at the
sediment water Interface can be conceptualized as shewn In Figure 1. This
mechanism assumes that the system is at equilibrium and that the instantaneous
concentration of a conservative contaminant in any one of the three components
can be expressed as a function of its concentration in either of the other two
and an appropriate constant. These constants have been used extensively to
determine accumulation In both abiotic and blotic components. In the former
case, they are commonly referred to as partition or sorption coefficients
while in the latter case they are being referred to as bioconeentration
factors. These quasi-equilibriua constants are defined below:
Sediment-Water Partition Coefficient (KD):
v m Concentration in Sediment
TJ Concentration in Interstitial/Interfacial Water
Bioconeentration Factor (BCF):
BCF » Concentration in Biota
Concentration in Water
Accumulation Relative to Sediment (ARS):
AUS m Concentration in Biota
Concentration in Sediment
Sediaent-Vater Partition Coefficient
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Figure 1
CONCEPTUAL REPRESENTATION OF CONTAMINANT PATHWAYS
AT THE SEDIMENT/WATER INTERFACE
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Anocher Independent estimate of KQ for Che organic compounds listed above was
obtained based on the octanol-water partition coefficient Kgy. The relation-
ship between KD ant* ^OW was established from the regression depicted in Figure
2 as obtained from literature data. KD values from the literature were
expressed on a sediment organic carbon basis. The KD values for the compounds
measured In Puget Sound were then calculated from values of KgW. Table 4
compares the field determined KD values with those obtained from the KQVJ
relationship. The agreement is good considering the associated uncertainties
In both quantities.
Bioconcent ration Factor (BCF) - These constants have been determined for many
compounds by both field and laboratory studies and are available in the scien-
tific literature. For these chemicals for which BCF values are unavailable,
they may be estimated on the basis of KOW (Veith et al., 1980; Gossett et al.,
1982). ' The relationship between these factors uas established for 36 com-
pounds reported in Puget Sound for which literature values for both BCF and
KQW were available (Figure 3). The regression equation was then used to
determine BCF for additional organic compounds for which K^y •was known.
Accumulation Relative to Sediments (ARS) - Although the ARS quantity does not
reveal the bioaccuaulation mechanism, it provides a tool for estimating the
potential accumulation in biota from the apparent contaminant burden in the
sediment. Typical ARS values are presented in Table 5 for various synthetic
organic compounds measured in Puget Sound. It can be seen that the chlori-
nated hydrocarbons show distinctly higher ratios than the polynuclear aro-
matics, reflecting the low reactivity of the chlorinated organics vs. the
higher reactivity (higher biotransformation potential) demonstrated by the
polyaromatic compounds.
If a large data base of biota and sediment concentrations is available, then
these constants may provide a gross indicator of bioaccumulation patterns
specific to classes of compounds.
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Q
u:
00
o
3
>-chlo«iblph»rl
ltnl° '
• k-chlerott»litnf I
J-chlotublpt»nrl
k»iyl
t-IIIC
log K = 0.931 log Kou - 0.697
r = 0.869
a < 0.01
t l.l-JIchlotopropint
Of 234S67B
log KIH|
Figure 2
REGRESSION PLOTS OF SEDIMENT SORPTION COEFFICIENT WITH OCTANOL-WATER PARTITION COEFFICIENT
(values taken from Dexter, 1976; Dexter, 1979; Kenaga & Coring, 1980;
Veith et al., 1980; and Versar, Inc., 1979)
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Table I*
COMPARISON OF FIELD DETERMINED KDs WITH VALUES
OBTAINED FROM THE KD vs. KQW RELATIONSHIP
KnxlO1*
Contaminant
PNAs
CPNAs
PCBs
As
Be
Cu
Pb
Hg
Zn
Field
(mean » sd)
0.8± 2
4*7
4±7
2±0.6
0.5 ±0.3
20
90
300
20
From KOW
Regression*
(mean * sd)
0.2* 22
20*15
9* 11
^Standard deviations (sd) are expressed as « rather
than ± since they are antilogs computed from the
original log-log regression in Figure 2.
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6H
• 4-4-DOT
.4-t-DOt
5-
4-
U
n
M
o
3-
4-chl«roblph«nyl . * .
* }-oblph«nrl • •• t-cMoioblph«n|l
- « /
4.4.0DD
Hcuchlorobuiidltnt •
• Chloiobtnitni
nio (A) inihr*cciit •
X
lOI-N
• N(il«l« •
Nllrebcnitnt •
1-
.A-IIIC
•l.l-4lchleiabtni«nl
• l.l-4lclilofabriiiiii«
• Ctibun ItlfiihlaMJr
()'c>ilara>lhrl) tikcr
•Chlareleia
.ftIf(Chiefoclhylin*
* Tf UMotoclhrltnt
log BCF - 0.74 losKow-0.075
r • 0.831
a < 0.01
• l.2-tflchlaro«ihii»
CD
n
I
RECKESSION PLOTS OF BIOCONCENTRATION FACTORS WITH
OCTANOL-WATCR PARTITION COEFFICIENTS
(values taken from Dexter, 1976; Kenaga &
CorlnR, 1980; Veith et al., 1980; Versar,
Inc., 1979)
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Table S
ACCUMULATION OF SELECTED TRACE ORGANIC COMPOUNDS
IN BENTHIC BIOTA OF PUGET SOUND RELATIVE TO SEDIMENTS3
ARSb
Crab
Compound Worn Shrimp Clam (Hepacop) Fish Liver
ARENES
1-2 Ring AHs 0.2*0.1 0.2*0.1 0.2*0.1 0.7*0.6 0.3*0.4
3-5 Ring AHs 0.32*0.22 0.13*0.07 0.36*0.18 0.05*0.01 0.05±0.06
Phenanthrene
i
Benz (a) anthracene
Benz(a)pyrene
CHLORINATED
HYDROCARBONS
Chlorinated
Pesticides
Chlorinated
Butadienes
Polychlorinated
Biphenyls
Hexachlorobenzene
<0. 7
0.9*0.6
0.6±0.5
1.7 * 1.1
1.3* 1.7
11 * 12
17* 19
<0.3
0.14* 0.06
<0.2
1.7 * 1.4
(3)C
15 ± 20
8.1 ± 5.6
<0.3
<0.54
<0.4
2.7* 2.9
(0.22)C
5.4* 5.4
4.0* 1.0
0.15 ±0.1
<0.06
0.02± 0.01
61 * 32
(0.2)c
77*33
74 ± 68
<0. 1
<0.27
<0.6
34* 23
1.3S 1.7
111 * 163
931 55
Based on data from Malins et al., 1980.
Accumulation Relative to Sediment (ARS), is defined as the ratio of the concen-
tration of a specific chemical in an organism (or specified tissue) to its
ambient concentration in the sediments.
Values in parentheses are from analyses of only one or tvo samples.
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2.4.2 Application of Partitioning Constants to the Development of .
Sediment Criteria
Four approaches were considered in establishing sediment criteria based on
sediment/water/biota Interfacial constants (Figure 4). All of these
approaches rely heavily on existing water quality criteria for priority
contaminants and the availability of biota threshold values above which a
toxic effect may occur.
Approach 91. uses KQ and the existing EPA water quality criteria (applied to
interfacial water) to compute a sediment threshold concentration. This cal-
culated value is then compared to the actual measured contaminant concentra-
tion in the ambient sediment of a designated site to estimate the extent of
violation. Conversely, using the ambient sediment burden and KD the
interfacial water concentration can be computed and compared directly to the
apropria-te &PA water criteria value.
Approach #2. is based on the application of water quality criteria to inter-
facial waters and the use of the BCF to compute a biota burden. The sediment
threshold value can then be calculated by using the ARS constant. Indirectly,
the computed biota burden may be compared to an existing body burden -.level
known to induce a toxic effect.
Approach 93, uses the ARS quantity with either a measured body burden which
induces a toxic effect (e.g., pathologic, behavioral or metabolic effect) or a
federally established tissue concentration (if public health risks are the
prime consideration) to compute a sediment threshold level.
Approach 04. is a combination of the above. It establishes a biological
threshold concentration and determines a corresponding sediment threshold
value via contaminant transfer through the aqueous phase.
lpa Associates _
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t
N)
/ "CRITERIA 1
I-
APPROACH 01
APPROACH n
"THRESHOLD I ^. J STHRESHOLD J
APPROACH
APPROACH 04
Figure 4
SCHEMATIC REPRESENTATION OF SEDIMENT CRITERIA DEVELOPMENT USING
EQUILIBRIUM PARTITIONING CONSTANTS
-------
The advantage of using partitioning'constants to establish sediment criteria
is that (1) the approach makes use of the toxicological data base that allowed
for the formulation of the EPA water quality criteria and (2) the approach can
be implemented immediately to establish a first-order approximation criteria
using existing data and some nominal field verification. However, this
approach is also limited by a number of factors: (1) the field derived KQS
which are based on SPM/water partitioning nay not be applicable to sediment/
interstitial water partitioning because of the different chemical conditions
of the sediments; (2) as discussed in Section 2.3, sediment criteria estab-
lished on the basis of EPA water quality values (Kn approach) do not address
direct sediment-biota contaminant transfer; (3) since Approaches 92 and /M
involve the use of multiple partitioning constants, they have a greater poten-
tial for error propagation; >and (A) the ARS constant does not address the
bloaccumulation mechanism.
2.5 ESTABLISHMENT OF CRITERIA ON THE BASIS OF BIOLOGICAL RESPONSE
2.S.I Bioassays
Bioassays have been employed nationwide and particularly in the northwest
region, to evaluate the toxicity of dredged material and sediments of polluted
harbors (Swartz et al., 1979; 1982; Chapman et al., 1982; Plerson etj al.,
1983). Though significant methodological differences among investigators
remain unresolved (i.e., selection of test organism, preparation of sediment
sample), the approach adopted by EPA/COE for evaluation of dredge spoils
involves laboratory exposure of test organisms to bulk sediment for a ten day
period after Jhich the number of dead organisms are counted (U.S. EPA/COE,
•
1977). Survival in the test sediments relative to that in control sediments
is taken as the biological response criterion. If sediment criteria for Puget
Sound are to be based on a biological response (percent mortality) rather than
a chemical burden (concentration) basis, then the sediment bioassay is of
immediate utility provided methodological questions can be adequately
resolved.
_ JRB Associates _
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A limitation of evaluating sediment toxicity of chemically-uncharacterized
sediment by current bloassay techniques Is that the chemical agent or agents
responsible for observed mortalities remain unidentified. Therefore, while
bioassays are valuable in assessing toxicity of sediments, their regulatory
use is limited by the fact that they provide no guidance for the establishment
of appropriate control measures. Bioassays, as presently employed, serve as a
pass/fall test without identifying Che corrective measures required.
Researchers at the EPA-NERC laboratories in Newport, Oregon are currently
developing a technique to Identify the pollutant or pollutants responsible for
observed mortality in sediment bioassays (Swartz, personal communication).
The technique involves eight steps:
1. Determine toxicity of a polluted sediment by standard
amphipod sediment bioassay
i
2. Chemically analyze sediment to Identify pollutants present and
their respective concentrations
3. On the basis of the magnitude of concentrations, bioaccumu-
latlon potential, and toxicological information in the litera-
ture, rank pollutants according to potential for inducing
amphipod mortality
4. Identify the highest ranking compounds and spike the original
sediment sample with these compounds
5. Reevaluate toxicity of sediment by same bioassay procedure
6. If toxicity of sediment has not increased, select alternative
compounds and repeat procedure
7. If toxicity of sediment has increased, continue spiking sedi-
ment at successively higher levels to obtain dose-response
relationship
8. Spike clean sediments with same compounds to evaluate toxicity
at comparatively low levels of contamination
Spiking of sediment with several contaminants simultaneously provides a
mechanism to address synergism. Synergism or antagonism can modify the
toxicity of a mixture of pollutants such that the toxicity of the mixture
____^ JRB Associates —
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cannot be predicted simply by knowing the toxlclty of each of the components.
Given our current state of knowledge, there Is no means to predict, on a
chemical basis alone, the toxicity of sediment containing a multitude of
pollutants, and bioassays remain the only means to account for synergistic
effects.
Sediment bioassays can potentially be used to develop sediment quality
criteria precisely in the same manner that aqueous bioassays were used to
develop existing water quality criteria. The simplest approach to develop
sediment criteria in this manner is to spike clean sediment with known
concentrations of a pollutant and derive a dose/response relationship. Such
an approach has been pursued to evaluate the toxicity of cadmium (Swartz,
personal communication) but for the most part, data of this kind are lacking.
Development of criteria in this manner would not address synergistic effects
but this may be a necessary simplification in the establishment of first-cut
criteria.
2.5.2 Biological Field Surveys
Several previous attempts by other investigators to establish sediment quality
guidelines (Section 1.2) made use of biological field surveys to establish
threshold levels of pollution. The general approach was to correlate sediment
pollutant burden in a wide variety of habitats with some measure of benthic
community health (e.g. diversity, abundance, species richness) and attempt to
establish a threshold value for each chemical below which no biological
effects were observed. A similar approach is currently being pursued by
NOAA/NHFS by attempting to relate incidence of histopathological abnormalities
in fish with levels of contaminants in the sediments of Puget Sound (Maiins et
al., 1982; McCain, personal communication).
Th. greatest difficulty encountered in attempting to establish criteria by
thfo approach is In determining the contaminant(s) responsible for an observed
impact on the biological community. If only one chemical was substantially
______________________ JRB Associates
24
J
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enriched above background levels then an observed biological response could be
accrlbuted co that chemical and a threshold, value established. However, in
most areas a diverse suite of contaminants are simultaneously enriched and it
is impossible to identify the causative agents responsible for observed bio-
logical Impacts. Multlvariate techniques have been applied in an attempt to
identify contaminants responsible for biological effects (Malins et al., 1982)
but Che relationships observed by these techniques are correlative rather than
causative.
Biological field surveys can also be applied in sediment criteria development
by establishing some measure of biological health as a criterion, in much the
same way that a certain mortality is considered a criterion in bioassays of
dredged material. Criteria can be based upon diversity indices, species even-
ness, species richness, presence or absence of Indicator species, producti-
vity, or some measure of similarity to a reference site. Sediment quality
would be considered to be in violation of criteria if indigenous communities
demonstrated some level of alteration beyond a threshold value. Benthic
organisms are the most appropriate indicator organisms for use in this manner
because of their Immobility and the high sensitivity of some groups to a wide
variety of pollutants.
The use of benthic organisms as Indicators of sediment quality has already
been Incorporated in the 301(h) section of the Federal Water Pollution Control
Act. Sediment quality criteria based on an indicator of benthic community
health could potentially be used to evaluate the toxicity of dredge spoil or
monitor environmental quality in the vicinity of point source discharges.
There are two major limitations in use of sediment criteria based on field
surveys of benthic communities. First, natural spatial and temporal vari-
ability of benthic communities often confounds efforts to ascribe an observed
change directly to a pollution impact. Secondly, unacceptable environmental
degradation is only detectable after the fact and the success of control or
clean-up measures can only be evaluated after adequate time (a few months to
several years) is provided to permit the benthic community to reflect a change
in environmental quality.
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2.6 ENVIRONMENTAL DEGRADATION ASSESSMENT
Three approaches useful In Identifying contaminated areas in need of remedial
action deserve special mention because of their potential application to
sediment criteria development. These approaches are:
• A multidisciplinary approach under development by NOAA (Long, 1983)
• A sediment-oriented ecological risk index (Hlkanson, 1980)
• A quality degradation factor under development by JRB
2.6.1 NOAA Approach
In recent years NOAA has been developing an approach to assessing toxicant
levels in Puget Sound and Identifying sites most urgently in need of clean-up
activities (Chapman and Long, 1983; Long, 1983; Long, personal communication).
The approach currently involves a three-tiered assessment of the extent of
environmental degradation. First, chemical analyses of surficial sediments in
the area are performed to establish the type and degree of contamination
relative to reference areas. Secondly, bioassays are performed using both
impacted and reference sediments to determine if the observed levels of
contamination are sufficient to Induce an adverse biological response through
direct exposure. Finally, a field survey of the benthic communities is
performed to establish if the contamination has induced a demonstrable charge
in the resident biota.
The approach proposed by NOAA can be considered to be a conglomerate of the
individual approaches discussed in Sections 2.2, 2.5.1, and 2.5.2. As a sedi-
ment criterion, this approach is too costly and labor-intensive for general
use. However, since examination of sediment pollutant burden, bioassay toxi-
city, and benthic community structure would provide a good measure of the
extent of environmental degradation, the approach may be useful for field
verification of any tentative criteria established.
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2.6.2 Ecological Risk Index
The ecological risk index of fUkanson (1980), and che Quality Degradation
Factors which follow in Section 2.6.3, are both indexing methods to assess the
relative extent of environmental degradation. It is important to note that as
they currently stand, both these techniques are ranking tools rather than
enforceable criteria. While they do provide an Indication of which sites show
the most severe environmental alterations, they do not establish a criteria or
threshold value above which remedial measures are required. The key advantage
of indexing methods is their ability to synthesize a diverse body of technical
information into a non-technical tool to identify sites and contaminants of
concern. They are Included in this report as a basis for criteria development
with the expectation that further refinement of the techniques may eventually
provide a tool for environmental policy decisions and a basis for initiating
remedial action.
i
HSkanson (1980) developed an ecological risk Index to evaluate the extent of
contamination in several Swedish lakes and obtain some estimate of the poten-
tial for adverse biological effects. On the basis of sediment contaminant
burden the index considered:
• The enrichment of each pollutant relative to ore-industrial levels
• The. xotal enrichment of all pollutants considered
• The relative toxicity of the pollutants present
• The sensitivity of the receiving water body to the pollutants present
All the above factors ware considered by inclusion in an equation which
yielded an ecological risk index (RI). Specific detailes are presented in
Appendix B. Rl values less than 150 indicated a low ecological risk for the
area, while RI values above 600 indicated a very high ecological risk. The
Index includes a number of ieatures which make It attractive for use in Puget
Sound, though some modifications would be required to include additional
pollutants of concern and adopt the index for marine rather than freshwater
environments.
. JRB Associates —.
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QDF - (1 - Bray/Curtis similarity relative to control) x 100
or
QDF - (1 - no. of species present at site ) x 100
no. of species present at control
The QDF quantities can be expressed In terms of a multiplicative or cumulative
contribution of various physical, chemical, biological, or toxicological para-
meters including contaminant concentrations in sediments, biota and inter-
stitial water, bioassay lethality indicators (e.g., percent mortality),
pathologic parameters (percent diseased organisms) and taxonomic indicators of
community stress. An overall QDF can be determined as well as QDFs for each
of the Individual components. Component QDFs can be assigned a weighting
factor if degradation of one factor is of more concern than another. The
precise equations and weighting factors are still under development but the
general approach is illustrated in the sample calculation of Appendix C.
2.6.3 Quality Degradation Factors
JRB is currently developing an index of overall environmental quality based on
the expression:
QDF - ACTUAL - CONTROL
MAXIMUM - CONTROL
where QDF is the relative quality degradation Index applicable to a given
site. ACTUAL is the actual value of the parameter determined at the site in
question, CONTROL is the same parameter measured at a control or reference
site, and MAXIMUM represents the maximum effect (or worst case scenario). The
value of QDF may vary between 0 and 100 with the latter indicating
degradation.
Obtaining QDF values with regard to contaminants in sediments, interstitial
water or biota is straightforward. Background concentrations can be obtained
either from an unpolluted control area or, in the case of sediment contami-
nants, from deeply buried sediments sampled by a coring device (Pavlou, et
•1., 1983). The maximum concentration would be the highest recorded level of
contamination ir. the sediments, interstitial water or biota of Puget Sound.
28
> JRB Associates „
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QOF factors can also be determined for the bioassay and pathology parameters
by considering the percent mortality or percent diseased organisms, respec-
tively, relative to a control and a maximum possible value (100Z). If the
controls induced no mortality in the bioassays or showed no evidence of
hlstopathological disorders then QDF would reduce to percent mortality or the
percent of organisms with histopathological abnormalities.
For the benthic community indicators, the QOF could be defined by possible
indices of community health such as:
JRB Associates _
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3.0 APPLICATION SCENARIOS
There are five major environmental quality related regulatory decisions
affecting Puget Sound to which sediment criteria are directly applicable:
• The issuance of CWA Section 301 (h) waivers
• The issuance of CWA Section 404 dredge and fill permits
• The designation or redesignatlon of dredged material disposal
sites
• The selection of remedial alternatives at three of the ten
designated Superfund sites in the State of Washington (The
Nearshore/Tldeflats and South Tacoma Channel sites in
Commencement Bay and the Harbor Island site in Elliott Bay)
• Issuance of NPDES permits
i
For the reasons presented in Section 1.0, sediment criteria are considered to
be a more effective means of preventing contaminant build up as well as eco-
logical degradation of the marine environment than what can be achieved with
the currently available water quality criteria. As part of this study it was
therefore deemed appropriate to examine the applicability of sediment criteria
to these major regulatory decisions. This section of the report presents a
number of possible scenarios where the approaches discussed earlier could be
used, under the major regulatory decisions presented above, to facilitate the
development of a management action plan involving either remedial action or
the formulation of control/enforcement/compliance protocols.
3.1 ISSUANCE OF CWA SECTION 301(h) WAIVERS
Under Section 301(h) conditions upon which modification of the secondary
treatment requirement in the NPDES permits may be allowed, include three items
to which the establishment of sediment criteria could be directly applicable
and beneficial: (1) applicable water quality standards must be in place; (*•*
no Interference with a water quality that assures protection of public wate
supplies; protection and propagation of a balanced indigenous population of
shellfish, fish and wildlife; and that allows recreational activities and (3)
an established system for monitoring the Impact on representative biota.
-- JRB Associates —
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Recent studies completed in the central basin of Puget Sound (Pavlou et al.,
1983) have revealed that existing water quality criteria levels for toxicants
are not exceeded in the water column even within the immediate vicinity of
point source discharges including STPs and CSOs. However, in the sediments
the concentrations are sufficiently elevated to cause localized biological
effects. It Is obvious that in Puget Sound the degree of environmental pro-
tection achieved by enforcement of water quality standards is questionable.
The applicability of optimum sediment criteria to control effluent quality may
involve setting up discharge limits commensurate to an acceptable sediment
threshold. The optimum criteria may be based on one or a combination of the
approaches presented in Section 2.0. Compliance with discharge limits may
include statistically allowable deviations during periods where there is a
high probability of exceeding a threshold value and the determination of the
total variability (field and analytical) associated with measurements of
contaminant* concentrations. Enforcement of these limits should take into
account these statistical considerations to establish the legal definition of
what constitutes a "violation".
The build up and/or reduction of contaminant concencracions in the sediments
may be estimated by employing a site specific mass balance model similar to
that used by Pavlou et al. (1983).
3.2 ISSUANCE OF CWA SECTION 404 DREDGE AND FILL PERMITS AND
DESIGNATION OF DREDGE MATERIAL DISPOSAL SITES
The key element within this decision issue is evaluation of the acceptability
of dredged material for open water disposal. Criteria for this evaluation are
already established under current federal regulations (U.S. EPA/COE, 1977).
These regulations require that the solid phase of all material intended for
open water disposal be evaluated by sediment bioassays employing three
representative species, unless certain exclusionary guidelines are met. If
toxicity of the tese sediment exceeds that of controls, the >«rait may be
denied.
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The general utility of bioassays are limited by the fact that the procedure
does not identify the contaminant or contaminants responsible for the observed
toxicity, providing no Information on appropriate remedial action. However,
since no corrective measures are addressed in evaluating the acceptability of
dredged material, bioassay techniques represent the best available technique
co make this evaluation, given our current state of knowledge on chemical
toxicity.
3.3 SELECTION OF REMEDIAL ALTERNATIVES AT SUPERFUND SITES
This decision may be based on the application of an integrated indexing method
as described in Section 2.6. Sites would be ranked according Co the magnitude
of a sediment degradation factor and compared to an a priori estimated
»
threshold value. A management action plan could then proceed according to a
decision scenario similar to the one shown in Figure 5.
There is a sufficient data base currently available for testing a ranking
approach at designated sites in Commencement Bay and Elliott Bay, but further
work is needed to establish threshold values.
3.4 ISSUANCE OF NPDES PERMITS
Any of the approaches presented In Section 2.0 could be applicable in estab-
lishing criteria based on either control conditions in the vicinity of an
existing discharge or current ambient conditions at sites where the proposed
facilities would be installed. However, an optimum approach could be to rank
the sites based on an indexing method similar to what has been proposed in
Section 2.6 and establish an unacceptable level of sediment quality. Effluent
requirements necessary to maintain sediment quality below a threshold value
could be forecasted. Considerations of effluent physical transport and
dispersion as governed by the ambient hydrodynamic and sediment transport
J processes should also influence the decision on effluent contaminant limits.
This can be accomplished by already developed transport and fate models
appropriately modified for application to the particular site.
_ JRB Associates -
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Determine Actual
•nd Threshold
Sediment Criteria
Dous
Actual
Value, Exceed
reehold'
Deceratne
Significance of
Contamination
(Spatial/Temporal)
No leased late
Remedial Action
Ncceeaary
la
ntanlnatlon
Historical?
Forecaat
Recovery
la
Recovery
Faat?
Implement
Remedial Action
Plan (Clean up,
lource control)
Develop/Implement
Long Term
Monitoring Plan
Develop
Compliance/
Enforcement Plan
Figure 5
DECISION SCENARIO FOR MANAGEMENT ACTION PLAN
AT SUPERFUND SITES INVOLVING SEDIMENT CRITERIA
.JRB Associates-.
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4.0 SUMMARY AND CONCLUSIONS
The current state of knowledge regarding sediment criteria was updated and
summarized. Five major approaches were identified and then ranked according
to nine ranking criteria: adequacy of the existing data base, development
costs, application costs, availability of methodology, cost effectiveness,
relative completexity, adaptability to new compounds and utility to management
division. The results are presented in Table 6.
Among the major categories of approaches listed, approaches based on bio-
logical response and the ranking schemes included in these evaluations scored
higher than the approaches which involved primarily chemical burden and bio-
concentration considerations. This Is not surprising, since the inherent
utility of establishing sediment criteria is to develop a tool for controlling
ecological degradation and minimizing potential human health risks. Both
biological approaches and ranking schemes account for these factors with the
ranking schemes appearing more favorable In that they address biological
effects associated with an observed chemical burden or enrichment in the
sediments. As pointed out in Section 2.6 the integrated assessment schemes
suffer from one major limitation: they are not as easily enforceable as, for
example, a combination of a biological response approach and criteria based on
equilibrium partitioning.
In addition to the overall ranking approaches on the basis of development and
implementation considerations there are a number of specific concerns which
need to be addressed in the establishment of sediment criteria:
• Influence of sediment organic content
• Implications of synergism/antogonism
• Temporal considerations in criteria enforcement
If sediment criteria are to be expressed In terms of a permissable concen-
tration, the impact of sediment organic content on contaminant burden and
.JRB Associates..
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Table 6
SEDIMENT CRITERIA RANKING
(L=Low, M = Medium, II "High, N/A » Not Applicable)
30
03
!
n
E'
ra
1
Approach
2.2 Background Levels
2.3 EPA Region VI
2. >i Partitioning:
SI - KD
; n - BCF/ARS
03 - ARS
H - BCF/KD
2.5 Biological Response:
2.5.1 Bloassay:
Unsplked Sediment
Spiked Sediment
2.5.2 Field Surveys:
Burden/Effect Relationship
Community Monitoring
2.6 Environmental Degradation Assessment*
NOAA/OMPA
Ecological Risk Index
Quality Degradation Factors (QDF)
*M
o
01
x *o w
U C IQ
cfl T-< O3
tr m «
01 1-1 U
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< CO Q
M
M
M
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L
N/A
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u
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•^ T> C
A -a x
L
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11
L
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•H a
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id 5 3
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id B
•a o o
< u o
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» ~*
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L
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II
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II
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H
« approaches are ranking methods designed to evaluate the relative degree of environmental degradation and
,uld be considered as aids for decision criteria her than sediment criteria.
-------
toxicity must be addressed. Not only does Che organic content of the sediment
effect the concentration of most contaminants, but it is also of major impor-
tance in determining bioavailability. For example, addition of small quan-
tities of sewage sludge to sediment can dramatically reduce the toxicity of
cadmium relative to sediments containing no sewage sludge (R. Swartz, EPA/
NERC, pers. comm.). Given equal contaminant burden, a sediment containing a
high proportion of organic carbon would be less toxic than a sediment con-
taining relatively little organic material.
An approach to addressing this issue which deserves further consideration is
to establish sediment criteria on the basis of organic content in much the
same way as EPA freshwater quality criteria for metals are based on water
hardness. The greater the water hardness the higher the pennlssable metal
concentration in the water. A similar approach for sediment quality criteria
could be based on organic content or a covariate such as percentage of silt
and clay or total volatile solids.
The effects of synergism and antagonism present a major difficulty in the
establishment of valid sediment criteria. There is presently no way to
predict the toxicity of a mixture of contaminants, given the toxicicy of each
of the individual components. Often the simultaneous action of several con-
taminants can have a much greater biological impact than would be predicted by
the sum of their individual effects. As applied to sediment criteria, this
implies that adherence to criteria established on the basis of individual
contaminants will not necessarily provide adequate protection against the
biological impacts of a mixture of contaminants.
Biological response criteria (bioassays, community analysis) provide the only
means to address synergism given our current state of knowledge. Establish-
ment of chemical criteria on an individual compound basis may be a necessary
simplification in the development of first-cut criteria. However, some
measure of biological response must be an integral component in application of
these initial criteria to adequately protect against synergistic effects.
, JRB Associates —
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Sediment criteria could potentially be used in point source control appli-
cations. Should sediment contaminant levels in the vicinity of a discharge
exceed established criteria, effluent control procedures would be appropriate.
An important consideration which must be addressed at this stage is the
recovery period necessary for • contaminant concentrations in surficial sedi-
ments to return to permissable levels. Since sediments serve as a reservoir
for most contaminants, their concentration in sediments would not be expected
to drop dramatically even if contaminant inputs were eliminated entirely. The
success or failure or effluent control measures could not be evaluated on the
basis of sediment criteria until sufficient time had elapsed to permit burial
of contaminated sediments by deposition of clean sediments. Depending upon
local sedimentation rates, natural depositional processes may be considered
too slow for burial of heavily contaminated sediments, and dredging or capping
may be required.
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5.0 REFERENCES
Armstrong, J.W., R.M. Thorn, K.K. Chew, B. Arpke, R. Bohn, J. Clock, R.
Hieronymus, E. Hurlburt, K. Johnson, B. Mayer, B. Stevens, S. Tettleback,
and P. Wacerstrat. 1978. The impact of the Denny Way combined sewer
overflow on the adjacent flora and fauna in Elliott Bay, Puget Sound,
Washington. College of Fisheries, Univ. of Wash., Seattle. 102 pp.
Chapman, P.M. and E.R. Long. 1983. The use of bioassays as part of a
comprehensive approach to marine pollution assessment. Mar. Poll. Bull.
14(3):81-84.
Chapman, P.M., G.A. Vigers, M.A. Farrell, R.N. Dexter, E.A. Quinlan, R.M.
Kocan, and M. Landolt. 1982. Survey of biological effects of toxicants
upon Puget Sound biota. 1. Broad-scale toxlcity survey. NOAA Tech.
Memo. OMPA-25, National Oceanic and Atmospheric Administration, Boulder,
CO. 96 pp.
Chiou, C.T., V.H. Freed, S.W. Schmedding, R.L. Kohnert. 1977. Partition
coefficients and bioaccumulation of selected organic chemicals. Environ-
mental Science and Technology 11:475-478.
Clayton, J.R., S.P. Pavlou, and N.F. Breitner. 1977. Polychlorinated
blphenyls in coastal marine 200plankton: bioaccunulacion by equilibrium
partitioning. Environmental Science and Technology 11(7):676-682.
Dexter, R.N. 1976. An application of equilibrium adsorption theory to the
chemical dynamics of organic compounds in marine ecosystems. Ph.D.
dissertation, Univ. of Wash., Seattle. 181 pp.
Dexter, R.N. 1978. Distribution coefficients of organic pesticides in
aquatic ecosystems.' Report submitted to Battelle Pacific Northwest
Laboratories, Rlchland, WA.
Dexter, R.N., and S.P. Pavlou. 1978. Distribution of stable organic
molecules In the marine environment: physical chemical aspects;
chlorinated hydrocarbons. Marine Chemistry 7:67-84.
Ferguson, D.E., J.L. Ludke, and C.G. Murphy. 1966. Dynamics of endrine
uptake and release by resistant and susceptible strains of mosquito fish.
Transactions of the American Fisheries Society 95(4):335-344.
Cakstatter, J.H., and C.M. Weiss. 1967. The elimination of DDT-C14,
Dieldrin-C14, and Lindane-C14 froa fish following a single sublethal
exposure in aquaria. Transactions of the American Fisheries Sociecy
96(3):301-307.
, JRB Associates —
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Crzenda, A.R.. D.F. Paris, and W.J. Taylor. 1970. The uptake, metabolism,
and elimination of chlorinated residues by goldfish (Carasslus auratus)
TranSaCCionS of the
Hlkanson L. 1980. An ecological risk' index for aquatic pollution control.
A sedimentological approach. Wat. Res. 14:975-1001.
R'C' Wfyb""» and R-C- Bal1- «71 • A proposal: exchange
control the degree chlorinated hydrocarbons are biologically
Tran"cCions of the ^^c" Fisheries
Issacs, J.D. 1975. Assessment of man's impact on marine biological
resources, pp. 329-340 ^n Marine Pollution and Marine Waste Disposal,
E. Pearson and E. DeFraja Frangipane (eds.). Pergamon Press, Ltd. New
• w f K •
Kenaga, E.E. and C.A.I. Goring. 1980. Relationship between water
solubility, soil sorption, octanol-water partitioning, and concentration
rh ^H? ^i8 ln"ota' PP. 78-115 In Aquatic Toxicology, Proceedings of
the Third Annual Symposium on Aquatic Toxicology ASTM Spec. Tech. Publ .
Long, E.R. 1983. A multidisciplinary approach to assessing pollution in
coastal waters, pp. 163-178 In Proceedings of the Third Symposium on
Coastal and Ocean Management, ASCE/San Diego, CA.
Malins, D.C., B.B. McCain, D.W. Brown, A.K. Sparks, and H.O. Hodgins. 1980.
Chemical contaminants and biological abnormalities In central and
southern Puget Sound. NOAA Tech. Memo. OMPA-2. National Oceanic and
Atmospheric Administration, Boulder, CO. 295 pp.
Malins, D.C., B.B. McCain, D.W. Brown, A.K. Sparks, H.O. Hodgins, and S-L.
Chan. 1982. Chemical contaminants and abnormalities in fish and
invertebrates from Puget Sound. NOAA Tech. Memo. OMPA-19. National
Oceanic and Atmospheric Administration, Boulder, CO. 168 pp.
Metcalf, R.L., J.R. Sanborn, P.Y. Lu, and D. Nye. 1975. Laboratory model
ecosystem: studies of the degradations and fate of radiolabelled tri-,
tetra-, and pentachlorobiphenyls compared with DDE. Archives of
Environmental Contamination Toxicology 3:151-165.
Neely, W.B., D.R. Branson, and C.E. Blau. 1974. Partition coefficients for
measuring bioconcentration potential of organic chemicals in fish.
Environmental Science and Technology 8:1113-1115.
Neuhold, J.M., and L.F. Ruggerio. 1975. Ecosystem processes and organic
contaminants: research needs and interdisciplinary perspective.
National Science Foundation, Washington, D.C.
39
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Pavlou, S.P. 1980. Thermodynamic aspects of equilibrium sorption of
persistent organic molecules at the sediment-seawater interface: a
framework for predicting distributions in the aquatic environment. In
Contaminants and Sediments, Volume 2, Robert A. Baker (ed.). Ann Arbor
Science Publishers, Inc., Ann Arbor, MI.
Pavlou, S.P. and R.N. Dexter. 1977. Environmental dynamics of
polychlorlnated biphenyls (PCB) in Puget Sound: interpretations and
criteria recommendations. Special Report No. 75, Ref. No. M77-38, Univ.
of Wash., Seattle.
Pavlou, S.P., R.N. Dexter, and W. Horn. 1977. Polychlorlnated biphenyls (PCB)
In Puget Sound: physical/chemical aspects and biological consequences.
pp. 100-133 _In The Use, Study and Management of Puget Sound: A
Symposium. Washington Sea Grant, Univ. of Wash., Seattle.
Pavlou, S.P. and R.N. Dexter. 1979. Distribution of polychlorinated
biphenyls (PCB) in estuarlne ecosystems; testing the concept of
equilibrium partitioning in the marine environment. Environmental
Science and Technology 13(1):65-71.
Pavlou, S.P.-, R.F.- Shokes, W. Horn, P. Hamilton, J.T. Gunn, R.D. Muench, J.
Vinelli, and E. Crecilius. 1983. Dynamics and biological impacts of
toxicants in the main basin of Puget Sound and Lake Washington. Vol. I:
evaluation of toxicant distribution, transport and fate. Submitted to
the Municipality of Metropolitan Seattle.
Plerson, K.B., B.D. Ross, C.L. Melby, S.D. Brewer, and R.E. Nakatani. 1983.
Biological testing of solid phase and suspended phase dredge material
from Commencement Bya, Tacoma, Washington. U.S. Army Corps of Engineers.
Final Report, Contr. No. DACW67-82-C-0038.
Riley, R.G., E.A. Crecellus, H.L. O'Malley, K.H. Abel, and D.C. Mann. 1981.
Organic pollutants in waterways adjacent to Commencement Bay. NOAA Tech.
Memo. OMPA-1'2. National Oceanic and Atmsopheric Administration,
Boulder, CO. 90 pp.
Swartz, R.C., W.A. DeBen, and F.A. Cole. 1979. A bioassay for the toxicity
of sediment to marine macrobenthos. J. Wat. Pollut. Contr. Fed.
51:944-950.
Swartz, R.C., W.A. DeBen, K.A. Sercu, and J.O. Lamberson. 1982. Sediment
toxicity and the distribution of amphipods in Commencement Bay,
Washington, USA. Mar. Pollut. Bull. 13:359-364.
U.S. EPA/COE. 1977. Ecological evaluation of proposed discharge of dredged
material into ocean waters. U.S. Army Waterways Exper. Sta., Vicksburg,
MS.
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Velth, G.O., K.J. Macek, S.R. Pecrocelli, and J. Carroll. 1980. An
evaluation of using partition coefficients and water solubility to
estimate bioconcentration factors for organic chemicals in fish. pp.
• 78-115 In Aquatic Toxicology, Proceedings of the Third Annual Symposium
on Aquatic Toxicology. ASTM Spec. Tech. Publ. 707.
Versar, Inc. 1979. Water-related environmental fate of 129 priority •
pollutants. Submitted to the U.S. Environmental Protection Agency by
Versar, Inc., Springfield, VA.
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APPENDIX A
INTERVIEW RESULTS
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APPENDIX A
INTERVIEW RESULTS
One of Che casks under Phase 1 was co interview a number of individual investi-
gators regarding their perceptions on the feasibility of establishing sediment
evidence in Puget Sound. In addition, an attempt was made Co ellicit sugges-
tions and/or recommendations on approaches Chat they felc would be worth
considering in this study. The list of individuals contacted through formal
and/or informal interviews, meetings and telephone discussions are listed in
Table A.I. The results of che most significant interviews are also attached
to this appendix. These consist of (1) comments received after che basic
seven approaches developed by JRB (submitted to EPA on September 19, 1983)
were presented to the attendees, and (2) summary of the discussions regarding
various approaches. We anticipate to expand this section and incorporate
additional viewpoints and informational feedback as they are obtained
throughout chis project. These will be assembled and included in che final
report.
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Table A-l
INDIVIDUALS CONTACTED DURING THE PHASE I ACTIVITIES
Name
John Armstrong
Richard Bauer
Don Baumgarcner
Joe Cummins
Tom Dillon
Ron Carton
Arnold Gayler
Howard Harris,
Karl Kassenbaum
Jim Krull
Henry Lee, II
Edward Long
Bernard Malo
Steve Martin
Bruce McCain
Alan Mearns
Gary O'Neal
Rick Parkin
Dan Petke
Keith Phillips
Pat Storm
Rick Swartz
John Underwood
Mike Watson
Fred Weinmann
Jack Vord
Affiliation
EPA-X
EPA-X
EPA/NERC/Newport
EPA-X, Laboratories
COE, WES
EPA/NERC/Corvallis
EPA-X
NOAA/OMPA
EPA-X
WDOE
EPA/NERC/Newport
NOAA/OMPA
uses
COE, Seattle District
NOAA/NMFS
NOAA/OMPA
EPA-X
EPA-X
EPA-X
COE, Seattle District
COE, Seattle District
EPA/NERC/Newport
EPA-X
EPA-X
COE, Seattle District
University of Washington
Area of Participation
Project Reviewer
Project Reviewer
Management Considerations
Bioassay Testing
Dredge Material Management
•
Freshwater Impacts
Chemical Analyses
Management Considerations
Dredge & Fill Permitting
Criteria Applications
Bioaccumulation
Impact Assessment Techniques
Sediment Alert Levels
Dredge Material Management
Biological Maladies
Management Considerations
Enforcement Aspects
Project COTR
Dredge Material Management
Dredge Material Management
Dredge Material Management
Bioassay Testing
Project Officer
Project Reviewer
Dredge Material Management
Benthic Ecology
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EPA REGION X - SEDIMENT CRITERIA DEVELOPMENT FOR PUGET SOUND
MEETING NOTES: EPA/NERC, NEWPORT, OREGON
September 23, 1983
ATTENDEES;
•
Spyros Pavlou, JRB
Donald Weston, JRB
Don Baungartner, EPA
Rich Swartz, EPA
Henry Lee, II, EPA
Ron Carton, EPA
SUMMARY;
The EPA participants commented on JRBs seven basic approaches. A concern was
•
expressed regarding the use of SPM Kns to predict interstitial water KQS. The
use of HHRi criteria may not be appropriate since organisms consumed by man
are generally not exposed to interstitial or interfacial water.
Don Baumg'artner thought that all approaches merit consideration. The use of
water quality criteria for interstitial water was worthwhile but there is a
need to demonstrate that these levels are not harmful to the interstitial
and/or interfacial fauna.
Henry Lee suggested that accumulation through water may not be the only uptake
mechanism; the particulate phase may be a contributor to contaminant burden in
biota. It was felt that the sediment/biota transport pathways should be
investigated more thoroughly.
Rick Swartz suggested that one should develop regression equations for con-
taminant concentrations vs. sediment communities such as texture and total
volatile solids; outU'rs should show impacted sites. He also noted the
importance of synerglsn* in establishing sediment criteria. For example, even
though a sublethal effect below IC$Q values may be shown for a sediment with
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one contaminant, elevated effect values above the two LCso threshold nay be
demonstrated by sediment containing a number of contaminants.
The determination of Infaunal recruitment rates is an alternative technique
for addressing toxicity of sediments to biota and could be incorporated in the
formulation of a sediment criterion.
Don Baumgartner also suggested that sediment criteria may be generated for
three or four sediment types dependent upon organic content. Bioassays and
benchic field surveys are currently used as criteria for sediment toxicity.
For example, benthic surveys are commonly employed to establish compliance of
point source dischargers with 301(h) requirements.
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EPA REGION X - SEDIMENT CRITERIA DEVELOPMENT FOR PUGET SOUND
NOAA/NMFS MEETING
September 27, 1983
ATTENDEES:
Donald Weston, JRB
Bruce McCain, NOAA
SUMMARY;
Much of NMFS work is presented in OMPA-19 (Malins et al., July, 1982).
Factor analysis was used to identify classes of compounds with similar spatial
patterns of concentrations. The PAH's were heavily weighted on Axis 1, select
metals and organics on Axes 2 and 3, the chlorinated hydrocarbons on Axis 4.
Measures of biological health were then correlated against concentrations of
these identified contaminants. The number of benthic taxa was linearly
related (making it arbitrary to establish a threshold).
Among four chemical groups considered, tumors and PAHs were best correlated,
suggesting they may be the causative factor. Chlorinated hydrocarbons were
least correlated with biological indices. ITI was not well correlated with
any sediment contaminant but number of ITI taxa worked better.
This method does not consider habitat differences other than sediment burden.
Covariates of burden (e.g., silt/clay) may be determining number of taxa or
incidence of tumors. The next step which they are currently pursuing is
sediment bioasssays.
The fish species examined (primarily sole) seem to have a very limited
mobility which makes it possible to relate abr -mallties with specific sites.
For example, there is a marked demarcation in r'ie incidence of fish lesions at
the mouth of the Duwamish.
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Evidence is contradictory in Commencement Bay. Sediment burdens of most
compounds are high and Swartz has demonstrated toxicity of sediments in
Hylebos; yet McCain found no toxicity in bioassays of sediments from Hylebos
and crabs maintained in cages in Hylebos showed 1002 survival.
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EPA REGION X - SEDIMENT CRITERIA DEVELOPMENT FOR PUGET SOUND
MEETING NOTES: NOAA/OMPA OFFICE
ATTENDEES;
Spyros Pavlou, JRB
Donald WesCon, JRB
Edward Long, NOAA
Alan Mearns, NOAA
Howard Harris, NOAA
SUMMARY;
Ed Long advocates a three way approach for establishing sediment criteria (1)
chemical characterization, (2) sediment bioassay, and (3) infaunal community
analysis. The three types of analyses when performed on the same sediment
sample may reveal what biota are being impacted and possibly the causative
chemical agent (ref. Chapman and Long, 1983). Long also pointed out the
importance of establishing contaminant concentrations vs. TOC and/or sediment
texture relationships as a method for discriminating sites at which contami-
nation is excesssive (above statistically derived confidence intervals) ' to
allow performance of bioassay and infaunal analysis.
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EPA REGION X - SEDIMENT CRITERIA DEVELOPMENT FOR PUCET SOUND
MEETING NOTES: EPA REGION X LABORATORY STAFF, JRB OFFICES
September 28, 1983
ATTENDEES;
Spyros Pavlou, JRB
Donald Weston, JRB
Joe Cumins, EPA
SUMMARY;
Joe Cumins commented on the applicability of various bioassay methods to the
sediment criteria development.
He pointed ^out that elutriate bioassays in general show lesser toxicity to
those performed with mixed substrates (water/sediment). Cummins had concerns
with the lack of approaches to address the effects of mixtures of chemicals
(synergism). He has observed that bioassay procedures may introduce artifacts
in results, e.g., when frozen sediments are used, toxicity is reduced by 20 to
302. He suggested that one should (1) develop methods for applying a weight-
ing factor to contaminant concentrations measured in sediments to reflect
level of concern; (2) examine multiple indicators and factor these irjto an
effective threshold level; and (3) develop bioassay methods for addressing
mixtures of chemicals.
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EPA REGION X - SEDIMENT CRITERIA DEVELOPMENT FOR PUGET SOUND
MEETING NOTES: COE SEATTLE OFFICE
September 29, 1983
ATTENDEES:
Donald Weston, JRB
Fred Velnmann, COE
Steve Martin, COE
Pat Storm, COE
Keith Phillips, COE
SUMMARY;
Bloassays are favored since they provide the most straightforward approach to
determining if sediments are an ecological threat. No mathematical manipula-
tions which (may or may not be valid are necessary.
There was concern that approaches involving WQC may not adequately guard
against direct exchange of contaminants from sediment to biota.
Currently the COE evaluates dredge material in two ways. For Inland disposal
a chemical characterization is first performed. If a regulatory official
believes levels of any contaminant are high enough to be of concern, he may
request a bioassay. For ocean dumping a bioassay must be performed without
consideration to the chemical make-up of the dredge spoil. Initially ocean
dumping criteria were the same as for inland, but they were challenged in
court on the basis that the subjective assessment of hazard may not provide
adequate protection. Now a bioassay must be performed in most cases.
Keith Phillips just returned from visiting WES and noted that they are using
BCF's and KQ'S to estimate exchange among ecosystem components just as we are.
There was some question whether organisms which humans ingested, and for which
the HHRL criteria were derived, were in fact exposed to our predicted inter-
stitial water concentrations.
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EPA REGION X - SEDIMENT CRITERIA DEVELOPMENT FOR PUGET SOUND
MEETING NOTES: UNIVERSITY OF WASHINGTON, COLLEGE OF FISHERIES
October 5, 1983
ATTENDEES;
Donald Weston, JRB
Jack Word, UW
SUMMARY;
The use of partition coefficients derived from exchanges between suspended
particulate material and water may be totally inappropriate to predict
exchange between sediment and interstitial water. The chemistry of the
sediments is profoundly different than that of the overlying water.
Any application of sediment quality criteria in pollution abatement programs
should address the aspect of time. Because sediaents serve as a sink for most
pollutants and integrate pollution levels over time, changes in pollutant
input may not be reflected by a change in sediment pollutant burden for a year
or more.
O'Connor and Swanson's index of environmental quality has been undergoing
extensive development. Jack Word will be testing the index employing data
from Puget Sound.
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APPENDIX B
COMPUTATION OF ECOLOGICAL RISK INDEX
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APPENDIX B
COMPUTATION OF ECOLOGICAL RISK INDEX
The ecological risk index of HSkanson (1980) was developed as a diagnostic
Cool for water pollution control purposes. It was first used to identify
toxic substances and lakes in need of corrective action. The risk index can
be expressed as:
where
RI • the risk index: RI<50 - low ecological risk; 150600 =
very high ecological risk
Ej1 - the'ecological risk factor for the contaminant of concern
n - the number of contaminants considered
CQ* - the observed concentration of the contaminant in surficial
sediments
Cj.* - the preindustrial reference level
Sci - an estimate of the contaminant's toxicity
K1 - a contaminant specific constant
BPI - the bioproduction index of the area which is a function of the
nitrogen and organic content of the sediments
The index takes into account four principal factors (taken directly from
HSkanson, 1980):
1. The concentration requirement which emphasizes that RI-value should
increase when the sediment contamination increases. This may be revealed
by a comparison between preindustrial deposits from deep sediment levels
and recent deposits from superficial sediments.
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2. The number requirements which states that a lake or a. sub-basin' polluted
by numerous substances should have a higher Rl-value than an area contami-
nated by only a few substances.
3. The toxicity factor requirement which Implies that the risk index should
account for the fact that various substances have different toxicological
effects; some are highly toxic, others slightly toxic. There Is a very
wide range here—from extremely poisonous substances like PCB and mercury
via lead and copper to iron. The requested RI-value should differentiate
between mildly, moderately and very toxic substances.
A. The sensitivity requirement which means that the risk index should account
for the fact that various lakes and water systems do not have the same
sensitivity to toxic substances. In waters of low pH and bioproductivity,
for example fish tend to have higher mercury concentrations than in waters
of comparable Hg-contamination but with more neutral pH and higher bio-
productivity.
S3
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APPENDIX C
QUALITY DEGRADATION FACTORS
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APPENDIX C
QUALITY DEGRADATION FACTORS •
The quality degradation factors were calculated from a hypothetical set of
data as presented in Table C-l. The chemical measurements consist of contami-
nant concentrations in biota, sediments and Interstitial water for a list of
typical contaminants found in Puget Sound.
The biological measurements presented in the table are a benthic community
structure index (Bray/Curtis similarity index) the percent amphipod mortality
and the percent diseased organisms. These parameters were chosen as represen-
tative of the benthic community structure, the toxicity potential of the
sediments, and the physiological (pathological) conditions of the type of
organisms sampled. Values are entered for the actual site, a control site,
and for the maximum observed quantity.
Table C-2 summarizes the calculations for the overall chemical quality degra-
dation factor at the site of interest and Table C-3 presents the calculations
performed to determine the overall biological/toxlcological factor. For this
hypothetical site, it is apparent that the biological score (50) is higher
than the chemical score (36) within the defined range of 0-100. Correlations
of individual contaminant scores can be performed with this data to estimate
contaminants that may be the most significant contributors to the observed
biological/toxicological response.
Combinations of these contributions are also useful in obtaining the overall
quality degradation of the site of interest. In this example by averaging the
chemical and biological factors, a score of 42 was obtained.
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Table C-l
ENVIRONMENTAL PARAMETERS
Paramecer
Designation
Biota
CPNAs (ppb)
DDTs (ppb)
PCBs (ppb)
Hg (ppm)
Zn (ppm)
As (ppm)
Sediment
CPNAs (ppb)
DDTs (ppb)
PCBs (ppb)
Hg (ppm)
Zn (ppm)
As (ppm)
Water (interstitial)
CPNAs (ppb)
DDTs (ppb)
PCBs (ppb)
Hg (ppb)
Zn (ppb)
As (ppb)
Bray/Curtis similarity of
benthic community to con-
trol/reference site
Z Amphipod Mortality
% Fish with Histopatho-
logical abnormalities
HYPOTHETICAL SITE IN
Actual
Site
100
23
300
0.5
270
31
12.000
20
1,200
0.5
300
10
0.12
0.0007
0.015
0.0009
2.2
1.8
0.8
60
75
MEASURED AT A
PUCET SOUND
Measurement
Reference/
Control Site
1
7
90
0.1
270
20
5,000
1
600
0.1
100
5
0.08
0.0003
0.0081
0.00049
2.0
1.7
1.0
5
10
Maximum
Observed
800
25
700
1.5
350
70
28,000
30
1,500
2
475
20
0.31
0.0009
0.021
0.008
4.1
3.0
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Table C-2
CALCULATION OF CHEMICAL QUALITY DEGRADATION
FACTORS FOR A HYPOTHETICAL SITE3
Chemical Quality Degradation Factor (QDF3?)
I
(b)
Contaminant
CFNAs
DDTs
PCBs
Hg
Zn
As
Mean
Overall
Chemical6
The data
Sediment
i= (SED)
30
66
66
21
53
33
45
34
is obtained from Table C-l.
C? - C?
- *,ACT t,REF „ inn
Tissue
(TIS)
12
89
34
29
-0-
22
31
Water
(WAT)
17
67
53
5
10
8
27
X _X
i.MAX " i.REF
yp
where x is the contaminant, C. is the concentration of x in matrix
i. » sediments (SED) , Tissue (TIS) and Interstitial Water (WAT)
The overall chemical degradation factor is defined as:
(QDFSvERALL)CHEM ' (QDFSED + QDFnS * QDFWAT)/3
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Table C-3
CALCULATION OF BIOLOCICAL/TOXICOLOGICAL QUALITY DEGRADATION
FACTOR FOR A HYPOTHETICAL SITE
QDFBENTHOS " (1 ~ Bray/Curtis similarity to control) x 100 - 20
QDF - 2 mortality at site - Z mortality control
qDFBIOASSAY 100 - Z mortality control x 10° ' 58
i
ODF . * disease at site - Z disease control
W PATHOLOGY 100 - % disease control x 10° = 72 '
QDFBIOL -
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PHASE II: DEVELOPMENT AND TESTING OF
THE SEDIMENT-WATER EQUILIBRIUM
PARTITIONING APPROACH
-------
EPA Report 910/9-83-117
INITIAL EVALUATION OF ALTERNATIVES FOR
DEVELOPMENT OF SEDIMENT RELATED
CRITERIA FOR TOXIC CONTAMINANTS IN
MARINE WATERS (PUCET SOUND)
• •» •
PHASE II: DEVELOPMENT AND TESTING OF
THE SEDIMENT-WATER EQUILIBRIUM
PARTITIONING APPROACH
FINAL REPORT
April 20, 1984
t--
.• ..
• '*•"» •. •
Prepared for: • " -. . .'..-:{"'•.•-'
U.S. Environmental Protection Agency
101 M Street, S.W.- . ', ••V.-
Washington, D.C. 20160 Y..."1..'/.i'.-~r-- j
• ". • . '•' . -•'- '• •'.' •'"••" "-I ,.'.' :. " .f
.. . ' .. "••*•".!
--«.-."<.,
Prepared by: . • .-
JRB Associates -' • /' "
A Company of Science Applications, Inc.
13100-B Northup Way, Suite 38
Bellevue, Washington 98005 • •
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ACKNOWLEDGMENTS
This report was prepared by Spyros P. Pavlou and Donald P. Weston.
The authors wish to thank the many people who reviewed the draft
report. The final report has benefitted greatly from their com-
ments. The following people submitted written comments on the
draft, participated in the review meeting or otherwise substan-
tially contributed to the ideas presented herein:
Kevin Anderson
John Armstrong
Bob Barrick
Dick Cunningham
Arnold Gahler
Howard Harris
David Jamison
Jim Krull
Henry Lee
Tom O'Connor
Gary O'Neal
Richard Parkin
Dick Peddicord
Dan Petke
Keith Phillips
Rich Tomlinson
John Underwood
Gary Voernian
Michael Watson
. .'.<
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TABLE OF CONTENTS
Page
1.0 EXECUTIVE SUMMARY ................................................ 1
2.0 INTRODUCTION [[[ 4
2. 1 Rationale and Objectives .................................... 4
2.2 Objectives .................................................. 6
2 . 3 Sunraary of Approach ......................................... 6
3 . 0 TECHNICAL DEVELOPMENT ............................................ 8
3.1 Basic Definitions ........................................... 8
3.2 Determination of Partition Coefficients ..................... 12
3.2.1 Trace Metals ......................................... 12
3.2.2 Synthetic Organic Compounds .......................... 18
3.3 Calculation of Sediment Criteria ............................ 21
3.3.1 Trace Metals ......................................... 26
3.3.2 Synthetic Organic Compounds .......................... 26
3.4 Limitations ................................................. 29
3.4.1 Lack of Comprehensive Water Quality Criteria ......... 29
3.4.2 Synergism and Antagonism ............................. 30
3.4.3 Level of Uncertainty in the Sediment Criteria ........ 30
3.5 Assumptions ....................... , ......................... 31
3.5.1 Validity of the Equilibrium Assumption ............... 31
3.5.2 Normalization of K-_ to Organic Content .............. 31
3.5.3 Influence of Environmental Variables on K .......... 32
Ut»
3.5.4 Bioavailability of Contaminants at the Sediment-
Water Interface ...................................... 34
3.5.5 Applicability of Water Quality Criteria to
Benthic Organisms .................................... 35
3.5.6 Summary of Assumptions ............................... 37
4 . 0 FEASIBILITY TESTING IN PUGET SOUND .............................. 40
4.1 Format of Presentation ...................................... 40
4.2 Trial Data Sets ............................................. 42
4.3 Comparison of Measured Concentrations with Derived Criteria. 43
4.4 Spatial Comparisons ......................................... 61 .>..;.'
4.5 Correlations with Other Sediment Criteria ................... 63 <"•'"''
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TABLE OF CONTENTS
(continued)
Page
5.0 RECOMMENDATIONS 67
5.1 Short-Tenn Technical Needs 67
5.2 Long-Term Technical Needs 69
5.3 Management Needs 70
6.0 REFERENCES 71
APPENDIX A - Sediment Contaminant Concentrations from Malins,
et al., 1980 74
APPENDIX B - Concentration of Trace Metals and Synthetic Organics
in the Sediments of Elliott Bay and in the West Point
Area 83
APPENDIX C - Estimation of Organic Carbon Content 89
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1.0 EXECUTIVE SUMMARY
With the increased use of our nation's coastal and inland waters, regulatory
agencies are frequently confronted with difficult decisions in resolving con-
flicts between alternate uses of these waters, while at the same time striving
to protect overall environnental quality. A significant number of management
decisions facing these agencies concern the definition of permissible levels
of contaminants in marine sediments. For example, in Commencement Bay the
Washington Department of Ecology and EPA are attempting to identify those
areas in which sediment contamination poses the greatest environmental threat,
with the ultimate intent of initiating remedial action in these areas. At the
Four Mile Rock dredge disposal site, regulatory agencies are confronted with
an immediate need to establish a permissible level of contamination for sedi-
ments which are to be disposed of at the site. In Commencement Bay, at Four
Mile Rock, and at countless other areas throughout the country, sediment-
related criteria which define environmentally safe levels of contaminants in
sediments would be invaluable tools in environmental management decisions.
However, given the current state of our technical knowledge, regulatory
agencies have been forced to adopt short-term, interim decision criteria until
scientifically-sound and legally defensible sediment criteria can ultimately
be established.
There are three general approaches currently being pursued to establish sedi-
ment-related criteria:
• Background level approach - criteria are established at some permis- 4
sible level of enrichment above background levels in a reference '
area.
• Burden-effect relationships - observations of adverse biological
impacts are related to contaminant concentrations in order to esta-
blish a "safe" level of contamination.
• Equilibrium partitioning approach.
In an effort to develop the equilibrium partitioning approach, JRB Associates
was contracted to develop the theoretical framework of the approach. Using
this framework, JRB then developed tentative criteria for trace metals and syn-
thetic organics and tested the proposed criteria against measurements of con-
taminants in the sediments of Puget Sound.
• - -— ' -i-fi'-VL'jf*7r~¥->- —".AA-i
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The resulcs of Chis study suggest Chat the equilibrium partitioning approach
is a method that holds much promise for establishing criteria for marine sedi-
ments. The approach provides a relatively simple mechanism whereby the large
toxlcological data base incorporated in the EPA water quality criteria can be
adapted to determine permissible contaminant concentrations in marine sedi-
ments which should insure protection of benthlc marine organisms. The basic
tenet of the equilibrium partitioning approach is that the concentration of
each contaminant In sediment should be at or below a level which Insures that
its concentration In interstitial water does not exceed the EPA water quality
criterion.
The key to this approach is the determination of the sediment-water partition
coefficient for each compound of interest. This coefficient was determined
empirically for trace metals based on measureaents of trace metal concentra-
tions in the interstitial water and bulk sediments from a wide variety of sub-
strates. The sediment-water partition coefficients for synthetic organics
were estimated from octanol-water partition coefficients. Since the partition-
ing of a contaminant between sediment and water is strongly dependent upon the
organic carbon content of the sediment, the partition coefficient is normal-
ized to organic content.
Sediment criteria were established for six trace metals and 47 synthetic
organic compounds of concern in Puget Sound by use of the equlibrium partition-
Ing approach. The derived criteria were tested against existing data on sedi-
ment contaminant concentrations in a variety of areas in Puget Sound including
Elliott Bay, Commencement Bay, Sinclair Inlet, Budd Inlet, Case Inlet, Port
Madison and the West Point area. In most cases the proposed criteria were
exceeded only in areas which historically have received high inputs of contami-
nants from point and nonpoint sources. Among the trace metals, chronic sedi-
ment criteria were exceeded most frequently for Hg, Pb, Cu and As in Elliott
Bay and Commencement Bay. Among the synthetic organics, only PCBs and DDT con-
sistently exceeded the proposed sediment criteria, primarily in the urban
embayments noted above. The polynuclear aromatic hydrocarbons we.e generally
well below criteria except for a few isolated sites in the West Point area.
Both numerical and graphical procedures are presented to relate the frequency
and magnitude of criteria violations to specific sites.
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During development of the equilibrium partitioning approach, a number of short-
comings in our current state of knowlege on pollutant interactions between
sediment, water and biota have been identified. The most significant of these
include:
• inability to consider synergistic or antagonistic interactions among
contaminants;
• the influence of environcental variables (e.g., organic carbon, pH)
on the chemical behavior of contaminants is poorly understood; and
• our inability to differentiate the bioavailable fraction of a con-
taminant from the total sediment burden of the contaminant.
Until some of the issues identified above are resolved, the sediment criteria
proposed in this report are not intended for adoption by regulatory agencies.
It is important to recognize that while the numerical values suggested in this
report as permissible levels of contaminants in marine sediments are, for sim-
plicity sake, referred to as "criteria", they are not appropriate for immed-
iate use in any regulatory, control or enforcement applications. However, as
a first step in a long process, the approach presented herein appears very pro-
mising for the eventual adoption of sediment criteria for regulatory appli-
cation.
The approach developed in this report is noteworthy in that it is capable of
providing numerical criteria for a wide diversity of contaminants in marine
sediments. This in itself is an elusive goal which has been unachieveable in
many past efforts. However it is the approach which has been developed,
rather than the criteria per se, which represents the most signficiant contri-
bution of this work. The criteria proposed in this report are presented with
the expectation that they will be refined through an iterative process involv-
ing input from both the scientific community and environmental management
agencies. With continued refinement, the criteria will find application on
the short-term basis as guidelines in assisting environmental managers in
assessment of the extent of contamination of marine sediments. On a long-term
basis, the criteria may ultimately be refined to the point where they find
broad regulatory application.
. JRB Associates .
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2.0 INTRODUCTION
2.1 RATIONALE AND OBJECTIVES
The Environmental Protection Agency has focused historically on the develop.-
ment of water quality criteria which are supported by a broad base of toxico-
logical studies. Use of these criteria provides some degree of assurance that
contaminant concentrations will be within acceptable limits for the protection
of aquatic life and human health. However, there is disturbing evidence of
environmental degradation In many of the heavily urbanized areas of Puget
Sound even though monitoring data does not show that water quality criteria
are exceeded in the water column. The majority of adverse biological impacts
recently observed are not among organisms-living in the water column but those
that live in or on the sediments. Macrobenthlc communities in the vicinity of
point source discharges have demonstrated significant changes in species com-
position and abundance (Armstrong, et al., 1978; Malins et al. , 1982; Comiskey
et al., 1983). Sediments from urbanized areas have been shown to induce mor-
tality in sensitive benthic species (Swartz et al., 1982), and demersal fishes
from heavily polluted areas have been shown to have a higher incidence of his-
topathologlcal abnormalities than those from reference areas (Malins et al.,
1980; 1982). These observations raise serious questions as to whether exist-
ing water quality criteria alone are adequate to protect the environmental
resources of Puget Sound.
It is becoming increasingly evident that some sort of sediment criteria are
needed to supplement existing water quality criteria in judging the signifi-
cance of contaminant concentrations and to provide a basis for remedial
action. There are a number of reasons why sediment criteria deserve considera-
tion:
• Most toxic compounds are highly Insoluble so the majority of the
contaminant is not dissolved in the water but is associated with
the organic matrix on sediment particles. For example, sediments
in Elliott Bay contain 60,000 times more PCBs than overlying water
(Pavlou and Dexter, 1979).
• Sediments serve to Integrate contaminant concentrations over time,
eliminating the high degree of temporal variability which plagues
sampling of toxicants in the water column.
. JRB Associates -
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• Sediments serve as a sink for most toxic materials, thus a long-
term low level discharge of a contaminant may result in a dangerous
build up in the sediment even though water quality criteria are not
violated at any given tine.
• Sediments can serve as a reservoir (source) of contaminants which
could be reintroduced to unpolluted overlying water.
• A large number of organisas, including many of commercial impor-
tance, spend most of their lives in or on the sediments. For these
species, Che contaminant level in the sediments may be of greater
concern than that in the overlying water and nay be the controlling
factor with regards to bioaccuaulation potential.
In response to the need for sediment-related criteria, the Environmental
Protection Agency initiated an effort to identify and evaluate alternative
approaches to the establishment of sediment criteria. The current state of
knowledge regarding sediment- criteria was updated and summarized in the Phase
I report (Pavlou and Weston, 1983) and a number of approaches to the establish-
ment of criteria were identified. Three approaches appeared to be of imme-
diate utility in developing sediment criteria for Puget Sound:
• Background level? approach - the concentration of contaminants in
the sediments of relatively unpolluted reference areas is deter-
mined and the criteria are then established at some permissible
level of enrichment above background levels;
• Burden-effect relationships - observations of adverse biological
impacts (alterations in benthic community structures, lethal or
sublethal effects observed in bioassays, incidence of pathological
disorders) are correlated with contaminant concentration in order
to determine those concentrations at which no impacts are evident;
• Equilibrium partitioning approach - the sediment criterion is esta-
blishe-d at a level which will insure that the EPA water quality
criterion is not violated in the interstitial water.
The development of sediment criteria by the background level approach and bur-
den-effect relationships is currently underway in connection with other work
within Region X. JRB was requested to develop the equilibrium partitioning
approach and to examine the suitability of the approach for the establishment
of sediment criteria for Puget Sound. The approach is simple, is immediately
adaptable to the chemical contaminants measured in Puget Sound, is based pri-
marily on existing data and provides "first cut" numerical criteria values.
• 5
- ..-...•..r-.fc.-.j
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2.2 OBJECTIVES
The specific objectives of the Phase II activities in this study were to:
1. Present the theoretical basis of the equilibriua partitioning
approach and the derivation of sedinent-water partition coeffi-
cients. Discuss their application in the marine environment'and
their dependence on environmental variables.
2. Establish preliminary numerical criteria for selected compounds
measured in Puget Sound and estimate the uncertainty in these
numerical values.
3. Discuss the assumptions and limitations of the approach and how
they may influence the application of the derived criteria.
4. Test the utility of the derived criteria in Puget Sound, with
representative data sets from contaminated eobayments.
5. Identify future research/data needs which may serve to improve
the utility of the equilibrium partitioning approach.
2.3 SUMMARY OF APPROACH
Sediment criteria were derived for six priority metals and 47 individual
priority organic compounds. These contaminants have been measured histori-
cally in the sediments of Puget Sound and have shown elevated concentrations
within certain subregions and embayments of the Main Basin.
In this study, a sediment criterion was defined as the concentration of a con-
taminant in sediment which insures that its concentration in interstitial
water does not exceed the established EPA water quality criterion, and there-
fore a designated water use, such as integrity of indigenous biota, could be
attained. The sediment criterion was expressed as the product of the com-
pound-specific sediment-water partition coefficient and its water quality
criterion.
For trace metals, the partition coefficients were computed from the literature
as an arithmetic mean with an associated standard deviation. For synthetic
organic compounds the partition coefficients were computed from existing rela-
tionship of experimentally derived sediment-water partition coefficients with
octanol-t ater partitioning ratios. Seven regression equations published in
the literature, for a variety of chemical classes, were considered for their
applicability to the compounds tested in this study. The optimum equation
selected was one derived for 19 priority organic chemicals.
6
. JRB Associates _
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Sediment criteria for each of 53 priority pollutants were derived to corres-
pond to both the acute and chronic values established for water, when avail-
able. The applicability of these derived criteria in Puget Sound was tested
wi-th two independent data sets. The contaminant concentrations measured in
the sediments of various subregions in Puget Sound were compared with the
criteria values. Violations were then estimated as excess factors from the
derived acute and/or chronic criterion value. A comparison of the frequency
of criteria violations values computed among a number of subregions and embay-
ments allowed for a preliminary assessment of the severity of contamination.
The discussion presented in the following sections of this report is a
detailed description of the above approach and results obtained.
. JRB Associates _
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3.0 TECHNICAL DEVELOPMENT
3.1 BASIC DEFINITIONS
A brief discussion of Che concept of equilibrium partitioning was presented in
the Phase I report, Section 2.4. As applied to the sediment-water interface,
contaminant transport between the solid and aqueous phase occurs via a rapid
molecular exchange. This exchange is continuous and therefore maintains the
system at chemical equilibrium. The instantaneous concentration of the con-
taminant in either of the two components can be expressed 'as a function of its
concentration in the other component and an equilibrium constant specific to
that contaminant. These chemical specific constants are commonly referred to
as partition coefficients and are expressed mathematically as:
CX
*D-^- (1)
where 1C is the partition coefficient and -C* and CX are the concentrations of
s w
contaminant x in the sediment (s) and surrounding water (w), respectively.
Contaminant concentrations are expressed as mass of x/dry mass of sediment and
mass of x/mass of water.
A schematic representation of the aqueous-solid components in a marine environ-
ment where this mechanism is operable is shown in Figure 1. Partitioning of a
contaminant occurs in both the water column and the sediments. In the former
case, the exchange is between suspended particulate matter (SPM) and ambient
water while in the latter case it is between sediment particles and the inter-
stitial water. In applying the equilibrium partitioning approach to sedi-
ments, the zone of interest for developing sediment criteria is the bioturba-
tion layer where most of the biological activity occurs. Sediment criteria
using the equilibrium partitioning approach were derived using equation (1) as
follows:
• The partition coefficient- Kg, was adjusted to account for the
dependence on organic carbo' . The modified partition coefficient is
defined as:
8
...
. JRB Associates _
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Organic
Microlayer'
Water
Colur-.n
Interface
Bulk
Sediment
Surface
Nepheloid Layer
Biocurbation Layer
Consolidated Sediments
Figure 1
SCHEMATIC REPRESENTATION OF AQUEOUS-SOLID
COMPONENTS IN THE MARINE ENVIRONMENT
. JRB Associates-.
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(2)
where KQC is the organic carbon normalized partition coefficient and
CX/OC iS n°W Che concentraclon of contaminant x in the sedioent
expressed in units of mass of x/oass of organic carbon. The term
CC refers specifically to the concentration of x in interstitial
water; the units remain the same as defined in equation (1).
Equation (2) can also be expressed as:
K o
OC jT X TOC a *D X TOG (3)
IW
where TOC refers to the total organic carbon content in sediment
expressed as the fractional mass on a dry weight basis (e.g., 3%
organic carbon equals 0.03 g organic carbon per 1 g of sediment dry
weight). This adjustment was made to eliminate the variability of
Kg on organic carbon. The dependence of K_ on organic carbon has
been well documented in the literature. For example, K_ values for
nitropyrin were shown to vary about 140-fold in different sediment
samples but when expressed on an organic carbon basis (KQ_) the
variation was reduced to only threefold (Kenaga and Goring, 1980).
A similar dependence on sediment-water partitioning on organic
carbon content is evident for benzo(a)pyrene as depicted in Figure
2. K_ values for each of three sediment types were found to vary
44
considerably (3.5 x 10 to 15 x 10 ) though when adjusted to organic
carbon content the variability was minimal (3.0 x 10 to 3.8 x 10 ).
The sediment criterion is defined as the concentration of contami-
nant x in the sediment which insures that its concentration in the
interstitial water does not exceed the established EP/ water quality
y
criterion. Modifying equation (2) by setting CTU as the water
X
quality criterion, cw/CRt Chen the corresponding sediment criterion
for contaminant x, Cc/cRX)C' can be exPressed as:
. JRB Associates —
10
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100
^ 90
ec
N«f
„ SO
u
V.
s
70
g 60
o
u
50
•- iO
K.
c
c 30
c
«w
fZ
« 20
5
u
c
u 10
BSe*r>vlll< Pond Scdloent (31 organic carbon); Kg - IS x 10k; K^ - 3.0 x 10f
ACoyocc Creek Stdlocnt (22 organic carbon); X0 • 7.6* 10"; K^ - 3.8x 10*
•Oet Molnc* River Sediment (12 organic carbon); KD • 3.5 x !0U; K^ • 3.5 x 10'
0.2 Q.t* 0.6 0.8
Cone en c vac ion of Benzo(a) pyrene in water (ng/nf.)
1.0
Figure 2
SORPTION ISOTHERMS OF BENZO(A)PYRENE
(From Smith ec al., 1978)
. JRB Associates _
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CS/CR/OC " KOC CW/CR
• In order to apply Che sediment criterion to a specific site, the
criterion normalized to organic carbon, may be adjusted to the
amount of organic carbon In the sediment of concern. This is
expressed as:
^/CR ' CS/CR/OC T°C (5>
in which T__ is again expressed as the fractional mass on a dry
weight basis as in equation (3). The sediment criterion for a given
^
organic carbon content, C* .__ can be compared directly to the mea-
sured contaminant concentration in the sediment of concern.
The procedures followed in deriving sediment criteria for specific priority
pollutants measured in Puget Sound and in testing the application of these
numerical values with existing data, are presented in detail in the following
sections of the report.
3. 2 ?• DETERMINATION OF PARTITION COEFFICIENTS (KQC)
Partition coefficients were computed for six priority metals and 67 priority
organic compounds which have been measured in Puget Sound sediments. The
methods used are presented separately for the two categories of pollutants.
3.2.1 Trace Metals
The distribution of trace metals between interstitial water and sediment is a
complex process which depends on a number of factors including chemical spec-
iation, the reduction-oxidation (redox) potential at the solid-aqueous inter-
face, the type of clay minerals present, the nature of the organic matter on
both sedimentary particles and in interstitial water, pH, salinity, and par-
ticle size. The redox potential and pH, because of their effects on chemical
speclation, are probably the most important factors in determining the sedi-
ment-water partitioning of trace metals (Jenne and Luoma, 1979). Though the
dependence of partitioning on pH and redox conditions is certainly of major
Importance, the precise nature of this dependence is unpredictable and poorly
understood.
JRB Associates —
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The environmental variables and physical/chemical processes responsible for
mediating the transport of trace netals in marine sediments are neither well
understood nor adequately quantifiable to allow a theoretical computation of
sediment-water partition coefficients. Therefore, these coefficients were
derived empirically by using measurements of trace metal concentrations in the
interstitial water and bulk sediments from a wide variety of substrate types.
Empirical KQC values were then calculated for each substrate type and a mean
of the individual KQC values was computed to determine a partition coefficient
most representative of that particular trace metal.
Upon examination of the recent literature, the most comprehensive data was
that of Brannon et al. (1980); the derivation of the K quantities presented in
the present report rely solely on this data base. In the study of Brannon et.
al, samples were taken from a wide variety of areas throughout the country,
primarily from marine sediments but including a few freshwater sites as well.
From each site, measurements were made of trace metal concentrations in the
bulk sediment and in the interstitial water. ^ values calculated from this
data are presented in Table 1. The K^ values were converted to KQC values by
dividing by the fractional mass of the sediment organic carbon concentrations.
As discussed in the previous section (Section 3.1) there is clear justifica-
tion for normalizing the partitioning coefficient of synthetic organics to
sediment organic content by use of K rather than K^ but for trace metals the
issue is more problematic and requires further examination. Of the six metals
evaluated, a statistically significant relationship between K_ and organic con-
tent was evident for three metals (Cu, Cd, Pb) as shown in Table 2 and Figure
3. For these three metals it is clear that K _ would be a better estimate of
the sediment-water partitioning than would K_. For the remaining three metals
(Zn, As, Hg) the apparent independence of partitioning on sediment organic con-
tent is not taken as definitive evidence against the use of K__ It is very
uc* .
probable that the diversity of sites and variations in other environmental
parameters a-i-jng sites (e.g., redox potential) may have masked the relation-
ship of Kp a,.d organic carbon. It is noteworthy that even though normaliza-
tion of mercury concentrations to organic carbon was not indicated as
appropriate by this analysis, Lindberg and Harris (1974) found comparisons of
mercury concentrations among sites to be more meaningful after the concentra-
tlons were first normalized to sediment organic content.
JRB Associates _
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Table 1
EMPIRICAL SEDIMENT-WATER PARTITION COEFFICIENTS FOR TRACE METALS
(Values calculated from Drannon et al., 1980, as the ratio of total sediment metal
concentration to the concentration of the metal In the interstitial water)3
Cu
c_
3)
03
>
g
o
B" '
»» . k
n ,j • :
Collection Site
Mobile Bay. AL
Mobile Bay. AL
Ouuaalsli Waterway. UA
Duuanlah Uatervay. UA
Duwaaleh Ualerway. UA
Iranford Harbor. CT
Braniord Harbor. CT
Bridgeport Harbor, CT
Bridgeport Harbor. CT
Aahiabula Harbor. Oil
Aahiabula Harbor. OH
Aahiabula lldibor. OH
Janes Hlver. VA
Jasiea River. VA
Oakland Inner Harbor. CA
Oakland Outer Harbor. CA
Hudson Blver. MY
Terry Creek. C.A
Brunswick lUrhur. CA
Houston Ship Channel. TX
Houaion Ship Channel. TX
Houaion Ship Channel , TX
Mean
Standard Deviation
Organic
Laib.m
0.81
2.14
1.42
2.84
1.98
4.26
1.12
6.01
6.16
0.92
2.44
2.18
1.11
2.01
1.94
1.69
4.6?
4.8)
1 91
1.68
1.24
4.21
«D
(»IO*)
1.8
16.9
8.4
111.4
49.1
184.9
91.1
4H1.0
211.1
1.9
10.1
1.0
1.1
11.4
16.1
4.1
8 8
184.0
140 0
1.4
12.1
14.2
X
2.2
6.2
1.9
46.1
21.1
41.4
18.1
19.9
16.1
0.8
4.1
2.1
O.I
11.6
4.2
2.8
1.9
11.8
11.4
1 0
10 1
1 4
11. i
11.0
In
""•
1.0
: i
II 8
1.1
11.4
4.1
0 9
10.1
11 6
4.1
1 0
0 4
1 »
0 1
6 1
1 4
0 i
1 1
6 1
4H 6
10 1
..
V
2.4
1.0
8 0
1.0
1 1
I.I
0 1
1.1
6.1
4.1
0.4
0.2
0.1
O.I
1.1
0 8
0 1
0 6
1 6
18 9
1.1
..
1.1
6.1
As
«U<
0.11
O.ll
0.44
0.16
0.18
0.44
U.ON
0 I'l
--
0.16
0.11
0.41
0.04
n.64
0.01
0 14
O.lb
0 09
0.00
0.114
1 14
0 10
"'".
o.m
O.ll
0 11
0 11
0.14
0.10
0.02
0.01
--
0.18
0.09
0 18
0.01
0.11
0 01
0.08
0.08
0.01
0 02
O.Ul
0 111
o o:
0 II
0.12
ra
"Ui
0.06
O.ll
O.U4
1 11
i.n:
1.11
i.n
1.811
11.80
1.20
1.80
I.M>
2.10
0.24
1.91
1.80
11.2
0 fiO
0 60
U (lO
0.10
1 111
•ue
0.0)
0.04
0.01
0 41
0.14
O.ll
0.22
0.46
2.89
1.10
0.14
0 62
0 80
0.12
0.10
1.01
1.11
0 11
0 11
0.16
0 U9
O.ll
0 6'.
0 16
I'b
s
1.1
1.9
4.0
ld.1
4.1
16.4
11.4
14 8
4.1
4.1
I.I
II. 1
0.2
1 B
,8.4
1.6
11.1
1 0
I.U
2.1
1 9
ft 1
"u
4.1
O.I
2.8
12 8
2.1
1.8
2.6
12.4
2.1
4.1
0.1
4.1
O.I
0.9
I.I
1.1
11.8
0.4
0 1
1.4
0 b
1.9
1 8
4 II
•U
O.ll
0.04
0 61
U 41
0 .'1
0 ON
u :o
0.09
O.ll.
U.UI
U II
U.04
0.11
0 10
--
--
0 11
0.10
--
o.oi
u o»
—
k
in
ISHI'-J
U. IH
II III
0 41
U II
0 II
0 II.'
O.U4
0 ill
U Ul
U Ul
0 Ul
il n:
0 01
II Ul
--
--
o u;
0 02
--
II HI
a o:
--
il UN
u II
*Cacludee one aberrant station In Milwaukee Harbor. Ul .
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Table 2
REGRESSION EQUATIONS ILLUSTRATING THE RELATIONSHIP OF THE
SEDIMENT-WATER PARTITION COEFFICIENT OF TRACE METALS
WITH THE PERCENTAGE OF ORGANIC CARBON IN SEDIMENTS
etal
Cu
-
As
c<
Pb
Hg
log K
log K
log K
log K
log K
log K
Regression
B = 0.33 (TOC)
^ = 0.074 (TOC)
_ = -0.05 (TOC)
B - 0.21 (TOC)
D = 0.20 (TOC)
D - 0.05 (TOC)
+ 3.28
+ 3.29
+ 2.46
+ 2.34
+ 3.10
+ 1.87
ar value significant at a <0.05.
n r
22 0.74a
21 0.19
21 -0.19
21 0.55a
22 0.47a
18 0.21
,JRB Associates —
15 .- -•!.'V~
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ii
c
3 •
Cu
Cd
Pb
Z Organic Carbon
16
Figure 3
RELATIONSHIP BETWEEN THE
SEDIMENT-WATER PARTITION
COEFFICIENT AND THE
SEDIMENT ORGANIC CARBON
CONTENT FOR THREE TRACE
METALS
(All regressions signifi-
cant ac a <*.'0.05)
, JRB Associates _
.r- ..r.......
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There is widespread evidence in the scientific literature that the trace metal
•
content of marine and freshwater sediments is highly correlated with the concen-
tration of organic carbon in the sediment. Crecilius et al. (1975) demon-
strated this relationship for arsenic, antimony and mercury in the sedizents
of Puget Sound. This correlation is a result of the fact that organic mate-
rial serves as one of the major trace metal sinks in marine sediments. Organ-
ic substances and iron plus manganese oxides dominate the trace metal sorptive
properties of sediment (Jenne 1977; Jenne and Luona, 1975). Thus sediments
with a high organic content can generally be expected to exhibit a greater
affinity for trace metals, and therefore have a higher K_, than sediments with
a low organic content. Normalization of trace metal concentrations to,organic
content, by use of KO_, can be expected to provide a better estimate of parti-
tioning, in most cases, than use of K_ alone. There is some limited evidence
(Luoraa and Jenne, 1975) that such an approach may not be appropriate for zinc
and cobalt, but pending a thorough review of the anomalous behavior of these
two metals, KQC has been adopted throughout this report for all metals.
There are also biological considerations which support the normalization of K_
for trace metals to organic carbon. These are directly related to the concept
of biological availability. Most of the studies addressing uptake of trace
metals by sediments and organisms have demonstrated that trace metals in sedi-
ments with high concentrations of organic mace rial are less available to depos-
it-feeding organisms than are those in sediments with little organic matter.
For example, the uptake of mercury by both a polychaete and a deposit-feeding
shrimp was significantly less when the sediment was rich in organic matter
than when the mercury was associated with iron-oxides (Luoma, 1974). Iron-
oxide bound cadmium was more available to the clam, Macoma balthica. than was
organic-associated cadmium (Luoma and Jenne, 1975). Similar effects have been
demonstrated for silver and copper as well (Luoma and Jenne, 1975; Jenne and
Luoma, 1975). Consideration of organic content in the derivation of sediment
criteria for trace metals makes the criteria more stringent for sediments with
lower concentrations of organic matter. This is consistent wiLh observations
of Increased bioavallabllity of trace metals in low organic environments. How-
ever, there are exceptions to this generality such as zinc and cobalt which
demonstrate increased bioavailability in high organic environments (Luoma and
,JRB Associates —
17
-------
Jenne, 1975). Such exceptions may warrant further examination and may pos-
sibly require modifying the approach to sediment criteria for select trace
metals.
3.2.2 Synthetic Organic Compounds
Partition coefficients for the synthetic organic priority chemicals were calcu-
lated from empirical relationships of KQC versus KQW> the latter quantity
denoting the octanol-vater partition coefficient for a given organic chemical.
KQW is a good indicator of the relative accumulation potential of a checical
in the environment, specifically in biotic components, since it reflects the
influence of molecular properties on the affinity of the 'chemical for an
organic matrix. KQW is also useful in estimating a chemical's relative sorp-
tion potential on solid surfaces when coated with natural organic matter as is
the case with aquatic sediments. As mentioned earlier, there is ample evi-
dence that the affinity of an organic compound for sedimentary particles is
determined to a large degree by the concentration of organic carbon in the sed-
iment, hence the use of KQC versus KQy relationships is a highly advantageous
technique for estimating sediment water partition coefficients for a variety
of organic chemicals.
Estimation of K
KOW is usually determined experimentally by adding a small amount of the chem-
ical to an octanol-water mixture, allowing the system to reach equilibrium,
and then measuring the concentration of the chemical in each phase. Reliable
estimates of KQW have also been obtained by chromatographic techniques (Veith
and Morris, 1978), from other solvent-water partition coefficients (Leo and
Hansch, 1971), and by the fragment constant method (Hansch and Leo, 1979).
KQW values obtained by at least one of the above methods are available for
most organic compounds. The K values used in this study were obtained pri-
marily from Karickoff (1981) and Kenaga and Goring (1980).
Development of KOC/KQW Relationships
KQC values have been determined experimentally fo*. about 70 organic compounds
(Kenaga and Goring, 1980; Karickhoff, 1981). Figure 4 and Table 3 illustrate
the various regression equations that have been used to predict K from K .
The variability among the regression equations is a result of the different
. JRB Associates __
•18
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5 •
e:
c
3 •
2 •
.. 6
log K
7
ow
Figure 4
REGRESSION EQUATIONS FROM THE LITERATURE USED TO PREDICT KO(, FROM KQW
(Numbers on each regression line refer to the equation numbers in Table 3)
JRB Associates —i
19
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CD
o :
n
Table .1
REGRESSION EQUATIONS FROM THE LITERATURE FOR THE ESTIMATION OF K FROM K
(Modified from Lymnn ct al., 1982)
No.
Regression
Number of
Compounds
Considered r
Chemical Class
Reference
1 log K
OC
0.544 log KQU + 1.377
45 0.86 Pesticides
Kenaga & Coring, 1980
2 log K__ = 0.937 log KrtII - 0.006 19 0.97
ut> ow
. 3 log KQC = 1.00 log KQW - 0.21 10 1.00
Aroma tics, polynuclcar aro-
matics, triazincs, dinitro-
anilinc herbicides
Mostly aromatic & polynuclcar
aroma tics
Broun ct al., in prep.
Karickhoff ct al., 1979
4 log K = 0.94 log K... + 0.02 9
UL* UW
Triazincs and dinitroaniltne
herbicides
Lyman ct al. , 1982
5 log KQC = 1.029 log KQU - 0.18 13 0.95
Variety of herbicides, insec-
ticides, and fungicides.
Rao & Davidson, 1980
6 log KQC = 0.524 log KQW + 0.855 30 0.92
7 log K-. = 0.989 log Kni, - 0.346 5 1.00
UL* uw
Substituted phenyl ureas and
alkyl N-phcnylcarbamatcs
Aromatic & polynuclear aro-
matic hydrocarbons
Brices. 1973
Karickhoff, 1981
8 log K = 0.843 log K + 0.158 19 0.96 Priority pollutants
L/L» IJw
Present report
•• v
•i '•
-------
chemical compounds used to derive each regression. For example, regression
six was derived for phenylureas and phenylcarbamates, neither of which are"
relevant to environmental quality of Puget Sound. In order to obtain a K -
KOC reSression oost applicable to those compounds measured in Puget Sound sedi-
ments, only the chemicals which were among the 129 EPA priority pollutants
were considered. Nineteen priority organic compounds consisting primarily of
polynuclear aromatic hydrocarbons and chlorinated hydrocarbons were identified
for which literature values of KQW and KQC were available. From those com-
pounds a regression equation was derived and the uncertainty in the computed
KOC values estimated. The results are shown in Figure 5. Estimates of K
wW
obtained by this regression were calculated to have a standard error of about
x '
A3 (±0.48 on log scale) though the error is somewhat greater (* 3.1) at very
high or very low values of KQW and lower (J 2.8) for KQW values in the middle
of the distribution. A comparison of measured K values from the literature
with those predicted by the regression is shown in Table 4 for the 19 priority
pollutants on which the regression was based. On the average, predicted K
were within a factor of 2 (0.3 on log scale) of Che measured values. The
large deviation noted for hexachlorobenzene and pentachlorobiphenyl (nearly by
a factor of 10) suggests either that these compounds exhibit anomalous chemi-
cal behavior or that the experimentally measured K values may be in error.
The predictive capability of the KQW - KQC regression was tested for an addi-
tional 45 non-priority pollutants for which literature K values were avail-
uc*
able. These data are superimposed on the regression obtained from the
priority pollutants as shown in Figure 6. The predicted Krt_ values from the
uc*
regression are compared to the literature values in Table 5. In general the
predictive capability of the regression is satisfactory for a wide variety of
compounds. The KQC values for polynuclear aromatics and chloro-s-triazines
were particularly close to the literature values, generally within a factor of
2 to 2.5 (0.3 - 0.4 on log scale). The KQ(, values for organophosphates and
phenylureas were the least reliable, with an average error of about a factor
of 5.
3.3 CALCULATION OF SEDIMENT CRITERIA
Sediment criteria for both the trace metal and priority organic contaminants
considered in this study were computed using equation (4), Section 3.1.
. JRB Associates —
•21
. , - ,- ,- I'
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30
09
n
a"
s
11
6-
5 -
to
o
2 •
0
i.r.O.v-rci
•Pn.chlorobfiistnr
ow
Figure 5
REGRESSION OF KQC and KOW AS DEP n FOR mE 19 PRJORITY POLLUTANTS SHOWN
Uncertainty limits on either side >e regression line are the standard errors
-------
Table 4
COMPARISON OF KQC VALUES PREDICTED BY THE KOW-KoC REGRESSION WITH MEASURED Koc VALUES
FROM THE LITERATURE FOR THE 19 PRIORITY POLLUTANTS ON WHICH THE RKCRLESION IS BASED
(All literature values from either Karickhoff, 1981 or Konaga and Coring, 1980)
31
CO
8
n
5'
Compound
Aromatic hydrocarbons
Anthracene
P>-ei 3
Phenanthrene
Naphthalene
Dibcnz(a,h)anthracene
Benzene
Halogenated hydrocarbons
1,2-dichloroethane
1,1,1-trichloroethane
1,1,2,2-tetrachloroethane
Tetrachloroethylone
1,2-dichlorobenzene
Hexachlorobenzene
DDT
Y-BHC (Lindane)
a-BIIC
0-BI1C
Halogenated biphenyls
2,2* ,4,5,5'-pentachlorobiphenyl
2,2',A,A1,5,5'-hexachlorobiphenyl
2,2',4,4',6,6'-hexachlorobiphenyl
log KOW
(literature)
log KQC
log K
OC
1.45
2.47
2.39
2.53
39
23
98
3.72
3.81
3.80
6.30
6.72
6.3-'.
(literature) (predicted)
Error
4.40
5.18
4.52
3.31
6.50
2.12
4.32
4.88
4.24
3.03
6.22
1.95
4.63
5.62
6.08
,87
,52
,97
,94
64
95
1.51
2.25
1.90
2.56
2.54
3.59
5.38
3.30
3.30
3.30
1.38
2.24
2.17
2.29
3.02
4.57
5.20
3.29
3.37
3.36
5.47
5.82
5.50
Average 0.29
-0.13
-0.01
+0.27
-0.27
+0.483
+0.983
-0.18
-0.01
+0.07
+0.06
Average 0.25
+0.843
+0.20
-0.58a
Average 0.54
Error exceeds one standard error.
-------
6 •
5 •
u
• CO
• o
Lcplopho*
• I.O-T
• Ftnuron
• Trlelopy*'
•Flclorai
I-Hetho.»-).J.»-irlchlorop»rldlne
• •
Ipilln* F»nl«enloioph*nol
Xlichlor
•1.1.6-lilcMoro-l-pyrldlnol
•
Ulnottb
CD
0
lof. Kol,
Figure 6
K0r AND Kow VALUES FOR A5 Nf IORITY POLLUTANTS SUPERIMPOSED ON
THE REGRESSION DEK , FOR PRIORITY POLLUTANTS
-------
Table 5
COMPARISON OF KQC VALUES PREDICTED BY THE K^-ROW REGRESSION
WITH MEASURED KQC VALUES FROM THE LITERATURE FOR 45 NON-PRIORITY POLLUTANTS
(All literature values from either Karickhoff, 1981; or Kenaga and Goring. 1980)
Aromatic hydrocarbon*
9-oethylanthracene
2-Mthylnaphthalene
7.12-dlMChylbent(a)anchracene
Tetracene
3-oethyl cholanthrcne
Halogenated hydrocarbons
Methoxychlor
Chloro-s-triazines
Atrazlne
Propazine
Slzuxine
Trletazlne
Ipazlnc
Cyanazlne
Carbaoates
Carbaryl
Carbofuran
Chlorprophao
Methoayl
Organephosphates
Malathlon
Parathlon
Hethylparathion
Chlorpyrlfos
Leptophos
Phenyl ureas
Dluron
Feouron
Llnuron
Monollnuron
Monuron
Fluoaecuron
Miscellaneous
2,4-0 acid
Plclorao
2.4.S-T
Trielopyr
Trifluralin
2-aethoxy-3,5.6-trlchloropyridlne
Nitrapyrin
3.5.6-trichloro-2-pyridinol
13Hdibenzo(a.i)carbazole
2.2'biquinollne
Dibenzothlophene
Acetophenone
Terbacil
Brooacil
Dlnoseb
Pentachlorophenol
Alachlor
Propachlor
(Literature)
5.07
4.11
5.98
5.90
6.42
4.68
56
94
16
35
3.94
2.24
2.64
1.B9
3.06
0.30
2.89
3.81
3.32
4.81
6.31
2.57
1.00
2.19
1.60
1.90
1.34
1.56
0.30
0.60
0.48
5.34
4.28
3.41
3.21
6.40
4.31
4.38
1.59
1.89
2.02
3.69
5.01
2.92
2.75
log *x
(Literature)
.81
.93
.35
.81
.09
log K^
(Predicted)
4.43
3.62
5.20
5.13
5.57
4.90
17
41
25
74
91
2.26
2.36
1.46
2.77
2.20
3.25
3.89
3.99
4.13
3.97
2.60
1.55
2.93
2.38
2.14
2.24
1.30
1.23
1.72
1.43
4.14
96
62
11
02
02
05
54
1.66
86
09
95
28
2.42
Average 0.40
4.10 -0.80*
32
64
1.98
2.98
3.48
2.05
2.38
1.75
2.74
0.41
2.59
3.37
2.96
4.21
5.47
2.32
1.00
2.00
1.51
1.76
1.29
1.47
0.41
0.66
0.56
4.66
.77
.03
.86
.55
.79
.85
.50
.75
.86
3.27
4.38
2.62
2.48
Average
+0.15
+0.23
-0.27
+0.24
+0.57*
-0.21
0.28
+0.02
+0.29
-0.03
-1.79*
Average 0.53
-0.66*
-0.52*
-1.03*
+0.08
+1.50*
Average 0.76
-0.28
-0.55*
-0.93-
-0.87*
-0.38
-0.95*
Average 0.66
+0.17
-0.82*
-1.06*
-0.87*
+0.52*
+0.81*
+0.41
+0.75*
-0.47*
-0.23
-0.20
-0.04
+0.09
-0-
+1.18*
+1.43"
+0.34
+0.06
Average 0.53
•Error exceeds one standard error.
'25
. JRB Associates _
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3.3.1 Trace Metals
Sedlmenc criteria were calculated based on the K values derived from Brannon
et al. (1980) and Che available water quality cricerla for protection of salt-
water aquatic life. The results are summarized In Table 6 together with the
corresponding water quality criteria. The standard deviation reflects the
uncertainty in the KQC values. Though many of the trace metal water quality
criteria presented are draft criteria, they were chosen as representative of
the most current toxicological information available.
3.3.2 Synthetic Organic Compounds
The derived sediment criteria for 47 priority organic compounds measured In
sediments of the Central Basin of Puget Sound (Pavlou et al., 1983) are pre-
sented in Table 7. These criteria were based on the K__ values estimated from
regression equation 8, shown in Table 3. Again the associated standard error
reflects the uncertainty in the K values as discussed in Section 3.3.1.
Though both acute and chronic sediment criteria are presented when available,
the chronic value is recommended in order to insure adequate protection of mar-
ine life. Specifically, chronic sediment criteria are more appropriate than
acute,values since: (1) sediment contaminant concentrations reflect long-term
conditions and do not demonstrate the extreme temporal variability of water
column contaminant concentrations; and (2) benthic organisms often lack the
mobility required to escape a contaminated environment and therefore are sus-
ceptible to impacts resulting from long-term 'chronic exposure. However, no
chronic criteria are currently available for the majority of organic compounds
and in these cases only acute sediment criteria have been presented in Table
7. It may be possible to establish an estimated chronic criteria by one of
two methods: (1) for those compounds having a freshwater chronic criterion
this may be used as an estimate of the saltwater criterion; and (2) the
chronic criterion can be estimated from the acute criterion using the general
"rule of thumb" that the acuterchronic ratio is 100:1. Both approaches war-
rant further consideration but a review of the toxicological literature is
necesary to determine if one or both api-jaches would be suitable for esta-
blishment of interim sediment criteria gui^lines.
It is Important to note that for many compounds EPA has not established a
water quality criterion but only identifies the lowest concentration at which
. JRB Associates _
26
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10
VI
Table 6
SUMMARY OF DATA USED TO DEVELOP SEDIMENT CRITERIA FOR TRACE METALS
EPA Water Quality3 . Sediment Criteria
riinm-i.--.i Criteria (|ig/£) S/CR/OC X °'Cm
c.
3)
00
1
u
M
(Trace Metals) Acute Chronic (KOC±o)xl° Acute (o)
Arsenic*3b 120 63 1.3*1.2 1,600 (±1,400)
Cadmlumb 38 12 6.4 ± 8.6 2,400 (±3,300)
Copperb 3.2 ... 2.0 170±210 5,400 (±6,700)
Leadb 220 8.6 38 ± 40 84,000 (±88,000)
Mercuryb 1.9 0.10 0.8+1.1* 15 (±21)
(inorganic)
•
Zinc 170 58 33 ± 63 56,000 (±110,000)
Chronic (o)
820 (±790)
770 (±1,000)
3,400 (±4,200)
3,300 (±3,400)
0.8 (±1.1)
19,000 (±38,000)
Acute water quality criteria are the maximum permissible concentrations for protection of saltwater
aquatic life as obtained from the Federal Register, Vol. 45, No. 231 (1930) or, in the case of some
trace metals from draft criteria documents soon to be released. Chronic criteria arc 24-hr average
concentrations when obtained from the Federal Register or 30-day average when obtained from draft
criteria documents.
Dral • c iteria documents.
-------
Table
7
SUMMARY OF DATA USED TO DEVELOP SEDIMENT CRITERIA FOR ORGANIC COMPOUNDS
Cecpound
Phenol
Acenaphthene*
Aathracene*
Bento(e)anthracane*
Benio(a)prrene*
8enio(b)fluorenthene*
Benio(k)flueranthene*
•luoranthene
riuorene*
Nephthaleiw*
Phenan t hrene*
Acenaphthalene*
9Ibeni(a.h)anthracene
Iiophorone
Kltrobeniene
1.2-dlchlerebcniene
l.4>dlchlorobcnicne
2,6-dlnltrotoluene
Benco((.h.l)peryleae
Chryiene*
Indenepvrene
Pyrene*
Butylbeniyl phthalate
Dl-n-buf)l phthalace
Dl-octyl phthalatr
Dlethyl phtnalate
Dlaethyl phthalate
He&achlorobuudiene
•
o-BHC
Lladane*
D30*
D3t*
03T*
Aldrin*
2-PCB*
3-KB*
t-PCB*
3-PCB*
6-PCB*
Beaiene
Ethvlbenzene
Hethvl chloride
Methylene chloride
Tetrachloraethylene
Toluene
Trichloroethvlene
l.2-0lrhloropropane
Veiar Quality
Acute Chronic
2.900*
A J«* _ _ _ f
•7S 333
lio*-'
ft d U
ISO*''
130*''
ISO*1'
20* .»
*U *J
130*''
I 174*
• • i * *
ISO*1'
ISO*1'
ISO*1'
6.430*
3.340*
M* «.«•
63
80* Oj»
-90*
«• TV
ISO*1'
ISO*1'
,.„».(
ISO
1.472*-'
1.47:*''
I.4T2'-'
I.4T:'1'
16*
f
0.17
01 A&
• JO
i •'
1.8
_•
7
0.138 0.0016
i • J
M Ml *•*••
O.OJ4 '•
t m
O.OI4-'*
M Ml *f . ft
0.014 •»
r _
0.014 •»
0.014f'«
2.SSO* 330*
3*4*
•to j
».000* 3.200*
6.000* 3.200*
3.100* 223*
3.JSO* 2.500*
1.000*
3.13.0* l.s:0*
lot "o«*
1.46
4.17
4.40
3.61
6.31
6.37
6.84
S.33
4.18
3.31
4.32
4.07
6.30
1.67
1.83
3.40
3.37
2.03
7.23
3.61
7.66
3.18
4.03
3.20
9.20
1.40
1.61
3.74
3.81
3.72
6.03
3.74
3.98
••V
4.81
3.38
3.73
6.30
6.37
2.12
3.13
0.91
1.23
2.33
2.21
2.42
2.28
«^b.c
24
4.700
7.400
37.000
300.000
300.000
840.000
43.000
4.800
890
9.300
3.900
160.000
37
30
1.100
1.000
77
1.830.000
77.000
4.100.030
33.000
3.700
33.000
82.000.000
22
33
2.000
2.300
1.930
180.003
99.033
160.000
h
400
4.600
73.003
100.000
370.000
300.000
97
630
8
16
200
100
160
120
fedlMnt Criteria
Acute d Chronic'
"~~^~^~
70
2.300 1.650
1.100
3.300
43.000
73.000
123.000
900 340
700
1.030
1.400
600
24.000
240
163
90 70
«O 03
_ _
270.000
11. sop
600.000
4.930
3.300
50.030
120.000.000
'
32
0.49
0.31
323
700
21 0.16
0. 52
0.064
1 .0
1.4
5. 2
7
245 34
140
48
95 SO
1.003 43
313 230
160
600 1 .O
•Criteria for the,, co.pound, te.t.d .(.in.t ..a.ur.d concentration, in PuS.t Sound (... Section 4.3).
^ »«1«» fro. Call.han ., .1. (1,79); Dexter (1976); K.n.S, and Coring (1980). V.lth et al. (1980)
Derived from regression 8 in Table 3.
'Standard error of K^ value. J 3. 931 confidence Interval * |0.
Standard error of ..dlnen, criteria J 3. 9SZ confidence Int.rv.l ? 10.
c-rlfikoff » • p«™« -.- • c,
Associates «
-------
adverse biological effects have* been reported. In these cases, a sediment cri-
terion has been determined on the basis a water quality "criterion" esta-
blished at one half the lowest concentration causing adverse biological
effects. The procedure closely parallels the protocol followed in developcent
of water quality criteria in which a Final Acute Value (FAV) designed to pro-
tect 95 percent of a diverse group of species is determined, and the criteria
is established at one half of the FAV. This approach has been adopted as an
Interim attempt to estimate the concentration at which a water quality criter-
ion may eventually be established. However, it is Important to recognize chat
for soae compounds the lowest concentration causing adverse effects is based
on a very limited toxicological data base. In these cases the estimated water
quality "criterion" used in this report could be substantially different from
the value eventually established. Therefore, these "criteria" may be inade-
quate to insure protection of marine life, and therefore any violation of
these "criteria" could be of serious consequence.
The EPA water quality criteria for-the PCBs, phthalates and polynuclear aroma-
tic hydrocarbons are class criteria based on the cumulative concentration of
all members of the class. In the derivation of the sediment quality criteria,
it has been necessary to apply the class criterion to each member of the class
individually, since each has a unique KQ . In environments where one class
member comprises the majority of the sediment burden of the class, this
approach should prove adequate. However, if numerous class constituents are
significantly enriched, a safe threshold for the class as a whole may be
exceeded even though no individual constituent violates the criteria.
3.4 LIMITATIONS
Although the advantages of using the equilibrium partitioning approach were
presented earlier in this report, there are a number of limitations inherent
in the approach that must be considered as well. These are discussed below
together with their implications in the use of the equilibrium partitioning
approach.
3.4.1 Lack of Comprehensive Water Quality Criteria
The equilibrium partitioning approach has the advantage of providing a simple
mechanism whereby water quality criteria can be adapted to sediment quality
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criteria. However, this fact is also a limitation in that sediment criteria
can only be established for those compounds for which water quality criteria
are available. For the majority of synthetic organic contaminants, EPA has
not yet established water quality criteria. This problem was addressed by
using one half the lowest concentration causing adverse effects in cases where
definitive water criteria were not available. As additional water quality
criteria are established by EPA, sedicent criteria can be readily determined
for the same compounds.
3.4.2 Synerzisa and Antagonism
Synerglstlc or antagonistic interactions among contaminants can result in a
mixture of contaminants having either a greater or lesser toxicity than would
be expected simply on the basis of the toxicitles of the individual contami-
nants. Thus there is some danger that although all individual contaminants
may be at concentrations below criteria, synergistic interactions may still
Induce adverse biological inpacts. While sediment criteria should ultimately
account for synergistic effects, there is at present no way to do so given our
current state of knowledge. The proposed criteria derived by the equilibrium
partitioning approach represent an interim solution of immediate applica-
bility. The only means currently available to address synergism is by using
bioassay methods. Therefore the optimal approach to insure protection of
marine life may be one whereby bloassays and the partitioning method may be
used concurrently.
3.^.3 Level of Uncertainty in the Sedinent Criteria
Unlike federal water quality criteria, the sediment criteria proposed in this
report are presented as a mean with a specified level of uncertainty. This
uncertainty is a result of our inability, based upon the current state of know-
ledge, Co accurately predict the degree of partitioning of a contaminant
between sediment and water. The water quality criteria is considered as a
fixed value, therefore the level of uncertainty associated with the sediment
criteria is entirely a consequence of the uncertainty in the K__ value.
UL
A number of options are available to environmental managers in attempting to
implement a sediment criterion with a given level of uncertainty. One pos-
sible approach is to establish an alert level at the mean sediment criterion
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and a maximum permissible sediment contaminant concentration at Che upper
bound of Che uncertainty limit. A sediment in which Che concentration of
contaminant falls between the mean criterion for that contaminant and the
upper bound of the uncertainty level could be identified for further studies
such as bloassays in order Co demonstrate the absence of any environmental dan-
ger. For those sices at which a contaminant concentration exceeds Che upper
bound of Che uncercainty limit, iomediace corrective action may be required.
This upper uncercaincy limit could be established either aC one standard devia-
tion froia Che mean or aC Che 95* confidence liolc depending upon Che degree of
conservatism desired.
3.5 ASSUMPTIONS
A number of necessary assumptions have been incorporated in developing the
equilibrium partitioning approach Co sediment criteria. These are listed in
Sections 3.5.1 through 3.5.5 below. Section 3.5.6 summarizes Chese assump-
tions and provides qualitative estimates of Che impact on Che criteria should
Che assumptions be violated.
3.5.1 Validity of The Equilibrium Assumption
The basic premise in Che equilibrium assumption is that che distribution of a
contaminant at the sediment-water interface is under thermodynamlc equilibrium
and che ratio of Che contaminant concentration in Che solid phase to its con-
centration in che aqueous phase is a constant. This assumption should gener-
ally hold except as che concentration of Che contaminant approaches saturation
at which point Che solid phase:aqueous phase ratio may no longer be constant.
However, Chis is noc expecced Co significancly impacc Che equilibrium approach
Co sedlmenc criteria since che criCerion for a contaminant should be violated
long before saturation is reached. Ic is possible Chat in che natural environ-
ment under cercain physical/chemical condicions, kinecically concrolled adsorp-
Clon may be operable, which may violate Che equilibrium assumption. These
processes are complex and poorly understood (Lyman ec al., 1982).
3.5.2 Normalizacion jf K Co Organic Concent
Throughout chis reporc organic carbon content of che sediments has been con-
sidered a major environmencal variable in determining che sediment-water parti-
tioning for both trace metals and synchetic organic compounds. Juscification
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for using KO(, rather Chan K^ was provided in Section 3.1 for the organics and
Section 3.2.1 for the trace metals. Though this appraoch is considered gener-
ally applicable, it may be necessary to modify it for a few select trace
metals as discussed earlier (e.g., zinc). Such a determination would require
careful review of existing literature and potentially additional experimental
work.
3.5.3 Influence of Environmental Variables on Kn_
""^™~—™ ™^~~™* "™"•^•^^"^ UC
Although as discussed above, organic carbon appears to be an important var-
iable influencing sediisent-uater partitioning other physical/chemical factors
nay affect the partitioning process. A brief discussion of the most important
variables is presented below.
Reduction/Oxidation Potential and pH
Most of the organic contaminants of greatest environmental concern are the
base-neutral compounds. These chemicals are relatively insensitive to changes
in the reduction/oxidation (redox) potential or pH. However, for the trace
metals, a change in the redox potential or pH can result in a change of oxida-
tion state and/or chemical speciation and thereby dramatically influence the
sediment-water partitioning and toxlcity of the metal. The approach used in
this report to derive K_ values for trace metals was designed to take into
account the dependency of partitioning on a variety of environmental var-
iables, while recognizing our Inability to predict these dependencies with our
current limited of knowledge. Trace metal K__ values were determined for a
uc
wide variety of environments (diversity of site locations) and then used to
calculate an overall mean and standard deviation. Therefore, the variability
in KQC induced by the site specific reduction/oxidation conditions or pH is
assumed to be incorporated into the estimate of the uncertainty about the mean.
Temperature
This physical variable may have a small influence on the partitioning of a
chemical ' etween sediment and water. For most contaminants, an increase in
temperature usually results in a decrease in K._, though there are exceptions.
uc
Lyman et al. (1982) calculated that a 10% decrease in KQC could be typically
expected for an increase in temperature from 20"C to 30s C. An 18% Increase
would be expected for a temperature decrease from 20° C to 5° C. Considering
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that Che values of KQC used in the derivation of sediment criteria have a stan-
dard error of a factor of 3, the uncertainty introduced by variations in temp-
erature is negligible.
Salinity
This variable may have some influence on K , though as with temperature the
impact is minimal. Karickhoff et al. (1979) reported a 15% increase in X_
with a change in salinity from 0 to 20Z. Salinity may be of greater impor-
tance for the organic acids, though the extent of this importance is dependent
upon the relationship of pH to the pKfl of the acid (Pionke and Chesters,
1973).
The salinity of the deep water layer in Puget Sound is fairly uniform and
constant, although some variability is expected in the nearshore environments,
specifically in the urban eiabayments. This variability may reflect small-
scale circulation phenomena- and tidal mixing. It should be pointed out that
the salinity in the water column may not be as important to the equilibrium
partitioning approach as variations of ionic strength within the interstitial
water.
Dissolved Organic Matter
Natural dissolved organic matter (DOM) consists primarily of refractory poly-
electrolytes resulting from the degradation of biological materials (Christman
and Minear, 1971). The DOM forms stable solutions which can scavenge trace
metals or organic chemicals either through electrostatic interactions (ion-
ion, ion-dipole or ligand) or through hydrophobic interactions with non-polar
sites of the DOM. At the sediment-water interface these interactions may
enhance the contaminant levels in the aqueous phase with the net result being
a reduction in the partition coefficient value.
The implication of this phenomenon is twofold (1) under these conditions, the
derived criterion should be a lower value, and Ci) if direct uptake from inter-
stitial water is the dominant mechanism of binaccumulatlon, contaminant bio-
availability will be increased. To this date these processes have neither
been investigated nor well understood due to their complexity. It should also
be noted that any elucidation of the chemical interactions at the sediment-
water interface will be further complicated by the effect of pH or ion content
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changes which In turn would influence Che degree of ionizatlon, che effective
charge density and the chemical form of the DOM.
Particle Size
The importance of particle size in determining the magnitude of the sediment-
water partition coefficient is largely a function of organic carbon content.
Sediments with a high percentage of silts and clays generally have a high
organic carbon concent and consequently have a higher sediment-water partition
coefficient (KQ). Sandy sediments have little organic carbon and have a lower
partition coefficient. Crain-size dependent variations of the partition coef-
ficient as a consequence of organic content is accounted for by expressing the
partition coefficient as a K.. value rather than K_.
There is some limited evidence that surface area and other factors related to
grain size may affect the partitioning beyond that which could be explained
solely on the basis of organic carbon content. Karickhoff et al. (1979)
examined the partitioning of pyrene and methoxychlor on a variety of particle
size fractions. While K remained essentially constant for all size frac-
tions from coarse silt to clay, the sand fraction exhibited a K only 20% of
that derived from the fines. For sediments with a high percentage of sand
(> 95%) some correction of the K va
tide size effects (Karickhoff, 1981).
(> 952) some correction of the K value may be required to account for par-
oc
As it pertains to sediment criteria, the work of Karickhoff suggests that in
very sandy sediments, pollutants would have a lower affinity for sediment
particles than predicted on the basis of a generalized K . The sediment
quality criteria for very sandy sediments would therefore be too high to
provide adequate protection. Further laboratory work and field verification
is necessary in order to define the dependence of K__ on particle size. In
the event such a dependence is established sediment criteria could easily be
adjusted on the basis of the percentage of sand as well as on the organic
carbon content.
3.5.4 Bioavallability of Contaminants at the Sediment-Water Interface
The soluble fraction of a contaminant is generally readily available for up-
take by marine organisms (Jenne and Luoma, 1975; Roesijadi et al., 1978).
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Therefore it is a relatively simple matter to establish a permissible concen-
tration of a contaminant in water. However, the development of sediment
quality criteria is complicated by the fact that the bioavailability of a
contaminant in sediments is strongly dependent upon specific geochemical asso-
ciations. Although the sediment quality criteria make the assumption that all
of the contaminant in the sediment is in a bioavailable form, this is in fact
rarely the case, for the total amount of a contaminant does not necessarily
reflect its potential for biological effects.
As an example, Luooa and Jenne (1975) exposed clans to a variety of metal-con-
taminated artificial sediments including iron oxides, manganese oxides, cal-
cium carbonate and an organic detritus. The concentration factors for the
trace metals in clam tissue varied over two orders of magnitude depending upon
the type of sediment in which they were held. The dependence of bioavail-
ability on geochemical associations between a contaminant and sediments is
probably most critical and best documented for.trace metals but may be of sig-
nificance for organics as well.
The question of bioavailability is not adequately treated in the sediment
quality criteria proposed, since the criteria are given for the total contami-
nant in the sediment. It would be advantageous if criteria could be developed
only for the bioavailable portion of the contaminant rather than the total con-
taminant load. Such an approach would require additional research but is not
infeasible. A number of investigators have used sequential leaching techni-
ques to extract only select fractions of the total contaminant load in sedi-
ments (Brannon et al., 1980; Vangenechten et al., 1983). If an extraction
procedure can be found which will reliably identify the bioavailable portion
of the total contaminant load, then a sediment criteria can be expressed in
terms of the amount of the contaminant extracted by that procedure.
3.5.5 Applicability of Water Quality Criteria to Benthic Organisms
EPA water quality criteria for the protection of saltwater aquatic li 'e are
designed to insure that the concentration of contaminants in the aqueous phase
do not exceed a level which would Induce adverse effects in marine biota. In
adapting the water quality criteria to sediment criteria, two assumptions have
been made: (1) the permissible concentration of a contaminant in the aqueous
35
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phase, as defined by Che'water quality criteria, are within safe limits for
the protection of benthic organisms; and (2) ingestion of sediment-bound con-
taminants by benthic deposit-feeders does not result in a greater uptake of
contaminants than that predicted by exposure to dissolved contaminants alone.
It is important to consider if benthic organisms would be afforded adequate
protection by application of water quality criteria to the interstitial water.
EPA water quality criteria are established on the basis of bioassays conducted
with representatives of a number of phyla. Though the test organisms are typi-
cally free-swimming (e.g., fish, shrimp) a number of benthic invertebrate
species have been included. Stephan et al. (1983) provides a list of marine
species used in toxicity tests and includes a large number of polychaetes, mol-
luscs and benthic crustaceans. Since benthic organisms have been employed in
the derivation of criteria, these criteria should provide adequate protection
to these animals. Additionally, there is no evidence to indicate that, as a
group, benthic organisms are any more sensitive to dissolved contaminants than
organisms in the overlying water column.
The role of uptake of sediment-bound contaminants by ingestion is a critical
question in application of any type of sediment criteria. Not only are ben-
thic organisms exposed to contaminants dissolved in the interstitial water,
but they may ingest sediment particles during feeding activities and absorb
sediment-bound contaminants through the gut wall. The concentration of con-
taminants on the Ingested particle may be several orders of magnitude greater
than in the interstitial water, but the amount of particle-associated contami-
nant available to an organism during passage through the gut depends upon the
strength of the contaminant-sediment bond.
The equilibrium partitioning approach to sediment criteria does not discount
the potential for uptake of contaminants by ingestion but only assumes that
the contaminant body burden of the organism is independent of the route of
uptake. If a system containing sediment, water and an orgaiism is allowed to
come to equilibrium, the level of a contaminant in each component should reach
a constant, predictable concentration. For the purposes of the partitioning
approach, it Is assumed to be Irrelevant whether the organism obtains the con-
taminant from the interstitial water or ingested sediment since the equili-
brium body burden would be the same regardless of the route of uptake.
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The experimental evidence•available to support this assumption is very limited
due to the experimental difficulties involved in assessing the route of pol-
lutant uptake. The limited evidence seems to indicate that for the transura-
nium elements (plutonium, aoerlciua) and some trace metals, ingestlon of
sediment does not significantly increase the body burden above that attribu-
table to absorption from the interstitial water (Renfro, 1973; Beasley and
Fowler, 1976; Miramand et al., 1982; Vangenechten et al., 1983). Uptake of
other trace metals and polychlorinated biphenyls on the other hand, may occur
largely by ingestlon of sediment as shown by a number of laboratory studies
(Luoma and Jenne, 1975; Courtney and Langston, 1978; Fowler et al., 1978).
The study of Fowler et al. (1978) is especially significant since the animals
were allowed to reach equilibrium with the surroundings. In this case, organ-
isms permitted to ingest sediment attained body burdens of PCB two orders of
magnitude greater than those exposed to PCB in the dissolved form. It should
be pointed out,.however, that available experimental evidence is inadequate to
either prove or disprove the assumptions of the equilibrium •partitioning
approach regarding the Importance of contaminant uptake by ingestion. For
most of the studies, the evidence presented is Inconclusive or the experi-
mental artifacts introduced are so great as to bring into question the applica-
bility of the results to natural systems. Additional research is necessary to
adequately evaluate the importance of pollutant uptake by ingestion of sedi-
ment.
3.5.6 Summary of Assumptions
Since Che equilibrium partitioning concept represents a new and unique
approach to sediment criteria, the analyses and evaluations presented in this
report have focused on the identifications of all assumptions inherent in the
approach. None of the assumptions are considered significant enough to inval-
idate the approach, but it was deemed essential to assess their potential
impact. They have been discussed at considerable length both to insure
against misuse of the approach and to direct further efforts of refinement.
The assumptions presented above are summarized in Table 8 and cross-referenced
with the report section In which they are discussed. For each assumption a
potential for violation has been given which represents the likelihood (high,
medium or low) that the assumption may prove invalid by further investigation.
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Table 8
ASSUMPTIONS OF THE EQUILIBRIUM APPROACH
AND THEIR POTENTIAL FOR VIOLATION
Assumption
Sediment-water partitioning
of • contaminant !• at
equilibrium
Magnitude of partition coef-
ficient dependent upon tedl-
oent organic content
Variations In the redox
potential and pH will not
impact criteria
Independence of partition-
ing on tecperature
Independence of partition-
Ing on salinity (ionic
strength)
Independence of partition-
ing on dissolved organic
matter (DOM)
Particle size Is not
important in determining
partitioning other than as
• covariate with organic
carbon
Entire contacinant burden
of sediments Is In a blo-
•vallable fora
Uater quality criteria are
appropriate for benthie
organisms
Ingestion of sediment-
bound contaminants by
deposit-feeders does not
Increase contaminant body
burden above levels attained
by exposure to the dissolved
contaminant fraction
Report
Section
3.S.I
3.5.2
3.5.3
3.5.3
3.5.3
3.5.3
3.5.3
3.5.4
3.S.5
3.5.5
Potential for
Violation of
Assusrtien
Mediua
Lew (organlcs)
High (eetals)
Low (base-neutral
organlcs); High
(aetals and some
organlcs)
Low
Medius
Medium
Low
High
Low
Medium
Impact of Violation on Proposed Criteria
Criteria Bay be too conaervative. Violations
would be site-specific and source-specific.
not compound-specific.
At low organic carbon levels the proposed cri-
teria would be too conservative. At high organl.
carbon levels the criteria would be liberal.
The effect of redox potential on trace metal
partitioning has been largely accounted for by
empirical derivation of partition coefficients.
In some Instances, the redox potential may effec1
partitioning beyond Che level already accounted
for. Field verification is needed to- determine
potential Impact on criteria.
Typical environmental variations in tecperature
will effect criteria by 102 or less.
For most contaminants of environmental concern.
variations in salinity typical of marine waters
will have a negligible Impact on the criteria.
Variation in salinity between fresh and salt-
water could effect criteria by about 251. An
Increaye In ionic strength of interstitial
water would result in a higher criteria val
therefore criteria cay be too conservative.
Criteria would be lowered as DO". Increases.
Criteria Bay be too liberal.
Evidence to date is very Halted but in very
sandy sediments criteria ma> be too liberal.
If a fraction of the contaminant is not bio-
available, the proposed criteria would be too
conservative.
Criteria would be either too liberal or too
conservative depending upon toxicant sensiti-
vity of benthlc organisms.
Criteria would be too liberal if assumption
were violated.
38
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Many of Che assumptions are unavoidable because of Che inadequacy of our
current state of knowledge. In these cases the potential for violation repre-
sents a "best guess" by the authors based on the limited infornation avail-
able. Should any of the assumptions be violated, the potential impact on the
•
proposed criteria is also given. The potential impact is quantified in some
cases (e.g., temperature and salinity) though for most assumptions ic is
impossible Co go beyond a qualitative statement of potential Impact at this
time.
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4.0 FEASIBILITY TESTING IN PUGET SOUND
4.1 FORMAT OF PRESE*?TATION
In order to compare a measured contaminant concentration in Puget Sound with
the sediment criterion for that compound it is cost convenient to use equation
(5) Section 3.1 and represent criteria limits as a plot of contaminant concen-
X
tration Ce/cR versus percent organic carbon (Figure 7). These plots (diagonal
lines) can be produced showing both the acute and chronic criteria as well as
the bounds for the uncertainty Halts around the criteria. For the purpose of
this report, the plots from now on will be referred to as the "criteria-graph"
for the contaminant of concern. Specifically, the criteria-graphs are deter-
mined by converting the organic carbon normalized criteria (Cc/rR/oc °^
Tables 6 and 7) to equivalent dry weight normalized concentrations (C* /__) at
.X S/CR
a given organic carbon content. For example, the chronic Cc/CR/OC
for Pb is 3,300 ppm. For sediments with 102 organic carbon (0.1 g o.c./g
sediment) the permissible concentration of lead in the sediments for protect-
ing the biota from chronic toxicity is 330 ppm. The criteria-graphs present
the permissible sediment contaminant concentrations at any specified organic
carbon content.
The contaminant concentrations and organic carbon content at sites of concern
can be plotted on the graph and readily compared to a criterion. Those sta-
tions to the left of a criterion line are below the criterion, while those to
the right of the line exceed criterion. In the example of Figure 7, Station A
Is below the chronic criterion for lead. Station B exceeds the mean criterion
but is within one standard deviation and station C exceeds the criterion by
more than one standard deviation. The example also illustrates the importance
of considering organic carbon content as well as contaminant concentration in
assessing the extent of contamination. Station A is the only station below
criterion despite the fact that it has a greater contaminant burden on a dry
weight basis than Station B.
' couple of points are important to bear in mind in evaluating Figure 7 and
similar figures throughout Section 4.3. First, in determining the KQC for
trace metals, the standard deviation of the KQ. was found to be greater than
the mean value (see Table 1). When the uncertainty of the K0_ is Incorporated
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3D
00
n
5*
I.RAI)
•I 9M r.l.
(rhmnlc)
•i «** c.i. «i «.*.
(rlircnlr) (chronic)
0.1
*l «» r.l.
(chronic)
c.l.
(iculr)
Concentration of Lead in Sediment (*ig/g dry weight)
Figure 7
PRESENTATION FORMAT FOR COMPARISON OF SEDIMENT CRITERIA
WITH ACTUAL MEASURED CONTAMINANT CONCENTRATION
-------
in Che derivation of sediment criteria for trace metals, the criteria minus
•
one standard deviation lies below a concentration of zero. Therefore it is
only possible to show the criteria plus one standard deviation on the cri-
teria-graphs for trace metals. A similar problem is not apparent in the cri-
teria-graphs for synthetic organics since the criteria for organics were
derived on the basis of the KQy - KQC regression in which the standard error
of KQC was less than the mean. Therefore both an upper and lover standard
error can be shown for the organics.
Secondly, the 952 confidence interval is equally as valid as the standard
deviation or standard error as a measure of uncertainty around the criteria.
Both the 95% confidence interval and the standard deviation are shown in
Figure 7 but only the standard deviation or standard error are shown in later
figures in Section 4.3 in order to simplify the presentation. It is possible
to calculate 95% confidence intervals using the methods shown in Sokal and
Rohlf (1981) and numerous other statistics books. For all the trace metals,
the 95% confidence intervals would appear on the criteria-graphs at approxi-
mately the same position relative to the mean and standard deviation as is
shown in Figure 7. For the synthetic organics, the 95% confidence intervals
would appear on the criteria-graphs as symmetrical about the mean, located at
a distance approximately two standard errors from the criteria value.
4.2 TRIAL DATA SETS
To test the applicability of the derived criteria values to Puget Sound, two
Independent data sets were selected that had sufficient ancillary information
to allow direct comparisons of contaminant sediment concentrations to the
numerical criteria values computed by the equilibrium partitioning approach.
1. The first set of test data used was that published by Malins et al.
(1980), encompassing six embayments in Puget Sound (Commencement Bay,
Elliott Bay, Sinclair Inlet, Port Madison, Case Inlet, and Budd Inlet).
These subregions arr Known to vary in degree of contamination and
therefore provided a '-j.de enough spectrum of contaminant concentrations
in sediments to determine the extent of sediment criteria violations.
The data used in the analyses are presented in Appendix A of this
report and extracted from Appendix 0 (Results of Chemical Analyses)
Tables D-2, D-3, D-4, D-5 and D-7-from Malins et al. (1980).
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2. Sediment criteria were also tested by comparison with the concentration '
of contaminants in sediments measured in Elliott Bay and within the
vicinity of the West Point Outfall as published in the Metro/TPPS Draft
Report (Pavlou et al. , 1983). These measurements constitute the most
recent information on toxicant accumulation in sediments in this urban
environment. The concentration data of the priority compounds used are
presented in Appendix B of this report and were extracted from Appen-
dices 7A.1, 7A.2 and 7B.1 of the Metro/TPPS Report, Volume I. The zone
designations for the specific subregions used were: Area EE, Central
Elliott Bay; Area B, South Elliott Bay; Area C, Eastern Elliott Bay;
and Area D, Northeast Elliott Bay/Denny CSO area. The West Point sam-
pling sites used were those included in Area F.
The Metro/TPPS data did not include measurements of sediment organic
carbon content taken concurrently with the samples for chemical analy-
sis. However, since the percentage of silt and clay particles in sedi-
ments is highly correlated with the organic carbon content, it is pos-
sible to estimate organic carbon content from grain size data. Grain
size and organic carbon content data from Malins et al. (1980) was used
to develop a regression which defined the relationship between these
variables (Figure 8). ^Metro/TPPS grain size data was then used to
estimate the organic carbon content of these sediments (Appendix C).
While this approach is the only alternative when organic carbon data is
lacking, it should be noted that the procedure adds an additional
degree of uncertainty in determination of the appropriate sediment cri-
teria.
4.3 COMPARISON OF MEASURED CONCENTRATIONS WITH DERIVED CRITERIA
The sediment contaminant concentrations in the trial data sets of Malins et
al. (1980) and Metro/TPPS were compared to criteria levels using the graphical
approach discussed above in Section A.I. The data from each test station were
illustrated as a scatterplot on a graph of sediment contamlnan' concentration
vs. percent organic carbon. The criteria-graphs were superimposed upon these
same plots using the solid and dashed lines to represent acute and chronic cri-
teria, respectively, as demonstrated in Figure 7. The results of the compari-
son of measured concentrations with criteria are Illustrated for the trace
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a)
CD
!
o
S"
m
I
t-1
W
It
to
u
u
l<
01
PL,
2 •
Z o.c. « 0.03 (S fines) *0.32
r = O.M, u <0.0l
0 10 20 10 /.O 50 hO 70 80 «)0 100
Percent Fines (pnrtir.les
-------
metals (Figures 9-14) and for the synthetic organics (Figures 15-23).
Illustrations are shown only for nine organic compounds. An additional 14
compounds were also examined as designated in Table 7, though observed
concentrations were generally well below criteria.
Examination of the graphs reveals the following:
• For the trace metals examined, the chronic criteria is exceeded in the
order: Hg>Pb>Cu>As>Zn>Cd. Acute values are exceeded primarily by the
metals Hg>Cu>As; no violations are apparent for Cd, Zn and Pb. Among
the subregions examined, proposed criteria are exceeded most frequently
in Elliott Bay and Commencement Bay. Chronic criteria for Hg are
exceeded in all areas suggesting that the criteria for Hg may be
unreallstically low.
• For the synthetic organic compounds tested, the absence of chronic cri-
teria for most contaminants prevented an evaluation of the significance
of the observed levels. However, for PCBs and DDT chronic values are
obviously exceeded within the most contaminated urban embaynents.
Acute values for the remainder of the chemicals examined were exceeded
only by fluoranthene, phenanthrene and pyrene within a fairly localized
area north of the West Point Outfall. It should be noted however that
for most of the polynuclear aromatic hydrocarbons (PNAs) the criteria
values used are both class criteria and one-half the lowest concentra-
tions at which toxic effects have been noted as reported in the Federal
Register, Vol. 45, No. 231 (1980). Individual compound criteria may
therefore be substantially lower, thus increasing the probability of
violations within the regions examined. Similar limitations should
also be considered in the use of class chronic criteria for PCBs.
• Most of the measured contaminant concentrations which exceed the
derived sediment criteria fall within plus one standard deviation or
standard error of the mean criteria values as computed from the uncer-
tainty assigned to the partition coefficient quantities (K_p). This
may have some implication on the enforceability of the numerical action
levels computed by this approach (see Section 3.4.3).
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o
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01
u
Lj
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O.
10
ARSENIC
0.1
V Elliott Bay. HETRO/TPPS
Quest Point. MF.TRO/TPPS
Chronic Criterion
Acute Criterion
(rKn'nlr)
Ar.,1, *l ••
-------
00
CD
0>
m
CADMFIIM
10
e
o
n
c
n>
c
Q)
U
o.i
y Elliott B«y. HITRO/TPPS
O Wtft Point. KtTRO/TPPS
Chronic Criterion
— Acute Criterion
I
y y
y .
y
c
o
•
o.oi
O.I
1.0
Chronic
Criterion
Aoiie
fr lu-rlon
«!•.*.
(.icuir)
»l ..d.
(chronic)
Concentration in Sediment (ug/g dry weight)
Figure 11
OBSERVED CONCENTRATIONS OF CADMIUM IN THE SEDIMENTS OF PUGET SOUND IN COMPARISON TO CRITERIA VALUES
(Cadmium concentrations reported by Malins et a 1980, are suspiciously high and were not includ
-------
CD
>
8
10
Chronic Aoite
ftUrtlon Cillrilnn
A Elliott Bay, Mallna ct al.
V Elliott Bay. KITHO/TPPS
Weat Point. METOO/TPPS
Comnenceoent Bay. Hallni ct al. (1980)
Sinclair Inlet. rUllna ct al. (1960)
Caac Inlet. Millnt ct al. (1980)
Budd Inlet. Mallna ct al. (1980)
VPort HadlEon. Hal Ins et al. (1980)
Chronic Criterion
Acute Criterion
Chronic Acute
Criterion Criterion
0.1
. 1000
..; O
' •»'
< (0
(chronic)
Concentration in Sediment (ug/g dry weight)
Figure 12
OBSERVED CONCENTRATIONS OF COPPER IN THE SEDIMENTS OF PUGET SOUND IN COMPARISON TO CRITERIA VALUES
-------
T S XT T
A Elliot! Bay, MaJIrti ci al.
Elliott Bay. METRO/TPPS
Ve«l Point, HF.TVO/TPPS
Comericrarnl Bay, Hal Ins ct al. (I960)
Sinclair Inlet, Mallns *t al. (1980)
Caar Inlet. Hallns (I al. (I960)
Budd Inlrl. Hallns el aj. (19BO)
VPort HaJlaon. H.illne et al. (1980)
Chronic Criterion
Acute Criterion
00
,f
•fl K.d.
(nrtite)
O.I 1.0
Concentration in Sedimen; (pg/g dry weight)
n
5'
Figure 13
OBSERVED CONCENTRATIONS OF MERCURY IN THE SED ^NTS OF PUCET SOUND IN COMPARISON TO CRITERIA VAf
-------
3)
00
2.
5*
•-*
(0
10
B
O
.0
t-i
n)
u
c
0)
u
I-.
0)
(X,
0.1
A Elliott Bay. M.lln. tl »1. (I960)
Elliott Bay. MITHO/TPPS
Point. METRO/TPPS
CooB.tnceo.cnt B.y, M«lln« tl •!. (19BO)
SInclalr Inlet. Millns rl •!. (1980)
C.sr Inlet. M.lln* ct «1. (1980)
Budd Inlet. Mallns et •!. (19BO)
VPort MadUon. Mallns «t •). (1980)
---- Chronic Criterion
Acute Criterion
10
• I a.il.
Concentration in Sediment (ug/g dry weight)
Figure 14
OBSERVED CONCENTRATIONS OF ZINC IN THE SEDIMENTS OF PUCET SOUND IN COMPARISON TO CRITERIA VALUES
-------
00
g
n
5'
re
(A
10
FLUORANTHENE
-I t.r.
(chronic)
ChrunU
Crlirrlitn
Elliott Bay. Hdlns et •]. (1960)
Elliott Bty, MTTRO/TPPS
|Uc«t Point, METBO/TPPS
ICoaaenccoent B«y, KUllni *l •!. (I960)
[Sinclair Inlet. M«llns et •). (1980)
)C*ic Inlet. H.llnt ct •!. (1980)
Budd Inlrt. Hillnt el •). (19AO)
Port H»di«on, M*))nt et •). (1980)
— Chronic Criterion
Acute Criterion
D
D
O
e
o
.0
n
00
1.0"
c
V ..
u -
w.
(U
0,
0.1
V H
0.01
-I s.e.
(jculc)
rr
i.o
i
Acute *l i.e.
Crltrrlun (chronic)
(•culr)
Concentration in Sediment (M8/8 ^ry weight)
Figure 15
OBSERVED CONCENTRATIONS OF FLUORANTHENE IN THE SEDIMENTS OF PUGET SOUND IN COMPARISON TO CRITERIA VALUES
-------
tn
CJ
DO
00
>
I
5'
S,>:.!
i '-
10
.rilENANTIIRRNF.
c
o
n)
o
u
•H
C
id
M
o
c
0)
u
u
HI
0.
1.0-
0.1-
D
D
O
o
Q
A
A Elliott Bay. Hal In* ct •!. (1980)
V Elliott B.y. METRO/IPPS
I Wcit Point. HFTHO/TFPS
I Conmenceoent Bay. Ha Una ct »1. O9AO)
ISlnclalr Inlet. Hallns rt al. (19RO)
)Caac Inlrl. Mallns rt al. (1980)
Budd Inlrl, Hallns ct tl. (1980)
Port HddUon. H-illns ct al. (1980)
Acute Criterion
0.01
0.1
(irulr)
Concentration in Sediment (pg/g dry weight)
Figure 16
OBSERVED CONCENTRATIONS OF PHENANTHRENE IN THE SEDIMENTS OF PUCET SOUND IN COMPARISON.TO CRITERIA VALUES
-------
PYRF.NE
10
Elliott Bay, Hallna et al. (1980)
Elliott Bay. MITRO/TPPS
i Weal Point. METRO/TPPS
I Comaencearnt Bay, Hal in* et al. (1980)
(Sinclair Inlet, Hallna el al. (1980)
jcaie Inlet, Halint et al. (1980)
Budd Inlet, Hallni et a). (I960) .-.
Port Hadicon. Haling eC al. (1980) U
B
Acute Criterion
O
in
a
o
rt
u
•H
a
rt
to
a
v
u
01
Qu
D
D
y
D
a
v
A
V A
1.0
V D
A A
0.1
|;.
0.01
0.1
1.0
100
-I i.e.
(•cult)
Concentration in Sediment (pg/g dry weight)
00
r- :,-: 8
Figure 17
OBSERVED CONCENTRATIONS OF PYRENE IN THE SEDIMENTS OF PUGET SOUND IN COMPARISON TO CRITERIA VALUES
2.
5'
-------
Oi
ii .*:
t* ''•'•
-1 ••*. Chronic *l ».«.
(chr.-nlc) Cillrrlnn . (chrunlc)
i n
1U
C
o
Ui
ID |
0
D
"i.o-
0
•
3
0
i_.
a.
0.1
DDT i , ,
/
/ y
° °/' • .
' n
O A ^x T
/ • a v
A ^A A
A U/ A A
V /
^ x
/
/
/x o
*
/ A
/ A
/ ' A Elliott B«y. Hallni rt •!. (I960) /
/ Y Elliott Bay. HITHO/TPPS /
/ QUrtl Point. KETKO/TPPS ./
S Q Cooarncrnrnt B«y. Htlini *t •!. (19801 /
, Hsinelilr Inlrt. Hillni rl tl. (1980) /
/ Oc«»« Inlrt. Hilln* rt •!. (1980) /
/ A Budd Inlrt, rUUni rt «1. (1980) /
/ yPort HjdUon. Haling rt •!. (1980) /
/ — Chronic Criterion /
f Acute Criterion f
s • /
\ 1 1 1 1 1 1
0.0001 ' ' 0.001 • 0.01 • ' 0.1
Chronic -»| §.«. -1 «•»• *cut« +1 »•«•
Criterion (chronic) ' (nculc) Criterion (jculc)
Concentration in Sediment (pg/g dry weight)
3J
• 00
r v 8
'-.-;
Figure 18
OBSERVED CONCENTRATIONS OF DDT IN THE SEDIMENTS OF PUCET SOUND IN COMPARISON TO CRITERIA VALUES
-------
s.
i
*•
•
1
*' .
y •
I
i
V
»
1
i"
<£
'
[ /.
f
J;
i:
P '•
(:.
},
r
V.
'." . C
3
; . •• • c
' - *
w
10
c
o
X)
m
u
u
T4
c
CO
Sl.O'
u
o
u
c .
o
•j
0)
0.1
•
0
D
>
j
|t
>'..i.. '
S -S: i'
•• .•
-!•••»• Chronic
, nrn (chronic) Crlxrlon
£ ""* •> \-» D 1 I
t 1
X n
D n
D B xx
0^
A '
O A x
/
0 a/
^V *^ A f
n A A A ^X A
n rj r« «J x
n A-X A
v A /x A
A x
J
J
'
/
H
v /
o
X
X
x' A Elliot! Bay. Mallni et al. (I960)
/ QComcnceornt Bay. Mallnt ft al. (1980)
/ rjSlnclalr Inlet. Hallnt el al. (1980)
' QCaae Inlet. Hallni rt al. (1980)
/ A Budd Inlrl. M.lln. el al. (1980)
x V Port HadlEon. Hallnl et al. (1980)
X
' ' Chronic Criterion
0.00001 ' 0.0001 ' 0.001 O.Jl
-1 »-e. Chronic +1 ••«.
(chronic) Crlirrl.-n (chn-nlc) . . •
Concentration in Sediment (ng/g dry weight)
Figure 19
OBSERVED CONCENTRATIONS OF 2-PCB IN THE SEDIMENTS OF PUCET SOUND IN COMPARISON TO CRITERIA VALUES
-------
1
1
.
'
i
t' '
|
*.•
>
,
i
in
'
?.
L • •
I'-
r:/'
r-*
^:: :
:•
i.
; '". ''*"•'•
f '- .V.
•' "V"
10-
c
o
M
CO
O
u
c
n)
"1.0"
0
u
C
!'•':'• •-.:.•
-1 B.v. ChronU
(chronlt) Criterion
3-PCB I |
**
EJ'
/
S3 /
D /
H XX
A D /
OA D vax v T T
•« T w ^
^^ 'tJ *
T X ••
A A A
n H A AAA /^ A
y BQ H Q A /A - T
A Ax
A X (^
/
^
• x
O Ox/ Q ^
• ^^ . j
^H ^».
• A * * • ^ / C
^ X
V X
) /
/ A Elliott B«y. Millns *t •!. (1980)
/ V Elliott B»y. METRO/TPPS
/ OUe.l Point. HI.TRO/TPPS
/ nComarnc«B«nt Bay. M«!lno et al. (1980)
X rjStnclilr Inlet. Mallni rl al. (1980)
X QCcic Inlet. Hallns ct «!. (1980)
/ ' A Budd Inlet, H«lln« ct al. (1980)
^ yporl MndlRon. H.llns rt •). (1980)
/ ' Chronic Criterion
1 1 f 1 i '~- n " ~
)001 0.001 0.01 O.I 1
-1 ».«. Acute «l s.e.
(acute) Criterion (ncule)
Concentration in Sediment (pg/g dry weight)
Figure 20
OBSERVED CONCENTRATIONS OF 3-PCB IN THE SEDIMENTS OF PUGET SOUND IN COMPARISON TO CRITERIA VALUES
\£\v
0
-------
t>
31
Jtf
CD
y*
-1 e.c. Chronic
(chronic) CHieflon
4-PCB , ,
10 '
c
0
.0
to
<0
o
u
•H
c
U
o
u
• C
• 01
u
u.
01
P-.
01
/
/ft
/
/
° r-, /
D / _
/ H
/\ |^j f
0 A a T x*a ' T v
T xx/ T
. 'A' */ ^
D n Q a • >
^ A / .
V A ^0/X A
A Ox^
X
X
O x
"* X
X
A A A
^ * 0 /• **
• * • « ° O xX/ • •
* • * ^ x'
V
X
XX A C-lllolt B«y. Mallns el •!. (1980)
XX V Elliott B«y. METRO/TPPS
x' ©Writ feint, MF.TItO/TrPS
x Q Comatnccarnt B»y. K»lln» «t •!. (1980)
xX Hsinel»ar lnl«t. H»lln» el «1. (1980)
' (jC««e Inlel , HiHn« *t •!• (1980)
/ ABudd Inlel. M«lln« *t •». (19BO)
/ • yPorl Madlion. Mallns et •!. (1980)
x
x . Chronic Criterion
x
•
. 1 ^ ; r n '
0.0001 0.001 ' 0.01 •).! 1.0
-| «... Chronic *' ••«•
(chronic) Criterion (chrmlc)
Concentration in Sediment (ug/g dry weight)
Figure 21
OBSERVED CONCENTRATIONS OF 4-PCB IN THE SEDIMENTS OF PUGET SOUND IN COMPARISON TO CRITERIA VALUES
-------
tn
.VO
5-PCB
1U
c
o
J3
CD
O
O
•H
Sl.,0
0
u
c
0)
u
01
a,
0.1-1
H
D D
D
[
0 T £ D y
A D Q v
A ^ A ' ' A ''
r, D A A A X
a ^ian,J A A/
^7 A A /
V A 0 0 ;x
• x'X
X
•' •••• ' Chronic
(chronic) Criterion
I ;
1 jL
X
X
X
X
X
X
X
1 X
X
X
/'T ^
•
T
O *^ xX O
• fi ^ A '
n %. ®Od • • x Q
D 0 0 A x
v /
0 /
/ A Elliott B.y.
/ T Elliott B.y.
/ QUctt Point.
X Ql Coaoencrarnt
i
Hallna et «1. (1980)
HETRO/TPPS
METRO/TPPS
B.y. rUIInt ct •!. (I960)
X MSlncLlr Inlet. H.IIni «t •!. (1980)
X OCair Inlet.
x A Budd Inlrt ,
XX V Port M/idleon
M.llnt et •!. (1980)
M.llni et •!. (1980)
. Hallns el *1. (1980)
x Chronic Criterion
o.oooi o.boi o.oi 1 o. i
- 1 •. C • f. 4 1 • .
. . . . Chronic *• «•«•
(chronlc> Ctllerl..n (chronic)
Concentraiton in Sediment (uo/c drv weicht^
1
.'. 00
•'.'• u' •
.- -.'•' ft :,..••. .
'••.'. • 0> ( '•' :• ' .
Figure 22
OBSERVED CONCENTRATIONS OF 5-PCB IN THE SEDIMENTS OF PUGET SOUND IN COhfPARISON TO CRITERIA VALUES
-------
6-PCB
in
1 U
c
o
.0
ra
u
u
•H
C
«1.0-
o
u
c
Figure 23
OBSERVED CONCENTRATIONS OF 6-PCB IN THE SEDIMENTS OF PUGET SOUND IN COMPARISON TO CRITERIA VALUES
-------
4.4 SPATIAL COMPARISONS
The frequency with which criteria are exceeded and the relative severity of
these occurrences can be used to evaluate the extent of degradation within var-
ious subregions of Puget Sound. Comparisons between subregions can be made
numerically or graphically. The methods presented below are intended as
examples of the tools which may be used to establish a priority listing of
sites where corrective action may be necessary.
Numerical Approach
The frequency .with which criteria are exceeded for individual contaminants can
be defined as:
X
fy • 9 measurements exceeding criteria x 100
total // measurements
X
where fy is defined as the frequency of criteria violation and x refers to the
X
specific contaminant measured. Values of fy were calculated for both acute
and chronic sediment criteria for six trace metals' as shown in Table 8. It is
X
possible to sum the individual fy values to obtain a frequency of criteria
violations for a given subregion integrated for a class of priority contam-
inants. This quantity is defined as:
n
where Fy is the class integrated frequency of criteria violation in a given
region and n is the number of contaminants in the class. Values of F are
illustrated in the last columns of Table 9. Although the sampling frequency
among the subregions is quite variable it is clear that Elliott Bay, Commence-
ment Bay, Sinclair Inlet and the area around the West Point Outfall exhibit
the highest frequency of violations. This, of course, is not surprising since
these areas have historically been known to receive high contaminant inputs
originating from land based point and nonpolnt sources.
Graphical Approach
Excess factors, representing the percent enrichment of a contaminant above
criteria, can be calculated at each sampling site as:
61
. JRB Associates _
-------
»
i
[
i
'
s
ON
KJ
i
1
f
f •
•*•
Table 9
FREQUENCY OF CRITERIA VIOLATIONS (f J) FOR SIX TRACE METALS IN SEVERAL SUDREGIONS OF PUCET SOUND
(Numbers in parentheses equal the number of stations which exceed criteria/total number of stations tested)
Al Cd Cu
Subreglon Acme Chronic Acute Chronic Acute
Elliott Bay 5.5 25 0 0 25
(2/36) (9/36) (0/36) (0/36) (13/53)
CooBencenent Bay — — — — 21
(3/14)
Sinclair Inlet — — — -- 0
(0/4)
Budd Inlet — — — — 0
(0/3)
Caae Inlet — — — — 0
(0/2)
Port Madison -- -- — — 0
(0/2)
West Pt. Outfall 10 36 0 0 3
Re8lon (3/31) (11/31) (0/31) (0/31) (1/31)
Total 7 30 0 0 16
(5/67) (20/67) (0/67) (0/67) (17/109)
3
0
t
0
J
> Excludes As and Cd.
5
v!{ 2-
- V 01 . .
' -."S
r':r\"'
Chronic
42
(22/53)
50
(7/14)
50
(2/4)
0
(0/3)
0
(0/2)
0
(0/2)
16
(5/31)
33
(36/109)
Pb
Acute
0
(0/53)
0
(0/14)
0
(0/4)
0
(0/3)
0
(0/2)
0
(0/2)
0
(0/31)
0
(0/109)
Chronic
74
(39/53)
50
(9/14)
25
(1/4)
0
(0/3)
0
(0/2)
0
(0/2)
21
(9/31)
51
(56/109)
UK
Arult*
59
(31/53)
43
(6/14)
100
(4/4)
0
(0/3)
0
(0/2)
0
(0/2)
52
(16/31)
52
(57/109)
Chronic
100
(51/53)
100
(14/14)
100
(4/4)
100
(3/3)
100
(2/2)
100
(2/2)
100
(31/31)
100
(IO-J/IU9)
Zn Fv
Acme
4
(2/53)
7
(1/14)
0
(0/4)
0
(0/3)
0
(0/2)
0
(0/2)
1
(1/31)
4
(4/109)
Chronic Aciitu
13 22
(7/53) (46/212)
7 IB
(1/14) (10/56)
0 25
(0/4) (4/16)
0 0
(0/3) (0/12)
0 0
(0/2) (0/8)
0 0
(0/2) (0/«)
16 15
(5/31) (IB/124)
II
(13/109)
Chronic
57
(121/212)
52
(29/56)
44
(7/16)
25
(3/12)
25
(2/8)
25
(2/8)
40
(50/124)
-------
cx cx
EF . US/ACT/OC - US/CR/OC
X
S/CR/OC
x
where ^s/ACT/OC e
-------
COPPER
Q 100-200
O 50-100
O io-io
O
COPKLK
8 10 12 1<4 16 18
-Cu
"S/ACT/OC
x 103yg/g o.c.
Figure 24
SPATIAL REPRESENTATION OF EXCESS FACTORS (EF) FOR CHRONIC CRITERIA
COMPUTED FOR Cu AND CORRESPONDING SEDIMENT CONCENTRATIONS
MEASURED AT SPECIFIC SITES IN ELLIOTT BAY
Data from Metro/TPPS (Pavlou ec al., 1983), and NOAA/NMFS
(Malins et.al., 1980)
,JRB Associates —
64
.-•x.^-^j*^'l
• ». f-V-
-------
Table 10
COMPARISON OF SEDIMENT CRITERIA FOR GREAT LAKES SEDIMENTS
TAKEN FROM THE LITERATURE AND CRITERIA ESTABLISHED BY
THE SEDIMENT-WATER EQUILIBRIUM APPROACH
(concentrations given in mg/kg dry weight)
Sediment Criteria
Sediment Criteria Derived by
Contaminant From the Literature Partitioning Approach3
16
15
68
66
0.006
380
0.06b
Based on a sediment containing 2% organic carbon.
D *
Based on an average criterion from 2-6 chlorinated biphenyls.
As
Cd
Cu
Pb
Hg
Zn
PCS
3-8
1-6
25-50
40-50
0.3-1
75-100
0.05-10
•:-- ,."•
JRB Associates _
'.65 .,:."•
-------
The criceria derived by Che equilibrium approach are in remarkably close agree-
ment with the criteria from the literature developed for Great Lakes sedi-
ments. With the exception of Hg, all criteria developed by the partitioning
approach are within one order of magnitude of the literature criteria and the
difference is generally much less. The fact that the proposed Hg criterion is
far below the literature value suggests that our estimate may be too strict as
discussed in Section 4.3. Though the proposed PCS criterion agrees well with
the literature values, it should be noted that this value represents the mean
criterion for 2-6 chlorinated blphenyls. The appropriate criterion can best
be determined only after consideration of the relative proportions of all PC3
isoners.
;;t.
.JRB Associates.
66
-------
5.0 RECOMMENDATIONS
In performing this study a number of immediate information and research needs
were identified to validate some of the inherent assumptions and improve the
utility of the equilibrium partitioning approach in the development of sedi-
ment criteria. The recommendations below are separated into three categories:
short-term technical needs, long-term technical needs and management needs.
Within each technical category, the needs are presented in approximate order
of priority taking into consideration both their contributions to validation
of the partitioning approach and their development costs/time. Those recom-
mendations ranked highly are of immediate need for application of the proposed
criteria and/or can be accomplished with a relatively low level of effort.
5.1 SHORT-TERM TECHNICAL NEEDS
The following technical needs are those which could potentially be accom-
plished in a relatively short time frame (less than one year). The needs iden-
tified below are recommended primarily to strengthen the equilibrium partition-
ing approach in two general areas: 1) verify the sediment-water partitioning
coefficients developed; and 2) provide additional assurance that the criteria
developed are biologically meaningful and adequate to protect marine life. If
the short-term technical needs identified are pursued, and the criteria
refined in light of new information developed, it should be possible for envir-
onmental managers to rely on the numerical values as guidelines in assessing
the extent of contamination of marine sediments and to use the values as a
tool in decision making.
• Ongoing studies funded by various federal and/or regional agencies should be
examined to determine flexibility for sampling contaminant and ancillary
sediment parameters to enhance application of the sediment criteria and/or
refine the preliminary numerical values derived by this approach. Inter-
agency coordination during field surveys is recommended to attain cost effec-
tiveness. EPA is currently directing an effort to achieve these objectives.
-•7->v:
.JRB Associates'_
67-
**• -. .J. -
• ••*•• — vr .
'
-------
• For sites where violations are predicted by the equilibrium partitioning
approach it is necessary to relate the occurrence of violations to the occur-
rence of biological effects on a site-specific basis. The occurrence of cri-
teria violations should be related to indication of localized biological
impact such as sediment bioassays or benthic community structure.
• The partition coefficients calculated in this study were based primarily on
empirical relationships. To determine whether these values are applicable
in Puget Sound, field studies should be performed Co verify the predicted
KQC values. These investigations should Include measurements of contami-
nants in both the interstitial water and sediments together with ancillary
variables at selected sites spanning a range of contaminant levels. An
effort should be made to review existing techniques in sampling interstitial
water and if necessary develop the appropriate methodology for obtaining
large quantities of water at the sediment water interface and bioturbation
layer.
• To test the sensitivity of criteria developed by the equilibrium partition-
ing approach, it is recodbended that sediment bioassays be performed to
determine if sediment criteria are indeed below concentrations causing
adverse biological effects. These bioassay experiments should employ appro-
priate sensitive marine species of common occurrence in the Puget Sound
environment.
• It is well established that the organic content of the sediments is a domi-
nant factor in controlling the magnitude of the partition coefficient and
hence the value-of the derived criteria. The development of a relationship
•
between organic content and sediment texture in this study was limited only
to one data base (Malins et al., 1980). Since 1980, additional sediment sur-
veys have been performed by various investigators in Puget Sound. It is
therefore recommended that all available data on organic carbon/sediment tex-
ture measurements be compiled and coherent plots be generated. The exist-
ence of subreglonal variability should also be examined to allow proper nor-
malization of the contaminant residue measurements.
68
v-
. JRB Associates.
-------
5.2 LONG-TERM TECHNICAL NEEDS'
The tschnical needs identified below are inportant in the ultimate establish-
ment of sediment criteria but would require a long-term development effort
(greater than one year). Several of the needs represent research efforts
needed to expand the current state of knowledge on the transfer of contami-
nants between sediment, water and biota. In this regard they are important
not only in development of the equilibrium partitioning approach but in provid-
ing Che technical basis in support of any sediment criteria eventually
adopted. It is recoaaended that the needs identified below be pursued prior
to adoption of legally defensible criteria for regulatory application.
• The bioavailability of contaminants at the sediment-water interface has been
Identified as a critical factor in deriving realistic sediment criteria
using the equilibrium partitioning approach. An effort should be made to
determine the factors effecting bioavailability of both trace metal and syn-
thetic organic chemicals of concern in Puget Sound. These studies should
Include efforts to evaluate the importance of ingestion of partlculate-bound
contaminants in determining the ultimate contaminant body burden of deposit
feeders. There is a need to examine the assumption made that ingestion of
contaminated particles will not increase the body burden above that which is
attained via the interstitial water.
• As pointed out in the report, the physical/chemical conditions at the sedi-
ment-water interface appear to control the chemical form of trace metals and
hence their bioavailability. It is therefore recommended that experiments
be performed to determine the sediment-water partitioning of trace metals as
influenced by environmental conditions (organic carbon, pH, redox, DOM, temp-
erature, salinity). These studies may Include: (1) a review of pertinent
literature; (2) field measurements; and (3) controlled experiments with
natural sediments.
• One of the limitations in establishing sediment criteria in using the equili-
brium partitioning approach is the lack of water quality criteria (chronic
and acute) for most of the contaminants encountered in Puget Sound. An imme-
diate need is therefore the update of the water quality criteria list to
include acute and chronic values for all contaminants of concern measured in
JRB Associates II
'. 69
-.j V» .'••-••*• . - -^--*s
-?-^Jifrf-JKJ*i- -*-—•*-*••. -—•-' ., ---, .---g-ft,
-------
Puget Sound. Though establishment of criteria for a wide diversity of con-
taminants would* involve a major, long-tern effort, it may be possible to
identify a few select contaminants of greatest concern and derive criteria
for these on a short-term basis.
5.3 MANAGEMENT NEEDS
• The historical and ongoing generation of sediment quality related informa-
tion comprises a substantial bank of numerical values that must' be properly
handled, processed and documented prior to use in the criteria development
program. To facilitate the use of this voluminous information a computer-
ized data management plan must be developed. This system must be flexible
and should be updated as more information becomes available. It is recom-
mended that EPA assumes the role of a regional data base coordinator and
"clearing house" and take the necessary steps to develop a regional data
base management plan for sediment quality information for timely implementa-
tion. Coordination with other agencies within the region (e.g., NOAA,
Washington State Department of Ecology, Army Corps of Engineers) should be
encouraged since these organizations, are both users and generators of infor-
mation and historically have developed project specific data bases for water
quality parameters and contaminants.
• The single most important need is for management agencies to continue to
encourage and support development of scientifically sound, legally defens-
ible and nationally adoptable sediment criteria. Several steps should be
taken to meet this need: (1) continued support of research in the areas of
contaminant transport, fate and effects as they pertain to sediaent cri-
teria; (2) development of protocols for application of criteria;(3) encourage
comparison of criteria developed by alternate approaches; and (4) provide a
forum for communication between scientists and agencies Involved in develop-
ment of sediment criteria.
. JRB Associates _
• 70 .-s-.,.'
•lil ••*.•/•.••<
-------
6.0 REFERENCES
Beasley, T.M. and S.W. Fowler. 1976. Plutonium and americium: uptake from con-
taminated sediments by the polychaete Nereis diversicolor. Mar. Biol.
38:95-100.
Brannon, J.M., R.H. Plumb, Jr. and I. Smith, Jr. 1980. Long-term release of
heavy metals from sediments. Chap. 13, p. 221-226. In: R.A. Baker (ed.).
Contaminants and Sediments. Vol. 2. Ann Arbor Science Publishers. Ann
Arbor, MI.
Briggs, G.G. 1973. A simple relationship between soil adsorption of organic
chemicals and their octanol/water partition coefficients. Proc. 7th
British Insecticide and Fungicide Conf. Vol. 1. The Boots Company, Ltd.,
Nottingham, G.B.
Brown, D.S., S.W. Karickhoff and E.W. Flagg. (in prep.) Empirical prediction
of organic pollutant sorption in natural sediments.
Callahan, M. , M. Slimak, N. Gabel, I. May, C. Fowler. R. Freed, P. Jennings,
R. Durfee, F. Whitmore, B. Maestri, W. Mabey, B. Holt and C. Gould. 1979.
Water-related environmental fate of 129 priority pollutants. Vol. 1. Pre-
pared by Versar, Inc. for the Environmental Protection Agency under EPA
Contract No. 68-01-3852 and 68-01-3867.
Christman, R.F. and R.A. Minear. 1971. Organics in lakes, p. 119-K3. In; S.J.
Faust and J.V. Hunter (eds.). Organic Compounds in Aquatic Environments.
Marcel-Dekker, New York.
Courtney, W.A.M. and W. J. Langston. 1978. Uptake of polychlorinaced biphenyl
(Aroclor 1254) from sediment and from seawater in two intertidal poly-
chaetes. Environ. Pollut. 15:303-309.
Crecilius, E.A., M.H. Bothner and R. Carpenter. 1975. 1975. Geochemistries of
arsenic, antimony, mercury, and related elements in sediments of Puget
Sound. Environ. Sci. Technol. 9:325-333.
Dexter, R.N. 1976. An application of equilibrium adsorption theory to the
chemical dynamics of organic compounds in marine ecosystems. Ph.D. disser-
tation, Univ. of Washington. Seattle. 181 pp.
Fowler, S.W., G.G. Polikarpov, D.L. Elder, P. Pars! and J.P. Vllleneauve.
1978. Polychlorinated biphenyls: accumulation from contaminated sediments
and water by the polychaete Nereis diversicolor. Mar. Biol. 48:303-309.
Hansch, C. and A.J. Leo. 1979. Substltuent Constants for Correlation Analysis
in Chemistry and Biology. John Wiley, New York.
•Tenne, E.A. 1977. Trace element sorption by sediments and soils—sites and
processes, pp. 425-553. In; W.R. Chappell and K.K. Petersen (eds.),
Molybdenum in the Environment, Vol. 2. Marcel Dekker, New York.
71
i._.,, ."-....-«.
, JRB Associates —
-------
Jenne, E.A. and S.N. Luoma. 1975. Foras of trace metals in soils, sediments,'
and associated waters: an overview of their determination and biological
availability, p. 213-230.- In: Biological Implications of Metals in the
Environment. ?roc. 15th annual Hanford life sciences symposium at
Richland, UA. ERDA symposium series, No. 42.
Karlckhoff, S.V. 1981. Seal-empirical estimation of sorptlon of hydrophobic
pollutants on natural sediments and soils. Chemosphere 10:833-846.
Karickhoff, S.W., D.S. Brown and T.A. Scott. 1979. Sorptlon of hydrophobic pol-
lutants on natural sediments. Water Research 13:241-248.
Kenaga, E.E. and C.A.I. Goring. 1980. Relationship between water solubility,
soil sorption, octanol-water partitioning and concentration of chemicals
in biota, p. 78-115. In; J.G. Eaton, P.R. Parrish and A.C. Hendricks
(eds.). Aquatic Toxicology, ASTM STP 707, American Society for Testing and
Materials. Philadelphia, Pennsylvania.
Leo, A.J. and C. Hansch. 1971. Linear free-energy relationships between par-
titioning solvent systems. J. Org. Chem. 36:1539-1544.
Lindberg, S.E. and R.C. Harris. 1974. Mercury-organic matter associations in
estuarlne sediments and interstitial water. Environ. Sci. Technol.
8:459-462.
Luoma, S.N. 1974. Mercury cycling in a Hawaiian estuary. Water resources
research center. Tech. Memo. No. 42. Univ. of Hawaii, Honolulu.
m
Luoma, S.N. and E.A. Jenne. 1975. The availability of sediment-bound cobalt,
silver and zinc to a deposit-feeding clan. p. 213-230. In; Biological
Implications of Metals in the Environment. Proc. 15th annual Hanford life
sciences symposium at Richland, WA. ERDA symposium series, No. 42.
Lyman, W.J., W.F. Reehl and D.H. Rosenblatt. .1982. Handbook of Chemical Pro-
perty Estimation Methods. Environmental Behavior of Organic Compounds.
McGraw-Hill Book Co. New York.
Malins, O.C., B.B. McCain, D.W. Brown, A.K. Sparks and H.O. Hodgins. 1980.
Chemical contaminants and biological abnormalities in central and southern
Puget Sound. NOAA Tech. Memo. OMPA-2. National Oceanic and Atmospheric
Administration, Boulder, CO. 295 pp.
Miramand, P., P. Germain and H. Camus. 1982. Uptake of americium and plutonium
from contaminated sediments by three benthic species: Arenicola marina,
Corophium volulator and Scrobicularla plana. Mar. Ecol. Prog. Ser. 7:59-65.
Pavlou, S.P. and R.N. Dexter. 1979. Distribution of polychlorinated biphenyls
(PCB) in estuarine ecosystems. Testing the concept of equilibrium parti-
tioning in the marine environment. Environ. Sci. Technol. 13:65-71.
Pavlou, S.P., R.F. Shokes, W. Horn, P. Hamilton, J.T. Gunn, R.D. Muench, J.
Vinelli and E. Crecilius. 1983. Dynamics and biological Impacts of toxi-
cants in the main basin of Puget Sound and Lake Washington. Vol. I: evalua-
tion of toxicant distribution, transport and fate. Submitted to the Munici-
pality of Metropolitan Seattle. ....
.JRB Associates -
72
-------
Pavlou, S.P. and D.P. Western. 1983. Initial evaluation of alternatives for'
development of sediment related criteria for toxic contaminants In marine
waters (Puget Sound). Phase I: Development of conceptual framework.
Prepared by JRB Associates for the Environmental Protection Agency under
EPA Contract No. 68-01-6388.
Pionke, H.B. and G. Chesters. 1973. Pesticide-sediiaent-water interactions. J.
Environ. Quality. 2:29-45.
Rao, P.S.C. and J.M. Davidson. 1980. Estimation of pesticide retention and
transformation parameters required in nonpoint source pollution models.
In: M.R. Overcash and J.M. Davidson (eds.). Environmental Impact of Non-
point Source Pollution. Ann Arbor Science Publishers, Inc. Ann Arbor,
Michigan.
Renfro, W.C. 1973. Transfer of zinc from sediments by marine polychaete
worms. Mar. Biol. 21:305-316.
Roesijadi, G. , J.W. Anderson and J.W. Blaylock. 1978. Uptake of hydrocarbons
from marine sediments contaminated with Prudhoe Bay crude oil: influence
of feeding type of test species and availability of polycycllc aromatic
hydrocarbons. J. Fish. Res. Board Canada 35:608-614.
Sokal, R.R. and F.J. Rohlf. 1981. Biometry. Second edition. W.H. Freeman and
Co., San Francisco, CA 859 pp.
Smith, J.H., W.R. Mabey, N. Bohonos, B.R. Holt, S.S. Lee, T.W. Chou, D.C.
Bomberger and T. Mill. 1978. Environmental pathways of selected chemicals
in freshwater systems; Part II: Laboratory studies. U.S. Environmental Pro-
tection Agency, Athens, CA. EPA-600/7-78-074.
Stephan, C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A.
Brungs. 1983. Guidelines for deriving numerical national water quality cri-
teria for the protection of aquatic life and its uses. Draft report.
Vangenechten, J.H.D., S.R. Aston and S.W. Fowler. 1983. Uptake of americium
241 from two experimentally labelled deep-sea sediments by three benthic
species: a bivalve mollusc, a polychaete and an isopod. Mar. Ecol. Prog.
Ser. 13:219-228.
Veith, G.D., K.J. Macek, S.R. Petrocelli and J. Carroll. 1980. An evaluation
of using partition coefficients and water solubility to estimate bloconcen-
tration factors for organic chemicals in fish. p. 78-115. _Inj J.G. Eaton,
P.R. Parrish and A.C. Hendricks (eds.). Aquatic Toxicology, ASTM STP 707,
American Society for Testing and Materials. Philadelphia, Pennsylvania.
Veith, G.D. and R.J. Morris. 1978. A rapid method for estimating log P for
organic chemicals. U.S. Environmental Protection Agency, Duluth,
Minnesota. EPA-600/3-78-049.
—^————————___^—_ JRB Associates _
73 .... -., .-.«-
-------
APPENDIX A
SEDIMENT CONTAMINANT CONCENTRATIONS
FROM MAL1NS ET AL., 1980
is-
,-. • -*j~' • •-.-•.-• . __..
mtimv;.^,
•"«•••-• '-. '".vais •V"'! - '.• • ••!-
-------
•J
*•
.
.;
•
Table A-l
TOTAL ORGANIC CARBON AND GRAIN SIZE ANALYSES OF SEDIMENTS FROM CENTRAL PUCET SOUND
(From M.i 1 ins et al., 1980, Appendix T.iblo D-7
Location Description
Sinclair Inlet:
Southwest end
Orydock area
Point Turner, southwest side
Point Herron. south side
Port Madison:
.
* Midway from Pt. Monroe to Pt. Jefferson
Indianola, southwest
Commencement Bay:
Hylebos Waterway, lower turning basin
. C. llth St. Bridge
Blair Waterwy
Sitcum Waterway
City Waterway
Puyallup disposal site
Between Hylebos and Blair
Brown's Point, south side
Creek at sewage plant
lacoma Yacht Club
Brown's Point
Hylebos Waterway, outside, to NW
Old Tacoma
Blair Waterway, turning basin
C.
31
CD
0
; 2. •'•
'• B" •
• § ,' .- .
,-
• '.
Station >-Z
Hunger
08004
08005
08006
08007
08106
08107
09027
09028
09029
09030
09031
09032
09033
09034
09035 0.56
09036 1.92
09037
09018
09039
09040
Grain Sue (I by weight)
-? to
0
0.48
0.21
0.73
0.03
1.44
0.06
0.03
1.45
0.25
0.01
0.10
0.23
3. 84
7.31
6.65
0.37
0.02
0 to
0.47
0.41
7.55
2.51
9.83
21.26
0.42
16.06
16.08
1.34
J.4I
0.67
3.48
2.05
52.54
40.1)3
56.81
0.22
10.37
3.22
• Z to
• 4
0.84
2.75
9.14
53.69
34.23
57.33
2.60
19.21
19.27
14.88
6.32
42.99
9.98
12.08
36.14
42.07
22.49
2.20
21.01
17.16
• 4 to
•a
65.03
46.00
46.49
20.95
35.56
15.12
77.54
52.114
46.85
64.15
66.57
49. BO
bb.99
6.1.97
2.98
3.53
7.64
70.07
44.34
52.48
>«B
33.20
49.84
36.11
22.82
18.93
6.21
19.41
10.44
18.14
19.64
25.70
6.54
19.45
23.67
3.95
5.15
6.41
27.51
23.92
27.11
Mean Grain
Sue «
...
7.10
5.24
5.12
2.95
6.88
4.76
5.13
6.08
6.71
4.28
5.99
6.15
1.H5
1.89
I.B6
6.69
5.66
6.54
Sand /Mud
Ratio
0.02
0.03
0.21
1.28
0.83
3.68
0.03
0.511
0.55
0.19
0.08
0.78
0.16
0.17
13.47
10.1,4
6.12
0.02
0.47
0.26
1 Organic "
Carbon
4.42
3.44
4.90
1.61
1.26
0.41
4.00
2.82
1.64
1.7B
5.17
1.56
1.51
2.49
0.40
1.72
0.48
2.64
6.98
1.60
-------
30
CO
J>
.8
. n .
•••
•• re
I
Table A-l
(cont'd)
drain Sue (1 liy xpiyhl)
Location Description
[Iliotl Bay:
Magnolia Bluff
Pier 54
Harbor Island, north end
Ouwamish Waterway. 1st Ave Bridge
West Point, north side
Alki Point, south side
• Duwamish Uau -wa^ near lumber mill
. *est channel
" * , cast channel
Pier 70
North of Pier 71
Pier 86
Corps dump site
Midway from Pier 91 to Ouwamish Mead
Uuwjinish Head. soullicdSl side
Pier 42
Case Inlet:
Reach Island
Stretch Island
Budd Inlet:
Entrance channel, south end
Priest Point
Qlyapia Shoal
Station
Number
10014
10015
10016
10019
10023
10028
10031
100)8
100)9
10040
10041
10012
100-13
1 11044
IOU45
10046
12062
12063
12130
121)1
12132
>-2 -2 to
0
0.54
0.21
no data
0.84
0.01
0.09
0.03
0.11
2.33
1.33
O.U7
2.U4
0.01
0.91 10. G?
i.oa
0.04
0.02
0 to
• 4
25.18
3.57
20.02
3.59
30.07
3.13
2.99
0.58
I4.0J
9.>2
2.40
20. If.
I.U9
?fi.'j6
24. 82
1.26
24.35
0.18
10.28
0.45
• 2 to
• 4
59.96
6.70
11.76
UO.U7
57.52
12.29
15.02
2.82
10.b9
25. 3b
•).44
.V.09
4.15
ff.l1}
60.74
4.67
65.36
4.73
35.311
0.93
• 4 to
• 8
6.95
58.33
52.35
11.11
I.2U
•4A.45
40.73
41.76
49.11
50.08
5-J.J3
4?. tO
4').1)
/)./0
10.40
59.00
5.97
67.23
29.00
47.85
< «B
7.38
31.19
15.04
5.22
3.02
38.09
41.15
52.63
23.74
13.51
2:1.76
I.'.OI
45.3?
15.42
2.01
35.07
4.28
27.86
25.32
50.77
(lean Cram
Sue a
2.63
7.02
no data
4.84
3.26
2.23
7.11
7.07
U.52
5.26
5.03
(,.77
4.0)
7.JI
).//
2.02
7.39
2.56
6.95
5.65
...
Rjlio
5.98
0.12
0.48
5.12
22.23
O.IH
0.22
O.U4
0.37
0.5)
11.14
O.M2
tl.Hb
l.'.n
7.02
0.06
8.75
0.05
O.K4
0.01
X Onunic
Larbon
1.13
1.63
1.50
0.50
0.39
l.:i)
I.U2
l./o
1.33-
I.M3
1.3)
l.'H
2. \'i
I.'.J
0.14
3.10 .
0.36
3.10
2.05
3.41 .
-------
Table A-2
CONCENTRATION OF METALS IN SEDIMENTS FROM CENTRAL PURET SOUND IN
MAY, 1979, IN ug/B MY WEIGHT (PPM)
(From Halins, ct al. 1980, Appendix Table D-2)
SINCLAIR 'INLET:
PORT HAOISON:
COMMENCEMENT BAY
ELLIOTT BAY:
CASE INLFT:
BUM) INLET:
SOURCE OF SEDIMENT SAMPLE
1
Southwest rnd <
Drydock area
Point Turner, southwest tide
Point Herron. south ilde
Mlduay from Pt. Monroe to Pt. Jefferson
Indianola. southwest
: llyleboa Waterway, lower turning ban In
llylebos Uatervny. E. llth St. hrldie
Blair Uaterw.iy, E. llth St. bridge
Sltcum Wnterw.iy
flty Uatrrway "
I'uyallup dlspunal site
Between llylchos k Blair
Brnwn'a Point, south ilde
Creek at srw.if.c I'lant
T.icoma Yaclit flub
Brown's Point
llylehos Waterway, outside, to NU
Old Tacoma
Rlalr Waterway, turn Inn basin
Mif.no Ha Bluff
Plrr 54
Harbor Island, north end
nuuamlsh W.ilcruay. |4th Ave. bridge
Weil Point, north fide
Alkl Point, south Hide
nuu.imlsh Waterway, nenr lurchrr mill
Duuamlsh Waterway, ue«C channel
Duwamiah Waterway, ca^t channel
Pier 70
North of Pier 71
Plrr 8ft
Corp* dump site
Midway from Pier 91 to DuwamMh Head
nuuamlsh Head, southeast aide
Pier 42
PIT 42
Reich Island
Stretch Island
Fntrsnce channel, south end
Prleiit Point
nlytnpla Shoal
tg
i-76
).&2
'92
•02
•97
•48
•91
•)S
•14
0-8
•02
•00
•70
•17
•94
• 72
•95
•52
•46
•18
•11
•92
•B9
•07
•45
•25
•99
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•77
•49
•80
•70
•77
•71
•05
•58
•62
•76
•81
•67
•66
•97
A|
18811
19G50
17796
11070
1)712
7109
>20000
noon
12857
12104
H'> 7 1
12027
15027
15A71
8501
9iJ9
9178
16666
11009
14110
9951
>20000
14586
>20000
10114
7879
>70000
>70000
>20000
1841)
17/.7)
19B01
17152
>20000
14530
1092)
10790
m«o
ft '-10
>70000
1741)
>70000
As B
67'
50-
SO-
18-
79>
7)'
19'
SI-
2)'
472 16-
4n>
17-
20-
2)-
14.
25-
28-
)0«
16-
20-
26-
16-
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16-
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282 45.
21-
28-
25-
29>
41-
2)-
15-
12-
SS-
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5
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5
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1 -574
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11097
7785
6511
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7279
7022
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6209
8044
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4915
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8467
7019
7741
506 1
7 160
6500
6607
5229
42f. 1
89ns
U54
Hfm
677]
6 5 2 i
(-92K
6fi85
777)
7109
57))
NS07
f)fi-t
164)
M)'.
8575
Bl 76)5
Cl
B> 14
7-71
7-|4
5'24
6-25
1-08
9-6:
A -60
5-41
i 6 • 2
9. n a
ij f
5-20
S-'iO
$•99
4 -70
5 -no
4-72
f. 'Of.
5*57
6-02
4 • /. f,
8 • SS
5 • 70
8-29
4 • 71
1-77
1 1 ••»
no
1 B- 1
7 -n;
u-49
7 • )•>
(,•!.(.
B • 2 J
7 • 10
4 • 57
7-52
7-Sr!
J- If-
11-2
8- 19
9-51
Co
14 -0
11-a
l)-7
9*66
11-5
5-71
20'6
ll'O
3-4*.
4 7 • S
11 • C
I'D
10-6
17-6
15*6
17*6
70 -0
14-1
15-5
1 4 • 1
i • j
13-3
8. it
• t
1 7 .(,
o -4i
•• J
U. «
J
6 '86
5 •))
17 •)
1)-J
79*7
« 'Rf
10 -y
14-7
B -04
15*4
17-0
7 *64
10- 2
\e-r-
P-/.P
2S-i
|7'3
25-B
t- •. 01
', n
-------
Table A-2
(cont'd)
&
SINCLAIR INLET:
PORT MADISON:
COHKENCEHLNT BAY:
.
ELLIOTT BAY:
CASE INLET:
BUDD INLET:
OURCE Of StDIHENT SAMPLE
Southwest end
Drydnck area
I'olnt turner, southwest side
Point llcrron, south side
Midway from Pt. Monroe to Pt. Jefferson
Indlanola. southwest
Hylebos Waterway, lower turning basin
Mylehos Waterway. £. lllh St. bridge
Blair Waterway.
Sit cum Waterway
City W.nerway
Puyallup disposal site
Between llylrbos 4 Blair
Brown's Point, couth side
Creek at arwnge plant
Tacomn Yacht Club
Brown'a Point
Mylebos Waterway, outside, to NW
Old Tacoma
Blnlr Waterway, turning basin
M.if>.nolln Bluff
Pier 54
ll.irhor Island, north end
l)iii"inileh Uatervay, 14th Ave. hrldRe
Writ Point, north aide
Alkl Point, south tilde
Duwnmlsh Waterway, near lumber mill
Puw.imlsh Uaterwny , west channel
Dnwamlsh Waterw.iy , cast channel
Pier 70
North of Pier 71
Pier 86
Corps dump site
Midway from Pier 91 to Duwamlsh Head
Duuaralsh Head, southeast side
PI *r LI
F 1 ^\ "* *
Pier 42
Rc.ich Island
Stretch Island
fntrance channel, south end
Priest Point
Olynpla Shoal
Cr
7l«
65-
57-
39-
45-
22*
47«
33-
27-
58-
66-
25-
26-
28-
31*
36-
25-
29'
28'
29-
27-
J4.
31-
35'
35-
27-
It •
63-
LI •
54-
53«
54.
38'
SI-
n9-
60 •
41-
52-
20-
49-
34-
50-
Cu
1SI
184
137
46-8
2S-8
10-4
259
Kl'R
59-6
1602
178
33'7
50'6
64 '8
43-0
110
22-
77-
12
69«
23-
91-
QO'
54-
IB-
10-
131
206
109
135
58-8
63'7
59-6
6°-l
60' 7
21-2
22-5
'. > • 0
11-2
8I-1
6 36-6
I 70-3
re Ca
31A17
32320
30289
27646
2896R
12687
39405
73507
25138
43354
27176
2262)
25445
26758
18233
26063
22530
2C55B
22752
20914
19055
33076
24636
34037
19052
15856
45569
45659
>5nono 86
37640
79460
34013
30767
37778
3 5 2 '• 7
20976
22214
2 S 1 0 .1
11120
36217
74748
34800
CLFMCNT
Ce Hg
1*06
1*02
1-15
•315
•113
•042
•790
•428
•132
•492
1-03
•065
•106
•173
•100
•255
•063
•197
•336
•157
•095
1-16
1-38
•750
•104
• 031
119 •)«!
8R >798
188 '350
•6)7
1*07
•355
«/.23
44 .449
•153
•076
•026
43 -118
-024
101 '379
46 -125
89 -283
K
190
193
181
128
1)6
5B-4
149
87-7
88-1
85«1
125
71*0
98*1
105
60-1
88*6
14|
125
98-2
102
107
179
116
167
76*2
69-4
222
22*
269
148
154
166
139
210
104
6 3 •'•
62-6
167
44-3
167
105
164
LI
20'
20*
19-
13*
15-
7-42
15-5
9-91
9*72
fl-96
13-4
703
11-0
11*5
8'B3
8*98
7. (-8
12*5
10> 7
10*6
8-56
19*3
ll-o
15-4
0.99
•-«0
71-4
71-6
25«4
ln-3
16-5
17-4
14-0
21-9
13-4
7 •'.(,
7-66
20-5
7-22
26-8
16*4
24-7
»8
10500
10543
9437
6895
8676
4720
11301
12961
5172
4904
7381
4259
5T-39
6405
5745
5675
4251
7790
5997
6110
4«M
•>SM
5435
11. )»
70°n
55P2
1.1 •» 1
«7«5
11 363
ft«0|
«3P4
°»35
7163
lit- 52
3T>5
( S in
ft".'
•nr-:
3533
10407
707»
10248
r!n
301
3? 2
301
334
345
204
751
702
16ft
1-Q4
193
14|
!•',
217
370
S77
713
173
2 It
lil
315
3'i
7ff
70?
741
35"7
41 V
43"
5'- 7
3>5
323
473
302
471
«.0 |
7-»5
', ; s
:°<
;n:
230
1S4
229
-------
Table A-2
(cont'd)
ELEHTKT
oo
3
CD
>
g
o
0_
S'
r»
CD
5UUNU
SINCLAU INLET:
PORT MADISON:
COMMENCEMENT BAY:
ELLIOTT BAY:
m
CASE IN1.ET:
BlfDO INLET:
( ur aeuinuiT SAHTLE
Southwest end
Drydock area
Point Turner, southwest aide
Point Herron, south side
Midway from Pt. Monroe to Pt. Jefferson
Indlanola, southwest
Hylebos Waterway, lower turning basin
Hyleboa Waterway , E. llth St. bridge
Bl.ilr Waterway. E. llth St. bridge
SI tcuni Waterway
City Waterway
Puyallup disposal alte
Bctveen Hylrboi & Blair
Brown's Point, south side
Creek at sewage plant
Tacoma Yacht Club
Brown's Point
llylehos Waterway, outside, to NW
Old Tacoma
Blair Waterway, turning basin
Mar.nclla Bluff
Pier )4
Harbor Island, north end
Dmiamlsh l-'.iterway. 14th Ave. bridge
West Point, north side
Alkl Point, south side
Duwamlsh Waterway, near lumber mill
Duwamlsh Waterway, west channel
Puuamlsh Waterway, cast channel
Pier 70
North of Pier 71
Plor 86
Corps dump site
Ml-lway from Pier 91 to Duwamlsh Head
Puuamlsh Head, southeast side
Pier 42
Plc«r 42
Rc.ich Island
Stretch Island
Fntrance channel, south end
Priest Point
Olympla Shoal
Mo Na
!)•) >20000
14-4 >20090
12*9 >20000
8-02 1)728
8- '-7 12)21
44)8
17<2 >:onon
11-2 17846
8-44 9770
114 10)18
13-1 170)9
8'19 7972
9'0f. 10966
10-3 13)4H
7-24 3ROO
10-4 4198
7-2) 4198
12-8 19112
14'I 12:)4
12*1 14768
6-16 )029
13-6 16400
7-94 9)84
14-8 1)084
6-24 )799
47)0
29-) 1)82)
26-4 11383
41-) 19744
10-9 1170)
9-98 17)77
ll>4 16270
10-2 12604
14 -8 >20000
9>9) 6640
6-71 4244
6-00 )2R6
13-3 >20000
)-8) 493)
29 -7 >20000
11'6 140)8
19-7 >70000
Nl
Jl-
4fl'
))•
42-
21 •
64 •
41-
21'
36'
18-
22*
24 •
29-
38-
22'
24.
2)'
22>
24'l
)6'
24.
29-
41>
)4-
36-1
38-
47-
)0-
)7-
)7-
)0>
4)'
))•
46'
49-
47 •
19-
47-
34-
44-
P
1227
9R)
89)
697
70)
1018
81)
812
7)9
1017
7)7
917
428
))7
491
940
I 800
1474
•> 551
I 868
I 680
\ 878
1 47)
9 394
1 1174
» 1020
) 1378
I 817
9 686
) 879
0 798
D 968
649
371
398
947
30)
917
8 670
7 10)1
Ph
97-6
1)6
12)
44-2
20'1
10- )
1)4
111
42')
79)
261
14«0
27'6
)9-9
28-8
6)'l
18-3
)0-1
170
49*0
37-1
111
60-8
40>1
16-1
ll'O
26)
627
160
88-6
74.)
72>8
6)*)
78*0
Ml
R*1R
• 9-)7
2J.«
7-93
60-1
22*6
49- 3
Sb
4)'
)2'(
48'
32*
17 •
64-
4).
3)
44*
79-
)«•
27-
)2-
25-
41'
)6-
)9-
2)'
48*
34>
48'
21'
17-
7)«
BO-
81'
41-
39-
45'
47'
)!•
34-
2)*
24-
46*(
I1*(
68-
43'
61-1
\
1
1
} t
)
) •
i <
1 1
)
Sc
•I)
•48
•81
•02
•92
•00
• 06
•17
•77
•76
•88
•84
•1)
•))
•AS
•81
•42
•4)
•82
•40
-47
•89
•9)
13-1
12-4
16-1
r-44
t*92
I'll
i'87
9-60
i'R)
1-78
1-32
r-72
r>89
)'49
i-16
9-7)
Se
10
30
27
22
14
27
2)
2)
2)
2)
22
)4
40
80
70
11)
78
2)
30
26
39
23
28
74
28
)9
SI
1)7
1)0
16?
1))
144
140
189
149
1 37
121
146
207
13)
1)7
I))
117
10)
171
101
91
104
100
88
1)7
1 17
1 10
101
101
700
1)6
1*0
1)0
D)
1")
1)7
716
179
117
14)
10)
17)
142
Sn
)7
3)
40
21
20
1 1
36
37
77
31
19
19
?0
1)
20
1)
19
70
18
20
36
22
30
I4
14
57
57
A)
37
31
31
26
37
71
1)
7*
9-6
38
76
-------
Table A-2
(cont'd)
\o
SINCLAIR INLET:
PORT MADISON:
COMMENCEMENT BAY:
ELLIOTT BAY:
CASE INI.ET:
BUDD INLET:
SOUKE OP SEDIHENT SAMPLE
Southwest end
Drydock area
Point Turner, southwest side
Polnc Herron. eouih side
Midway liom Pt. Monroe to Pi. Jefferson
Indlanola. southwest
llylebos Waterway, lower turning basin
Hylebos Waterway. E. llth Si. bridge
Blair Waterway. E. llth St. bridge
Sltcun Waterway
City Waterway
Puyallup disposal site
Between llylebos » Blair
Brown's Point, south side
Creek 04
10-7
9-12
10-}
-------
Table 'A- 3
CONCENTRATIONS OF TARGET ORGANIC COMPOUNDS IN SEDIMENTS
FROM ELLIOTT BAY, IN ng/g DRY WEIGHT (PPB)
(From Malins ec al.. 1980, Appendix Table D-3)
tr. MOM MI^IU
l-»OFTLICM|Ci«
—••OP\. »>.•€"/€•*
• I M 47
'"S'a '°i"2 "?'J 10e" "X1" 100" IOC3' 18C" 100" 10048 18°" 'O"4' ••"' "»" '«>"' •<»•• 100..
» O 40 10 40 10 .0-90 TO 19 10 4O M JO 39«'UX
ici»i3rux»*oc«.
i"so*3ii.a.3-eoi»«e>*i
1.3. > T.l^m^J-^
XI>CX.O>Oir»(CN<
t<»T.{>«.a>
**>C*l't
°-» • OOC
*"t>*-0*0'*""'
• '' - °OC
0 » - 000
"•* • 86°
• • - eeo'O • - DOT
• »' - OOT
oicx.o>oiin«ii>i.s
t»ICK.OiO« I »«*•»»!. S
rcr>.:w.a«e(i*««i»i.i
•cnr*c>«.a*>oti»««i»i.9
«'r.CM.(»ail»X«.LS
£KI^-Nl.o»Oi !»-'•.. U
•aM»c.«.<»aii»-«.i.s
OKM|.o*OIC»(CNt
»ICM.C*OIUI»OIC~
•.oic'«
* °" "'
»f
•O < . O < 3 0 70 10 10 id < I 0 10 10 *0 30 10 10 30 10 10
10. 30 70 * 0. i. 80 M r 0 30 .0 «O TO JO *O « O 10 M 10
10 • 0 410 30 4M 0 O M 310 TO M :30 I4O 14O HO «O 9 o IO
10 oo to *o jo - in • *o ,. i o 10 *o TO .0 . o i o c *o < 30 < 20
30 1300 130 30 300 1 o M IM M 4O «O TO M OO M 1 0 * 0
ao 1*0 no 10 130 a o 30 o » ao c aao ' 010 . 10 ao ao 40 10 ao 10 10 TO » o M 10 034 o«o
11 « 0 I O l IO OOO 10 t ao *O 10 10 10 10 10 30 4O 034 OM
ao i o 40 10 «9 ao ' ao *o ao *o *o TO *o 3 o 30 ' oio oio
»• 4*) •' !» 7* 77 «7 «9 43 57 IT l, 9* 90 41 14 y*>
«7 T «o 1 toa ICO 101 «7 | IOO IOO 101 IOO IOO IOO IOJ 101 •*) I 101 IO3
,JRB Associates _
80
-------
Table A-4
CONCENTRATIONS OF TARGET ORGANIC COMPOUNDS IN SEDIMENTS FROM
-COMMENCEMENT BAY, IN ng/g DRY WEIGHT (PPB)
(From Malins et al., 1980, Appendix Table D-4)
.C.,OT-,
•M*J« Mt^lB ^^ " * ^*
^v*7 7 ^O*^tl *O«V VQ3O *001 *O3i? VQ 33 9B34
10 »0 40 20 90 M 20 30
40 2O • 0 I O 4O IO *O 2O
«
rma.~'.*>c
'*"'"*
IOl(..lMn««0«
,0 9M .,
ao 2ro TO
.0 .30 ,30
« 70 »0 ,. ,0
40 310 *0 100
40 iao tO 00
»0 370 40 7O
400 7300 »30 3^1
MO .70 170 100 2300
,700 ..oo «o 3M .,00
••« »?0° •« 330 10000
,.00 HOO ,,e HO 4700
9 o 40<.o
•0>fOC*irr«04t
iMDn«iii.a.3-e»i»T.o«
».3.» ni^TWnjM
«i*c>«.a»oiCMn>c
LI»OM«
»C»T*c»«.a«
*CB*1"
a. f - oat
A-CK.OBOW4I
rrao uooo
,aoo i«oo
MO ,700
MO 470
430 noo
40 410
jo 40
790
tte
1*0
220
IM
,70
,ao 3100
7O »«"O 90
M 430 9 0
40 1300 40
40 MM 40
203010
• 0 M
30 .,o
M 100
,0 4O
10 40
« o TO
. o 4o
71O
2.0
IM
9.0-
,,O
«O
l«0 3IO
3O 3IO
I3OO ,«OO
M too
3O
• 0
340 4O «O IOO IBOO JIOO
110 M M 4O 7» 2IOO
100 M 30 40 1700 1700
MO M 70 70 laoo noo
100 10 so so 770 7«o
,0
„
.0
10
30
,O
IO
7 0
3O
ISO
4Q
930
ItO
IM
}4O
ITO
W>
IOO
70
10
< 3 O < 090 < 10 < 0*0 < 2 0 < 10 M
< I O < 050 < 90 < 10 ' 2 0 < 10 < 10
< , O < 0*0 < JO 3 O < 2 O < 10 10
M 4O • O M IO3M34O
M 7O * 0 3O M I4O I4O
M 30 a o 10 < «o IM no
M I«O • O M M 49O 34O SO
40 10 aoio so»oao
I 0 C 010 '. OIO < OIO 20 7 0 < 04O
I 0 < OIO < 090 '. OIO < 10 30 < JO
70 < 030 '. 040 7O 4 0 < 1 0 <. O»O
'•*' * BB€
0>'' • BBD
«.»• - 000
».»•- 000/0. »•- OOT
*'*' *BBT
OICM.O>0«l»Mnvt.S
T»IC.«.OIIOII«CI«M
20
20
'«
»»
I0
,0
10
30
20
,0
,0
2020
M M
i 0 40
«« >0
10 10
40«0
*0 40 < TO < 10 < ooo
2 0 < 30 «O 10 < 0«O
« o < 20 oo » o < o«o
9 O 20 M 70 < 090
10 < 040 < 40
IO < OIO «O
10 050 a o
040 C OIO M
30
JO
10
7 O
to
10
to
JO
>«i«e>«.aiaii»>4mvL9
OICX.I»0«CNIM
r»ICM.ai>Otur«.OIM
0 < 30 < 40
40 30 «0 , o
1*0 • O , 0 20
3V) | O 10 20
440 4 o to 20
IOO < 2 0 IO < 3 0
1,0 < 20 20<20
< 30 < I O I 0 < M < 3 O ' 10
20 > O < 30 < 20 SO O4O
3 0 C 20 < M < 90 < 10 < 030 < UM < M 90 < 20
IO<30<)OCIO<20<030 40 C 7O < 4 0 M
3O209O IO< IO M SO 3 O 10 3 O
2020IO»0 4O 4OI4O2O
40 * 0 . IM < ,O < M I O IOO 29O 7 O
100 2 0 N «O < IO < 4O «0 7O • 33O 4 0
130 M » M < 10 * «o < M 30 140 o o
4O < 3O M 3D r OHO • JO < 40 10 120 10
30 < 30 * to O*O , 3O ' JO i 0 »O »O
M 3 0 < 030 • O'O • U40 70 2 O . 90
<0 . 70 (MO ^ 0*O ,. OM 4O 40 040
,70
*0
IO
20
4 O
to
4 0
toe IOO «• 4
*»• » 4|
101 101
1 0
3 o
100
40
i4o
M
30
97
*7O
,40
,40
102
3 0
(o
40
10
70
IOI
5 0
M
30
30
7«
»• 4
7 0
to
'. 0
40
74
IAI
/O 3«UO
120 2eoo
1OI2OO
4OIIUO
43 4J 9.
«O 7 UM •* 3
40
10
2O
30
. JRB Associates _
81
-------
Table A-5
CONCENTRATIONS OF. TARGET ORGANIC COMPOUNDS IN SEDIMENTS
FROM OTHER SITES, IN ng/g DRY WEIGHT (PPB)
Fron Malins ec al.. 1980. Appendix Table D-S
a. *-oiif tMn.MtfMTMH.cNC
AC c •«*•<'•<•<
»«•€•<
IN9O43I I. I. 3-COi'v'C*!
3 3. S T>|P«TMVIM*MTMH.C• - OK
•-en. o* DM c
»•••• - oac
o. P- - eeo
«.»• - oee
».»• - ooo/o. »• - DOT
••.»•- ear
0 I CMLOTOl I»MCN»I S
*CNT«C>4.a*a* f 'MZMVI.S
MZIMWJ.OBOI I'MCMUS
•*»'•< •*-(!• 01 l»Xl»LS
oc f*c>*.o
OICM.O*OICl«C»»
«r
Mr .
'O
• to*
a o
3O
1 O
30
40
ao
IO
IO
«. IO
3 0
IO
IO
4O
IO
M
110
70
SO
•0
40
3O
4O
3O
ao
10
< 0*0
< OIO
< OIO
30
39
39
ao
003
IO
30
10
ao
4O
a o
a o
a o
a o
4O
0*3
07O
33
•0
49
39
1*
101
• 10'
1 0
a o
• o
e so
7 0
3 0
l IO
<. 10
4O
3 0
ao
3 O
JO
30
ao
30
4O
IO
• o
IO
IO
4 O
030
' OIO
< OIO
< OIO
< 04O
< oao
< oao
< oao
< 040
f 040
IO
M
IO
4O
1 0
1 0
ao
• ao
• 10
I 04O
i. IO
so
a o
oso
ao
Tt
•• 1
3S
III JO
' 0
so
30
30
10
IO
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. JRB Associates _
-------
APPENDIX B
CONCENTRATION OF TRACE METALS AND
SYNTHETIC ORCANICS IN THE SEDIMENTS OF
ELLIOTT BAY AND IN THE WEST POINT AREA
• " t-f t
Concentration of trace metals in ^g/g >.ry -weight; organics in ng/g dry weight.
Data from Metro/TPPS report (Pavlou, et al.. 1983).
-------
AREA B: ELLIOTT BAY/DUWAMISH WATERWAY
00
u>
AKTIMOHY
ARSENIC
BERYLLIUM
CADMIUM
CHROMIUM
COPPER
LEAD
MANGANESE
MERCURY
NICKEL
SELENIUM
SILVER
TAIILL11IH
ZINC
0149
5.9
Jl
0.61
0.92
36
100
200
390
0.48
21
0.6
0 19
0.1
220
1.8
28
0.58
0 6
68
100
223
320
0.004
2'.
0.14
2 4
0 01
1420
A062
1.2
3.1
1.4
2 3
4.2
4*n
240
340
0 OBB
40
0 09\
O.I)
0 028
240
BO A 2
0 021
4.3
0.94
2.6
50
120
240
270
0 02
• 38
0 Old
0 9
0.009
270
C602
1.5
11
1.3
2 8
50
ISO
340
340
0 032
'.2
0 33
1 3
0.009
350
$0036
4.4
23
0.41
0.5J
52
150
310
360
0.44
32
0 24
2.2
0.1
210
50037
1.3
I*
0 i
0 17
A 4
56
77
J«0
0 13
/.9
0 5
2 4
O.I
120
SOOJ«
0 7
14
054
1 6
56
94
150
160
0 )8
3S
0 42
0 29
0 1
1"»0
SOOK3
3 9
7.1
0.7
0 28
27
90
190
160
0.4
4 9
0.2
0.16
0 1
84
S0064
4.3
23
0.46
1 1
53
*>9
120
240
1.2
24
0.51
1 8
O.I
160
II* in 1
2.5 «
16 «
0.70 »
1.3 •
44 »
142 »
209 *
317 «
0.32 *
31 «
0.31 »
1.2 *
O.OAA *
32» *
S.D.
2 0
9.8
0.34
0.15
17
1M
81
73
0.36
13
0 20
0.91
0 045
l«l
-------
AREA C: ELLIOTT BAY
ANTIMONY
ARSENIC
BERYLLIUM
CADMIUM
CHROMIUM
COPPER
LEAD
MANGANESE
MERCURY
NICKEL
SELENIUM
SILVER
THALLIUM
ZINC
A061
0.41
8.4
0.36
0.49
59
64
130
260
0.024
45
1.1
1.9
0.007
1020
B061
0.35
13
0.41
0.37
63
64
130 •
290
0.072
47
0.39
1.9
0.01
1080
C061
0.22
8.8
0.31
2.2
45
36
55
240
0.022
41
0.35
1.6
0.006
757
S0090
1.3
4.2
0.18
0.75
28
11
84
290
0.12
25
0.20
2.1
0.10
210
S0065
3.5
20
0.46
0.62
42
64
100
300
0.92
31
0.7
1.9
0.1
120
S0064
0.7
9.9
0.35
0.4
45
46
63
210
0.18
30
0.2
1.2
0.1
120
MEAN
1.1 ±
11 +
0.35 +
0.81 +
47 +
48 +
94 +
282 +
0.22 +
37 +
0.49 ±
1.8 +
0.054 + 0
551 +
- SLD.
1.3
5.3
0.10
0.70
. 13
21
32
26
0.35
9.0
0.35
0.32
.051
454
3
09
2.
I
-------
00
AREA D: N.E. ELLIOTT BAY/DENNY WAY CSO
ICTIMMI
uiroic
IIIIU.IIM
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CHinnlCH
corrti
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100
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AREA F: WEST POINT
•001 10 4IOIII 400110
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cwtro It if |i ll ll i
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liino III II ill 14 loot
UK 44 II II II II |
'III 410 1141 l| It 140
II fl II 10 II II II U II
4 1 0 •• 1 0 01 1 0 II 0 01 0 01 110
1 II 1 I 1
1 U II •
II II 1
t 1 It »
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II II It 1 1
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t 1
f
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tft 4 | II
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-------
AREA EE:
u
3)
DO
o
S*
S
4A
ANTIMONY
ARSENIC
BERYLLIUM
CADMIUM
CHRONIUM
COPPER
LEAD
MANGANESE
MERCURY
NICKEL
SELENIUM
SILVER
THALLIUM
ZINC
*
'•
\ .
! •
i
0150
0.31
8.8
0.45
0.25
53
61
87
290
0.004
32
0.49
2.9
0.01
1180
401230
0.5
13
0.36
0.25
54
62
55
420
0.43
32
0.2
3.9
0.1
100
0.67
14
0.4
0.46
47
50
81
380
0.29
38
0.3
0.24
0.1
100
CENTRAL ELLIOTT BAY
401630
0.8
12
0.45
0.23
37
55
68
380
0.63
27
0.33
3.6
0.1
120
0.53
8
0.07
0.05
11
13
30
130
0.06
13
0.2
0.05
0.1
50
401830
1
10
0.44
0.3
47
50
62
340
0.53
31
0.2
2.3
0.1
110
0.67
11
0.24
0.14
47
46
72
330
0.34
43
0.34
0.74
0.1
100
S0015
1.1
14
0.83
0.38
59
49
53
400
0.22
36
0.36
0.41
0.53
130
S0062
0.86
10
0.35
0.36
56
61
68
300
0.52
29
1
0.75
0.1
100
MEAN ^
0.72 +
11 +
0.40 ±
0.27 +
46 +
49 +
64 +
330 ±
0.34 +
31 +
0.38 +
1.7 +
0.14 +
221 +
- S.D^
0.25
2.2
0.20
0.12
15
15
17
87
0.21
8.4
0.25
1.5
0.15
360
-------
AREA D: NORTHEAST ELLIOTT BAY/DENNY WAY CSO
00
31
00
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5'
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2
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•
-------
APPENDIX C
ESTIMATION OF ORGANIC CARBON CONTENT
Utrw; -.-.ju'-:-
-------
Table C-l
PERCENTAGE OF SEDIMENT ORGANIC CARBON AT METRO/TPPS
STATIONS AS ESTIMATED FROM THE PERCENTAGE OF FINES
(The regression used is shown in Figure 8)
Scacion
Number
Area B
0149
A062
B062
C062
S0063
S0064
Area C
A061
B061
C061
S0090
S0065
Area D
40K06
401512
401603
401606
401612
401810
A060
B060
C060
% Fines
68.4
74.2
61.1
89.1
16.4
69.9
57.9
52.4
52.0
84.5
81.4
75.6
81.8
39.9
91
82
68.7
40.1
89.2
91.5
Z Organic
Carbon
2.4
2.6
2.2
3.0
0.8
2.4
2.1
1.9
1.9
2.9
2.8
2.6
2.8
1.5
3.1
2.8
2.4
1.5
3.0
3.1
Scacion
Nunber
Area F
400310
400330
400430
400510
400530
400621
400712
400730
400810
400830
S0004
S0005
S0010
S0099
SHOO
S0101
S0102
S0103
S0104
Area EE
.
0150
401230
401630
401830
S0015
S0062
7. Fines
12.3
IS. 6
26.8
7.8
13.1
4.8
11.7
7.7
7.5
29.8
5.7
8.2
7.4
7.4
6.7
7.4
9.5
8.2
11.9
71.4
7.5
68.7
92.4
55.1
83.4
2 Organic
Carbon
0.69
0.83
1. 12
0.55
0.71
0.46
0.67
0.55
0.54
1.21
0.49
0.57
0.54
0.54
0.52
0.54
0.61
0.57
0.68
2.46
0.55
2.38
3.09
1.97
2.82
89
,JRB Associates —
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