-8Z2-R-$7-100
                                               Draft
                                               9/25/87
AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR

            2. 4. 5-TRICHLOROPHENOL
    U.S. ENVIRONMENTAL PROTECTION AGENCY
     OriflCE OF RESEARCH AND DEVELOPMENT
     ENVIRONMENTAL RESEARCH LABORATORIES
              DULUTH. MINNESOTA
         NARRAGANSETT. RHODE ISLAND

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                                    NOTICES
This document has been
                                   the Criteria and
Mention of trade names or commercial products does not constitute *nitn
or recommendation for use.                             constitute endorsement
This document is available to the public through the National

Informanon Service (NTIS). 5285 Port Royal Rofd. Sprin«neti.
                                                                   i. •

                                                                   22?6t
                                      11

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NOTICES
This document has been revi»w»H K^

of *ater Re.ul ations^s^ JarSl.

approved for publication.
                          Dlvisi°-  Office
                   Protection Agency,  and

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                                                  Draft
                                                  9/25/87
AMBIENT AQUATIC  LIFE WATER QUALITY CRITERIA FOR

             2.4,5-TRICHLOROPHENOL
     U.S. ENVIRONMENTAL PROTECTION AGENCY
      OFFICE OF RESEARCH AND DEVELOPMENT
      ENVIRONMENTAL RESEARCH LABORATORIES
               DULUTH.  MINNESOTA
          NARRAGANSETT. RHODE  ISLAND

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                                    FOREWORD
  accurately reflect th. latest JclStifiS k»~l.^   "^   ^ "iteria that
  .11 Identifiable effects on h.alth and "elfar* th.t°mi±  t"* ""* '^'" °l
  presence of pollutants in any body of water  %,1rJ,   ^   ! «xPe<=tei1 fr
  document proposes water quality criteria               °  th" "ld' this
 Th-. criteria do not involve
  After
  issue th.  criteria  in  final
  previously published EPA
                                  at
                                                                 ... EPA win
                        ..i  /
pollutant concentrations that can b4 nsld to Lri^! J"1™"" ««eptabl«
for discharges to such waters.                     * enforceable permit limits
          under section  304  to  reflec    r
incorporation  into water qua UtJ«S£
assist States  in the modification ofseSon
development of water quality standards    Ui
part of State water qualit/standard,*^'^
                                                                      criteria
                                                                      Before
                                                           aiable fr°B EpA to
                                                                 *"* i
                                   Martha G.  Prothro
                                   Director
                                   Office of  Water Regulations and Standards
                                     iii

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                                ACKNOWLEDGMENTS
 Daniel J. Call
 (freshwater author)
 University of Wisconsin-Superior
 Superior, Wisconsin
Jeffrey L.  Hyland
Richard K.  Peddicord
(saltwater authors)
Battelle Ocean Sciences
Duzbury, Massachusetts
Charles E. Stephan
(document coordinator)
Environmental Research Laboratory
Duluth, Minnesota
David .'.  Hans en
(saltwater coordinator)
Environmental Research Laboratory
Narrajansett, Rhode Island

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                                     CONTENTS
                                                                         Page

  Notices	
                                     	  11

  Foreword	
                                   	 ill

  Acknowledgments	
                           	  iv

  Tables	
                                    	'	  v i





  Introduction	



 Acute Toxicity to Aquatic Animals	           2


 Chronic Toxicity  to Aquatic  Animals	           4


 Toxicity to Aquatic Plants	               »


 Bioaccumulation	                                        a
                                         	    o


 Other Data	



 Unused Data	                                           0
                                     	    o

 Summary	
                         	    8


 National Criteria	


 Implementation	






References	
                                        *'*'•***••	   40

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TABLES
                                                                         Pii
 1.   Acute Tozicity of 2.4,5-Trichlorophenol  to  Aquatic  Animals  	   :

 2.   Chronic  Toricity of  2.4.5-Trtchlorophenol  to  Aquatic  Animals  	

 3.   Ranked Genus  Mean Acute  Values  with Species Mean Acute-Chronic
      Ratios  	

 4.  Toxicity  of 2,4,5-Trichlorophenol  to  Aquatic  Plants ..

5.  Bioaccumulation  of 2.4.5-Trichlorophenol by Aquatic Organisms  	   22

6.  Other Data on Effects of 2.4.5-Trichlorophenol  on Aquatic  Organi
                                      18

                                      21
                               sms
23

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    I ntroduction
       2,4,5-Trichlorophenol (2,4,5-TCP)  is a  crystalline solid at room
   temperature.   It  is soluble in water up  to  2.000 mg/L. has an ionization
   constant  (pKa) of 7.0 to 7.4 (Ahlborg  and Thunberg  1980; Doedens 1964-  U  S
   EPA  1980), and a  log n-octanol/water partition  coefficient of 3.70 (Hansch
   and  Leo 1979).  2.4.5-TCP is used as an  algicide. fungicide, and bactericide
   and  as an antimildew and preservation  agent in  cooling towers, pulp mills.
 .  and  in hide and leather processing (Ahlborg and Thunberg 1980; U.S. EPA
   1980).  It is also used in the  production of  the pesticides erbon.
   fenchiorphos,  fenoprop  (2,4.5-TP).  hexachlorophene. and 2,4.5-trichloro-
  phenoxyacetic acid (2.4.5-T)  (Ahlborg  and Thunberg  1980; Buikema et al. 1979;
  Doedens 1964;  Kozak  et  al.  1979;  Stolzenburg  and Sullivan 1984).
      Contamination  of waters  with  2.4.5-TCP  and  other  chlorophenols has
  resulted from  the  use of  chlorophenoryacetic  acid herbicides containing
  chlorophenolic  impurities, from the  chlorination of waste treatment plant
  effluents,  and  from pulp  bleaching  (Ahlborg and Thunberg 1980; Buikema et al.
  1979; Jolley et al. 1978; Rockwell  and Larsen 1978).  Residues have been
 detected in fish and other organises collected  downstream fro» pulp am,
 (Paasivirta et al.  1985).  Considerable  concern has been expressed that
 2.3.7.8-tetrachlorodib«ni<>-p-diosin  (TCOD)  can  be an  impurity  in  2.4.5-TCP
 (Anonymous  1978; Firtstono et al.   1972).
     At rerj lew concentrations,  some phenolic compounds impair  the odor  and/
 or taste of wattr  and fish.   2.4.5-TCP has  a  taste  threshold  concentra-
 tion  in  water  of 1  m/L  arid an odor  threshold concentration  of  200 Mg/L
 (Dietz and  Traud 1978).   However.  Shumway and Palensky  (1973)  did not  observe
 flavor impairment  in  rainbow trout exposed  to 320 m/L  for  48 hr.
    An understanding  of  the  "Guidelines  for Deriving  Numerical  National  water
Quality Criteria for  the  Protection of Aquatic  Organisms  and Their Uses
                                        1

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ues
   (Stephtn et al.  1985).  hereinafter referred to as  the  Guidelines, and the
   response to public  comment  (U.S. EPA 1985a) ,, necessarj  in order to
   understand the  following  text,  tables,  and calculations.  Results of such
 .  intermediate  calculations as  recalculated LCSOs and Species Mean Acute Val
   are  given  to  four significant figures to prevent round off error in
   subsequent  calculations, not  to reflect the precision  of  the  value.  The
   criteria presented herein supersede the aquatic life information in  a
   previous criteria document (U.S. EPA 1980) because these  criteria are baaed
   on additional information.  The latest  literature  search  for  information  for
   this document was conducted in July.  1988; some more recent  information  was
   included.  Data that are in the files of the U.S.  EPA's Office  of  Pesticide
  Programs concerninf  the effects of  2,4.5-TCP on aquatic life  and its uses
  have  not been evaluated for possible  use in the derivation of aquatic  life
  criteria.

 Acute Toxicitv to Aquatic  Anim.lj
     Data  that  can be  used.  accordinf  to  the Guidelines, in  the  derivation of
 Final Acute  Values for  2.4.5-TCP are  presented in  Table I.   The rainbow
 trout. iiil2 Hird.ne.ri.  »*«  the  «o»t  sensitive freshwater species  with a
 96-hr LC50 of 280 ftg/l.  Thw cladoceran.  fliaHnH. lltai. was  the »ost
 resistant species, with  a 48 hr  ECSO  of  2.660 M|/L.  The  range of  acute
 values for fish was fro* 260 Mf/L in  the  trout to  3.060 M|/L in the
 «uppjr,  poecUlj rtm.lltl.  A si.ilar  ranfe for invertebrates extended  from
 338 ni/L in.the aaphipod, Gaaaarm  oseudol iana.e.u.j  to 2.880 M|/L in
 Paohnia.
    The  effect  of  pH on  the acute toxicity of 2.4.5-TCP w»,  examined with  the
«upp7. Pmilli rctjculiti (Saarilcoski  and Viluksela  1981.1982; Salkinoj*-
Salonen  et al.  1981).   The 98-hr LCSOs  at pH = 6.  7.  and 8 were 990.  1.240.
                                         2

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   and 3.060  MK/L.  r«3p«ctive17.  The freshwater criterion was not made
   pH-dependent because data are available  for onlf one species.
       Freshwater Species Mean Acute Values  (Table 1) were determined from  the
   available  acute  values.  Genus Mean Acute  Values (Table 3) were the  same  as
   the:Species Mean Acute Values.   Of the ten freshwater genera for which mean
  acute values are available,  the most sensitive genus, Sal mo. is about 10
  times more sensitive than the most resistant, Daohnia.  The freshwater Final
  Acute Value for 2.4,5-TCP was calculated  to be 199.2 »g/L using the
  procedure described in the Guidelines and  the Genus Mean Acute Values in
  Table 3.   The Final  Acute  Value is lower  than the lowest available Species
  Mean Acute  Value.
      The  stock of  2,4.5-TCP that was  used  in freshwater acute tests reported
  b7 Sabourin et  al.  (1986)  and Spehar (1986) w«, found to contain  U.2 ng/g of
  the  contaminant,  2.3.7,8-tetrachlorodibenzo-p-dioxin (TCDD) (Durhan  1988).
  This  resulted in  estimated 2.3.7,8-TCDD concentrations in the  exposure water
  as high as  115 pg/L  (Table 1).   it  is not  known if 2.3.7.8-TCDD
 concentrations of 115 pf/L or less  had an  effect upon the observed toxicity.
 Concentration, of 2.3.7.8-TCDD  were  not determined in the other  freshwater
 acute tests.
     Tests of the tout* twicity of 2.4.5-TCP to resident North American
 saltwater ammals hav, been performed with six species of  invertebrates  and
 five  species of  fish (T.kle I).  The range of acute  values  for invertebrates
 extends  fro. 492 MC/L for the amphipod.  Rhepoxvnim  tbron.ua  (Battelle
 Ocean  Sciences 1987) to 3.830 Mg/L  for adult mjaids. Mrsidonsi, hahji
 (U.S.  EPA  1978).   The range of acute values for saltwater  fish is narrower,
 from 588 m/L for  both juvenile English sole. Paroohvs vetulua.  and adult
P»cific sand  lance.  Afliadj.tC-1 h«tDterus  (Battelle Ocean Sciences 1987) to

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    1.680 pc/L for both juvenile sheepshead minnows. Crprinod^ varier-.lt
    (Heitrauller et al. 198 ,  and juvenile  inland silversides,  Mgnid^   .rynina
    (Hughes and Pruell 1987).
       The 24- and 98-hr LCSOs  differed little with both mysids and  sheepshead
   minnows (Heitmuller et al.  1981; U.S.  EPA 1978).  In contrast,  mortalities
   continued  throu«hout  acute tests with  polychaete worm,,  urchiannelids.  and
   inland  silversides (.Battelle  Ocean Sciences 1987).   Rao  et al.  (1981)  found
   that  2,4,5-TCP  was about twice as toric to molting jrass shrimp as  it  was  to
   intermolt  shrimp.   The effect of environmental  factors such as  salinity and
   temper  ure on  the  acute toricity of 2.4,5-TCP to saltwater animals is not
   known.
      Of the  ten fenera for which saltwater Genus Mean Acute Values  are
  available  (Table 3). the most sensitive (enus,  Rhea0Tvn,hlf  is  about 7 a
  times  sore  sensitive than the most  resistant,  Mvsidomi.   The  six  most
  sensitive jenera are within  a factor of 1.8  and include  four invertebrates
  and  two  fishes.   The saltwater Final  Acute Value for 2,4,5-TCP  *.,  calculated
  to be 472.9 »g/L.  which is  lower  than the  mean  acute value for  the  most
  sensitive tested  saltwater species.
 Chronic TotieitT ta A^q^tie ini..|g
     Th« available data that are  uieable  accordinj  to tht Guidelines con-
 cerninc tht chronic toxicitf of  2.4,5-TCP  are  presented in Table 2.  In a
 seven-d»7 lif«-cjcl« tt»t with Ceriodaphni*  dj^j^   tn  0rCtnis«s died at a
 concentration of 1.480 Mf/L (Speh.r  1986).   A  concentration of 748 M|/L
 did  not  cause •ortalitj.  but sijnificantlj reduced production of 7ounc.  A
 concentration of 375 M€/L affected neither survival nor reproduction.  The
 resultinf chronic value was 528.9 /^/L and eh« acute-chronic ratio was
3.294 (Table  2).

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         in a 90-day ear!7 nfe-3tage  test with rainbow trout  (Spehar 1986).  a
    concentration of 441  Mg/L  caused  im mortalit7 of 3wim_up  ^^   ^
    concentration of 208  Mg/L  did not affect hatchability  or  swim-up larvae
    but Signmcantly (P  < 0.05) decreased surviva,  of juveniles.
    effects  .ere  observed at 108 Mg/L or below.   The  chronic  vaiue and
    acute-chronic  ratio were 149.9 Mg/L and 1.734,  respectively  (Table 2).
       Fathead minnow,, P^*^ prone I a,.  eKposed to IQQ
   adversely affected in an early life-,tafe  test  (Spehar  1986).  Reduced growth
   and approximately 50% mortality occurred at  342 M«/L.   Complete mortality
   was observed at 673  and 1.322  n/L.   The chronic value  wa, 233.9
   and the  acute-chronic  ratio  was  5.421  (Table 2)
       The  stock 2.4.5-TCP that wa, used  in the freshwater chronic test,
   reported by  Spehar (1986) contained up to  14.2 Bf/f of 2.3.7. 8-TCDD (Durhan
   1986).  This  resulted  in estimated maximu. 3.3.7.8-TCDD concentration, in the
  exposure water of 40.9 Pf/L |B th. ^^^ t-it§
  trout test,  and 18.8 Pf/L in the fathead minnow test.   It i, not known at
  present  if  2.3.7.8-TCDD at these concentration, had any effect upon the
  observed  toxicitj.
     The chronic  toxicitj of  2,4.5-TCP ha, been «a,ured in salt water with
 Che ini.nd silver.id..  M^d^ j^UJni (Hughe, and PrueU  1987).   ,„ thl,
 earl7 life-,t.f. t..t.  M% of the  e.br7o, expo.ed to 104 n/L died before
 h*cchinf.   SurTir.1 of  both  e.bryo,  and  fry  „., reduced at 59.8 MI/L. but
 no  effect, „„ dtt.cted at  25.1 MC/L.   The  resultinj  chronic value wa,
 38.88  MC/L,  tnd the acute-chronic  ratio  was  42.92 (Table 2).
    The available Specie, M,ean Acute-Chronic  Ratio, are 3.294. 5.421. and
 1.734  in fresh  water and 42.92 in  s.U water  (Table 3).   The freshwater F.nal
Acute-Chronic Ratio of 3.140 wa, calculated  a,  the  Ceo.etric mean of the

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   three  ratios. whereas 42.92 was used a,  the  saltwater Final Acute-Chronic
   Ratio.  Division of the freshwater and  saltwater Final Acute Values  by  the
   respective Final Acute-Chronic Ratios results  in freshwater and saltwater
   Final Chronic Values of 63.4* and  11.02  Mf/L,  respectively.  These Final
  Chronic Values are lower than the  lowest available respective chronic values
  in fresh and  salt water.

  Toxicitv to Aquatic  Planta
     Two  toxicity  tests  with exposure periods of four or more days have been
  conducted on  2.4,5-TCP  with aquatic  plants (Table 4).  An EC50, based on
  reduction of  chlorophyll a,, was  1.200 ng/L for the freshwater «reen alga.
 ?tUnmry(B glgMwnWllH (U.S.  EPA  1978).   The ECSO, based on reduction in
 chlorophyll  A. was 890 Mf/L for  the  saltwater diatoa, SJceletone»a
 c.9?my.B. "berets the EC50 based on cell counts was 960 M|A (U.S. EPA
 1978).   These  concentrations are abore the Final Acute Values for 2.4.5-TCP.
 A Final  Plant  Value,  a, defined  in the Guidelines,  cannot be obtained because
 no test  in which the  concentrations of 2.4.5-TCP were .easured and the
 endpoint  wa, bioloficallj important has  been conducted with an i-portant
 aquatic plant  species.
14
 Bioaccuaulatjflfl
     In  a  bio«w»centration test with  the  fathead .Innow,  equilibrium of
   C-labeitd f,4.5-TCP between water  and  fish occurred within 24 to 48 hr at
exposure  concentrations of 4.8 and 49.3  Mf/L (Call  et at.  1980).  At the
hifher concentration,  78.8% of the radiolabel  was associated with 2.4.5-TCP
at the end  of  the  28-day uptake phase.   The  BCF was 1.410 and the half-life
    12 hr (Table 5).

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      Inland silversides, Menidia beryl 1ina.  that  survived a 28-day early life-



  stage toxicity  test  accumulated 2,4,5-TCP to concentrations between 47.2 and



  71.3 times the  concentration measured in test solutions (Table 5).  Biocon-



  centration factors for grass shrimp,  Palaemonetea  pugjo. exposed  for one hour



  to  14C-trichlorophenol were 13 for intermolt and 32  for new molt  stages



  (Table  6).  Concentrations after 12 hours of exposure  of  intermolts were




  highest  in the  digestive tract and hepatopancreas  and  lowest  in  the cephalo-



  thorax  and  abdomen.  Shrimp depurated 98% of accumulated  2,4.5-TCP  in  24 hr



  (Rao et  al. 1981).




    ; No U.S. FDA action level or other maximum acceptable  concentration in




 tissue,   as defined in the Guidelines, is available for 2,4,5-TCP.  Therefore,



 a Final  Residue Value cannot be calculated.
 Other Datt




     Additional  data on the lethal  and sublethal  effects of 2,4.5-TCP on



 aquatic  species are presented in Table 8.   Exposures of an alga.  Chlorella



 Pmn9Jd.9?l.  to 2,4.5-TCP for 3 days at concentrations from 1.000 to



 10,000 Mg/L reduced chlorophyll by 12 to 1007. (Huang and Gloyna 1967.



 1988).   The 24-hr EC50 for the protozoan,  Tetrahragn. prriformia. was



 680 MI/L (Yoshiok* et al.  1985).  A 24-hr exposure to 1.912 ng/L caused



 100% aortalitj  of ly»natid snails (Batte and Swanson 1952).  A 24-hr EC50  of



 2.080 fig/L was  obtained with the cladoceran. Daphnit mtrn«  (Devillers  and



Chambon  1986).   A 48-hr exposure of rainbow trout to 2.4,5-TCP  at



 1.000 MI/L resulted in 100% mortality (Shuaway and  Palensky 1973).   LC50s



of 900.  533.  and 1.700 Mf/L were obtained at 24 hr  with  the brown trout.



guppy. and  goldfish,  respectively.

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       Ribo and  Kaiser  (1983) reported a 30-min  EC50 of 1.300 ng/L,  based  on
   reduction in  light production by the photoluminescent bacterium,
   Phocabacterium phosphor-en^ (Table 6).   Rao  et al. (1981) found that exposure
   to  500  and 750 Mg/L  for 9 days inhibited  limb regeneration by the grass
   shrimp.  Palaemonetea pugio.   Limb regeneration was not affected in
   100
  Unused Data
      Some data on the effects  of  2.4,5-TCP  on aquatic organisms were not used
  because the tests were  conducted with  species that are not resident in North
  America (e.g..  Hattori  et  al.  1984;  Hosaka et al. 1984; Nagabhushanam and
  Vaidya 1981).   Kaiser et al.  (1984), LeBlanc (1984). and Persson (1984)
  compiled data  froa other sources.   Bringaann and Kuhn  (1982) cultured
  organisms  in one  water  and conducted tests in another.  Dojlido (1979) did
  not specify which trichlorophenol was  used.  Blackaan  et al. (1955a.b)
 conducted  tests at  pH below 8.5.
     Results were  not  used when th«  test procedures were not  adequately
 described  (Knie et  al.  1983).  Studies 07  Kobayashi et al. (1984)  on  the
 sulfate conjugating enxjM systta and  McKia et al. (1985)  on the efficiency
 of  cheaical uptakt bj fish gills did not provide data  pertinent  to water
 quality crittria.
Summary
    The acute  toxicitj of 2,4,5-trichlorophenol  to  freshwater aniaals ranged
froa 260 ^g/L  for the rainbow trout to 2.660 Mg/L for Danhnia aatna.
The acu:e toxicitj of 2.4.5-TCP to the gupp/  increased as the pH of the water
decreased.  Chronic toxicitf values for  three  freshwater species ranged from

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    150 to 529 m/L,  and the  three  acute-chronic ratios ranged from  1.734 to



    5.421.  A freshwater alga was affected at a concentration of  1.220 Mg/L.



    A BCF of 1,410 was obtained  with the fathead minnow.




       Acute values  for 2. 4.5-trichlorophenol are available  for  eleven  saltwater



   animal species in ten genera and range from 492 Mg/L for  the  amphipod.




   Rhep°^niu3  *fr""iM?.  to  3.830 Mg/L for the mysid,  M^idon.,, bahia.  The



   six most  sensitive  species include three crustaceans,  two fishes,  and a



   polychaete worm and  their acute values are all  within  a factor of  1.8.  The



   only saltwater species with which a chronic test has been conducted  is  the



   inland silverside, MgJlilU ber7}|ina.   The chronic  value  is 38.68  Mf/L.



  and the acute-chronic ratio is  42.92.   The saltwater ditto..
          -  was «ffected by 890 ,,,/L.   BCFs determined with the  inland
  silverside  ranced from 47 to  71.
  National
     The procedures  described  in  the  "Guidelines  for  Deri*inC  Numerical



 National W.ter Quality Criteria  for  the  Protection of  Aquatic Organisms  and



 Their Use," indicate that, except possibly  where  t locally  important  specie,



 is very sensitive,  freshwater tquttic orftnis.s  and  their uses should not be



 affected untccepttbiy if tht four-dty arerije  concentrttion of 2.4.5-tri-



 chlorophenol  dots not tzcttd 63 Mf/L .ore Chtn once  erery three yetrs on



 the  trertft and if tht ont-hour evertfe  concentrttion  does  not exceed



 100  ng/L mort  thtn onet every three  yetrs on the  trertfe.   Because



 sensitive  freshwater tni.tls appear  to have a  narrow ranfe  of acute



 susceptibilities  to  2. 4. 5-tr ichlorophenol .  this  criterion will probably be as



protective  as  intended  only when the mafnttudet  and/or durations of



excursions  are  appropriately small.

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       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 3pecies
   is  very sensitive,  saltwater aquatic organisms and their uses should not be
   affected  unacceptably if the four-day average concentration of
   3.4.5-trichlorophenol does not  exceed 11  Mg/L more than once every three
   years on the average and if the one-hour  average  concentration does not
   exceed 240 ng/L more than once  every three  years-on the average.  Because
   sensitive saltwater  animals appear  to have  a narrow range of acute
  susceptibilities to  2.4.5-trichlorophenol.  this  criterion will probably be as
  protective as intended  only when the magnitudes  and/or durations of
  excursions are  appropriately  small.

  tmplementati op
     As discussed  in  the Water Quality Standards  Regulation (U.S. EPA I983a)
 and the  Foreword  to  this  docuaent.  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 .ore  uses for  each  body of water  or segment
 thereof and adopt criteria  that are  consistent with the use(s)  (U.S.  EPA
 I983b,1887).   In each standard  a state  aay  adopt  the  national  criterion,  if
 one exists,  or,  if adequately justified,  a  site-specific  criterion.
    Site-specific criteria aay  include  not  only  site-specific  criterion
concentrations (U.S.  EPA 1983b). but  also site-specific,  and possibly
pollutant-specific, durations of averaging  period, and  frequencies of allowed
excursion,  (U.S.  EPA  I985b).  The averaging per.od, of  "one  hour"  and  four
                                        10

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  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
  aquatic 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 I985b).  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  model, are preferred for the application
 of  these  criteria  (U.S.  EPA I985b).  limited data or other consideration,
might  require  the  use  of a steady-state model (U.S.  EPA  1986).  Guidance on
mixing zone,  and the  design of monitorinc pro|ra., i, also available  (U.S.
EPA 1985b,1987).
                                       11

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  Blaokman, G.E., M.H. Parke and G.  Carton.  1955b. The physiological  activity of



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                                        26

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    Dojltdo, J.R. 1979. Investigations  of  the biodejrabi 1 i ty and toxicity of
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  Huang, J.C. and E.F.  Gloyna.  1967. Effects of toxic organic*  on photosynthetic
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                                        31

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 SColzenburf.  T.  and J.  Sullivan.  1984. Dioxin - a cause  for  concern?
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                                        32

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