Q 822R93024
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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 RESEA=:H AND DEVELOPMENT
ENVIRONMENTAL RESEARCH LABORATORIES
DULUTH, MINNESOTA
NARRAGANSETT. =HC:E ISLAND
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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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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 thrcugr.
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 tne
states and Indian tribes in modifying the criteria presented in this dcc-r-e-t
are contained in the Water Quality Standards Handbook (December 1983). 7U..3
handbook and additional guidance on the development of water quality sta-^ir-s
and other water-related programs of this Agency have been developed by •-»
Office of Water.
This document, if finalized, would be guidance only. It would r.ct
establish or affect legal rights or obligations. It would not estabiu- t
binding norm and would not be finally determinative of the issues addr««§«:
Agency decisions in any particular situation will be made by applying *.*•
Clean Water Act and EPA regulations on the basis of specific facts pr*«« -•:
and scientific information then available.
Tudor T. Davies
Director
Office of Science and Technology
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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
, V
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CONTENTS
Page
Notices
11
Foreword
111
Acknowledgments
Tables
VI
Introduction ,
Acute toxicity to Aquatic Animals
Chronic Toxicity to Aquatic Animals 4
Toxicity to Aquatic Plants 6
Bioaccumulation -,
Other Data
Unused Data . 3
Summary Jj_
National Criteria I3
Implementation ^3
References
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TABLES
Page
1. Acute Toxicity of Aniline to Aquatic Animals 15
2. Chronic Toxicity of Aniline to Aquatic Animals 19
3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic
Ratios 2 *
4. Toxicity of Aniline to Aquatic Plants 24
5. Other Data on Effects of Aniline on Aquatic Organisms 26
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Introduction
Aniline (aminobenzene, benzenamine, phenylamina) is the simplest of the
aromatic amines (CjHjNH,). It occurs naturally in coal-tars (Shelford 1917)
and is manufactured by the catalytic reduction of nitrobenzene, amination of
chlorobenzene and ammonolysis 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 ^g/L (Verschueren 197-,..
The log,0 of the octanol-water partition coefficient for aniline is 0.9C cr-..3u
1985a) . Through direct disposal, such as industrial discharges and ncn-pc..-.t
sources associated with agricultural uses, it enters the aquatic envj.rcr.mer.' .
It is removed from the aquatic environment by several mechanisms. The -« -t
pathway of removal from water is by microbial decomposition (Lyons et i.
1984, 1985). Several minor pathways have been identified including
evaporation, binding to humic substances and autoxidation.
Additions to the aniline molecule of certain functional group* -••• -••«-
found to increase toxicity (Brooke et al. 1984; Geiger et al. 1986, H«
Tests with th« fathead minnow tPimeohales promelasl have demonstrated •-«-.
substitutions with halogens, (chlorine, fluorine, and bromine) incre«««i
toxicity. The addition of alkyl groups also increased toxicity; the •....-.,
increases in proportion to the increase in chain length. Twenty-four
substitutions were tested and all except aiJ^ additions of methyl and -.-..--
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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-specifi=
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 tr-.e
response to public comment (U.S. EPA 1985), is necessary to understand t.-.e
following text, tables, and calculations. The latest comprehensive literature
search for information for this document was conducted in September :??:.• s^r.e
more recent information is included.
Acute toxicitv to Aquatic Animals
The data that are available according to the Guidelines concer-. , -.-«
acute toxicity of aniline are presented in Table 1. Cladocera were -.-. -•:
sensitive group of the 19 species tested. Several species of larva. -.:;••
and embryos and larvae of the clawed toad, Xenopus laevis, were the - ••
resistant to aniline in acute exposures. Fish tended to be in the -. . •
of sensitivity for aquatic organisms.
Forty-eight-hour ECSOs for the cladocerans Cerj,odaphnia dub;4 .
Daohnia maana were 44 pg/L and 530 ^g/L, respectively. Several inse,. •
exposure* conducted with both species showed consistency among the ••• •
(Table 1). However, there appears to be a large increase in tolerate
aniline between cladocerans and other aquatic species. The 96-hr .: «
next most sensitive species, a planar ran, pugesja. tiqrina, was 31,3-. - ,
Ninety-six-hour LCSOs for fish ranged from 10,600 to 187,000 ..
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rainbow trout (Oncorhvncua mvkiss ) was the most sensitive species of fish
tested, with 96-hr LCSOs ranging from 10,&00 to 41,000 ^g/L. The bluegill
(Leoomis macrochirusl was slightly more tolerant of aniline with a 96-hr LC50
of 49,000 /jg/L. Fathead minnows, Pimeohales promelas. and goldfish, Carassius
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 pig/L. A 96-hr LCSO for the goldfish was 187,000 ng/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, Clinotanvpus pinauis. was the moat tolerant of the four species tested;
a 48-hr LCSO of 477,900 /jg/L was calculated for this species. LCSOs for other
midge species tested by Franco et al. (1984), ranged downward to 272,100 ^ig/L.
Holcombe et al. (1987) tested another species of midge (Tanvtarsus dissirnilisi
and reported a 48-hr LCSO >219,000 jjg/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 ^g/L for the larvae.
Genus Mean Acute Value* (GMAVs) are ranked from most sensitive to -nca-
resistant for the nineteen freshwater genera tested (Table 3). The fr«»r.w«t«r
Final Acute Value (FAV) of 56.97 ^ig/L was calculated using the GMAVs rcr --•
four most sensitive genera, ceriodaphnia. Daphnia. Duoesia. and Oncorr.,r.:r.~*
which differ from one another within a factor of 251. The Final Acute .*.-•
is 2.2 time* less than the acute value for the most sensitive freshwater
species.
Th« acute toxicity of aniline to resident North American saltwater
animals has been determined with five species of invertebrates and three
species of fi«h (Thursby and Berry 1987a, 1987b; Redmond and Scott 198'.
Table 1). Grass shrimp, tested as larvae, was the most sensitive spec.««
based on an acute value of 610 pg/L. Crustaceans comprised the three T.C«-
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sensitive species tested; acute values ranged from 610 to 16,600 pg/L. Acute
values for three fishes, a mollusc and an echinoderm ranged from 17,400 to
>333,000 pq/l. Mortalities in acute tests with mysids, grass shrimp,
sheepshead minnows and inland silversides increased during 96-hr tests. GMAVa
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 jjg/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, cerlodaphnia 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 Mg/L, but net at
8.1 /ig/L. The chronic value, based upon reproductive impairment, is 1C.:
pg/L. This number may be under-protective since it is based upon initial
measured concentrations of aniline and did not take into considerate -..-.at
the study showed nearly 100% loss of aniline from solution in 24 hr. A
companion acute test was conducted with the chronic study and results .-. i
48-hr ECSO of 44 M/L. Division of this value by the chronic value ;.-«r,-.es
an acute-chronic ratio of 4.356 for CPr;odaphnia dubia.
EaEbnia masna ware exposed -.= aniline for 21 days in a renewal -•«
(Gersich and Milazzo 1988). Mean concentrations for the exposures ra-;.: '. : ~
12.7 to 168.6 yg/L *or the five concentrations tested. Mean total
young/surviving adult and mean breed aize/aurviving adult were not
significantly different from the control organisms at 24.6 M/L but w.r.
significantly different at 46.7 Mg/L. 3as.d upon these two reproduce.,,
endpoints, the chronic value is 33.9 -;,-. The companion acute value ;£-.-
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ECHO) used to compute an acute-chronic ratio was 170 M
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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 ^g/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 maana. 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 not 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 yq/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 Aig/L by 4.137 results in a saltwater Final Chronic Value
of 37.08 fjg/L. The freshwater Final Chronic Value is approximately 1.4 times
greater than the lowest freshwater chronic value of 10.1 pg/L for Cericdasr.r. ia
dubia. The saltwater Final Chronic Value is a factor of 21 times less -r.a.-.
the only saltwater chronic value of 770.7 pg/L.
Toxicitv to Aouatic Plants
Results of tests with two species of freshwater green alga expo* : - :
aniline are shown in Table 4. Sensitivity to aniline differed between -. • • •-:
species. Four-day exposures with aniline and Selenastrum caoricornut ._- •• -•:
that the ECSOs ranged from 1,000 yg/L (Adams et al. 1986) to 19,000 *q .
(Calamari et al. 1980, 1982) with reduced growth as the effect. Sloof! . •-.
determined an ECSO of 20,000 pg/L for an unidentified species of Selern-.; .-
with reduced biomass as the effect. The studies by Adams et al. (1986 -«:•
conducted both with and without a carrier solvent (acetone). The lowest »•>--.-
ECSOs were obtained from exposures using acetone. However, this relat .cn«- .p
was reversed when the exposure duration was increased to five and six 3*.t
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(Table 4). The green alga, Chlorella vulgaris. is considerably more tolerant.
to aniline than Selenastrum. In 14-day exposures, growth of C. vulaaris was
reduced 58% by 306,000 M9/L and 1S* by 184,000 Aig/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.
Bioaceumulation
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. Daohnia maana 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 .n 74=.•
5. Effects on two species of bacteria were seen at aniline concentr••..:-•
ranging from 30,000 to 130,000 wg/L.
Three genera of algae were exposed to aniline. One species of &..••;.'••-
algae, Microevstis aeruoinosa. (Bringmann and Kuhn 1976, 1978a,b), snc«««a «cr«
sensitivity to aniline than other species. Inhibition of cell replies.;' :?
this species was observed after an 8-day exposure to 160 ^g/L. Fitxger«.a •-.
al. (1952) reported a 24-hr LC50 of 20.000 M9/L with the same species * **%
reduction of photo.ynthe.is by the green algae, Se;epast;ru^ Capricorn*;••• -••
reported by Gidding* (1979) after a 4-hr exposure to 100,000 ng/l of aru..-e
Several species of protozoans were exposed to aniline. A 28-hr *n...-«
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exposure with Hicroreoma heterostoma showed that food ingestion was reduced at
20,000 M9/L (Bringmann and Kuhn 1959a). Other species of protozoa were tested
and showed lass sensitivity to aniline (Table 5).
The hydrazoan, Hvdra oliaactis, showed sensitivity to aniline in a 48-hr
test. The LCSO for this species of 406 ^g/L was determined by Slooff (1983)
in a static, unmeasured test using river water. Other organisms such as
planariana fDuaesia luoubrisl. tubificid worms (Tubif i.cidae) , and snails
fLvmnea ataonalis) 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 LCSO of 132 pg/L for Ceri,odaphnia dubia in an exposure
in which the organisms were fed their culturing ration. In the same study, a
LCSO of 44 pg/L was determined for unfed Ceri.odaphnta duJDia.. The difference
in resultB could have been due to the complexation of aniline by the food
and/or increased hardiness of the fed organisms, paphn^a maana was affected
(acoustic reaction and mortality) at aniline concentrations ranging frcm AGO
to 2,000 Mg/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 Mar*..-.
(1975) exposed the midge, chironomus d2£sali2, to aniline through its :=.-?.e-.e
life cycle and reported 100% survival at 3,000 Mg/L and 5% survival a-. V*::
ttg/L. Slooff (1983) exposed mayfly and mosquito larvae to aniline f=r 43 -r
and reported LCSOs of 220,000 and 155,000 pg/L, respectively.
The toxicity values for rainbow trout in Table 5 are in genera.
agreement with those used in Tabl. 1. Rainbow trout were exposed « .-...-•
by several workers using different .xpcsure durations. Shumway and ?...-.*..
(1973) found 100% mortality of rainbow trout at 100,000 *g/L in a 48-.r
exposure and 100% survival at 10,000 ug/L. Lysak and Marcinek (1972, *..=
reported 100% mortality for a 24-hr «po.ur. at 21,000 Mg/L and observe ,o
mortality at 20,000 pg/L. Abram and SUns (1982) determined the 7-day i.".: - -
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be 8,200 pg/L in two separate tests using rainbow trout.
Several tests 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, Ictaiurus
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, Microoterus 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 ^9/L resulted in reduced epiderrr.a..
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,CCO -g/_
for 96-hr, 6% of the frog larvae developed abnormalities (Dumont et al. 19*?;
Davis et al. 1981). Frog embryos had 50% teratogeny in 120- and 96-hr
exposures at 91,000 and 370,000 ^g/L, respectively (Table 5). One hur.sr*:
percent mortality of immature frogs occurred during a 12-day exposure -. :
90,000 pg/L (Dumpert 1987) and 50* mortality during a 48-hr exposure ::
560,000 yg/L (Slooff 1982; Slooff and Baerselman 1980).
Concentrations of the free anuno acids aspartate, glutamate and • * •
in the sea anemone, Bunodosoma cavernata. increased after seven days ;f
exposure to aniline at 500,000 ^g/L (Kasschau et al. 1980; Table 5). * •
lethal threshold (geometric mean of tr.e highest concentration with nc
mortality and tha next higher concentration) was 29,400 pig/L for sand t
Cranoon septemspinosa. and >55,000 fcr aoft-shelled clams, Mva arenar^a
(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 (19S5b); 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 (1937)
compiled data from other sources. Results were not used where the test
procedures or test material were not adequately described (Buzzell et ai.
1968; Canton and Adema 1978; Carlson and Caple 1977; Clayberg 1917; Demay ar.d
Menzies 1982; Kuhn and Canton 1979; Kwasniewska and Kaiser 1984; PawlaczyX-
Szpilowa et al. 1972; Sayk and Schmidt 1986; Shelford 1917; Wellens 1932 •.
Data were not used when aniline was part of a mixture (Giddings and Frar.ra
1985; Lee et al. 1985; Winters et al. 1977) or when the organisms were exccsefa
to aniline in food (Lee et al. 1985; Loeb and Kelly 1963).
Babich and Borenfreund (1988), Batterton et al. (1978), Bols et a.
(1985); Buhler and Rasmusson (1968), Carter et al. (1984), Elmamlouk et i.
(1974), Elmamlouk and Gessner (1976), Fabacher (1982), Lindstrom-Seppa «• .
(1983), Maemura and Omura (1983), Pedersen et al. (1976), Sakai et ai.
and Schwen and Mannering (1982) exposed only enzymes, excised or homc^« •
tissue, or cell cultures. Anderson (1944), and Bringmann and Kuhn ( 1 ~? - .
cultured organisms in one water and conducted tests in another. Batr«:
al. (1978) conducted a study in which organisms were not tested in wa-.•
were tested on agar in the "algal lawn' test.
Results of one laboratory t««t -«r« not used because the test -««
conducted in distilled or deioniz«d w*t«r without addition of appropr.» •
salts (Mukai 1977). Results of laocratory bioconcentration tests wer«
used when the test was not flow-througn or renewal (Freitag et al. 193l • •
et al. 1981; Geyer et al. 1984) and BCf« sotained from microcosm or me :•
ecosystem studies were not used wh«r« •-.-.• rsncentration of aniline in - • «
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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 from 125.8 pg/L for Ceriodanhnia dubia to 250
/jg/L for Daphnia maqna. The planarian, Duqesia tiqrina, 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. Rair.bcw
trout, Oncorhvnchus mvkiss. were the most sensitive fish tested, with species
mean acute values of 26,130 pg/L. The bluegill, Lepomis macrochirus. was
nearly as sensitive to aniline as rainbow trout, with a 96-hr LC50 of 49,300
Aig/L reported for this species. The fathead minnow, Pimeohales promelas. and
goldfish, Carassius auratus. were the most tolerant fish species exposed -o
aniline, with species mean acute values of 106,000 ^ig/L and 187,000 pg/L,
respectively.
The most tolerant freshwater species tested with aniline was a mii-«,
Clinotanvpus pinauis, with a 48-hr LC50 of 477,000 ng/L. Developmental «*>^«s
of an amphibian, Xenopus laevis, had differing sensitivities to anilir* '-«
embryos were the most tolerant with a 96-hr LCSO of 550,000 ng/l* and --•
larvae had a 96-hr LCSO of 150,000 ng/L.
Data on the acute toxicity of aniline are available for eight sp« •«
saltwater animals. Species Mean Acute Values ranged from >333,000 ^g,- ' -
larval winter flounder, Pseudopleuronectea americanus. to 610 Aig/L for • •.
grass shrimp, Palaemonetes puaio. Arthropods appear particularly sent.- • •
aniline. There are no data to support the derivation of a salinity- cr
temperature-dependent Final Acute Equation.
Chronic tests have been conducted with four species of freshwater
organisms. A chronic value of 10.1 yg/L for the cladoceran, Ceriodaphr^j
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dubia, was based upon reproductive impairment. A chronic value of 33.9 ^g/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 ^g/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 ^g/L was also based upon growth.
One saltwater chronic value was found. A chronic value of 770.7 Hg/-
for the mysid, Mvsidopsis bahia, was based upon reproductive impairment.
Effects due to aniline have been demonstrated with two freshwater plar.-
species. The green alga, Selenastrum caoricornutum, had ECSOs ranging frc~
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 ^ig/L in a 14-day exposure. No acceptable
saltwater plant data have been found. Final Plant Values, as defined ..-. v.e
Guidelines, could not be obtained for aniline.
No suitable data have been found for determining the bioconcentrat .:-. ::'
aniline in freshwater or saltwater organisms.
Acute-chronic ratio data that are acceptable for deriving numeriri.
water quality criteria are available for three species of freshwater a-.-*.«
and one species of saltwater animal. The acute-chronic ratios range '.: -
2.504 to 5.357 with a geometric mean of 4.137.
The freshwater Final Acute Value for aniline is 56.97 ^g/L and • . .
Chronic Value is 13.77 /jg/L. The Freshwater Final Chronic Value is 1 • ••
greater than the lowest chronic value observed for one species of CiaJ • •
indicating that sensitive species of this group may not be adequately
protected if ambient water concentrations exceed this value. The sa.--« •
Final Acute Value for aniline is 153.4 pg/L and the Final Chronic Va..« •
37.08 pg/L. Chronic adverse effects to the only saltwater species ex; .•
aniline occurred at concentrations that are higher than the saltwater ' •
Chronic Value which should be protective of saltwater organisms.
12
-------
-RATT
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 pig/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 ^g/L more than once every three years on the average and if the one-hour '
average concentration does not exceed 77 ^g/L more than once every three years
on the average.
Implementation
A3 discussed in the Water Quality Standards Regulation (U.S. EPA :?=:a
and the Foreword to this document, a water quality criterion for aquatic ..'.«
has regulatory impact only after it has been adopted in a state water q_*..-
standard. Such a standard specifies a criterion for a pollutant that .»
consistent with a particular designated use. With the concurrence of •-• ;
EPA, states designate one or more uses for each body of water or segmert
thereof and adopt criteria that are consistent with the use(s) (U.S. EPA
1983b, 1987). Water quality criteria adopted in state water quality st«--«r:«
could hav« the same numerical values at criteria developed under Secticr. ;;4,
of the Clean Water Act. However, in many situations states might want •.;
adjust water quality criteria developed under Section 304 to reflect ice*.
environmental conditions and human exposure patterns. Alternatively, at .»•.«•
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 narrative 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 tr.e
average amount of time aquatic ecosystems should be provided between
excursions (Stephan et al. 1985; U.S. EPA 1991). However, various spec.es a.-.:
ecosystems react and recover at greatly differing rates. Therefore, if
adequate justification is provided, site-specific and/or pollutant-spec i'. .:
concentrations, durations and frequencies may be higher or lower than tr:3«
given in national water quality criteria for aquatic life.
Use of criteria, which have neen adopted in state water quality
standards, for developing water qvial.ty-based permit limits and for de».;~. .
waste treatment facilities requires selection of an appropriate wastelca:
allocation model. Although dynamic Bedels are preferred for the applies-..-
of these criteria (U.S. EPA 1991), limited data or other considerations -.;-*-
require the use of a steady-state model (U.S. EPA 1986).
Guidance on mixing zones and tr.e design of monitoring programs is
available (U.S. EPA 1987, 1991).
-------
Table 1. Acute Toxicity of Aniline to Aquatic Animals
Species
Planarian,
Dugesia tigrina
Annelid.
Lumbriculus variegatus
Snail (adult).
Aplexa hvonorum
Snail.
Heltsoma trivolvis
Cladocaran « 24 hr).
Ceriodaphnia dubia
Cladocaran « 24 nil.
Certodaohma dutoa
UaJuiwan l< 24 hi).
Cladoceran « 24 hi).
Cenodaphnia dubia
Cladoceran « 24-hr).
Ceriodaphnia dubia
Cladoceran ( < 24-hr),
Ceriodaphnia dubia
Cladoceran « 24-hr),
Daphnia magna
Cladoceran « 24-hr).
Daphnia magna
Cladoceran (juvenile).
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
Chemical" pH
FRESHWATER SPECIES
Reagant Grada 6.5-8.5
Reagent Grade 6.5-8.5
7.4
Reagant Grada 6.5-8.5
99.5% 7.4-7.9
995% 7.47.7
99.5% 7.4-7.9
99.5% 7.47.7
99.5% 7.5-8.0
99.5% 7.8
-
Reagent Grade 6.5-8.5
LC50
or EC50
31.600
> 100 .000
> 219,000
100.OOO
119
193
146
184
146
44
150
530
210
Species Mean
Acute Value
uali- Reference
31,600 E well et al. 1886
> 100.OOO Ewell et al. 1986
> 2 1 9.OOO Holcombe et al. 1 987
1OO.OOO Ewell et al. 1986
Norberg-King 1987
Norberg-King 1987
Norberg-King 1987
Norberg-King 1987
Norberg-King 1987
125.8 Spehar 1987
Biesinger 1987
Biesinger 1987
Ewell et al. 1986
Duuhnia maflna
.41..
7779
170
Gersich and Mayas 1 986
-------
Table 1. (continued)
Species
Cladocaran ( < 24-hr).
Daphnia magna
Isopod,
Asellus intermedium
Amphipod,
Gammarus fasciatus
Midge (larva).
Chironomus tentans
Midge (larval,
Clinoianypui pinauis
Midg* llervn).
Midg* (larva).
Tanypus neopunclipennis
Midge (3rd-4lh inslar),
Tanvtarsus dissimilis
Rainbow trout (juvenile),
Oncorhvnchus mvkiss
Rainbow trout,
Oncofhvnchus mvkiss
Rainbow trout,
Oncorhvnchus mvkiss
Rainbow trout,
Oncorhvnchus mvkiss
H.,4.,,» F.V...I.I
..... .•.,...'...! •;.,» i
......I «• 1
• ' i ' . ' : " I *
LC50
or EC50
Method' Chemical" pH 0/g/U
F.M 7.4 250
S.U Reagent Grade 6.5-8.5 > 100.OOO
S,U Reagent Grade 6.5-8.5 > 100.000
S.U Reagent Grade 7.8 399,900
S.U Reagenl Grade 7.8 477.900
S.U Reaganl Grade 7.8 427. 9OO
S.U Reagenl Grade 7.8 272. 10O
F,M 7.4 > 21 9,000
F,M 7.1-7.7 10.600
S,M Analytical Grade - 41,000
S.M Analytical Grade - 20,000
F.M - 7.68.2 36,220
, M 74 40.500
. u . . • . I ti 30.000
^s
Species Mean
Acute Value
f/Q/L
25O.O
> 1OO.OOO
>1OO.OOO
399,900
477.900
427.900
272.100
> 219,000
26.13O
Reference
Holcombe et al. 1987
Ewelletal. 1986
Franco et al. 1986
Franco et al. 1984
Franco et al. 1984
Franco et al. 1984
Franco el al. 1984
Holcombe et el. 1987
Abram and Sims 1982
Calamari et al. 1980, 1982
Calamari et al. 1980. 1982
Hodsonet al. 1984
Holcombe at al. 1987
Spehat 1987
-------
Table 1. (continued)
Species Method* Chemical1* pH
Fathead minnow (juvenile). F.M 99% 7.6
Pimephales promelas
Fathead minnow (juvenile), S.U Reagent Grade 6.5-8.5
Pimephales promelas
Fathead minnow (juvenile), F.M - 7.4
Pimephales promotes
Fathead minnow (juvenile). F.M 99% 7.5
Pimephales promelas
Goldfish (juvenile). f M 7.4
Ceresstus auraius
t^jTtf" Ifwvemtel F.M 7.4
w»»i» •ucfce< (juvenile). F.M • 7.4
(.•leilomuB imiwr*»i»oot
Alncen clewed liog S.U
(embryo),
Xenopus lee vis
African clawed frog S.U
(tailbud embryo),
Xenopus laevis
African clawed frog (larva), S,U
Xenopus laevis
LC50
or EC50
Qyg/LI
1 34.0OO
32.0OO
77.900
114.OOO
187.OOO
49.000
78.4OO
550.OOO'
940,000°
1 50,000
Species Mean
Acute Value
uali. Reference
Brooke et al. 1984
E well «t al. 1986
Holcombe et al. 1987
Geiger et al. 1990
106.0OO Geiger et al. 1990
187,000 Holcombe et al. 1987
49,000 Holcombe et al. 1987
78,400 Holcombe et al. 1987
Davis el al. 1 98 1
Davis et al. 1 98 1
150.000 Davis et al. 1981
Eastern oysler (anibrvod.
(. 'Ui'-'iUM I'.'.tf'.'Lt
s u
SALTWATER SPECIES
1OO% 7.9-8.0 > 30,000
.«/X
/ 4 / b
1.030
> 30,000 Thursby and Berry 1987a
Thuisby and Beny 1987a
-------
Tabla 1. (continued)
Species Malhod*
Mysid (juvenile). * F.M
Mvsidopsig bahia
Amphipod (juvenile). R.U
Amoelisca abdita
Graaa shrimp (larva), R,U
Palaemonelas puoio
Saa urchin (embryo-larva), S.U
Arbacia punclulala
Shaapshaad minnow H.U
l|u venial.
C vunitwJun vaneualut
i«ri«*Ml »4v*fM«Je 4|uvemlel. R.U
Wmlai llouitdar (larval. S.U
PueuUupleuionaclea
•mancaruis
LC50 Species Mean
or EC50 Acute Value
PhfffPic"l> PH itin/L) ug/L Reference
100% 7.57.6 1.930 1.93O Thursby end Berry 1987b
100% 7.57.6 16.600 16.6OO Redmond and Scott 1987
1OO% 7.9-8.0 610 610 Thursby and Berry 1987a
100% 7.6-7.7 >20O.OOO >2OO.OOO Thursby and Berry 1987a
100% 7.88.2 1 2O.OOO 120.000 Thursby and Berry 1987a
100% 8.08.2 17.400 17.4OO Thursby end Berry 1987a
1OO% 7.98.1 >330.000 >330.OOO Thursby and Berry 1987u
• S = Static; R = Renewal; F = Flow-through; M <= Measured; U = Unmeasured.
' Purity o( tha test chamical.
' Results from less sensitive bfa stages ara not usad in tha calculation ol the Species Maan Acute Value.
-------
Table 2. Chronic Toxicity of Anilina to Aquatic Animals
Species
Cladoceran,
Ceriodaphnia dubia
Cladocaran,
Daohnia maana
Rainbow trout.
Oncorhvnchui rnvkits
Fathead minnow,
pimephales promelej
My«M)
Jest* Chemical* pH
FRESHWATER SPECIES
LC 99.5% 7.8
LC 99% 7.88.1
ELS 99.5% 7.8
ELS 99.5% 7.93
SALTWATER SPECIES
LC 1OO% 7.47.6
Chronic Limits Chronic Value
u/Q/Uc uvfl/L) Reterence
8.112.7 10.14 Spehar1987
24.646.7 33.89 Gersich and Milazzo 1 988
4.OOO 7.800 5.6OO Spehar 1987
422-735 557 Russom 1993
540- 1 , 1 00 770.7 thursby and Barry 1 98 7b
H. - hi* cyila 01 pailial lile cycle; ELS - early lile ilaga.
Puiily ul the leil chermcal.
He*ulis ere based on measured concentration* of aniline.
-------
Table 2. (continued)
Species
Rainbow trout,
Oncorhvnchog mvfcist
Cladoceran,
Daphnia mean*
Cladoceran.
Ceriodaphnia dubia
My«id.
MvsidopBis bahia
_BtL
7.8
7.78.1
7.8
7.4 7.6
Acule-Chronic Ratio
Acute Value
um/Ll
3O.OOO
170
44
SALTWATER SPECIES
1.930
Chronic Value
u/g/U
5.600
33.9
10.1
770.7
Ratio
5.3S7
5.015
4.356
2.504
-------
Table 3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic Ratios
iflnk'
19
18
17
16
15
14
13
12
11
10
9
8
7
Genus Mean
Acute Value
uvg/U
477,900
427.900
399.900
272,100
> 2 19.OOO
>219.OOO
1B7.0OO
150.00
106.OOO
>100.OOO
> 100.000
> 100.000
too ooo
Species
FRESHWATER SPECIES
Midge.
Clinolanypus pjnouis
Midge.
Einteldia natchitocheae
Midge.
Chironomm tentans
Midge,
Tanypus neopunclipennis
Midge.
Tanvtarsus dissimillis
Snail.
Aplexa hypnorum
Goldfish.
Carassius auralus
African clawed frog,
Xenopus laevia
Fathead minnow,
Pimephales promelas
Annelid,
lumbnculua varieoalus
Amphipod,
Gammarus (ascialus
Isopod,
Asellus intermedius
Snail.
Hali^tiMta Ilivoluib
vVI-io >.,. kai
Species Mean Species Mean
Acute Value Acute-Chronic
uyg/L)1' Ratio'
477.9OO
427,900
399,900
272,100
> 219.000
>219,OOO
187.000
1 50,000
106, OOO
> 100,000
> 100,000
>100.00O
100,000
;a.40o
-------
Table 3. (continued)
Rank'
5
4
3
2
1
8
7
6
5
4
3
Genus Mean
Acuta Value
frg/Ll
49.000
31.600
26,130
250
125 8
>333.00O
> 200.OOO
1 20.0OO
> 30,000
17,400
If) b()()
Species
Bluegill.
Lepomls macrochitus
Planarian.
Dugesia ligrina
Rainbow trout.
Oncofhvnchus mvfciss
Cladoceran.
Daphnia magna
Cladoceian.
Cefiodaphnia dubia
SALTWATER SPECIES
Winter flounder,
Pseudopleuronectes
americanus
Sea urchin,
Arbacia ounctulala
Sheepshead minnow,
Cyprinodon variegauts
Eastern oyster,
Crassostrea viiginica
Inland silverside,
Menidia beryllina
Amphipoil.
An.j .i-hti a «I_"_'!!J!
Species Mean
Acute Value
O/a/LI11
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
Ratio'
-
5.357
5.015
4.356
-------
Table 3. (continued)
Rank*
2
1
Genus Mean
Acute Value
uVQ/U
1.930
610
Species
Mysid.
Mvsidopsis bahia
Grass shrimp,
Pelaemonetes pugio
Species Mean
Acute Value
(ualU"
1.930
610
Species Mean
Acule-Chronic
Ratio'
2.504
* Ranked from most resistant to most sensitive based on Genus Mean Acute Value.
* From Table 1.
* From Table 2.
Fresh WBIBI
Final Acul* Value •- &6 97 >/g/L
Criterion Maximum Concentration = 56.97 //g/L / 2 *• 28 49
Final Acute Chionic Ratio «• 4.137 (see text)
Final Chronic Value = (56.97 /yg/L) 74.137 - 13.77/yg/L
Salt water
Final Acute Value = 153.4>/g/L
Criterion Maximum Concentration = (153.4//g/L) 12 = 76.7 //g/L
Final Acute-Chronic Ratio = 4.137 (see text)
Final Chronic Value = (153.4^/g/U /4.137 - 37.08//g/L
-------
Table 4. Toxicily of Aniline to Aquatic Plants
Species Chemical*
Green algae. Analytical Grade
Selenastrum
capricornutum
Graan alga*.
Selenastrum
capricornutum
Graan algae.
Selenastrum
caoricornutum
Graan algae.
Selenastrum
capricornuium
Green algce.
^.'IfSL
<,,..« -«••
:iSSn,
Gieen algae.
Solenaslium
capricornutum
Green algae.
Selenastrum
capricornuium
Green algae.
Selenaslrum
capricornutum
Green algae.
Selenaslrum sp.
Glean •ign
I IJ..inll. .. .!.!•••»
pH Duration
FRESHWATER SPECIES
4 days
7 days
7 day*
4 days
4 days
5 days
5 days
6 days
6 days
4 days
14 duyi
Effect
EC50
(growth)
No effect
(cell number)
No effect
(growth rate)
Incipient effect
(growth)
Incipient effect
(growth)
Incipient effect
(growth)
Incipient effect
(growth)
Incipient effect
(growth)
Incipient effect
(growth)
EC50
(biontuss)
16% i eduction
in yiu w III
Result
(jJQ/U Reference
19.OOO Clamariatal.
1980. 1982
<5.OOO Adams et al. 1986
10.OOO Adams et el. 1986
3.OOO Adams et el. 1986
1.000' Adams et al. 1986
3.OOO Adams et al. 1986
5.OOO' Adams et al. 1986
3.OOO Adams et al. 1986
5.000' Adams et al. 1986
20.0OO Sloof 1982
184.OOO Anunann and Terry
ia«fa
-------
Table 4. (continued)
Sp«ci>$ Chemical*
Green alga,
ChloreUa vuigaris,
Green alga.
ChtoreNa vuloaris
Green alga.
Chlorela vutoaris
pH Duration
14 days
14 days
14 days
SALTWATER SPECIES
Effect
58% reduction
in growth
66% reduction
in growth
75% reduction
in growth
Result
0/u/U
306.OOO
613.2OO
817.000
Refarence
Ammann and Terry
1985
Ammann and Terry
1985
Ammann end Terry
1985
No acceptable toxicity data for saltwater plants
Purity of the test chemical.
Acetone cairiei used
Kl
m
-------
Table 5. Other Data on the Effects of Aniline on Aquatic Organisms
Concentration
Species
Bacterium.
Pseudomonas pulida
Bacterium,
Spirillum volutana
Blua-green alga.
tdicrocvslta
aeruoinosa
Blue green alga,
Miciocyslib
aeniflinoga
Giean alga*.
Scenede»iiu»
ouadiicaude
Green algae,
Scenedesmut
quadricauda
Green alga,
Scenedesmus
ouadricauda
Graan algae.
Selenastrum
capncornulum
Protozoan,
Chilomonas
paramaecium
Piulojuan
t'"'-f'" ••
I'!1' t'.X'
Chemical*
Raagant Grada
7.0
6.8
7.5
6 9
Duration
FRESHWATER SPECIES
Effect
Reference
16 hr
1 hr
24 hr
8 days
4 days
8 days
24 25 hr
4 hr
48 hr
72 hi
Incipient inhibition
Inhibition of
motilily
50% mortality
Incipient inhibition
Incipient inhibition
Incipient inhibition
BCF - 91
66% reduction in
photosynthesis
Incipient inhibition
Incipient inhibition
130.00O Bringmann 1973;
Bnngmann and
Kuhn 1976.
1977b, 1980b
30.OOO Bowdre and Krieg
1974
2O.OOO Fitzgerald et al.
1952
1 6O Bringmann and
Kuhn 1976.
1978a.b
1 0.OOO Bringmann and
Kuhn 1959a,b
8.3OO Bringmann and
Kuhn 1977b.
1978a.b, 1980b
Hardy et al. 1985
100.0OO Giddings 1979
250.000 Bringmann at al.
1980; Bringmann
and Kuhn 1981
24.OOO Bringmann 1978;
Bimgmann and
Kuhn 19801). 1981
-------
Table 5. (continued)
Concentration
Species Chemical* pH
Protozoan, - 7.5-7.8
Microreoma
hetnrostoma
Protozoan, - 6.3
Telrahvmena
pvritormis
Protozoan, - 6.9
Uronema parduczi
Hydiozoan, >98%
Hydra oligactis
Planarian. > 9iX
Duu«ii« tuoutMU
;^;^u- -98%
Snari >98%
Clotloceian. 99.5% 7.8
Cenodaphnia dubia
Cladoceran, - 7.5
Daphnia maana
Cladoceran, - 7.67.7
Daphnia maana
Cladoceran. Pure Analytical 7.4
Daphnia maana Grade
Cladoceran,
Daphnia maona
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
Edaci
Incipient inhibition
EC50
(growth)
Incipient inhibition
LC50
LC50
LC50
LC50
EC50 (ted)
EC50
(acoustic reaction)
EC50
(immobility)
EC50
BCF = 5.0
(/jg/L) Reterence
20.OOO Bringmann and
Kuhn 1959a
154.270 Schultz and Allison
1979
9 1 .OOO Bringmann and
Kuhn 1980a. 1981
406.000 Stood 1983
155,000 Stood 1983
450.000 Stood 1983
80O.OOO Stood 1982, 1983
132 Spehar 1987
400 Bringmann and
Kuhn 1959a,b
1960
50O Bringmann and
Kuhn 1977a
23.000 Clamari et al.
1980. 1982
Dauble et al.
1984. 1986
«* t
10 hi
IT50
1O.OOO
Lakhnuvu 1975
\J I.I
I IbO
a. ooo
Lukhnova 1975
-------
Tabla 5. (continued)
Species
Cladoceran,
Daohnia niaona
Cladoceran.
Daphnia maona
Cladoceran.
Daphnia maona
Cladoceran,
Paohnia maona
Cladoceran,
Oaphnia rnagna
Cladoceran.
Daphnu mean*
ClaUoceien (•dulll.
Mvina
Chemical'
Concentration
Chtronomui dortali*
Midge.
Chironomus dorsalis
Midae.
Chironomus dorsalis
Mayfly (larva).
Cloaon dipterum
Mosquito (3rd
instar).
Aedes aeqypti
Rainbow trout
(|uvenilt>).
Otii 01 h^it« IMI^
99%
99%
Analytical Grade
>98%
>98%
7.4
Duration
1 .0 day
1 .5 daya
2.0 days
3.5 days
14 days
1 4 days
3 hr
20 21 days
20-21 days
20-21 days
48 hr
48 hr
7 days
EHect
LT50
LT50
LT50
LT50
MATC
• MATC
LC50
95% Mortality
30% Mortality
0% Mortality
LC50
LC50
LC50
(J/U/LI
6.OOO
4.OOO
2.000
1.OOO
29.9
14.9
1 .000.000
7.8OO
7.000
3.00O
220.000
1 55.OOO
8,200
Reference
Lakhnova 1975
Lakhnova 1975
Lakhnova 1975
Lakhnova 1975
Gersich and
Miluzzo 1990
Gersich and
Milazzo 1990
Yoshioka et al.
1986b
Puzikova and
Markin 1975
Puzikova and
Markm 1975
Puzikova and
Markin 1975
Slooff 1983
Sloolf 1982
Abram and Sims
1982
-------
Tabla 5. (continued)
Concentration
Species Chemical*
Rainbow trout
(juvenile).
Oncofhvnchue
mvkiss
Rainbow trout
(juvenile).
Oncorhvnchus
mvkisf
Rainbow trout
(2 yr).
Oncorhvnchus
mvkiss
Rainbow trout
12 yi 1
UlAili
H.,^,0. 1,001.
Oil*. MlftV'KtHlft
mv*lii
Rainbow lioul,
Oncorhvnchus
rnvkiss
Guppy, 99%
Poecilia reticulate
Fathead minnow >98%
(3-4 wk).
Pimephales
pcomelas
Channel catfish
(embryo, larva).
'tlflKf'Ut fiviKlaluA
. ••-- . »• .»
• « . » •
9 • •• •
_Bb_ Duration Effect (^g/L) Reference
74 7dav» LC50 8.200 Abram and Sims
1982
7.4 72 hr BCF = 507 Dauble at al. 1984
24 hr No mortality 10.OOO 20.OOO Lysak and
Marcinek 1972
24 hr LC10O 21.000 Lysak and
Maicmek 1972
7 -O-8.0 48 hr No impairment of 10, OOO Shumway and
flavor Palensky 1973
7.08.0 48 hr 100% mortality 100.OOO Shumway and
Palensky 1973
Hd«V« LC50 125.629 Hermens el al.
1984
48 hr LC50 65.00O Slooff 1982
77 To hatch LC50 5.600 Birge et al. 1979b
(4 5 days) (5.500)"
u b j.Vk LCbO b.OOO Birge el al. 1979b
|4 1-,. >....! ('j.OUOl1'
I...I, III
-------
Tabla 5. (continued)
Speciag Chemical'
Channel catfish
(embryo, larva).
Ictalurus punclatug
Channel catfiah
(embryo, larva).
Ictaiurui punctatus
Goldfish
(embryo, larva).
Caraggjug auratug
Goldfish (embryo.
larva).
Caratitut auratug
Gufclltett
t«n«.ivu (a,..,
LwMMua ffuiatu*
bufcllisn
Iwntiiyo. laival.
Caiaggiut atiratug
Goldfish
(embryo, larva).
Carasgius auratug
Goldfish
(embryo, larva).
Carasgius auralug
Largemouth bass
(embryo, larva),
Micropterug
salmoides
1 etuentouirt (*•••
gH Duration
7.7 To hatch
(4.5 days)
7.7 8.5 dayg
(4 days post-
hatch)
7.7 To hatch
(3.5 dayg)
7.7 7.5 dayg
(4 dayg post-
hatch)
77 115 dayg
(4 days pos.1
hatch)
77 To hatch
(3.5 days)
7.7 7.5 dayg
(4 days post-
hatch)
7.7 11. 5 days
(8 dayg post-
hatch)
7.7 To hatch
(2.5 3.5 days)
77 6575 days
|4 ,UV> !"•:>'
I..,, i,,
Effect
LC5O
LC50
LC5O
LC5O
LC50
LC50
LC50
LC50
LC50
LC50
Concentration
Ij/n/LI
7.4OO
(6.300)*
7.000
(6.200)*
10.2OO
(9,300)*
5.600
(5.500)'
5.500
10.000
(7.600)L
4.800
(4,600)*
4.700
47.300
(32.7OO)'
10.5OO
(7.100I1-
Reference
Birgeet al. 1979b
Birga at al. 1979b
Birgeet al. 19796
Birge at al. 19796
Birga at al. 19796
Birge at al. 19796
Birga at al. 19796
Birga el al. 19796
Birga at al. 19796
Birga et al 19796
-------
Table S. (continued)
Concentration
Species Chemical*
Largemouth bass
(embryo, larva).
Micropterus
salmoides
Largemouth baas
(embryo, larva).
Microplerus
salmoides
Largemouth bass
(embryo, larva).
Micropterus
salmoides
Largemouth bass
(embryo, larva).
Micrupleiuf
sattrxxdes
Afucan clewed frog
|enil>ryol.
Xenopus laevis
Africen clawed frog
(embryo).
Xenopus laevis
African clawed frog
(larva).
Xenopus laevis
African clawed frog
(tadpole).
Xenopus laevis
African clewed frog
(embryo),
?2-»jjji!i !««Y'i
» 1 «• ..•.!'„ • • -
1 4 «» »
• • t (••••»
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)
77 10.5-1 1.5 days
(8 days post-
hatch)
96 hr
1 20 hr
36 hr
1 2 days
12 weeks
use
Effect
LC50
LC50
LC50
LC50
EC50
(teralogeny)
EC50
(teratogeny)
6% abnormalities
100% mortality
Slowed
metamorphosis.
reduced growth
bbO.OOO
»>a/u
5,200
43.200
(29,900)'
8.4OO
(7.100)"
4,400
370.000
91.OOO
10.000
9O.OOO
1.0OO
Reference
Birge et al. 1979b
Birge et al. 1979b
Birge et al. 1979b
Birge et al. 1979b
Davis et al. 1981
Davis el al. 1981
Dumont el al.
1979;
Davis et al. 1981
Dumper! 1987
Dumperl 1987
Slooll 1982;
Sloult and
Buerselinan 1980
-------
Table 5. (continued)
Species
Sea enemone,
Bunodosoma
cavetnala
Sand shrimp
(adult).
Crangon
soi>lamspinosa
Chemical*
pH Dufalion
SALTWATER SPECIES
7 days
96 hr
Effect
Significant
increase in
concentration of
free aspartate,
glulamale, alanine
Lethal threshold
Concentration
U/P./L) Reference
5OO.OOO
29.400
Kasschau et al.
1980
McLeese el al.
1979
* Pumy ol Ilia lebl chemical
* (Jala in pureiuhas.i UIB lion) Biige et al. 1979a.
-------
2RAFT
9/22/93
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