«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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                                                          DRAFT
                                                        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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                                                                         3 RAFT
                                                                       !/22/S3
                                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
                                                                       9/22/93

 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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                                                                         3RAFT
                                                                       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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                                                                       9/22/9 3
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

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                                                                       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

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                                                                       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

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                                                        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




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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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