AMBIENT WATER QUALITY ADVISORY
ETHYLBENZENE
OFFICE OF WATER REGULATIONS AND STANDARDS
CRITERIA AND STANDARDS DIVISION
U.S. ENVIRONMENTAL PROTECTION AGENCY
WASHINGTON, D.C. 20460
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NOTICES
This document has been reviewed by the Criteria and Standards
Division, Office of Water Regulations and Standards, U.S.
Environmental Protection Agency, and approved for distribution.
Mention of trade names or commercial products does not constitute
endorsement or recommendation for use.
This document is available to the public through the Criteria and
Standards Division, Office of Water Regulations and Standards,
U.S. EPA, Washington, DC.
ii
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FOREWORD
The Criteria and Standards Division of the Office of Water
Regulations and Standards has instituted water quality advisories
as a vehicle for transmitting the best available scientific
information concerning the aquatic life and human health effects
of selected chemicals in surface waters. Advisories are prepared
for chemicals for which information is needed quickly, but for
which sufficient data, resources, or time are not available to
allow derivation of national ambient water quality criteria.
Data supporting advisories are usually not as extensive as
required for derivation of national ambient water quality
criteria, and the strength of an advisory will depend upon the
source, type, and reliability of the data available. We feel,
however, that it is in the best interest of all concerned to make
the enclosed information available to those who need it.
Users of advisories should take into account the basis for
their derivation and their intended uses. Anyone who has
additional information that will supplement or substantially
change an advisory is requested to make the information known to
us. An advisory for an individual chemical will be revised if any
significant and valid new data make it necessary.
We invite comments to help improve this product.
Edmund M. Notzon, Director
Criteria and Standards Division
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ACKNOWLEDGMENTS
AQUATIC LIFE
Mary D. Balcer, author
University of Wisconsin-Superior, Superior, WI
iv
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CONTENTS
Page
Notices ii
Foreword iii
Acknowledgments iv
I. Advisories 1-1
II. General Information II-l
A. Biological, Chemical and Physical Properties II-l
III. Aquatic Toxicity III-l
IV. Referance IV-1
V. EPA Contacts V-l
v
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SECTION I. ADVISORIES
AQUATIC LIFE
If the estimated or measured ambient concentration of
ethylbenzene exceeds 14 g/L in fresh or salt water, one or more
of the following options must be completed within a reasonable
period of time:
1. Obtain more measurements of the concentration.
2. Improve the estimate of the concentration.
3. Reduce the concentration.
4. Obtain additional laboratory and/or field data on the
effect of ethylbenzene on aquatic life so that a new
aquatic life advisory or water quality criterion can be
derived.
After a reasonable period of time, unless a consideration of all
the available data concerning the ambient concentration and the
effects of ethylbenzene on aquatic life indicates that the
ambient concentration is low enough, it must be reduced.
1-1
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SECTION II. GENERAL INFORMATION
A. Biological. Chemical. and Physical Properties
The following information on the properties of ethlybenzene
and its persistence in the aquatic environment was obtained from
the Handbook of Chemistry and Physics~ha~s or from the QSAR system~hb~s
on May 1, 1987. Some of the values were calculated using
structure-activity relationships.
Property
Value
Source
Molecular Weight
Relative Density (20C)
Log P
Melting Point
Boiling Point
Vapor Pressure
Heat of Vaporization
pKa
Solubility in Water
BCF
Absorption Coef.[Log (Koc)]
106.2 g/mole
0.8670
3.15
-95.C
136. C
7mm Hg
8,550. cal/mole
(not applicable)
153. mg/L
167.
3.14
Calculated
Measured
Calculated
Measured
Measured
Measured
Calculated
Measured
Calculated
Calculated
Hydrolysis Half-life = 1000 days
Hydrolysis is not likely to be an important
mechanism for this chemical.
transformation
Biodegradation Half-life Analysis
Cannot be predicted by the data base.
3
Log 10 (Henry's Constant) = -2.06 atmm /mole
It could be concluded that a chemical with these properties
will vaporize rapidly from and will not persist in open water.
Neely 100-day Partitioning Pattern
Air = 66.31%
Water = 22.96%
Ground = 5.55%
Hydrosoil = 5.18%
a Handbook of Chemistry and Physics, 67th Ed.
Raton, FL.' 1986-1987.
CRC Press, Boca
For information on the QSAR system, see: Hunter, R., L.
Faulkner, F. Culver and J. Hill. Draft user manual for the
QSAR system. Center for Data Systems and Analysis, Montana
State University. November, 1985.
II-l
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SECTION III. AQUATIC TOXICITY
Introduction
Aquatic life advisory concentrations are conceptually
different from national aquatic life water quality criteria.
Aquatic life criteria are based on toxicity and bioconcentration
data for a sufficiently diverse group of animals and plants to
provide reasonable confidence in the appropriateness of the
criteria. Advisories are issued for selected chemicals for which
sufficient data are not available to allow derivation of national
water quality criteria for aquatic life. Because aquatic life
advisories are intended to be used to identify situations where
there is cause for concern and where appropriate action should be
taken, the advisory concentration for a chemical is derived to be
equal to or lower than what the Criterion Continuous
Concentration (Stephan et al. 1985) would be if a national water
quality criterion for aquatic life could be derived for the
chemical. If the concentration of a chemical in a variety of
surface waters is found to exceed the aquatic life advisory
concentration, this may indicate that the U.S. EPA should
consider deriving aquatic life water quality criteria for that
chemical.
The literature searching and data evaluation procedures used
in the derivation of aquatic life advisories are identical to
those used in the derivation of water quality criteria for
aquatic life (Stephan et al. 1985). However, advisories do not
contain a section on "Unused Data" as in a criteria document.
This aquatic life advisory concentration for ethlybenzene was
derived using the procedures described in the "Guidelines for
Deriving Ambient Aquatic Life Advisory Concentrations" (Stephan
et al. 1986). A knowledge of these guidelines is necessary in
order to understand the following text, tables, and calculations.
The latest comprehensive literature search for information for
this aquatic life advisory was conducted in February, 1987.
In static toxicity tests, the amount of ethylbenzene in the
exposure chambers declines rapidly. Benville and Korn (1977) and
Caldwell et al. (1977) noted that the ethylbenzene concentrations
decreased by 38-99% in 24 hr and that less than 1% of the
original concentrations remained after 48 hr. Brooke (1987)
calculated that, ethylbenzene's half-life in solution was only
16.3 hr. Brooke also ran a set of comparison tests to determine
if the 96-hr LC50 for fathead minnows exposed to ethylbenzene was
dependent on the exposure method. He reported that the LC50 from
a measured flow-through exposure (9,100 g/L) was similar to
that obtained from static exposures that were measured at 48 hr
intervals (mean LC50 = 10,140 g/L). However, if the static 96-
hr LC50 had been calculated using only the 0-hr measurement, the
III-l
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average value would have been 23,870 g/L, i.e. 2.623 times
larger than the value obtained from the flow-through exposure. In
order to allow a more direct comparison of the effects of
ethylbenzene on different species of aquatic organisms, the
results from the various types of exposures must be standardized.
Therefore, acute toxicity data in Table 1 that were obtained from
static tests that were not measured, or were only measured
initially, were divided by a factor of 2.623 to equate them with
flow-through results.
Effects on Freshwater Organisms
Acceptable data on the acute toxicity of ethylbenzene to
freshwater organisms are available for two cladocerans and six
species of fish (Table 1). The adjusted 48-hr EC50 for the
cladoceran, Daphnia magna, was 28,600 g/L. The amphipod,
Gammarus pseudolimnaeus was much more sensitive to exposure to
ethylbenzene (96-hr LC50 = 1,940 g/L). Among the fish, the
Species Mean Acute Values (SMAV) ranged from 5,340 g/L for the
rainbow trout (Salmo gairdneri) to 80,060 g/L for the channel
catfish (Ictalurus punctatus). Although the adjusted 96-hr LC50
for juvenile bluegill (Lepomis macrochirus) varied from 21,300 to
108,700 ug/L depending on the exposure water conditions, no
significant correlation was found between toxicity and water
temperature, hardness, or pH (Mayer and Elllersieck 1986).
No acceptable data are available describing the chronic
effects of ethylbenzene on freshwater organisms.
Additional data are available on the acute effects of
ethylbenzene on freshwater bacteria, algae, and protozoans (Table
3). Although some of these results are from static unmeasured
exposures, the data were not adjusted to flow-through conditions
and therefore may not be directly comparable to the values
contained in Table 1.
Cell replication in the bacterium, Pseudomonas putida was
affected by an ethylbenzene concentration of 12,000 g/L, while
near saturation levels (>55,000 to >140,000 g/L) were required
to inhibit cell replication in three species of protozoans. Algal
photosynthesis was reduced by 50% after a 3-hr exposure to
ethylbenzene concentrations of 51,000 and 63,000 g/L
(Hutchinson et al. 1979, 1980).
111-2
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Effects on Saltwater Organisms
Acceptable data on the acute toxicity of ethylbenzene to
saltwater organisms are available for four species of
invertebrates and two fishes (Table 1). Embryos of the Pacific
oyster, Crassostrea qiqas. were quite resistant to ethylbenzene
(adjusted LC50 = 123,100 g/L). The bay shrimp, Cranqon
franciscorum. was much more sensitive than the dungeness crab,
Cancer maqister. or the mysid, Mysidopsis bahia, (adjusted LC50s
= 420, 13,000, and 33,400 g/L, respectively). Ethylbenzene was
approximately twenty-seven times more toxic to juvenile striped
bass, Morone saxatilis. (adjusted LC50 = 3,700 g/L) than to
juvenile sheepshead minnows, Cyprinodon varieqatus. (adjusted
LC50 = 100,000 g/L).
No acceptable data are available on the chronic toxicity of
ethylbenzene to saltwater organisms.
Potera (1975) found that algal photosynthesis was affected
by ethylbenzene concentrations of 13,000 g/L (Table 3). The 24-
hr LC50s for an adult copepod, Nitocra spinipes. and larval and
adult grass shrimp, Palaemonetes puqio. were quite similar
(10,200 to 40,000 g/L) and were not greatly affected by
salinities of 15 and 25 g/kg or by temperatures of 10 and 20C.
Calculation of Advisory Concentration
A total of fourteen Species Mean Acute Values (SMAV) and
Genus Mean Acute Values (GMAV) are available for freshwater and
saltwater organisms (Table 2). The GMAVs ranged from 420 g/L
for the bay shrimp, Cranqon franciscorum. to 123,100 g/L for
the Pacific oyster, Crassostrea qiqas. The combined freshwater
and saltwater data set is adequate to allow the calculation of a
Final Acute Value (FAV) of 348.6 g/L. Due to the absence of any
acceptable data on the chronic toxicity of ethylbenzene to
aquatic organisms, an empirical value of 25 is used as the
Advisory Acute-Chronic Ratio (AACR). Division of the FAV (348.6
g/L) by the AACR (25) results in an Advisory Concentration of 14
g/L.
111-3
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Table I. Acute Toxicity of E1hyI benzene to Aquatic Animals
rRFSHWATER SPfCIES
Spec i es Method"
\
C I adoceron S , U*
(<21 hr),
Dophn i o magna
Amph i pod T, W
(adult)
Gammorus
ps eudoIi mnoeus
Roinbo> t rout S, 0
(2 4 9).
So I mo go i rdneri
Goldfish S, U
(3 8-6 4 cm).
Caress ius
ourat us
Fathead minnow S, II
{3.8-6.4 cm),
Pi mephoIes
promelos
Fathead minnow S, U
(3 8-6. 4 cm) .
Pi meptiol es
promelas
Fathead minnow S, U
(juvenile),
T i ineplio I os
pr ninp I o~.
Chomi coI
(99*)
(993!)
Hardness IC5D
(mg/L as or EC5I1
CaCO,) l/tg/i)
I 73
50
4*.
20
360
20
51-53
75,0(10
I ,940
14,000
94,440
42,330
48.510
77,1 no
Adj usted
LC50 or EC50
Ihq/1)°
28,6011
5.340
36,000
16,140
18,490
29,470
Species Mean
Acute Value
(iio/l)
28,600
I .940
5,340
36,000
Ref erence
LeBlanc 1980
Brooke 1987
Johnson and Finley
1980; Mayer and
[llersiecti 1986
Pickering and
Henderson 1966
Pickering and
Henderson I 966
Pickering and
Henderson 1966
Brooke 1987
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Table I (continued)
Spec i es
fat head mi nno«
(juvenile)
Pi mephnIes
promeIas
Tot head mi nnow
(j u v e n i I e) ,
Pi mephaIes
promelos
Fathead minno*
(juven iIe).
Pimephales
promelos
fathead minno*
(j uveniIe),
Pitnephol es
promel05
Cotheod minnow
(juvenile).
Pireepholes
promelas
Tat head mi nnow
(juwenile),
Pimepholes
Hardness
(mg/L os
Met hod0 Chemi co I ^ CaCO,1
S. U (99?) 51-53
*
S. Uo (99?) 51 -53
S. U0 (99:) 51-53
S, U (99X) 51-53
S. U ( 995!) 51-53
7. U (99*) 50
promelas
LC5n
or EC50
Adjus ted
LC50 or EC50
(«q/t)c
Species Ueon
Acute Value
, (fq/U .
Reference
88.800 33.850
25,7 00 9,81)0
22,100 8,425
11 .000
8,600
Brooke 198/
Brooke 1987
Brooke 198/
Brooke I 98/
Brooke 198/
9.100
9.100
Brooke 198/
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Table I (continued)
Hardness
»• (mg/L os
Spec i es Met hod" Chemi col _C_a_CO
Channel catfish S, U - 44
(0 I 9).
Ic t 0 I urus '
puncI 0 t us *
Guppy S, II - 2D
(6 mo).
Poec i I i 0
ret iculoto
BIuc9 i11 S, U - 20
(3 8-6.4 cm),
tepomi s
mocroch i rus
BI ueg ill S, II - 32-48
(young of year),
Lepomi s
mocroch i rus
81uegi11 S, U - 44
(0.2 g). (I7°C
Lepomi s pH=7.4)
mocroch i rus
Bluegi11 S, U - 44
(juvenile), (22°C
Lepomis pH=7.4)
macroch i rus
Bluegill S. U - 44
(j uven iIe), (27°C
Lepomi s pH=7.4)
mocrochi ru".
LC50 Adjusted Species Mean
or EC5fl LC50 or EC50 Acute Value
(na/L) (ua/l)C («iq/H Reference
210,0110 80.060 80,060 Johnson ond Finley
I960; Mayer and
C I Iers i eck I 986
97.100 37,020 37,020 Pickering ond
Henderson 1966
32,0n0 12,200 - Pickering and
Henderson 1966
150,000 57,200 - Buccofusco et al.
1981
88,000 33.500 - Johnson and Finley
1980; Moyer and
Ellersieck 1986
84.000 32.000 - Mo*"- <"«1
Cllersieck 1986
I 4(1,000
53.400
Mayer and
Cllersieck 1986
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Table I (conli nued)
Hardness
(mg/l os
Species MetHftd0 Chemicolb CoCO^)
BIuegiI I S, U - 44
(juvenile). (I9"C
Lepomis pHr6 5)
mqc roc h i rus 1
*
Bluegill S, U - 44
(j uven i1e) , (I 9°C
Lepomi s pH=7.5)
mocroc h i r us
BI ueg i II S , II - 44
(juvenile), (I9°C
Lepomis pH=8.5)
macrochirus
BluegiII S, U - 12
(juvenile). (17°C
Lepomis p H= 6.0 J
mocrochi rus
BluegilJ S, U - 44
(juvenile), (I7°C
Lepomis pH=8 0)
macrochi rus
Bluegill S. U - 162
(juvenile), (I7°C
lepomis pH=8 0)
moo roch irus
6 I ueq iI I S , U - 300
(juvenile). (I7°C
lepomi s pM=8 0)
mac r oc li i rus
LC50
or EC50
Adjusted Species Mean
LCSO or EC50 Acute Value
Referenc e
56,110(1 21 ,300
se.nnn 32,buo
285,000 K1B.70G
135.000 51,470
134,0(10 51,090
80.000 30.500
Uayer and
E11 ers i ecI 1986
Mayer and
E11 ers i eck I 986
Uayer and
Ellersiect 1986
Uayer and
Ctlersiecfc 1986
Uayer and
C11ers i eck I 986
Uayer and
Ellersiect 1986
135,01)0 51.470 39,040 Uayer and
Ellersicck 1986
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Table I (conti nued)
SALTWATER SPECIES
Spec i os Met hod
I
Poc i f i c oyster S , U*
(embryo),
Crossostreo
q i qos
Mys id, S, U
Hys i dops i s
boh i a
Chemi caI
Salinity
(g/Ko)
25 3-30 8
LC50
or CC5D
323,nno
Adj usted
LC50 or EC50
123,10(1
87,6(10 33,400
Species Mean
Acute Value
fuq/L)
123.100
33,400
Reference
Legore 1374
U S. [PA 1978
Boy shrimp S, M
(adult) ,
Cronqon
f rone i scorum
Dungeness crab R, U
(1st zoeo),
Cancer moqister
Sheepsheod S, U
mi nno«
(juveniIe) ,
Cypr i nodon
vor i egot us
(>99Z)
25
420
420
Analyt ical
(>80Z)
30
10-31
13,000 13,000
280.000 106,700
13,000
106,700
Benv i11e and Karn
1977
Cold«elI et a I. 1977
HeltmulIer et al.
1981
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Table t. (conli nued)
Spec i <>s
Slriped ba-.s
(j uven iIe).
Morone
s o x o I i I i s
Method
S. U
C h em i c a 1
(>99:}
Sat i ni1y
25
LC50
or CC50
(ft/1 )
3,700
Adjusted
LC50 or CC50
(>iq/L)C
Species Mean
Acute Value
t^q/U
3.700
Ref erencr;
Benvilie and Kara
(977
0 S - Static; R = Reneoel ; F * f I on-1 hrough, M = Measured, = 0-lir measurement only; U = Unmeasured
Percent purity is listed in parentheses vhen avoilable.
Static unmeasured and static 0-hr measured data ore adjusted by dividing by a Tactor of 2.623
to adjust them to flon-through conditions
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Table 2
Ranked Cenus Mean Acute Values ¦ i t h Spec
Genus Uean
Acute Value
Rant i¦ (
-------
Table 2 (cont inued)
Ratrk
Genus Uean
Acute Va I ue
(/'"/'-I
Spec i es
Species Mean
Acut e Value
f/'q/tlb
Species Mean
Acute-Chroni c
Ratio
5.340 Rainbow trout, 5,34(1
So Imp ga i rdner i
3,700 Striped boss, 3,700
Morone so»at iI is
I , 940 Amph ipod, I,940
Goirimorus pr>eudoI i moaeus
420 Bay shrimp, 420
Cronqon f rune i scor urn
0 Ranked from most resistant to most sensitive based on Genus Mean Acute Value.
^ From Table I.
rinol Acute Volue = 348.6 /19/L.
Advisory Acute-Chronic Ratio = 25
Advisory Concentration = (348.6 fiq/l)/ 25 = 14 /J9/L
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Table 3. Other Data
Spec i es
Bacterium,
Pseudomonns
pu t i do
Blue-green alga,
Anacvst is
oeruqi noso
Green alga,
ChIamydomonas
anquIosa
Green alga,
Chlorel la
vu I gar i s
Green alga,
Scenedeswus
guadr icoudo
Protozoan,
Chi Iomoros
poromaeci um
Protozoan,
Entosi phon
Hardness
(mg/L as
Chemi col CoCO,)
suI cat um
Effects of EthyI benzene on Aquatic Organisms
fRESHWATER SPECIES
Durat i on
Effect
Concentrat i on
(160,000
8ringmann ond Kuhn
1977a, 1978a,b.
1980a
48 hr
Inc i p i ent i nhIbi 11 on
of cell repli cat i on
>55.000
BrIngmann et al.
1980; Bringmann and
ond Kuhn 1981
72 hr •
Incipient inhibition >140,000
of cell repli cat I on
Bringmann 1978;
Bringmann ond Kuhn
1980a, 1981
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Table 3 (continued)
Hardness
(mg/L as
Spec i es Chemi col CoCOj)
Protozoan,
Uronoma
p o r d u c ? i
Clodoceran - 286
(24 hr),
Dophn i a magna
Spec i es
Green alga,
Chlorella sp.
Chemi col
Reagent
Sali ni t y
fq/Kq)
is
Copepod
(odult),
Hi tocra
spi nipes
Copepod
(adul t)
Hi tocra
Reagent
Reagent
IS
25
spi ni pes
Durot i on
Effect
Concent rat i on
(»q/L) Ref erencp
20 hr
I nc i p i ent inhibition
of cell replication
>110.000
Bringmann and Kuhn
1980b; 1981
24 hr
ecsn
(i mmobiIi zat i on)
190,000
BrLngmann ond Kuhn
1977b
SALTWATER SPECIES
Duration [f f ec t
12 hr Inhibited photo-
synthesIs/respi rot i on
rat I o
Concentrat i on
(uo/L)
13,000
Reference
Potera 1975
24 hr
LC50
16,000
Potera 1975
24 hr
LC50
40,000
Potera 1975
-------
Toble 3 (continued)
Spec i es
Gross shrimp
(larva),
PoIagmnnet es
pun i o
Crass shrimp
(larva),
Pa Iaemonet es
pug i o
Grass shrimp
(adu11) ,
PoIaemonet es
pug i o
Grass shrimp
(adult),
Pa Ioemonetes
pug i o
Grass shrimp
(adult),
PoIoemonetes
Salinity
Chemi coI Iq/Kq) Durot ion
Reagent 15 24 hr
Reagent 25 24 hr
Reagent 15 24 hr
(20°C)
Reagent 25 24 hr
(20°C)
Reagent 15 24 hr
(I0°C)
pug i o
Concentrot i on
Effect (t/g/L) Reference
LC50 10,200 Potera 1975
LC50 22,100 Potero 1975
LC50 14,500 Potera 1975
LC50 14,400 Potera 1975
LC50 17,300 Potera 1975
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Table 3 (continued)
Spec i es
Gross shrimp
(adult),
Pn I oomonet <»s
p ii q I o
Coho silmon
(5-40 q).
One orby nc hus
It i s u t c h
Salinity
Chemi coI (q/Kq)
Reaqent 25
(in°c)
3D
Duro t i on Ef f ec t
24 hr LC50
Concent rat i on
(iiq/l)
. 17,300
Ref erence
Potera 1975
24 l.r
Let ha Ii t y
50,000
Morro* et a I. I 975
-------
SECTION IV.REFERENCES
Benville, P.E., Jr. and S. Korn. 1977. The acute toxicity of six
monocyclic aromatic crude oil components to striped bass (Morone
saxatilis) and bay shrimp (Craqo franciscorum). Calif. Fish and
Game 63:204-209.
Bringmann, G. 1973. Determination of the biological damage from
water pollutants from the inhibition of glucose assimilation in
the bacterium Pseudomonas fluorescens. Gesund.-Ing. 94:366-369.
Bringmann, G. 1978. Studies on the biological effects of
waterborne pollutants in protozoans, I. Bacteriophage
flagellates (model organism: Entosiphon sulcatum Stein). Z.
Wasser Abwasser Forsch. 11:210-215.
Bringmann, G. and R. Kuhn. 1977a. Limiting values for the
damaging action of water pollutants to bacteria (Pseudomonas
putida) and green algae (Scenedesmus quadricauda) in the cell
multiplication inhibition test. Z. Wasser Abwasser Forsch. 10:87-
98.
Bringmann, G. and R. Kuhn. 1977b. Results of the damaging effect
of water pollutants on Daphnia magna. Z. Wasser Abwasser Forsch.
10:161-166.
Bringmann, G. and R. Kuhn. 1978a. The effect of water pollutants
on blue-green algae (Microcystis aeruginosa) and green algae
(Scenedesmus quadricauda) in the cell multiplication inhibition
test. Vom Wasser 50:45-60.
Bringmann, G. and R. Kuhn. 1978b. Testing of substances for their
toxicity threshold: Model organisms Microcystis (Diplocystis)
aeruginosa and Scenedesmus quadricauda. Mitt. Int. Ver. Theor.
Angew. Limnol. 21:275-284.
Bringmann, G. and R. Kuhn. 1980a. Comparison of the toxicity
thresholds of water pollutants to bacteria, algae, and protozoa
in the cell multiplication inhibition test. Water Res. 14:231-
241.
Bringmann, G. and R. Kuhn. 1980b. Determination of the harmful
biological effect of water pollutants on protozoa. II.
Bacteriovorous "clliates. Z. Wasser Abwasser Forsch. 13:26-31.
Bringmann, G. and R. Kuhn. 1981. Comparison of the effects of
harmful substances on flagellates as well as ciliates and on
holozoic bacteriophagous and saprozoic protozoa. Gas-Wasserfach,
Wasser-Abwasser 122:308-313.
IV-1
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Bringmann, G. , R. Kuhn and A. Winter. 1980. Determination of the
biological effects of water pollutants to protozoa. III.
Saptfozoic flagellates. Z. Wasser Abwasser Forsch. 13:170-173.
Brooke, L.T. 1987. Center for Lake Superior Environmental
Studies, University of Wisconsin-Superior, Superior, WI.
(Memorandum to L.J. Larson, CLSES, University of Wisconsin-
Superior, Superior, WI). August 31.
Buccafusco, R.J., S.J. Ells and G.A. LeBlanc. 1981. Acute
toxicity of priority pollutants to bluegill (Lepomis
macrochirus). Bull. Environ. Contam. Toxicol. 26:446-452.
Caldwell, R.S., E.M. Caldarone and M.H. Mallon 1977. Effects of a
seawater-soluble fraction of Cook Inlet crude and its major
aromatic components on larval stages of the dungeness crab Cancer
magister Dana. In: Fate and effects of petroleum hydrocarbons in
marine ecosystems and organisms. Wolfe, D.A. (Ed). Pergamon
Press, New York, NY. pp 210-220.
Heitmuller, P.T., T.A. Hollister and P.R. Parrish. 1981. Acute
toxicity of 54 industrial chemicals to sheepshead minnows
(Cyprinodon varieqatus). Bull. Environ. Contam. Toxicol. 27:596-
604.
Hutchinson, T.C., J.A. Hellebust, D. MacKay, D. Tam and P. Kauss.
1979. Relationship of hydrocarbon solubility to toxicity in algae
and cellular membrane effects. J. Am. Petrol. Inst. 4308:541-547.
Hutchinson, T.C., J.A. Hellebust, D.Tam, D. MacKay, R.A.
Mascarenhas and W.Y. Shiu. 1980. The correlation of the toxicity
to algae of hydrocarbons and halogenated hydrocarbons with their
physical-chemical properties. Environ. Sci. Res. 16:577-586.
Johnson, W.W. and M.T. Finley. 1980. Handbook of acute toxicity
of chemicals to fish and aquatic invertebrates. Resource
Publication 137. U.S. Fish and Wildlife Service, Washington, DC.
LeBlanc, G.A. 1980. Acute toxicity of priority pollutants to
water flea (Daphnia magna). Bull. Environ. Contam. Toxicol.
24:684-691.
Legore, R.S. 1974. The effect of Alaskan crude oil and selected
hydrocarbon compounds on embryonic development of the pacific
oyster, Crassostcea qjqas. Ph.D. thesis University of Washington,
Seattle, WA. Available from: University Microfilms, Ann Arbor,
MI. Order No. 74-29, 447.
Morrow, J.E., R.L. Gritz and M.P. Kirton. 1975. Effects of some
components of crude oil on young coho salmon. Copeia 2:326-331.
IV-2
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Pickering, Q.H. and C. Henderson. 1966. Acute toxicity of some
important petrochemicals to fish. J. Water Pollut. Control Fed.
38:1419-1429.
Potera, G.T. 1975. The effects of benzene, toluene and
ethylbenzene on several important members of the estuarine
ecosystem. Ph.D. thesis. Lehigh University, Bethlehem, PA.
Available from: University Microfilms, Ann Arbor, MI. Order No.
75-24, 012.
Stephan, C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A.
Chapman and W.A. Brungs. 1985. Guidelines for deriving numerical
national water quality criteria for the protection of aquatic
organisms and their uses. PB85-227049. National Technical
Information Service, Springfield, VA.
Stephan, C.E., G.A. Chapman, D.J. Hansen and T.W. Purcell. 1986.
Guidelines for deriving ambient aquatic life advisory
concentrations. December 2 draft. U.S. Environmental Protection
Agency, Environmental Research Laboratory, Duluth, MN.
U.S. EPA. 1978. In-depth studies on health and environmental
impacts of selected water pollutants. (Table of data available
from Charles E. Stephan, U.S. EPA, Duluth, MN).
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SECTION V. EPA CONTACTS
AQUATIC LIFE ADVISORIES
For further information regarding the aquatic life and fish and
water exposure advisories contact:
FTS 382-7144
FTS 475-7315
(202)382-7144
(202)475-7315
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