«EPA
United States
Environmental Protection
Acencv
Office of Water
(MC-4304)
EPA-822-F-93-OOI
October, 1993
Fact Sheet
Ambient Aquatic Life Water Quality Criteria
for Aniline
AUTHORITY
Ambient water quality criteria are published pursuant to Section 304(a) of the Clean Water
Act and may form the basis for enforceable standards if adopted by a State into water quality
standards. The criteria reflect the latest scientific knowledge on the identifiable effects of
pollutants on public health and welfare, aquatic life and recreation. They are developed
using a process described in the "Guidelines for Deriving Numerical National Water Quality
Criteria for the Protection of Aquatic Organisms and Their Uses" (Stephan et al.. 1985).
BACKGROUND
Aniline (aminobenzene, benzenamine, phenylamine) occurs naturally in coal tars and is
manufactured through various chemical procedures. The major uses of aniline are in the
polymer, rubber, agricultural and dye industries. Aniline is used to manufacture
polyurethanes, antioxidants, antidegradants, vulcanization accelerators, and sulfa drugs.
Aniline derivatives are used in herbicides, fungicides, insecticides, repellents, and defoliants.
Aniline has also been used as an antiknock compound in gasolines. Aniline is the simplest of
the aromatic amines C
CRITERIA VALUES
Except where locally important species are
very sensitive:
* Freshwater aquatic organisms and
their uses should not be affected
unacceptably if the four-day
average concentration (i.e., chronic
exposure) of aniline does not
exceed 14 ug/1 more than once
every three years on the average
and if the one-hour average
concentration, (i.e., acute exposure)
does not exceed 28 ug/1 more than
once every three years on the
average, and
Saltwater aquatic organisms and
their uses should not be affected
unacceptably if the four-day
average concentration (i.e., chronic
exposure) of aniline does not
exceed 37 ug/1 more than once
every three years on the average
and if the one-hour average
concentration (i.e., acute exposure)
does not exceed 77 ug/1 more than
once every three years on the
average.
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IMPLEMENTATION INTO STATE
STANDARDS
Ambient water quality criteria may form
the basis for enforceable standards if
adopted by a State into water quality
standards. States may opt td develop site
specific criteria (Water Quality Standards
Handbook, December, 1983, EPA#:
440/5-83-011). Replacement of national
criteria with site specific criteria may
include site specific criterion
concentrations, mixing zone considerations
(Water Quality Standards Handbook,
December, 1983, EPA#: 440/5-83-011),
averaging periods and site-specific
frequencies of allowed exceedences
(Guidelines for Deriving Numerical
National Water Quality Criteria for the
Protection of Aquatic Organisms and Their
Uses, Stephan et al.. 1985). When the
basis for site specific criteria relate to the
averaging period, there should be a
justification for why variability
assumptions underlying national criteria
are inappropriate.
AVAILABILITY OF DOCUMENT
Copies of the proposed criteria document,
and other referenced documents, may be
obtained from the address below.
Aniline Proposal
Water Resource Center, (RC-4100)
U.S. Environmental Protection Agency
401 M Street, S.W.
Washington, D.C., 20460
For further information please contact:
Mrs. Amy L. Leaberry
U.S. Environmental Protection Agency
Office of Water
Water Quality Criteria Section
(Mail Code - 4304)
401 M Street, SW
Washington, DC 20460
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9/22/93
AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR
ANILINE
(CAS Registry Number 62-53-3)
SEPTEMBER 1993
U.S. ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF WATER
OFFICE OF SCIENCE AND TECHNOLOGY
HEALTH AND ECOLOGICAL CRITERIA DIVISION
WASHINGTON, D.C.
OFFICE OF RESEARCH AND DEVELOPMENT
ENVIRONMENTAL RESEARCH LABORATORIES
DULUTH, MINNESOTA
NARRAGANSETT, RHODE ISLAND
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* / <• -, - J,
NOTICES
This document has been reviewed by the Environmental Research
Laboratories, Duluth, MN and Narragansett, RI, Office of Research and
Development and the Health and Ecological Criteria Division, Office of Science
and Technology, U.S. Environmental Protection Agency, and approved for
publication.
Mention of trade names or commercial products does not constitute
endorsement or recommendation for use.
This document is available to the public through the National Technical
Information Service (NTIS), 5285 Port Royal Road, Springfield, VA 22161.
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5/22/93
FOREWORD
Section 304(a) (1) of the Clean Water Act of 1977 (P.L. 95-217) requires
the Administrator of the Environmental Protection Agency to publish water
quality criteria- that accurately reflect the latest scientific knowledge on
the kind and extent of all identifiable effects on health and welfare that
might be expected from the presence of pollutants in any body of water,
including ground water. This document is a revision of proposed criteria
based upon consideration of comments received from other federal agencies,
state agencies, special interest groups, and individual scientists. Criteria
contained in this document replace any previously published EPA aquatic life
criteria for the same pollutant(a).
The term "water quality criteria" is used in two sections of the Clean
Water Act, section 304(a)(l) and section 303(c){2). The term has a different
program impact in each section. In section 304, the term represents a non-
regulatory, scientific assessment of ecological effects. Criteria presented
in this document are such scientific assessments. If water quality criteria
associated with specific stream uses are adopted by a state as water quality
standards under section 303, they represent maximum acceptable pollutant
concentrations in ambient waters within that state that are enforced through
issuance of discharge limitations in NPDES permits. Water quality criteria
adopted in state water quality standards could have the same numerical values
as criteria developed under section 304. However, in many situations states
might want to modify water quality criteria developed under section 304 to
reflect local environmental conditions and human exposure patterns. ^
Alternatively, states may use different data and assumptions than EPA in
deriving numeric criteria that are scientifically defensible and protective of
designated uses. It is not until their adoption as part of state water
quality standards that criteria become regulatory. Guidelines to assist the
states and Indian tribes in modifying the criteria presented in this document
are contained in the Water Quality Standards Handbook (December 1983). This
handbook and additional guidance on the development of water quality standards
and other water-related programs of this Agency have been developed by the
Office of Water.
This document, if finalized, would be guidance only. It would not
establish or affect legal rights or obligations. It would not establish a
binding norm and would not be finally determinative of the Issues addressed.
Agency decisions in any particular situation will be made by applying the
Clean Water Act and EPA regulations on the basis of specific facts presented
and scientific information then available.
Tudor T. Davies
Director
Office of Science and Technology
in.
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ACKNOWLEDGMENTS
Larry T. Brooke David J. Hansen '
(freshwater author) (saltwater author)
University of Wisconsin-Superior Environmental Research Laboratory
Superior, Wisconsin Narragansett, Rhode Island
Robert L. Spehar Suzanne M. Lussier
(document coordinator) (saltwater coordinator)
Environmental Research Laboratory Environmental Research Laboratory
Duluth, Minnesota Narragansett, Rhode Island
iv
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CSN7ENTS
Page
Notices ii
Foreword . iii •
Acknowledgments iv
Tables vi
Introduction ". . . . 1
Acute toxicity to Aquatic Animals . .' 2
Chronic Toxicity to Aquatic Animals 4
Toxicity to Aquatic Plants 6
Bioaccumulation 7
Other Data 1
Unused Data 10
Summary 11
National Criteria 13
Implementation 13
References 33
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TABLES
Pace
1. Acute Toxicity of Aniline to Aquatic Animals '. IS
2. Chronic Toxicity of Aniline to Aquatic Animals 19
3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic
Ratios 21
4. Toxicity of Aniline to Aquatic Plants 24
5. Other Data on Effects of Aniline on Aquatic Organisms 26
vx.
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OP-AFT
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Introduction
Aniline (aminobenzene, benzenamine, phenylamine) is the simplest of the
aromatic amines (CjH5NH:) . It occurs naturally in coal-tars (Shelford 1917)
and is manufactured by the catalytic reduction of nitrobenzene, amination of
chlorobenzene and immonolysis of phenol.
The major users of aniline are the polymer, rubber, agricultural and dye
industries. Demand for aniline by the dye industry was high prior to the
1970's but decreased markedly in the United States thereafter because of the
increased use of synthetic fabrics. Aniline is used today primarily by the
polymer industry to manufacture products such as polyurethanes. The rubber
industry uses large amounts of aniline to manufacture antioxidants,
antidegradants and vulcanization accelerators. The pharmaceutical industry
uses aniline in the manufacture of sulfa drugs and other products. Important
agricultural uses for aniline derivatives include herbicides, fungicides,
insecticides, repellents and defoliants. Aniline has also been used as an
antiknock compound in gasolines (Kirk-Othmer 1982).
Aniline is soluble in water up to 34,000,000 nq/l, (Verschueren 1977).
The log,0 of the octanol-water partition coefficient for aniline is 0.90 (Chiou
1985a). Through direct disposal, such as industrial discharges and non-point
sources associated with agricultural uses, it enters the aquatic environment.
It is removed from the aquatic environment by several mechanisms. The «*;or
pathway of removal from water is by microbial decomposition (Lyons et al.
1984, 1985). Several minor pathways have been identified including
evaporation, binding to humic substances and autoxidation.
Additions to the aniline molecule of certain functional groups have o*«n
found to increase toxicity (Brooke et al. 1984; Geiger et al. 1986, 1987).
Tests with the fathead minnow (Pimephales promelasl have demonstrated that
substitutions with halogens, (chlorine, fluorine, and bromine) increased
toxicity. The addition of.alkyl groups also increased toxicity; the tojn.ci.ty
increases in proportion to the increase in chain length. Twenty-four
substitutions were tested and all except oara additions of methyl and nitre
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groups increased the toxicity to the fathead minnow.
All concentrations reported herein are expressed as aniline. Results of
such intermediate calculations as recalculated LCSO's.and Species Mean Acute
Values are given to four significant figures to prevent round-off error in
subsequent calculations, not to reflect the precision of the value. Whenever
adequately justified, a national criterion may be replaced by a site-specific
criterion (U.S. EPA 1983a) that may include not only site-specific
concentrations (U.S. EPA 1983b) but also site-specific frequencies of allowed
excursion (U.S. EPA 1985).
A comprehension of the "Guidelines for Deriving Numerical National Water
Quality Criteria for the Protection of Aquatic Organisms and Their Uses"
(Stephan et al. 1985), hereinafter referred to as the Guidelines, and the
response to public comment (U.S. EPA 1985), is necessary to understand the
following text, tables, and calculations. The latest comprehensive literature
search for information for this document was conducted in September 1992; scne
more recent information is included.
Acute toxicitv to Aquatic Animals
The data that are available according to the Guidelines concerning -.-.•
acute toxicity of aniline are presented in Table 1. Cladocera were the ac«t
sensitive group of the 19 species tested. Several species of larval oudgec
and embryos and larvae of the clawed toad, Xenopus laevis. were the mo«t
resistant to aniline in acute exposures. Fish tended to be in the nu3-rar;«
of sensitivity for aquatic organisms.
Forty-eight-hour ECSOs for the cladocerans Ceriodaphnia dubia and
Daphnia maona were 44 pg/L and 530 ng/L, respectively. Several indeperx^^t
exposure* conducted with both species showed consistency among the t««t»
(Table 1). However, there appears to be a large increase in tolerance at
aniline between cladocerans and other aquatic species. The 96-hr LC50 for tr.«
next most sensitive species, a planarian, Duaesia tiorina. was 31,600 *q/l.
Ninety-six-hour LCSOs for fish ranged from 10,600 to 187,000
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rainbow trout (Oncorhvr.cus mvkiss) wa3 the most sensitive species of fish
tested, with 96-hr LCSOs ranging from 10,6flO to 41,000 Aig/L. The bluegill
(Lepomis macrochiruai .was slightly more tolerant of aniline with a 96-hr LCSO
of 49,000 pg/L. Fathead minnows, Pimephales promelas. and goldfish, Carassiua
auratus. were the most tolerant of aniline of the fish species tested.
Ninety-six-hour LCSOs for tests with fathead minnows ranged from 32,000 to
134,000 pg/L. A 96-hr LCSO for the goldfish was 187,000 pg/L.
Franco et al. (1984) exposed four species of midge larvae to aniline and
found them to be the most tolerant of- aniline of all species tested. The
midge, Clinotanypus pinquis. was the most tolerant of the four species tested;
a 48-hr LCSO of 477,900 tJg/L was calculated for this species. LCSOs for other
midge species tested by Franco et al. (1984), ranged downward to 272,100 ^tg/L.
Holcombe et al. (1987) tested another species of midge (Tanvtarsus dissimilis)
and reported a 48-hr LCSO >219,000 pg/L.
The African clawed frog, Xenopus laevis. was relatively tolerant of I
aniline. In a series of three tests, Davis et al. (1981) found that embryos
of African clawed frogs were more tolerant than the larvae. The 96-hr LCSOs
for embryos and tailbud embryos were 550,000 and 940,000 pg/L, respectively,
compared to 150,000 pg/L for the larvae.
Genus Mean Acute Value* (GMAVs) are ranked from most sensitive to most
resistant for the nineteen freshwater genera tested (Table 3). The freshwater
Final Acute Value (FAV) of 56.97 pg/L was calculated using the GMAVs for the
four most sensitive genera, Ceriodaohnia. Daphnia. Duaesia. and Oncorhvnchus
which differ from one another within a factor of 251. The Final Acute Value
is 2.2 times less than the acute value for the most sensitive freshwater
species.
The acute toxicity of aniline to resident North American saltwater
animals has been determined with five species of invertebrates and three
species of fish (Thursby and Berry 1987a, 1987b; Redmond and Scott 1987;
Table 1). Grass shrimp, tested as larvae, was the most sensitive species
based on an acute value of 610 yg/L. Crustaceans comprised the three most
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9/2 2-7 9 3
sensitive species tested; acute values ranged from 610 to 16,600 ^g/L. Acute
values for three fishes, a mollusc and an echinoderm ranged from 17,400 to
>333,000 /jg/L. Mortalities in acute tests with mysids, grass shrimp,
sheepshead minnows and inland silversides increased during 96-hr tests. GMAVs
are ranked from the most sensitive to the most resistant (Table 3) for the
eight saltwater genera tested. The Final Acute Value for saltwater species is
153.4 /jg/L which is four times less than the acute value for the most
sensitive saltwater species tested.
Chronic Toxicitv to Aquatic Animals
The data that are available according to the Guidelines concerning the
chronic toxicity of aniline are presented in Table 2. Four chronic toxicity
tests exposing freshwater organisms to aniline have been reported. The
cladoceran, Ceriodaphnia dubia. was exposed to initial concentrations ranging
from 1.07 to 26.5 pg/L for seven days with daily renewed exposures (Spehar
1987). Survival was not significantly affected at any exposure concentration;
however, effects on young production were observed at 12.7 pg/L, but not at
8.1 M9/L. The chronic value, based upon reproductive impairment, is 10.1
A
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9/22/S3
EC50) used to compute an acute-chronic ratio was 170 pg/L (Gersich and Mayes,
1986). Division of this value by the chronic value of 33.9 /jg/L results in an
acute-chronic ratio of 5.015.
A 90-day early life-stage test was conducted with rainbow trout (Spehar
1987). The test was started with newly fertilized embryos. After 56 days
(swim-up stage), wet weight was significantly reduced at concentrations of
4,000 pig/L and above. After 90 days of exposure, an effect was not seen at
4,000 Aig/L but weight was reduced at 7,800 Aig/L. Survival was reduced at only
the highest exposure concentration (15,900 pg/L). The chronic value for
rainbow trout is 5,600 pg/L, based upon growth. Spehar (1987) also conducted
a 96-hr acute test which resulted in an acute value of 30,000 A/g/L. Division
of the acute value by the chronic value generates an acute-chronic ratio of
5.357.
The fathead minnow was exposed to aniline concentrations that ranged
from 316 to 2,110 nq/L in 32-day exposures (Russom 1993). Percentage normal
fry at hatch and survival at the end of the test did not differ significantly
from the control fish at any aniline concentrations. Growth (weight and
length) was significantly (p<0.05) reduced at aniline concentrations of 735
pg/L and greater, but not at 422 M9/L- Wet weight was reduced by 13.3% and
total length by 6.4% compared to control fish wet weight and total length at
735 M9/L- The chronic value for this test, based upon growth, is 557 ^g/L.
The companion acute test resulted in a 96-hr LC50 of 112,000 ^g/L (Geiger et
al. 1990). Division of this value by the chronic value results in an acute-
chronic ratio of 201.1.
The only chronic toxicity test with aniline and saltwater species was
conducted with the mysid, Mvsidopsis bahia (Thursby and Berry 1987b).
Ninety-five percent of the my•ids exposed during a life-cycle test to 2,400
pq/L died and no young were produced by the survivors. Reproduction of mysids
in 1,100 /jg/L was reduced 94 percent relative to controls. No significant
effects were detected on survival, growth, or reproduction in mysids exposed
to <540 pq/L tor 28 days. The chronic value for this species is 770.7
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based upon reproductive impairment. A comparison acute test was conducted
with the chronic test which resulted in an acute value of 1,930 jjg/L.
Division of this value by the chronic value results in an acute-chronic ratio
of 2.504.
The Final Acute-Chronic Ratio of 4.137 is the geometric mean of the
acute-chronic ratios of 4.356 for the freshwater cladoceran, Ceriodaphnia
dubia. 5.015 for the freshwater cladoceran, Daphnia maqna, 5.357 for the
rainbow trout, Oncorhvnchus mvkiss. and 2.504 for the saltwater mysid,
Mvsidopsis bahia (Table 2). The acute-chronic ratio of 201.1 for the fathead
minnow was not used in this calculation because, as described in the
Guidelines, this species is hot acutely sensitive to aniline and its Species
Mean Acute Value is not close to the Final Acute Value (Table 3). Division of
the freshwater Final Acute Value of 56.97 A/g/L by 4.137 results in a
freshwater Final Chronic Value of 13.77 pg/L. Division of the saltwater Final
Acute Value of 153.4 pq/L by 4.137 results in a saltwater Final Chronic Value
of 37.08 jjg/L. The freshwater Final Chronic Value is approximately 1.4 times
greater than the lowest freshwater chronic value of 10.1 pig/L for Ceriodaphnia
dubia. The saltwater Final Chronic Value is a factor of 21 times less than
the only saltwater chronic value of 770.7 pg/L.
Toxicitv to Aquatic Plants
Results of tests with two species of freshwater green alga exposed to
aniline are shown in Table 4. Sensitivity to aniline differed between the two
species. Four-day exposures with aniline and Selenastrum eapricornutum showed
that the ECSOs ranged from 1,000 ng/L (Adams et al. 1986) to 19,000 Aig/L
(Calamari et al. 1980, 1982) with reduced growth as the effect. Slooff (1982)
determined an BCSO of 20,000 ^g/L for an unidentified species of Selenastrum
with reduced biomass as the effect. The studies by Adams et al. (1986) were
conducted both with and without a carrier solvent (acetone). The lowest 96-hr
ECSOs were obtained from exposures using acetone. However, this relationship
was reversed when the exposure duration was increased to five and six days
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9/22/93
(Table 4). The green alga, Chlorella vuloaris. is considerably more tolerant
to aniline than Selenastrum. In 14-day exposures, growth of C. vulaaris was
reduced 58% by 306,000 ^ig/L and 16% by 184,000 pg/L (Ammann and Terry 1985).
The study also demonstrated that aniline had significant effects upon
respiration and photosynthesis of the species. There are no acceptable plant
data for saltwater species for aniline. A Final Plant Value, as defined in
the Guidelines, cannot be obtained for aniline.
Bioaccumulation
Studies to determine the bioconcentration of aniline with three species
of organisms have been reported (Table 5). In all these studies, steady-state
bioconcentrations were not demonstrated. Daphnia maona bioconcentrated
aniline five times in a 24-hr exposure (Dauble et al. 1984, 1986), a green
alga 91 times in a 24- to 25-hr exposure (Hardy et al. 1985) and rainbow trout
507 times in a 72-hr exposure (Dauble et al. 1984). Because tests were not of
sufficient duration according to the Guidelines, and no U.S. FDA action level
or other maximum acceptable concentration in tissue is available for aniline,
no Final Residue Value can be calculated.
Other Data
Other data available concerning aniline toxicity are presented in Table
5. Effects on two species of bacteria were seen at aniline concentrations
ranging from 30,000 to 130,000 yg/L.
Three genera of alga* were exposed to aniline. One species of bluegreen
algae, Microcvstis aeruoinosa. (Bringmann and Ruhn 1976, 1978a,b), showed more
sensitivity to aniline than other species. Inhibition of cell replication of
this specie* was observed after an 8-day exposure to 160 pg/L. Fitzgerald et
al. (1952) reported a 24-hr LC50 of 20,000 yg/L with the same species. A 66%
reduction of photosynthesis by the green algae, Selenastrum caoricornutum. was
reported by Giddinga (1979) after a 4-hr exposure to 100,000 yg/L of aniline.
Several species of protozoans were exposed to aniline. A 28-hr aniline
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exposure with Microreoma heterostoma showed that food ingestion was reduced at
20,000 pg/L .(Bringmann and Kuhn 1959a). Other species of protozoa were tested
and showed lass sensitivity to aniline (Table 5). .
The hydrazoan, Hydra oliaactis. showed sensitivity to aniline in a 48-hr
test. The LC50 for this species of 406 pg/L was determined by Slooff (1983)
in a static, unmeasured test using river water. Other organisms such as
planarians (Duoesia luoubrisl, tubificid worms (Tubificidaei, and snails
(Lvmnea staonalis) were also tested and had much higher 48-hr LCSOs of
155,000, 450,000 and 800,000 pg/L, respectively.
Cladocera appeared to be the group most sensitive to aniline. Spehar
(1987) reported a 48-hr LC50 of 132 pg/L for Ceriodaphnia dubia in an exposure
in which the organisms were fed their culturing ration. In the same study, a
LC50 of 44 pg/L was determined for unfed Ceriodaphnia dubia. The difference
in results could have been due to the complexation of aniline by the food
and/or increased hardiness of the fed organisms. Daphnia maana was affected
(acoustic reaction and mortality) at aniline concentrations ranging from 400
to 2,000 pg/L (Bringmann and Kuhn 1959a,b, 1960; Lakhnova 1975) for 48-hr
exposures. Calamari et al. (1980, 1982) found this species to be more
resistant to aniline with a reported 24-hr EC50 of 23,000 pg/L.
Insects showed varying sensitivities to aniline. Puzikova and Markin
(1975) exposed the midge, Chironomus dorsalis. to aniline through its complete
life cycle and reported 100% survival at 3,000 pg/L and 5% survival at 7,800
pg/L. Slooff (1983) exposed mayfly and mosquito larvae to aniline for 48 hr
and reported LCSOs of 220,000 and 155,000 pg/L, respectively.
The toxicity values for rainbow trout in Table 5 are in general
agreement with those used in Table 1. Rainbow trout were exposed to aniline
by several workers using different exposure durations. Shumway and Palensky
(1973) found 100% mortality of rainbow trout at 100,000 pg/L in a 48-hr
exposure and 100% survival at 10,000 pg/L. Lysak and Marcinek (1972) also
reported 100% mortality for a 24-hr exposure at 21,000 pg/L and observed no
mortality at 20,000 pg/L. Abrara and Sims (1982) determined the 7-day LC50 to
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9 / 2 : , 9 3
be 3,200 i^g/L in two separate testa using rainbow trout.
Several testa were run with aniline in dilution waters of different
water quality. Water hardness appeared to have little,, if any, impact on
aniline toxicity (Birge et al. 1979a,b). Young channel catfish, Ictalurus
punctatus. were exposed to aniline in waters with a four-fold difference in
hardness (53.3 and 197.5 mg/L as CaCO,) . The resulting LCSOs indicated only a
slight decrease in toxicity with increasing hardness. In a similar test they
also exposed goldfish and largemouth bass, Micropterus salmoides. and reported
the opposite effect on toxicity. pH does not appear to affect toxicity of
aniline with aquatic organisms (Table 5).
The African clawed frog demonstrated varied effects over a broad range
of concentrations of aniline. Davis et al. (1981) and Dumpert (1987) observed
that aniline concentrations of 50 and 70 Aig/L resulted in reduced epidermal
pigmentation or failure of larvae to develop normal pigmentation. In a
12-week exposure, Dumpert (1987) showed that 1,000 pg/L of aniline slowed
metamorphosis and reduced growth. At an exposure concentration of 10,000 yg/L
for 96-hr, 6% of the frog larvae developed abnormalities (Dumont et al.- 1979;
Davis et al. 1981). Frog embryos had 50% teratogeny in 120- and 96-hr
exposures at 91,000 and 370,000 pg/L, respectively (Table 5). One hundred
percent mortality of immature frogs occurred during a 12-day exposure to
90,000 pg/L (Dumpert 1987) and 50% mortality during a 48-hr exposure to
560,000 Atg/L (Slooff 1982; Slooff and Baerselman 1980).
Concentrations of the free amino acids aspartate, glutamate and al*n.-«
in the sea anemone, Bunodosoma cavernata. increased after seven days of
exposure to aniline at 500,000 pg/L (Kasschau et al. 1980; Table 5). T!-.«
lethal threshold (geometric mean of the highest concentration with no
mortality and the next higher concentration) was 29,400 pg/L for sand sr.ri.rp.
Cranqon septemspinosa. and >55,000 for soft-shelled clams, Mva arenaria
(McLeese et al. 1979).
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Unused Data
Some data on the effects of aniline on aquatic organisms were not used
because the studies were conducted with species that are not resident in North
America or Hawaii (Freitag et al. 1984; Hattori et al. 1984; Inel and Atalay
1981; Juhnke and Ludemann 1978; Lallier 1971; slooff and Baerselman 1980;
Tonogai et al. 1982; Yoshioka et al. 1986a). Chiou (1985b); Hermens et al.
(1985); Hodson (1985); Koch (1986); Newsome et al. (1984); Persson (1984);
Schultz and Moulton (1984); Slooff et al. (1983); Vighi and Calamari (1987)
compiled data from other sources. Results were not used where the test
procedures or test material were not adequately described (Buzzell et al.
1968; Canton and Adema 1978; Carlson and Caple 1977; Clayberg 1917; Demay and
Menzies 1982; Kuhn and Canton 1979; Kwasniewska and Kaiser 1984; Pawlaczyk-
Szpilowa et al. 1972; Sayk and Schmidt 1986; Shelford 1917; Wellens 1982).
Data were not used when aniline was part of a mixture (Giddings and Franco
1985; Lee et al. 1985; Winters et al. 1977) or when the organisms were exposed
to aniline in food (Lee et al. 1985; Loeb and Kelly 1963).
Babich and Borenfreund (1988), Batterton et al. (1978), Bols et al.
(1985); Buhler and Rasmusson (1968), Carter et al. (1984), Elmamlouk et al.
(1974), Elmamlouk and Gessner (1976), Fabacher (1982), Lindstrom-Seppa et al.
(1983), Maemura and Omura (1983), Pedersen et al. (1976), Sakai et al. (1933),
and Schwen and Mannering (1982) exposed only enzymes, excised or homogenized
tissue, or cell cultures. Anderson (1944), and Bringmann and Kuhn (1982)
cultured organisms in one water and conducted tests in another. Batterton et
al. (1978) conducted a study in which organisms were not tested in water but
were tested on agar in the "algal lawn" test.
Results of one laboratory test were not used because the test was
conducted in distilled or deionized water without addition of appropriate
salts (MuJcai 1977). Results of laboratory bioconcentration tests were not
used when the test was not flow-through or renewal (Freitag et al. 1985; Geyer
et al. 1981; Geyer et al. 1984) and BCF» obtained from microcosm or model
ecosystem studies were not used where th« concentration of aniline in water
10
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decreased with time (Lu and Metcalf 1975; Yount and Shannon 1987). Douglas et
al. (1986) had insufficient mortalities to calculate an LC50 and Sollmann
(1949) conducted studies without control exposures.
Summary
Data on the acute toxicity of aniline are available for nineteen species
of freshwater animals. Cladocera were the most acutely sensitive group
tested. Mean 48-hr ECSOs ranged frorn^ 125.8 pg/L for Ceriodaphnia dubia to 250
pg/L for Daphnia maqna. The planarian, Dugesia tiarina. was the fourth most
sensitive species to aniline with a 96-hr LC50 of 31,600 pg/L.
Freshwater fish 96-hr LCSOs ranged from 10,600 to 187,000 pg/L. Rainbow
trout, Oncorhvnchus mvkiss. were the most sensitive fish tested, with species
mean acute values of 26,130 A/g/L. The .bluegill, Lepomis macrochirus. was
nearly as sensitive to aniline as rainbow trout, with a 96-hr LC50 of 49,000
A/g/L reported for this species. The fathead minnow, Pimephales promelas. and
goldfish, Carassius auratus. were the most tolerant fish species exposed to
aniline, with species mean acute values of 106,000 ^g/L and 187,000 pg/L,
respectively.-
The most tolerant freshwater species tested with aniline was a midge,
Clinotanvpus pinouis. with a 48-hr LC50 of 477,000 pg/L. Developmental ttag««
of an amphibian, Xenooua laevis. had differing sensitivities to aniline. ?*•
embryos were the most tolerant with a 96-hr LC50 of 550,000 nq/L and the
larvae had a 96-hr LC50 of 150,000 fjg/L.
Data on the acute toxicity of aniline are available for eight specict of
saltwater animals. Species Mean Acute Values ranged from >333,000 pg/L for
larval winter flounder, Pseudooleuronectes americanus. to 610 pig/L for l*rv«.
grass shrimp, Palaemonetes puoio. Arthropods appear particularly sensitive to
aniline. There are no data to support the derivation of a salinity- or
temperature-dependent Final Acute Equation.
Chronic tests have been conducted with four species of freshwater
organisms. A chronic value of 10.1 pg/L for the cladoceran, Ceriodaphnia
11
-------
9/22/53
dubia. was based upon reproductive impairment. A chronic value of 33.9 pg/L
for another cladoceran, Daphnia maona. was also based on reproductive
impairment. Rainbow trout were exposed for 90 days to aniline and the results
showed that survival was reduced at 15,900 pg/L and growth (wet weight) at
7,800 pg/L. The chronic value for trout of 5,600 pg/L was based upon growth.
The fathead minnow was exposed for 32 days in an early life-stage test. The
chronic value of 557 pg/L was also based upon growth.
One saltwater chronic value was, found. A chronic value of 770.7 pg/L
for the mysid, Mvsidopsis bahia. was based upon reproductive impairment.
Effects due to aniline have been demonstrated with two freshwater plant
species. The green alga, Selenastrum caoricornutum. had ECSOs ranging from
1,000 to 19,000 pg/L in 4-day exposures. Another green alga, Chlorella
vulaaris. was considerably more resistant to aniline, showing a growth
reduction of 58% by 306,000 pg/L in a 14-day exposure. No acceptable
saltwater plant data have been found. Final Plant Values, as defined in -r.e
Guidelines, could not be obtained for aniline.
No suitable data have been found for determining the bioconcentraricn cf
aniline in freshwater or saltwater organisms.
Acute-chronic ratio data that are acceptable for deriving numerical
water quality criteria are available for three species of freshwater an!.-&*:•
and one species of saltwater animal. The acute-chronic ratios range from
2.504 to 5.357 with a geometric mean of 4.137.
The freshwater Final Acute Value for aniline is 56.97 pg/L and the F.-«.
Chronic Value is 13.77 pg/L. The Freshwater Final Chronic Value is 1.4 t .«••
greater than the lowest chronic value observed for one species of Cladoc«r«
indicating that sensitive species of this group may not be adequately
protected if ambient water concentrations exceed this value. The saltwater
Final Acute Value for aniline is 153.4 pg/L and the Final Chronic Value ;•
37.08 pg/L. Chronic adverse effects to the only saltwater species expo»«d *. a
aniline occurred at concentrations that are higher than the saltwater Firai
Chronic Value which should be protective of saltwater organisms.
12
-------
9/22/93
National Criteria
The procedures described in the "Guidelines for Deriving Numerical
National Water Quality Criteria for the Protection of Aquatic Organisms and
Their Uses" indicate that, except for certain sensitive species of Cladocera,
freshwater organisms and their uses should not be affected unacceptably if the
four-day average concentration of aniline does not exceed 14 pg/L more than
once every three years on the average and if the one-hour average
concentration does not exceed 28 ^g/L more than once every three years on the
average.
The procedures described in the "Guidelines for Deriving Numerical
National Water Quality Criteria for the Protection of Aquatic Organisms and
Their Uses" indicate that, except possibly where a locally important species
is very sensitive, saltwater organisms and their uses should not be affected
unacceptably if the four-day average concentration of aniline does not exceed
37 /jg/L more than once every three years on the average and if the one-hour
average concentration does not exceed 77 pg/L more than once every three years
on the average.
Implementation
As discussed in the Water Quality Standards Regulation (U.S. EPA 1983a)
and the Foreword to this document, a water quality criterion for aquatic life
has regulatory impact only after it has been adopted in a state water quality
standard. Such a standard specifies a criterion for a pollutant that is
consistent with a particular designated use. With the concurrence of the U.S.
EPA, states designate one or more uses for each body of water or segment
thereof and adopt criteria that are consistent with the use(s) (U.S. EPA
1983b, 1987). Water quality criteria adopted in state water quality standards
could have the same numerical values as criteria developed under Section 304,
of the Clean Water Act. However, in many situations states might want to
adjust water quality criteria developed under Section 304 to reflect local
environmental conditions and human exposure patterns. Alternatively, states
13
-------
may use different data and assumptions than EPA in deriving numeric criteria
that are scientifically defensible and protective of designated uses. State
water quality standards include both numeric and narrat-ive criteria. A state
may adopt a numeric criterion within its water quality standards and apply it
either state-wide to all waters designated for the use the criterion is
designed to protect or to a specific site. A state may use an indicator
parameter or the national criterion, supplemented with other relevant
information, to interpret its narrative criteria within its water quality
standards when developing NPDES effluent limitations under 40 CFR
122.44(d)(1)(vi).2
Site-specific criteria may include not only site-specific criterion
concentrations {U.S. EPA 1983b), but also site-specific, and possibly
pollutant-specific, durations of averaging periods and frequencies of allowed
excursions (U.S. EPA 1991). The averaging periods of "one hour" and "four
days" were selected by the U.S. EPA on the basis of data concerning how *
•rapidly some aquatic species react to increases in the concentrations of some
pollutants, and "three years" is the Agency's best scientific judgment of the
average amount of time aquatic ecosystems should be provided between
excursions (Stephan et al. 1985; U.S. EPA 1991). However, various species and
ecosystems react and recover at greatly differing rates. Therefore, if
adequate justification is provided, site-specific and/or pollutant-specific
concentrations, durations and frequencies may be higher or lower than those
given in national water quality criteria for aquatic life.
Use of criteria, which have been adopted in state water quality
standards, for developing water quality-based permit limits and for designing
waste treatment facilities requires selection of an appropriate wasteload
allocation model. Although dynamic models are preferred for the application
of these criteria (U.S. EPA 1991), limited data or other considerations might
require the use of a steady-state model (U.S. EPA 1986).
Guidance on mixing zones and the design of monitoring programs is
available (U.S. EPA 1987, 1991).
14
-------
Tul.le I Aculo Toxicily ol Anilino lu Aquatic Animals
Species
Plananan,
Dugasia tigrina
Annelid,
lumbriculua vahegattia
Snail (adult).
Aplexe hvpnofum
Snail.
Hatiaoma UivolviB
Cladoceran (< 24-hr),
Ceriodaphnia dubia
Cladoceran « 24-hr),
Ceriodaphnia dubia
Cladocaran «24-hrl.
Cariodaphnia dubia
Cladoceran « 24-hr),
Ceriodaphnia dubia
Cladoceran « 24-hr),
Ceriodaphnia dubia
Cladoceran « 24-hr),
Ceriodaphnia dubia
Cladoceran I < 24-hr),
Paphnia maona
Cladoceran ( < 24-hr),
Paphnia maona
Cladoceran (juvenile),
Daphnia magna
Cladoceran « 24-hr).
Method*
S.U
s.u
F.M
S.U
S.U
S.U
S.U
S.U
S.U
S.M
S.M
S.M
S.U
S.U
Chemical'' pH
FRESHWATER SPECIES
Reagent Grade 6.5-8.5
Reagent Grade 6.5-8.5
7.4
Reagent Grade 6.5-8.5
99.5% 7.4-7.9
99.5% 7.47.7
99.5% 7.4-7.9
99.5% 7.4-7.7
99.5% 7.58.0
99.5% 7.8
-
-
Reagent Grade 6.5-8.5
>99% 7.7-7.9
LC50
oc EC50
OJH/LI
31.600
> 100.000
> 219,000
100.OOO
119
193
146
184
146
44
150
530
210
170
Species Maun
Acme Valua
/ni/L Reference
.31.600 Ewell el al. 1986
> 100,000 Ewell et al. 1986
> 2 1 9.000 Holcombe et al. 1 987
100,000 Ewell ol al. 1986
Norberg-King 1987
Norberg-King 1987
\
Norberg-King 1987
Norberg-King 1987
Norberg-King 1987
125.8 Spehar 1987
Biosinger 1987
Biesinger 1987
Ewell et al. 1986
Gersich and Mayas 1 9
Paprmia mauna
-------
Table 1. (continued)
O\
Species
Cladocaran « 24-hr).
Daphnia maana
Isopod,
Asellut Infefpfiedius
Amphipod,
Gammaruf fasciatus
Midge (larva).
Chironomus jeptans
Midge (larva),
Clinotanvous pinauis
Midge (larva),
Einfeldia natchitocheae
Midge (larva),
Tanvpus neopunclipennis
Midge (3rd 4lh instar),
Tanvtarsus dissimilis
Rainbow trout (juvenile).
Oncorhvnchus mvkiss
Rainbow trout.
Oncorhvnchus mykiss
Rainbow trout,
Oncorhvnchus mvkiss
Rainbow trout,
Oncorhvnchus mvkiss
Rainbow trout (juvenile),
Oncorhvnchus mykiss
Rainbow trout,
Method* Chemical" pH
F.M - 7.4
S.U Reagent Grade 6.5-8.5
S.U Reagent Grade 6.5-8.5
S.U Reagent Grade 7.8
S.U Reagent Grade 7.8
S.U Reagent Grade 7.8
S.U Reagent Grade 7.8
F.M 7.4
F.M 7.1-7.7
S.M Analytical Grade
S.M Analytical Grade
F.M 7.68.2
F.M - 7.4
F.M 99.5% 7.8
LC50
or EC50
yyil/L)
250
> 100.000
> 100.000
399.900
477.900
427. 9OO
272.100
> 21 9.000
10.600
41,000
20.000
36.220
4O.500
3O.OOO
Species Mean
Acute Value
vaH- Reference
250.0 Holcombe et al. 1987
> 100, 000 E well el al. 1986
> 100,000 Franco el al. 1986
399.900 Franco et el. 1984
477.900 Franco et al. 1984
\
427.900 Franco el al. 1984
272.100 Franco et al. 1984
> 21 9. 000 Holcombe et al. 1987
Abram and Sims 1982
Calamari et al. 1980. 1982
Calamari et al. 1980, 1982
Hudson et al. 1984
Hulcumbe at al. 1987
26.13O Spehar 1987
Oncorhvnchus mykiss
-------
Table 1. (continued)
Species
Fathead minnow (juvenile),
Pimaphalai pfomelas
Fathead minnow (juvenilel,
Pimeohalef promolas
Fathead minnow (juvenile),
Pimaphalai promotes
Fathead minnow (juvenile),
Pimeohalee promalag
Goldfish (juvenile),
Carassius auratus
Bluegill (juvenile)
Leoomit macrochnut
While sucker ((uvenila),
Celattomus commersoni
African clawed frog
(embryo),
Xenopus laevis
African clawed frog
(tailbud embryo),
Xanoous laevis
African clawed frog (larva),
Xanopus laevis
Eastern oyster (embryos),
Crassostrea vifginica
Mysid (juvenile),-
Mvsidopsis batna
Method'
F.M
S.U
F,M
F.M
F.M
F.M
F.M
S.U
S.U
S.U
S.U
R.U
LC50
or EC 50
Chemical1' pH (vg/ll
99% 7.6 134.000
Reagent Grade 6.5-8.5 32,000
7.4 77.900
99% 7.5 114,000
7.4 187,000
7.4 49.000
7.4 78,400
550.000'
940.000'
150.000
SALTWATER SPECIES
100% 7.9-8.0 > 30.000
100% 7.4-7.5 1.090
Species Mean
Acute Value
nail. Reference
Brooke et at. 1984
Ewell et el. 1986
Holcombe et el. 1987;
Geiger el al. 1990
106,000 Geiger et al. 1990
187.000 Holcombe el al. 1987
49, 000 ' Holcombe el al. 1987
78.400 Holcombe et al. 1987
Davis at al. 1981
Davis et al. 1981
150.000 Davis et al. 1981
> 30.000 Thursby and Berry 1 98
Thursby and Bony 198
-------
Tablo 1. (continued)
CO
Spacing Method*
Myiid (juvenile). * F.M
Mvsidopsjfl bahia
Amphipod (juvenile), R.U
Ampelisca, abdila
Giant shrimp (larva), R.U
Palaemonetes ouoio
Saa uichin (embryo-larva), S,U
Arbacia punclulala
Sheepshead minnow R.U
(juvenile!.
Cypfinodon varieoalus
Inland silverside (juvenile), R.U
Me nidi a bervllina
Winter flounder (larva), S.U
Pseudopleuronectea
americanus
LC50 Species Mean
or EC50 Acute Value
Phgrnjcpf PH IttalU va/L Reterence
1% 7.5-7.6 1.930 1.930 Thuriby and Barry 1987b
1OO% 7.57.6 16.600 16.600 Redmond and Scott 1987
1OO% 7.9-8.0 610 61O Thuriby and Beny 1987a
100% 7.6-7.7 > 200.000 > 200.000 Thursby and Berry 1987a
100% 7.8-8.2 120.000 120,000 Thursby and Berry 1987a
100% 8.08.2 17.400 17.4OO Thursby and Berry 1987a
100% 7.98.1 > 3 30.000 > 3 30,000 Thursby and Berry 198 7a
• S " Static; R - Renewal; F » Flow-through; M « Measured; U •= Unmeasured.
* Purity ol the le»l chemical.
' Results Irom less sensitive Ufa stages ate not used in the calculation ol the Species Mean Acute Value.
-------
Table 2. Chronic Toxicily ol Anilina to Aquatic Animals
Spaciai
Cladocaran.
Cariodaphnia dubia
Cladocaran,
Daohnia maun*
Rainbow trout.
Oncofhvnchui mvfciia
Falhaad minnow.
Pimaphelaa promalas
Mywd.
MvmJooiii baNa
Chronic Limits Chronic Valua
Tail* Chemical* pH \»atl\* 0/n/H Rafarance
FRESHWATER SPECIES
LC 99.5% 7.8 8.1127 10.14 Spahar 1987
LC 99% 7.8-8.1 24.6-46.7 33.89 Gersich and Milaiio 1988
ELS 99.5% 7.8 4.000-7.800 5.600 Spahar 1987
ELS 99.5% 7.93 422-735 557 Russom 1993
SALTWATER SPECIES
LC 100% 7.47.6 5401.100 770.7 Thursby and Barry 19875
LC - liU-cycl* or partial hla-cycla; ELS - aarly lila-ataga.
1 Purity ol the last chamical. '
RasullB ara based on measured concentrations of anilina.
-------
Tabla 2. (continued)
Acute-Chronic Ralio
Spaciet
Rainbow trout.
Oncorhvnchug rnvfcia*
Cladocaran,
Daohnia manna
Cladocaran,
Cariodaphnia dubia
Mycid.
Mvsidopita bahia
r-j
O
Acula Valua Chronic Valua
JH uvn/l) Uvd/Ll
7.8 30.000 5.600
7.78.1 170 33.9
7.8 44 10.1
SALTWATER SPECIES
7.4-7.6 1.930 770.7
Ratio
5.357
5.015
4.356
2.504
-------
Table 3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic Ratios
3ank'
19
18
17
16
IS
14
13
12
11
10
9
8
7
•
Genus Mean
Acule Value
u/g/U
477.900
427.900
399.900
272.100
> 21 9,000
> 21 9.000
187,000
150.00
106.000
> 100.000
> 100.000
> 100.000
1OO.OOO
ft 4OO
Species
FRESHWATER SPECIES
Midge,
Clinolanypus pinpuis
Midge.
Einleldia natchitocheae
Midge,
Chironomua lentana
Midge.
Tanypus neopunclipennis
Midge,
Tanvtarsufl dissimillis
Snail.
Aplexa hvpnorum
Goldfish,
Carassius auratus
African clawed frog,
Xenopus laevis
Fathead minnow,
Pimephales promelas
Annelid.
lumbficulua variegalus
Amp hip od.
Gammarus fascialus
Isopod,
Asallus intermedius
Snail,
Helisoma ulvoluis
WUl« kuckei,
C^l.ibloiiiii^ t.iirnniersuni
Species Mean Species Mean
Acuta Valua Acute Chronic
Q/g/l)1" Ratio'-
477.900
427,900
399.900
272,100
> 21 9,000
> 21 9,000
187.000
150.000
106.000
> 100.000
> 100,000
> 100.000
1OO.OOO
78.400
-------
Table 3. (continued)
Rank*
5
4
3
2
1
KJ
K)
8
7
6
5
4
3
Genus Mean
Aculo Value
u/g/U
49,000
31.600
26.130
2SO
125.8
> 333.000
> 200,000
120.000
> 30.000
17.400
16.600
Species
Bluegill.
Lapomis macrochirus
Planarian,
Dugesia ligrina
Rainbow trout,
Oncofhvnchus mvkiss
Cladoceran,
Oaphnia magna
Cladocaran,
Ceriodaphnia dubia
SALTWATER SPECIES
Winter flounder,
Pseudopleuronectes
amertcanus
Sea urchin,
Arbacia punclulala
Sheepshead minnow,
Cyprinodon variagauis
Eastern oyster,
Crassoslrea virginica
Inland silverside,
Menidia bervllina
Amphipod.
Ampelisca abdita
Species Mean
Acute Value
(uallf
49.000
31.600
26.130
250.0
125.8
> 333,000
> 200,000
1 20.000
> 30.000
17.400
16,600
Species Mean
Acute-Chronic
Raiio'
5.357
5.015
4.356
\
-------
Table 3. (continued)
KJ
Ul
flank'
2
1
Genus Mean
Acute Value
uva/L)
1.930
610
Species
Mysid.
Mvsidopsis bahia
Grass shrimp,
Palaemonalaa puqig
Species Mean
Acule Value
(vallf
1.930
610
Species Mean
Acute-Chronic
Ratio'
2.504
* Ranked from most resistant to most sensitive based on Genus Mean Acute Value.
' From Table 1.
* From Table 2.
Fresh waler
Final Acute Value = 56.97 >/g/L
Criterion Maximum Concentration = 56.97 j/g/L / 2 = 28.49>yg/L
Final Acute-Chronic Ratio «= 4.137 (see text)
Final Chronic Value = 156.97 >/g/L> / 4.137 - 13.77/yg/L
Salt water
Final Acute Value = 153.4>/g/L
Criterion Maximum Concentration - <153.4pg/L) 12 = 76.7 pg/L
Final Acute-Chronic Ratio ° 4.137 (see text)
Final Chronic Value = (153.4/
-------
Table 4. Toxicity ol Aniline to Aquatic Plants
Species Chemical*
Graan algae. Analytical Grade
Selenaslrum
capricomulum
Graan algae.
Selenasuurn
capricornuium
Graan algae.
Selenaslrum
caorlcornulum
Graan algae,
SelenasUum
caoricornuium
Grean algae.
Selenaslrum
capricornuium
Green algae.
Selenaslrum
caoricornuium
Green algae,
Selenaslrum
caprjcornuium
Graan algae.
Selenaslrum
caoricornuium
Graan algae.
Selenastrum
capricornutum
Graan algae.
Selenastrum sp.
Green alga.
Chloiella vtilnarts
pH Duration
FRESHWATER SPECIES
4 days
7 days
7 days
4 days
4 days
5 days
S days
6 days
6 days
4 days
14 days
Ellecl
EC50
(growth)
No affect
(cell number)
No effect
(growth rule)
Incipient effect
(growth)
Incipient effect
(growth)
Incipient effect
(growth)
Incipient effect
(growth)
Incipient effect
(growth)
Incipient effect
(growth)
EC50
(biomass)
16% reduction
in growth
Result
Ivil/ll Ralerenco
19.000 Clamari at al.
1980. 1982
< 5.000 Adams el al. 1986
10.0OO Adams al el. 1986
3.000 Adams el al. 1986
1.000* Adams el al. 1986
\
3.OOO Adams el al. 1986
5.000* Adams al al. 1986
3.00O Adams el al. 1986
5.000* Adams el al. 1986
20.000 Stool 1982
.184.000 Animann arid Terry
13«b
-------
Tabla 4. (continued)
Species Chemical*
Green alga.
Chloralla vuloarls
Green alga.
Chlorella vulgaris
Green alga,
Chloralla vuloaris
pH Duration
14 days
14 days
14 days
EUect
58% reduction
in growth
66% reduction
in growth
75% reduction
in growth
Result
(ua/L\ Reterence
306.OOO Ammann and
1985
613. 200 Ammann and
1985
817.000 Ammann and
1985
Terry
Terry
Terry
SALTWATER SPECIES
No acceptable loxicity data
for saltwater plants
* Purity of the last chemical.
' Acetone carrier used.
N>
in
-------
Table 5. Oihai Data on the Effects ol Aniline on Aquatic Organisms
Species
Chemical*
Duration
Concentration
ll/t) ReleiencB
K)
Bacterium.
Pseudomonas pulida
Bacterium,
Spirillum volutani
Blue- green alga.
Microcvslit
aeruoinosa
Blue-green alga.
Microcvstis
aeruoinosa
Green algae,
Scenedesmus
quadficauda
Green algae.
Scenedasmut
quadficauda
Green alga.
Scenedesmus
quadficauda
Green algae, Reagent Grade
Selenaslrum
capricornulum
Protozoan,
Chilomonas
paramaecium
Protozoan.
Entosiphon
sulcalum
FRESHWATER SPECIES
7.0 16 hr Incipient inhibition
6.8 1 hr Inhibition of
motilily
24 hr 50% mortality
8 days Incipient inhibition
7.5 4 days Incipient inhibition
8 days Incipient inhibition
24-25 hr BCF = 91
4 hr 66% reduction in
photosynthesis
48 hr Incipient inhibition
6.9 72 hr Incipient inhibition
130.000 Bringmann 1973;
Btingniann and
Kuhn 1976.
1977b. 1980b
30.000 Bowdre end Kfieg
1974
20.OOO Fitzgerald el al.
1952
1 60 Bringmann and
Kuhn 1976.
1978a.b
\
10.000 Bringmann and
Kuhn 1959a,b
8,300 Bringmann and
Kuhn 1977b.
1978a.b. 1980b
Hardy at al. 1985
100,000 Giddings 1979
250,000 Bringmann el al.
1980; Bringmann
and Kuhn 1981
24.OOO Bringmann 1978;
Biingmann and
Kuhn I980U. 1981
-------
Table 5. (continued)
Species Chemical* pH
Protozoan, - 7.5-7.8
Microreama
heterosloma
Protozoan, - 6.3
Tetrahvmena
pvriformis
Protozoan. - 6.9
Uronome oarduczi
Hydrozoan. >98%
Hvdra oliaactis
Planarian, >98%
Ouaesia luaubris
Tubilicid worm. >98%
Tubificidaa
Sn«4. >98%
Lvmnooe staanalia
Cladoceran. 99.5% 7.8
Ceriodaphnia dubia
Cladoceran, - 7.5
Daphnia manna
Cladoceran. - 7.6-7.7
Daphnia maana
Cladoceran. Pure Analytical 7.4
Daphnia maana Grade
Cladoceran,
Daohnia maana
Cladoceran.
Daphnia maana
Cladoceran.
Daphnia mauna
Duration
28 hr
72 hr
20 hr
48 hr
48 hr
48 hr
48 hr
48 hr
48 hr
24 hr
24 hr
24 hr
10 hr
12 hr
Effect
Incipient inhibition
EC50
(growth)
Incipient inhibition
LC50
LC50
LC50
LC50
EC50 (fed)
EC50
(acoustic reaction)
EC50
(immobility)
EC50
BCF = 5.0
LT50
LT50
Concentration
(j/g/t-i
20.000
154.270
91.000
406.000
1 55.000
450.000
800.000
132
400
50O
23.000
10.000
8.OOO
Reference
Bringmann and
Kulin 1959a
Schultz and Allison
1979
Bringmann and
Kuhn 1980a. 1981
Slooff 1983
Slooff 1983
Sloolf 1983
Sloofl 1982. 1983
Speher 1987
Bringmann and
Kuhn 1959a.b
1960
Bringmann and
Kuhn 1977a
Clamari et al.
1980. 1982
Dauble et al.
1984, 1986
Lakhnova 1975
Lakhnova 1975
-------
Table 5. (continued)
Concentration
rv>
00
Special
Cladoceran,
Paphnia mauna
Cladoceran,
Daphnia maona
Cladocaran.
Daohnia maana
Cladocaran,
Daphnia, manna
Cladocaran,
Paphnia magna
Cladoceran.
Daphnia maona
Cladoceran (adult).
Moina macrocopa
Midge.
Chironomus dorsalis
Midga,
Chironomua dorsalia
Midga.
Chifonomus dorsalis
Mayfly (larva).
Cloeon dipierum
Mosquito (3rd
instar),
Aedes aeovpti
Rainbow troul
(juvenile),
Oncornvnchus
mvkiss
Chemical'
99%
99%
Analytical Grada
>98%
>98%
7.4
Duration
1 .0 day
1 .5 days
2.0 days
3.5 days
14 days
14 days
3hr
20-21 days
20-21 days
20 21 days
48 hr
48 hr
7 days
Eltacl
LTSO
LTSO
LT50
LTSO
MATC
• MATC
LCSO
95% Mortality
30% Mortality
0% Mortality
LCSO
LCSO
LCSO
(vu/L)
6.000
4,000
2.000
1.000
29.9
14.9
1 .OOO.OOO
7.800
7.000
3.000
220.000
155.000
a. 200
Reterence
Lakhnova 1875
Lakhnova 1975
Lakhnova 1975
Lakhnova 1975
Gersich and
Miluuo 1990
Garsich and
Milazjo 1990
Yoshioka el al.
1986b
Puzikova and
Markin 1975
Puiikova and
Markin 1975
Pu/ikova and
Markin 1975
Slooll 1983
Slooll 1982
Abrant and Sims
1982
-------
Table 6. (continued)
•£>
Species Chemical*
Rainbow trout
(juvenile),
Oncorhvnchus
mvkiss
Rainbow trout
(juvenile),
Oncorhvnchus
mvkist
Rainbow trout
(2 yr).
Oncorhvnchus
mvkisg
Rainbow trout
(2 yr).
Oncofhynchus
mvkmt
Rainbow trout.
Onctxhvocitui
mvkist
Rainbow trout.
Oncorhvnchus
mvkiss
Guppy. 99%
Poecilia reticulate
Fathead minnow >98%
•3-4 wk).
Pimephales
promelas
Channel cattish
(embryo, larva).
Ictalums punctalus
Chaonal c*lli»lt
(••Ifelyu k«.*l
1. !«•...,,. tna* !Ul!»
pH Duration
7.4 7 days
7.4 72 hr
24 hr
24 hr
7.0-8.0 48 hr
7.0 8.0 48 hr
14 days
48 hr
7.7 To hatch
(4.5 days)
11 85 days
(4 Jay:» pubT
hutch)
Concuiilralion
Ellact U7Q/L)
LC50 8,200
BCF=507
No mortality 10.000-20.000
LCI 00 21.000
V
No impairment of 10,000
flavor
100% mortality 100.000
LC50 125.629
LC50 65.000
LC50 5.600
(5.500)'
LC50 5.000
(5.000)'
Relarence
Abram and Sims
1982
Daubla at al. 1984
Lysak and
Marcinek 1972
Lysak and
Maicinek 1972
Shumwey and
Palensky 1973
Shumway and
Palensky 1973
Hermens at al. .
1984
Slooff 1982
Birge at al. 1979b
Birga al al. 1979b
-------
Table S. (continued)
Concentration
Species Chemical*
Channel catfish
(embryo, larva).
Ictalurus minctalus
Channel catfish
(embryo, larva).
Ictalurut Dunctatug
Goldfish
(embryo, larva).
Carasiius auratus
Goldfish (embryo.
larva).
Carassius auratus
Goldfish
(•mbryo. larval.
Carastius autalut
Goldfish
lembiyo. larva).
Caiasstus auiaius
Goldfish
(embryo, larva),
Carassius auratua
Goldfish
(embryo, larva).
Carassius auratus
Largemouth bass
(embryo, larva).
Microoterus
salmoides
Largemouth bass
(embryo, larva),
Miciupleitis
salmuides
gy Duration Effect
7.7 To hatch LC50
(4.5 days)
7.7 8.5 days LC50
(4 days post-
hatch)
7.7 To hatch LC50
(3.5 days)
7.7 7.5 days LC50
(4 days post-
hatch)
7.7 11. 5 days LC5O
(4 days post-
hatch)
7.7 To hatch LC50
(3.5 days)
7.7 7.5 days LC50
(4 days post-
hatch)
7.7 11. 5 days LC50
(8 days post-
hatch)
7.7 To hatch LC50
(2.5-3.5 days) ~
7.7 6.5 7.5 days LC50
(4 days post-
hutch)
If/fl/M
7.400
(6.300)'
7,000
(6.200)*
10.2OO
(9.3001*
5.600
(5,500)'
5.500
10.000
(7.600)'
4.800
(4.600)'
4.700
47,300
(32.700)*
10.500
(7,100)*
Reference
Birge et al. 19796
Birge et al. 1979b
Birge el al. 1979b
Birge al al. 1979b
Birge el al. 1979b
Birga el al. 1979b
Birge et al. 1979b
Birge et al. 1979b
Birge et al. 1979b
Birga el al. 19796
-------
Table 5. (continued)
Concentration
Spacias Chemical*
Largemoulh bast
(embryo, larva).
Microplerus
salmoides
Largemouth bass
(embryo, larva).
Micropterus
salmoides
Lergemouth bass
(embryo, larva).
Micropterut
•almoides
Largemouth bass
(embryo, larval.
Micropterus
salmoides
African clawed (rog
(embryo).
Xenoous laavis
Alrican clawed frog
(embryo).
Xanoous laevis
Alrican clawed Irog
(larva),
Xenoous laevis
Alrican clawed Irog
(tadpole).
Xenopus laevis
Alrican clawed Irog
(embryo).
Xenopus laevis
African clawed Irug tUX
13 4 *hl.
XeiMAjuft la*vta
pH Duration
7.7 10.5-11.5 days
(8 days post-
hatch)
7.7 To hatch
(2.5-3.5 days)
7.7 6.5-7.5 days
(4 day post-hatch)
7.7 10.5-1 1.5 days
(8 days post-
hatch)
96 hr
120 hr
96 hr
1 2 days
12 weeks
,
LCSO
Ellect
LCSO
LCSO
LC50
LCSO
.
EC50
(teratogeny)
EC50
(teralogeny)
6% abnormalities
100% mortality
Slowed
metamorphosis.
reduced growth
560,000
(PQ/LI
5.200
43.200
(29.9001'
8.4OO
(7.100)'
4,400
\
370.000
91.000
10,000
90.00O
1.000
Reference
Birge el al. 19796
Biryo el al. 1979b
Birge el al. 1979b
Birge el al. 19796
Davis el al. 1981
Davis el al. 1981
Dumont et al.
1979.
Davis el al. 1981
Dumper! 1987
Dumpert 1987
Slooff 1982,
Slooll and
Bt»«f selman 1980
-------
Table 5. (continued)
Chemical*
Duration
SALTWATER SPECIES
Effect
Concentration
(j/a/U
Reference
Sea anemone.
Bunodosoma
cavernala
Sand shrimp
(adult).
Crangon
seplemspinosa
7 days Significant
increase in
concentration ol
Iree asparlale,
glutamute, ulanine
96 hr Lethal threshold
500,000 Kasschuu el
1980
29.400 McLeese et
1979
<
al.
al.
• Purity of the test chemical.
b Data in parenthesis are from Birge et al. 1979a.
-------
9/22/93
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