United States
        Environmental Protection
        Agency
Office of Water
Office of Research and Development
Washington • DC 20460
EPA xxx/x-xx-xxx
XXXX1994
        WATER
«yEPA  Ambient Aquatic Life Water
        Quality Criteria for:
        HEXACHLOROBENZENE
        (HCB)

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                                          823R94005
AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR

        HEXACHLOROBENZENE  (FRESHWATER)     :


         (CAS Registry Number 118-74-1)
                 AUGUST 1994
     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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                                   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.
                                       11

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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(s).

      The term "water quality criteria" is used in two sections of the Clean
Water Act, section 304(a) (1)  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 adjust 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
                                      111

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                                ACKNOWLEDGMENTS
Daniel J. Call
(Freshwater author)
University of Wisconsin-Superior
Superior, Wisconsin
Robert L.  Spehar
(Co-author and document coordinator)
Environmental Research Laboratory
Duluth,  Minnesota
                                        IV

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                                   CONTENTS




                                                                          Page




Notices	•.	ii




Foreword	iii




Acknowledgments	•.•	iv




Tables	'	vi







Introduction   	  1




Acute Toxicity to Aquatic Animals	'•....	3




Chronic Toxicity to Aquatic Animals	'-.  .	4




Toxicity to Aquatic Plants	••	5




Bioaccumulation	'	5




Other Data	9




Unused Data	10




Summary	12




National Criteria	13







References	-....•	28

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                                    TABLES
                                                                          Page




1.  Acute Toxicity of Hexachlorobenzene to Aquatic Animals  	 14




2.  Chronic Toxicity of Hexachlorobenzene to Aquatic Animals  	 16




3.  Ranked Genus Mean Acute Values with Species Acute-Chronic Ratios  ... 17




4.  Toxicity of Hexachlorobenzene to Aquatic Plants 	 19




5.  Bioaccumulation of Hexachlorobenzene by Aquatic Organisms 	 20




6.  Other Data on Effects of Hexachlorobenzene on Aquatic Organisms .... 25
                                      VI

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Introduction



       Hexachlorobenzene (HCB)  has been detected in environmental  samples  from



around the world in recent years, and  is recognized as a global-pollutant



(Ballschmiter and Zell  1980; Brevik 1981; Brunn and Manz 1982; Chovelon et al.



1984; Ciborowski and Corkum 1988; Galassi et al. 1981; Gobas and Mackay 1987;



Herve et al. 1988; Jan  and Malnersic 1980; Johnson et al.  1974; Kaiser 1977;



Kuehl et al. 1983,1984; Laska et al.. 1976; Marquenie et al.  1986; Mhlanga and



Madziva 1990; Muncaster et al.  1989, 1990; Niemi et al.  1986; Niimi 1979; Ober



et al. 1987; Paasivirta et al.  1981; Sackmauerova et al.  1977; Schmitt et al.



1985; Skaftason and Johannesson 1982;  Suns and Hitchin 1992; Swackhamer and



Kites 1988; Tarhanen et al. 1989; Tsui and McCart 1981;  Veith et al.  1979b).



Contamination of Lake Ontario with HCB and other chlorobenzenes has occurred



since 1915, with larger amounts in recent decades  (Oliver and Nicol 1982).



However, it should be noted that concentrations of HCB in Lake Ontario



sediment cores indicate a trend of deceased concentration near the surface of



the cores, an observation which correlates with decreased chlorobenzene



production since the mid-1960s (Eisenreich et al. 1989).



       HCB is  soluble  in water  to about 5 or  6  ^g/L (Abernethy et  al.  1986;



Metcalf et al. 1973; Yalkowsky et al.  1979),  and its concentrations in rivers



and lakes are generally reported in terms of ng/L  (Niimi and Cho 1981).   It



has an octanol/water partition coefficient (log P) of 6.18  (Neely et al.



1974) .  The common occurrence of HCB in  tissues of aquatic organisms can be



attributed to its high  affinity for lipids and its persistence in the



environment.  Metabolic transformation of HCB is considered to.be



insignificant (Gobas and Mackay 1987) .   Fate information on HCB indicates that



photolysis, oxidation or hydrolysis are  not important processes for this



chemical in aquatic systems  (Callahan  et al.  1979), although some photolysis



of HCB appears to occur in aquatic systems in increased amounts in the



presence of nitrogenous compounds  (Hirsch and Hutzinger 1989) .  Limited



information indicates that volatilization might be important in the absence  of



other processes  (Callahan et al. 1979).

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       Connor (1984)  estimated that HCB contributed little  to increased risk



of cancer associated with consumption of freshwater fish from contaminated



water.  Residues found in fish from the environment are usually reported in



low hg/g concentrations  (e.g., Cleland et al. 1987, I988a,b; Johnson et al.



1987; Niimi and Oliver 1989;  Peterson and Ray 1987; Schmitt et al. 1990; Suns



et al. 1991; Tarhanen et al.  1989), although some highly contaminated waters



have had fish with residues that were two to three orders of magnitude greater



(Koss et al. 1986; Kype-Hutter et al.  19"86; Luckas and Oehme 1990).  HCB did



not induce the liver microsomal mixed-function oxidase (MFO) enzyme system in



rainbow trout  (Lau and Addision 1981;  Tyle et al.  1991),  even though it has



been shown to be an inducer of cytochrome P-448 and P-450 in mammals (Linko et



al. 1986) .



       HCB  is used as  a  seed grain fungicide,  a  peptizing agent  in the



production of nitroso and styrene rubber for tires, a wood preservative, a



porosity controller in the manufacture of graphite electrodes, a  fluxing agent



in aluminum smelting, and in  pyrotechnics manufacture (Courtney 1979;



Quinlivan et al. 1975/1977; U.S. EPA 1980a; Young et al.  1980).   The degassing



of aluminum smelt with chlorine gas resulted in HCB production and river



contamination in one documented case  (Vogelgesang et al.  1986).   HCB is



largely derived as a byproduct of general chlorobenzene production (Eisenreich



et al. 1989) .  HCB wastes also originate from the production of certain



pesticides  (Cleveland et al.  1982), chlorinated solvents,  vinyl chloride



monomers, and chlorine or sodium chlorate when produced electrolytically



(Quinlivan et al. 1975/1977).  Some of the commercial formulations of HCB



contain toxic impurities, including pentachlorobenzene, polychlorinated



dibenzo-p-dioxins, and polychlorodibenzofurans  (Villanueva et al. 1974).



       HCB  loading to North American watersheds  has been shown to  occur via



atmospheric precipitation and runoff  (Johnson et al. 1987; Strachan 1985).



HCB is readily adsorbed by suspended sediments and algae (Autenreich and



DePinto 1991).  Suspended sediments, especially near industrial discharges,



have been shown to be responsible  for considerable transport of HCB in river

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systems  (Lau et al. 1989).  Elevated concentrations of HCB have been



identified in certain industrialized areas, such as the St. Clair River near



Sarnia, Ontario  (.Chan et al. 1986; Kauss and Hamdy 1985; King and Sherbin



1986; Oliver and Kaiser 1986).   Annual loadings from municipal sources were



insignificant relative to industrial loadings  (Marsalek 1986).



       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 in order to understand



the following text,, tables, and calculations.   Results of such intermediate



calculations as recalculated LCSOs 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 values.  The criteria



presented herein supersede  previous national aquatic life water quality



criteria for HCB (U.S.  EPA  1980) because these new criteria were derived using



improved procedures and additional information.  The latest comprehensive



literature search  for information for this document was conducted in April,



1993; some more recent information was included.  Data in the files of the



U.S. EPA's Office  of Pesticide Programs concerning the effects of



hexachlorobenzene  on aquatic organisms and their uses have been evaluated for



possible use in the derivation of aquatic life criteria.



       This  document  does  not contain information  concerning  the  effects of



HCB on  saltwater species.







Acute Toxicitv to  Aquatic Animals



       Data  that  could potentially be used,  according to the  Guidelines,  in



the derivation of  a freshwater Final Acute Value for HCB are presented in



Table l.  Twenty-six acute  tests were conducted with fourteen genera and



sixteen species.   The only  experimentally determined acute values were at



concentrations that are at  least 1,000 times  the water solubility limit.  In



those tests where  concentrations of HCB approached the solubility limit,

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 mortalities were insufficient to calculate definitive acute values .

'Therefore,  the LC50 or EC50 was reported as a "greater than"  value.

       Some acute exposures were continued  for longer than 96 hr with no

 resultant mortalities.   For .example,  survival of  adult crayfish,  Procambarus

 clarki,  was unaffected over a period of 20 days at a mean HCB concentration of

 27.3  ng/L,  and the  largemouth bass,  Micropterus salmoides.  was unaffected over

 10  days  at  25.8./ig/L (Laseter et al .  1976;  Laska  et al .  1978) .   Because so few

 quantitative Species Mean Acute Values are available for freshwater  species,

 the procedures described in the Guidelines cannot be used to calculate  a Final

 Acute Value.   However,  the data strongly suggest  that acute toxicity does not

 occur at concentrations below the water solubility limit for HCB of  6
 Chronic Toxicitv to Aquatic Animals

       The available data- that are useable according to the Guidelines

 concerning the chronic toxicity of HCB are presented in Table 2.   Six chronic

 tests  have been conducted with five species.   The oligochaete,  Lumbriculus

 variegatus ,  was exposed to a mean concentration of 4.7  ^g/L of HCB for 49 days

 with no significant adverse effects upon survival,  growth or asexual

 reproduction (Nebeker et al .  1989).   In a 7-day life-cycle test with  the
                                                           i
 cladoceran,  Ceriodaphnia dubia.  HCB did not cause any measurable effect upon

 survival or reproduction at concentrations as high as 7.0 MSF/L (Spehar 1986).

 The amphipod,  Hvalella azteca.  was unaffected in its survival and reproduction

 in two tests at mean HCB exposure levels of 4.5 and 3.8 \iq'/l> for 30 days

 (Nebeker et al . 1989).                                    :

       Rainbow  trout,  Oncorhvnchus mvkiss, were exposed to HCB  in a 90 -day

 early  life-stage test (Spehar 1986) .   No adverse effects on hatching,

 survival,  or growth were observed at the highest tested concentration of 3.68

 ng/L (Table 2) .  Similarly, fathead minnows,  Pimephales promelas,  were not

 affected at exposures up to 4.8 M9/L in a 32-day early  life-stage test (Ahmad

 et al.  1984; Carlson and Kosian 1987).  Survival at hatch, survival at 32

 days,  and wet weight were the same at all exposure concentrations as  in the

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control.



       Because chronic values  are  not  available  for  any species,  neither  a



Final Chronic Value nor a Final Acute-Chronic Ratio can be calculated for HCB.







Toxicitv to Aquatic Plants



       Data  are available  on the toxicity of  HCB to  two species  of  aquatic



plants (Table 4).  Geyer et al. (1985) reported that the green alga,



Scenedesmus subspicatus. was not affected in 4 days by HCB at a concentration



of 10 jjg/L,  Calamari et al.  (1983) observed that a concentration above water



solubility  (27 M9/D caused a slight growth inhibition  (12 percent) in a 4-day



exposure of Selenastrum capricornutum.   Based on these available data, a



Final Plant Value, as defined in the Guidelines, cannot be obtained.







Bioaccumulation                                        ;



       The  available data  that are useable according to the Guidelines



concerning HCB accumulation are shown in Table  5.  HCB exposure of the



oligochaete, Lumbriculus variegatus. at concentrations between 0.8 and 5.8



/Kj/L for 28-49 days resulted  in bioconcentration factors  (BCFs)  ranging from



4,600 to 106,840  (Nebeker et  al. 1989, 1990; Schuytema et al'. 1988).  Oliver



(1987) exposed mixed oligochaetes  consisting of mainly Tubifex tubifex and



Limnbdrilus hoffmeisteri to 0.250  M9/L HCB f°r  79 days.  With a whole body



lipid content of  1.0 percent, the  BCF (both normalized and not lipid-



normalized) was 3,120.                                \



       Nebeker et al.  (1989)  showed, that  whole body  BCFs for  amphipods,



Gammarus lacustris. exposed to HCB concentrations of 0.4 to 3.3 M9/L ranged



from 18,750 to 33,000  in 28-day exposures.  Lipid-normalized BCFs based on a



lipid concentration of  5.3 percent ranged from  3,538 to 6,226.-  The BCF  (not



lipid-normalized)  for  this same species exposed to  4.5 M9/L f.or 30 days in



another study was 41,200  (Schuytema et al. 1990).   The amphipod, Hvalella



azteca. was exposed to  HCB  for  30  days in 10  separate  tests at concentrations



between 0.3 and 4.5 jxg/L  (Nebeker  et  al.  1989).  Whole body lipid content was

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2.3 percent.   Lipid-normal!zed BCFs were between 9,617 and 32,609.  Three



exposures of Hvalella azteca to HCB for 28 days at 1.1 to 5.7 /ig/L yielded



whole body BCFs that were not lipid-normalized between 13,900 and 23,000



(Schuytema et  al. 1988,  1990).  Oliver and Niimi (1983) reported that'



equilibration  had not yet occurred after a 119-day exposure of rainbow trout



to HCB at a concentration of 0.00032 ng/L, at which time the BCF was  12,000



{1,412, lipid-normalized).  An exposure to 0.008 fJ.g/L resulted in a BCF of



20,000 (2,353, lipid-normalized)  with the trout.  Veith et al.  (1979a)



determined the BCF for rainbow trout to be 5,500 after a 32-day exposure



period.  Common carp, Cyprinus carpio, exposed to 0.366 ng/L of HCB for 21



days with whole body lipid content ranging between 1.5 and 6.5 percent had a



lipid-normalized BCF of  approximately 3,020  (Tadokoro and Tomita 1987) .



       HCB  residues  in  fathead minnows  continually  increased  in 28-day tests



to concentrations that were from 19,635 to 39,000 times greater than  the



concentrations of HCB in water (U.S. EPA 1980b;. Kosian et al. 1981).   Percent



lipid determinations for this species were different in these studies and



yielded lipid-normalized BCFs of 10,908 and 3,361 to 4,577, respectively.  In



ciddition, HCB was found  to be in equilibrium with the water concentrations in



one study (U.S. EPA I980b) but not in the other (Kosian et al.  1981)   after 28



days.   Following a rapid uptake during the first week of exposure, HCB



residues in fathead minnows gradually increased through 115 days  (Veith et al.



1979a) .  HCB residues in the minnows were from 16,200 to 45,700 times greater



than concentrations in water following exposures of 32 to 115 days.   Lipid-



normalized BCFs ranged from 2,132 to 6,013.  Carlson and Kosian (1987)



obtained similar BCFs that ranged from 4,568 to 7,026  (lipid-normalized) for



fathead minnows exposed  for 32 days.  Fathead minnows exposed to 1.3  and 2.0



M9/L of HCB for 28 days  had BCFs (not lipid-normalized) of 29,600 'and 50,600



(Schuytema et al.  1988).  Other BCFs for fathead minnows exposed :tp 0.3 and



3.8 /Kj/L for 28 days in  five separate exposures ranged from 12,240 to 21,140



(Nebeker et al. 1989).    Lipid-normalized BCFs for these fish (6.9 percent



lipid) were between 1,774 and 3,064.   Bioconcentration equilibrium was

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reached in this study after the 28-day exposure period which is in contrast to



the results shown by Kosian et al.  (1981).  Higher BCFs  (not lipid-normalized)



of 95,400 and 93,800 were reported  for fathead minnows by Schuytema et al.



(1990) .



       In  a  test with a mixture .of chlorinated benzenes,  an  apparent  steady-



state BCF of 15,660 was obtained  for HCB with the guppy, Poecilia reticulata



within 7 days (Konemann and Van Leeuwen 1980) .  One-year-old male guppies



exposed to 1.96 ng/L of HCB for 42  days had a non-normalized BCF of 19,500 and



a lipid-normalized BCF of 6,500 (Opperhuizen and Stokkel 1988).  Green



sunfish, Lepomis cvanellus. bioconcentrated HCB to a level that was 21,900



times the water concentration  (Veith et al. 1979a) .



       Other studies  showed that coho  salmon (Oncorhvnchus kisutch) and green



sunfish accumulated HCB when fed  contaminated food (Leatherland and Sonstegard



1982; Sanborn et al. 1977).  Crayfish  (Procambarus clarki)  exposed at a



contaminated field site to a mean HCB concentration of 74.9 M9/L had a mean



whole-body concentration factor of  1,464  (Laseter et al. 1976).  Fox et al.



(1983) found a direct correlation between HCB concentrations in surficial



sediments of Lake Ontario and HCB concentrations in oligochaetes that inhabit



the sediments.  They also reported  that HCB accumulation was greater at the



higher trophic  levels.  One study showed that uptake via food might be more



important than direct uptake from water for top carnivores,  particularly  in



waters where HCB concentrations are very low  (Niimi and Cho 1980).   However,



other studies indicate that the water might be a more important source for HCB



accumulation than the food  (Callahan et al. 1979).  Studies have indicated



that HCB and other lipophilic, persistent chlorinated organics are passed from



parent to offspring via the yolk  and oil of the fish egg (Niimi 1983; Westin



et al. 1985) .  Survival and growth  of larvae might be affected by this route



of uptake in some fish species.



       Several  investigators have  studied the elimination of HCB from a



variety of aquatic species.  Norheim and Roald  (1985) determined the half-life



of HCB in rainbow trout that had  been injected intraperitoneally and

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maintained at a water temperature of 7°C to be 81,  146,  and 139 days in liver,


fat, and muscle, respectively.  Niimi and Cho  (1981) reported the biological


half-life of HCB to be 224 to 770 days  in rainbow trout fed HCB and maintained


at a water temperature of 15°C.   In a subsequent study (Niimi  and Palazzo


1985) ,  HCB-fed rainbow trout held at 12 and 18°C had HCB half-lives  of 173 and


198 days, respectively, whereas fish held at 4°C did not eliminate HCB.  In


contrast, studies by U.S: EPA (1980b) and Nebeker et al.  (1989) show  that HCB


elimination is rapid, approaching zero  in less  than 30 days, once fish are


placed in clean water.   'Crayfish that  were exposed to 74.9 ^g/L for  10 days


under field conditions eliminated about 15% of  the HCB after three days in


clean water.  Males eliminated 47% and  females  64% after 25 days  (Laseter et


al.  1976) .   These authors also found that largemouth bass eliminated  from 73.1


to 91.4% of the whole body HCB residue  during 13 days in uncontaminated water.


McKim e't al.  (1985) studied the uptake  efficiency of HCB and 13 other


chemicals by rainbow trout gills.  HCB  was among the chemicals most


efficiently removed from water by gills.  However, it did not appear  to be


removed much more efficiently than several chlorophenols, which by comparison


to HCB,  have a reduced capacity for bioaccumulation.

                        .•
      The  high accumulation levels of  HCB in  aquatic organisms .can  be


explained by its slow ra;te of conversion to water soluble metabolites,


combined with an efficient uptake from  water due to its high n-octanol water


partition coefficient of 6.18.  However, experimentally determined rates of


depuration appear to be substantially more rapid than those for other


persistent chemicals, such as DDT.  Callahan et al.  (1979), in a review of the


water-related environmental fate of HCB, suggest that biomagnification of HCB


in aquatic systems probably does not occur.         '           >


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


tissue,  as defined in the-Guidelines,  is available for HCB.  Therefore, a


Final Residue Value cannot be calculated.                      :

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Other Data                                                 :



       Additional data on the lethal and sublethal  effects'Of  HCB on



freshwater species are presented in Table 6.  A green alga, Ankistrodesmus



falcatus. was unaffected in a 4-hr exposure to 3 pig/L (Wong et al.  1984) .



Chlorophyll was  slightly reduced (<10 percent) in the green alga, Chlorella



pyrenoidosa,  following a 46 hr exposure to 1 ng/L of HCB, but growth was



stimulated, as measured by chlorophyll production after 90 days  (Geike and



Parasher 1976).  Reduced growth was shown in this species when they were



exposed to 10,000 ^g/L  (Parasher et al. 1978), a concentration much higher



than the water solubility limit for HCB.  The green alga Oedoaonium cardiacum



bioconcentrated  HCB 623 times above the concentration in water after 7 days



(Laseter et al.  1976).  No effect was observed in the protozoan, Colpidium



campvlurn, exposed to HCB at 10,000 M9/L for 43 hr  (Dive et al. 1980), and  .



Yoshioka et al.  (1985) found that the 24-hr EC50-for the protozoan,



Tetrahvmena pyriformis, was greater than 50,000 pig/L.  However,  Figueroa and



Simmons  (1991) showed that a concentration of 2.0 M9/L caused a'50  percent



reduction in the DNA content of the diatom, Cvclotella meneghiana.  following a



48 hr exposure.  The authors discussed the use of the DNA measurement as a



quantitative parameter for determining the toxicity effects of chlorobenzenes



on algae.



       Daphnia magna were not adversely affected after  24  to  28.3 hours  at



concentrations, that exceeded the solubility of HCB in water (Calamari et al.



1983; Sugatt et  al. 1984).  However, a concentration of IS./xg/L  caused a 50



percent inhibition in reproduction  (EC50) in daphnids after 14 days  (Calamari



et al. 1983) .  Another cladoceran species, Moina macrocopa, was  not adversely



affected  (i.e.,  mortality was <50 percent) at water solubility  (Yoshioka et



al. 1986).  Shucked mussels  (Elliptic complanata) bioconcentrated HCB 3,650



times after 11 days of exposure  (Russell and Gobas 1989).  Nebeker  et al.



(1989) observed  that a concentration of 3.3 fig/L caused significant mortality



(40 percent)  to  the amphipod, Gammarus  lacustris. after 28 days,  although  this



mortality was not much greater than that observed  in other HCB  concentrations.

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The authors felt that the mortalities were probably not due to HCB because all



surviving animals appeared healthy and normal.  Crayfish, Procambarus clarki,



exposed to higher concentrations ranging from 27.3 to-36.1 ^g/L appeared to



accumulate much less HCB than amphipods.   BCFs  (not lipid-normalized) for this



species were between 75 and 149  (Laseter et al.  1976).



       Due  to  insufficient  deaths,  LCSOs  could not be determined for  rainbow



trout exposed to 27 jig/L for 24 hr (Calamari et al. 1983), for fathead minnows



exposed to 3.8 Mg/L for 28 days  (Nebeker et al.  1989), or for guppies exposed



to >320 ng/L for 14 days (Konemann 1979,1981).  However, 5 ng/L caused



hepatopancreas damage in crayfish and 3.5 to 25.8 ^tg/L caused liver,  kidney



and gallbladder damage in largemouth bass after 10 days of exposure  (Laseter



et al.  1976).  Studies with largemouth bass showed that BCFs  (not lipid-



normalized) ranged from 18,200 to 44,400 after 15 days of exposure (Laseter et



al. 1976) .







Unused Data



       Some data  on the  effects  of  HCB on aquatic  organisms  and their uses



were not used because the studies were conducted with specie's that are not



resident in North America  (e.g., El Nabawi et al. 1987; Hattori et al. 1984;



Huang et al. 1986; Kammann et al. 1990; Kasokat et al. 1989; Sugiura et al.



1984; Venant and Cumont 1987).  Data were not used when HCB was a component of



a mixture or wettable powder  (e.g., Gjessing et al.  1984; Mayer and Ellersieck



1986; Poels et al. 1980).  Anliker et al.  (1988), Chiou  (1985), Chiou et al.



(1977), Connell and Schuurmann  (1988), Davies and Dobbs  (1984), Glass et al.



(1977), Gobas and Mackay (1987), Gombar  (1987),  Hawker and Connell (1986,



1988),  Kaiser et al.  (1984), Klein et al.  (1984), Koch  (1982a',b) , Matsuo



(1980,1981), Oliver  (1984a), Sabljic  (1987), Sabljic  and Protic  (1982), and



Schuurmann and Klein  (1988) compiled data  from  other  sources.:  Johnson and



Finley  (1980) was not used because the data from  this publication were re-



ctnalyzed and subsequently published in another  article.  Studies were not used



if the exposure duration was not specified  (e.g.,  Blum and Speece 1991).
                                       10

-------
       Tests were not used when only physiological  effects  or  enzyme  activity



were measured  (e.g., Gluth and Hanke 1984; Hanke et al.  1983;  Law and Addison



1981).   Schmidt-Bleek et' al.  (1982) did not adequately describe the methods



used for the toxicity tests.  Toxicity data were not used when the test was



conducted in distilled water  (e.g., Abernethy et al.  1986; Bobra et al.  1985).



       Studies  of HCB residues in aquatic  organisms were  not used when there



were insufficient tissue residue data or accompanying data on HCB



concentrations in the water to determine" a bioconcentration or bioaccumulation



factor  (e.g., Atuma  and Eigbe 1985; Clark et al.  1984; DeVault 1985; Evans et



al. 1982; Giesy  et al. 1986; Glass 1975; Heida 1983;  Jaffe and Hites 1986;



Kaiser  1982; Kaiser  and Valdmanis 1978; Keck and Raffenot 1979; Kuehl et al.



1980,1981; Niimi 1979; Norstrom et al. 1978; Paasivirta et al.1983a,b;



Pennington et al. 1982; Schmitt et al. 1985; Schuler et al. 1985; Swain 1978;



Veith et al. 1977,1981; Wiemeyer et al. 1978; Zitko 1971).  Results of studies



in which HCB was administered by gavage, injection, or in the food were not



used (e.g., Clark and Mackay  1991; Devault et al.  1988;  Hall et al.. 1987;



Holmes  1988; Ingebrigtsen and Skaare 1983; Niimi and Oliver 1988; Safe et al.



1976; Saiki and  Schmitt 1986).                        '        .



       Studies  using radiolabeled HCB in which only radioactivity was  measured



in the  water or  in exposed organisms were not used (e.g., Clark and Mackay



1991; Freitag 1987;  Freitag et al. 1982,1984,1985; Geyer et al;. 1981,1984;



Mailhot 1987; Niimi  and Oliver 1988; Schauerte et  al. 1982).  Results of



laboratory bioaccumulation tests were not used when the test was not flow-



through or renewal  (e.g., Belluck and Felsot 1981; Korte et al. 1978; Lu and



Metcalf 1975; Metcalf et al.  1973; Zitko and Hutzinger 1976),  or when the



concentration of HCB in the test solution was not  adequately measured (e.g.,



Isensee 1976; Isensee et al.  1976; Knezovich and Harrison  1988).  Studies of



the bioaccumulation  of HCB by organisms inhabiting contaminated sediment were



not used  (Knezovich  and Harrison 1988; Oliver 1984b; Schrap and Opperhuizen



1989) .   Bioconcentration data were not used when  the duration of exposure was



not specified  (e.g.,  Neely et al.  1974), or if the exposure duration was short
                                       11

-------
and if evidence for Che establishment of an equilibrium between water and fish



was not presented  (e.g., Opperhuizen et al.  1988).



       Studies on  the  dynamics and transport of  HCB  at  the  sediment-water



interface were not used  (Baker et al.  1985;  Gerould and Gloss 1986; Karickhoff



and Morris 1985).   Studies were not used if HCB residues in environmental



samples were only reported as  "less than" values or were below analytical



detection limits  (e.g., DeVault et al. 1988; Hall et al.  1987; Holmes 1988;



Saiki and Schmitt 1986) .







Summary



       Data  on the acute toxicity of HCB  are available  for  sixteen  species.of



freshwater animals.   In nearly all tests, the highest concentrations were not



acutely toxic and only greater-than ECSOs or LCSOs could be reported for this



document.  The definitive LCSOs that could be calculated ranged from 7,000 to



13,500 M9/L, which are approximately 1,000 to 2,250 times the water solubility



limit.  Because not enough definitive acute values exist to meet the minimum



data base requirements according to the Guidelines,  a Final Acute Value for



HCB and freshwater organisms cannot be calculated.



       Chronic toxicity tests with HCB  have  been conducted  using  five  species



of freshwater animals.  No adverse effects were observed with any of the



species at the highest tested concentrations,  which were near water



solubility.   Therefore, neither a Final Chronic Value nor a Final Acute-



Chronic Ratio for this chemical and freshwater organisms can be calculated.



       Tests  with  HCB  and two species  of  algae were  conducted and only  slight



adverse effects were  observed at concentrations above water solubility.   No



Final Plant Value, as defined  in the Guidelines, can be calculated for HCB and



freshwater plants.



       Bioaccumulation of HCB has been determined with  a  variety  of freshwater



species.  Invertebrate BCFs  that are not lipid-normalized ranged from 3,120 to



106,840 compared to 5,500 to  95,400 for fish.  Hexachlorobenzene accumulates



to high levels in freshwater organisms due to its high n-octanol water
                                       12

-------
partition coefficient combined with its slow rate of conversion to water



soluble metabolites, but  it appears to depurate more rapidly than other



persistent chemicals indicating that biomagnification in aquatic systems



probably does not occur.  Because there is no FDA action limit or an available



maximum dietary intake value derived from a chronic feeding study or a long-



term field study with wildlife, a Final Residue Value for HCB cannot be



calculated.



       Other  data  from  a variety of  tests  showed,  in general,  that  HCB  did not



adversely affect the survival, growth and reproduction of the tested species



at or below the water solubility limit of 6 ^g/L.  Although HCB caused some



sublethal effects such as DNA reduction and histological damage at



concentrations below this solubility limit, the ecological implications of



theses effects are unknown, and water quality criteria based upon these



endpoints cannot be derived at this time.



       Based  on the  above test results,  not enough data  are  available



according to the Guidelines to calculate a Final Acute Value, Final Chronic



Value, Final Plant Value  or a Final Residue Value for HCB.







National Criteria       •         •



       The  procedures described in the  "Guidelines for Deriving  Numerical



National Water Quality Criteria for the Protection of Aquatic Organisms and



Their Uses" do not allow  for the derivation of national criteria for



hexachlorobenzene (HCB) 'based on the available test information.  The



available data indicate .that HCB does not cause significant adverse effects on



the survival, growth and  reproduction of freshwater aquatic life at or below



the water solubility limit of approximately 6
                                       13

-------
                                          Table 1.  Acute Toxicity of Hexachlorobenzene to Aquatic Animals
Species

Hydra (adult).
Hydra sp.
Oligochaete,
Lumbficulus varieaatus
Snail (adult),
Aplexa hypnomm
Cladoceran,
Cefiodaphnia dubia
Amphipod,
Gammarus lacustris
Amphipod (adult),
Gammarus pseudolimnaeus
Amphipod,
Hyalella azteca
Amphipod,
Hvalella azteca
Crayfish (adult),
Procambarus clarki
Crayfish (juvenile),
Procambarus sp.
Stonefly (nymph),
Pteronarcys sp.
Midge (3rd-4th instar),
Tanvtarsus dissimilis
Rainbow trout (0.5 g),
Oncorhvnchus mvkiss
Rainbow trout (juvenile),
Oncorhvnchus mykiss
Rainbow trout (juvenile).
Method*

S.M
F.M
S.M
S.M
F,M
S.M
F.M
F.M
F.M
S.M
S.M
S.M~
F.M
F.M
F.M
Hardness
{rrsg/L as
Chemical CaCOJ
FRESHWATER SPECIES
97% 49.7
2535
97% 49.5
45
25-35
97% 49.5
25-35
25-35
-
-
97% 47.4
97% -40.7
97% 44.3
97% 44.3
45 46
LC50
or EC50
(J/Q./I-1

>65.9
>4.7
>77.6
>7.0
>3.3
>77.6
>3.8
>4.5
>27.3
>5.2
>69.7
>58.V
>80.9
>80.9
>3.76
Species mean
Acute value
if/g/U

>65.9
>4.7
>77.6
>7.0
>3.3
>77.6
-
>4.5
-
>27.3
>69.7
>58..V
-

>80.9
Reference

Sabourin et al. 1986
Nebeker et al. 1989
Sabourin et al. 1986
Spehar 1986
Nebeker et al. 1989
Sabourin et al. 1986
Nebeker et al. 1989
Nebeker et al. 1989
Laseter et al. 1976;
Laskaet al. 1978
Laseter et al. 1978;
Laska et al. 1978
Sabourin et al. 1986
Call et al. 1983.
Ahmad et al. 1984;
Call et al. 1983
Ahmad et al. 1984;
Call et al. 1983
Spehar 1986
Oncorhvnchus mvkiss

-------
  Table 1.  (continued)


Species
Fathead minnow (30 days).
Pimephales promelas

Fathead minnow (0.7g),
Pimephales promelas
Fathead minnow (juvenile).
Pimephales promelas
Channel catfish (0.8g),
Ictalurus punctatus
Channel catfish 11. 3g),
Ictalurus punctatus
Channel catfish (sac fry).
Ictalurus punctatus
Bluegill (1.5g),
Lepomis macrochirus
Bluegill (1g),
Lepomis macrochirus
Bluegill (1.6g),
Lepomis macrochirus
Largemouth bass.
Micropterus salmoides
Largemouth bass (0.5g),
Micropterus salmoides



Method'
F,M


S.U

F,M

S.U

S,U

S.U

F.M

S,U

F,U

F,M

S.U


Hardness
tmg/L as
Chemical CaCO,)
97% 45


96% 44

2535

96% 44

96% 40

96% 272

97% 45.4

96% 272

96% 272

-

96% 272


LC50
or EC50
U/Q./LI
>7


> 10,000

>3,8

13,500

• > 100,000°

7,000

>78.4

1 2,000

> 1 ,000

>25.8

12,000


Species mean
Acute value
Urti/Li Reference
Veith et al. 1983a,b;
Ahmad et al. 1984;
Carlson and Kosian 1987
Mayer and Ellersieck 1986

> 10,000 Nebeker et al. 1989

Mayer and Ellersieck 1986

Mayer and Ellersieck 1986

9,720 Mayer and Ellersieck 1986

Cadet al. 1983

Mayer and Ellersieck 1986

12.000 Mayer and Ellersieck 1986

Laseter et al. 1976;
Laskaet al. 1978
12,000 Mayer and Ellersieck 1986


• S = static; R = renewal; F = flow-through; M = measured; U = unmeasured.
° Not used in calculation of Species Mean Acute Value.

-------
                                        Table 2. Chronic Toxicity of Hexachlorobenzene to Aquatic Animals
Species
Oligochaete,
Lumbrlculus variegatus
Amphipod.
Hvalella azteca
Amphipod,
Hvalella azteca
Cladoceran,
Ceriodaphnia dubia
Rainbow trout,
Oncorhvnchus mykiss
Fathead minnow,
Pimephales promelas
Hardness
(mg/L as
Test' Chemical CaCOJ
FRESHWATER
LC - 25-35
LC - 25-35
LC - 25 35
LC - 45
ELS - 43-47
ELS 97% 44-46
Chronic
Limits
Ua/L)"
SPECIES
>4.7C
>4.5C
>3.8e
>7.0e
>3.68C
>4.8C
Chronic
Value
uva/Ll
>4.7
>4.5
>3.8
>7.0
>3.68
>4.8
Reference

Nebeker et al. 1989
Nebeker et al. 1989
Nebeker et al. 1989
Spehar 1986
Spehar 1 986
Ahmad et al. 1984;
Carlson and Kosian 1987
' LC = life-cycle or partial life-cycle; ELS =  early life-stage.




° Measured concentrations of hexachlorobenzene.




' Highest tested concentration; no tested concentration caused an unacceptable effect.

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


Rank*

14

13

12

11

10

9

8



7

6

5

4

3
Genus Mean
Acute Value
0/a/LI

12,000

12.000

> 10,000

9,720

>80.9

>77.6

>77.6



>69.7

>65.9

>58.1

>27.3

>7.0


Species
FRESHWATER !
Largemouth bass.
Micropterus salmoides
Bluegill,
Lepomis macrochirus
Fathead minnow,
Pimephales promelas
Channel catfish.
Iclalurus punctatus
Rainbow trout.
Oncorhynchus mykiss
Snail,
Aplexa hypnorum
Amphipod,
Gammarus pseudolimnaeus
Amphipod,
Gammarus Lacustris
Stonefly.
Pteronarcvs sp.
Hydra (adult).
Hydra sp.
Midge,
Tanvtarsus dissimilis
Crayfish,
Procambarus clarki
Cladoceran.
                                          Species Mean
                                           Acute Value
                                             12,000


                                             12,000


                                            >10,000


                                             9,720


                                             >80.9


                                             >77.6


                                             >77.6


                                              >3.3

                                             >69.7


                                             >65.9


                                             >58.1


                                             >27.3


                                              >7.0
Species Mean
Acute-Chronic
    Ratio'
        Ceriodaphnia dubia

-------
 Table 3. (Continued)
Rank*
2
1
Genus Mean
Acute Value
(JJQ/L)
>4.7
>4.5
Species
Oligochaete,
Lumbriculus varieqatus
Amphipod,
Hyalelja azteca
Species Mean
Acute Value
>4.7
>4.5
Species Mean
Acute-Chronic
Ratio'
C
_c
 * Ranked from most resistant to most sensitive based on Genus Mean Acute Value.



 ° From Table 1.



•' Acute-chronic ratio was not calculated, as values ot both numerator and denominator were "greater than" values.
 Fresh water




      Final Acute Value = Cannot be calculated (see text)




      Criterion Maximum Concentration =  Cann. , be calculated




         Final Acute-Chronic Ratio = Cannot be calculated (see text)




      Final Chronic Value  = Cannot be calculated

-------
                                                           Table 4. Toxicity of Hexachlorobenzene to Aquatic Plants
             Species
                                             Hardness
                                             (mg/L as        Duration
                              Chemical        CaCCs)        (days)
                     Effect
                                                                                                       Concentration
                                                                                                                        Reference
Alga,
Scenedesmus subspicatus

Alga.
Selenastrum capricornutum
                                             98.0
FRESHWATER SPECIES

        4            EC50


        4            EC12
                                                                                                           -27
                                                                                                                        Geyer et al. 1985
                                                                                                                        Calamari et al. 1983
              Analytical grade.
vo

-------
Table S. Bioaccumulation of Hexachlorobenzene by Aquatic Organisms
Species
Oligochaete,
ILumbficulus vanegalus)
Oligochaete,
(Lumbficulus variegatus)
Oligochaete,
(Lumbficulus variegatusl
Oligochaete,
(Lumbficulus variegatus)
Mixed oligochaetes,
(Tubifex tubitex and
Limnodrilus hoffmeisteri)
KJ
Amphipod,
(Gammarus lacustris)
Amphipod,
(Gammafus lacustris)
Amphipod,
(Gammarus lacustfis)
Amphipod,
(Gammarus lacustris)
Amphipod,
(Gammarus lacustris)
Amphipod,
(Gammarus lacustris) . ••„-•.'..
Amphipod,
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Concentration in
Chemical Water Uro/LI'
0.8
2.2
1.0
1.9
4.7
5.8
0.250
0.4
0.8
1.0
1.8
3.3
4.5 .
0.3
0.4
Duration
(days)
28
44
49
49
49
28
79
28
28
28
28
28
30
30
30
Tissue
FRESHWATER SPECIES
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body . .
Whole body
Whole body
Percent
Lipids


1.8
1.8
1.8

1.0
5.3
5.3
5.3
5.3
5.3
-
2.3
2.3
BCFor
BAF"

4,600
13,200
50.000"
106,840"
47.450"
25,100
3.120
20,000
18,750
33,000
29,440
23,940
. , 41,200 .
28,330
35,000
Normalized
BCF or BAF<


-
27,800
59,400
26,400
-
3,120
3.774
3,538
6.226
5,555
4,517
•
12,317
15.217
Relerence
Schuytema et al. 1988
Schuytema et al. 1988
Nebeker et al. 1989
Nebeker et al. 1989
Nebeker et al. 1989
Schuytema et al. 1990
Oliver 1987
Nebeker et al. 1989
Nebeker et al. 1989
Nebeker et al. 1989
Nebeker et al. 1989
Nebeker et al. 1989
...Schuytema et al. 1990
Nebeker et al. 1989
Nebeker et al. 1989

-------
Table 5.  (Continued)
Species Chemical
Amphipod,
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Amphipod.
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Amphipod,
(Hvalella azteca)
Rainbow trout (juvenile),
Oncorhvnchus mvkiss
Rainbow trout (juvenile).
Oncorhvnchus mvkiss
Rainbow trout (fingerling).
Oncorhvnchus mvkiss
Concentration in Duration
Water U/g/L)1 (days)
0.5 30

0.7 30

0.7 30

OB 3O
.O »JV/
2.0 30

3.3 30

3.8 30

4.5 30

1.1 28

2.5 28

5.7 28

0.00032 119 -
0.008 105

32

Percent
Tissue Lipids
Whole body 2.3

Whole body 2.3

Whole body 2.3

Whole body 2.3

Whole body 2.3

Whole body 2.3

Whole body 2.3

Whole body 2.3

Whole body

Whole body

Whole body

Whole body 8.5 ...
less digestive
tract
Whole body 8.5
less digestive
tract
Whole body

BCF or
BAF"
28.000

40,000

38,570

75.000

24.500

22.120

26,580

38.220

13,900

23.000

20.700

. .12,000V
20,000*

5,500

Normalized
BCF or BAFC
12,174

17,391

16.770

32,609

10,652

9.617

11,557

16,617



-



1,412
2,353
,


Reference
Nebeker et al. 1989

Nebeker et al. 1989

Nebeker et al. 1989

Nebeker et al. 1989

Nebeker et al. 1989

Nebeker et al. 1989

Nebeker et al. 1989

Nebeker et al. 1989

Schuytema et al. 1988

Schuytema et al. 1988

Schuytema et al. 1 990

Oliver and Niimi 1 983
Oliver and Niimi 1983

Veith et al. 1979a


-------
Table 5. (Continued)
                                           Concentration in     Duration
                              Chemical      Water uvg/U*        (days)       Tissue
Percent      BCF or
            BAF"
 Normalized
BCF or BAFC   Reference
Common carp (20-30g),
Cyprinus carpio
Fathead minnow (0.73g),
Pimephales promelas
Fathead minnow (juvenile).
Pimephales promelas
Fathead minnow (juvenile),
Pimephales promelas
Fathead minnow (juvenile).
Pimephales promelas
Fathead minnow (juvenile),
Pimephales promelas
Fathead minnow (newly
hatched fry),
Pimephales promelas
Fathead minnow (30 days),
Pimephales promelas
Fathead minnow (90 days),
Pimephales promelas
Fathead minnow (adult),
Pimephales promelas
Fathead minnow (adult),
Pimephales promelas
Fathead minnow (adult),
Pimephales promelas
Fathead minnow (juvenile), 97%
Pimephales promelas
Fathead minnow (juvenile), 97%
0.366
0.18
0.17
0.16
0.15
0.18
-5
-5
-5
-5
-5
-5
4-4.8
0.3
21
28
28
28
28
28
-115
-40
115
-32
-115
-32
32
32
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
Whole body
- -^ 	
-1.5-6.5'
1.8
9.22
9.52
8.52
9.27
7.6"
7.6"
7.6"
7.6"
7.6"
7.6"
-
3.8
-
19.635
33,000'
32,000"
39,000'
37.000'
45,700
18,200
1 7,800
18,500
16,600
16,200
20,200-
23,400
26,700
3,020'
10,908
3.579
3,361
4,577
3,991
6,013
2,395
2,342
2,434
2.184
2,132
' -
7,026
Tadokoro and Tom
U.S. EPA 1980b
Kosian et al. 1981
Kosian et al. 1981
Kosian et al. 1981
Kosian et al. 1981
Veith et al. 1979a
Veith et al. 1979a
Veith et al. 1979a
Veith et al. 1979a
Veith et al. 1979a
Veith et al. 1979a
Ahmad et al. 1984
Carlson and Kosian
 Pimephales promelas

-------
Table 5.  (Continued)
   pecies
                                            Concentration in      Duration
                              Chemical      Water U/q/LI'         (days)      Tissue
Percent     BCF or
 lipids       BAF"
 Normalized
BCF or BAFC    Reterence
Fathead minnow (juvenile), 97%
Pimephales promelas
Fathead minnow (juvenile), 97%
Pimephales promelas
Fathead minnow (juvenile), 97%
Pimephales promelas
Fathead minnow (44 mg),
Pimephales promelas '
Fathead minnow (150 mg),
Pimephales promelas
Fathead minnow (juvenile),
Pimephales promelas
Fathead minnow (juvenile),
Pimephales promelas
Fathead minnow (juvenile).
Pimephales promelas
Fathead minnow (juvenile).
Pimephales promelas
Fathead minnow (juvenile),
Pimephales promelas
Fathead minnow
(Pimephales promelas)
Fathead minnow
(Pimephales promelas)
Guppy (1 yr old 
-------
'   Measured concentration of hexachlorobenzene.




"   Bioconcentration factors (BCFs) and bioaccumulation factors (BAFs) are based on measured concentrations of hexachlorobenzene in water and tissue.




c   When possible, the factors were normalized to 1 % lipids by dividing the BCFs and BAFs by the percent lipids.




"   A quartz sand substrate was provided for the test organisms.




•   The hexachlorobenzene concentration had not equilibrated between water and fish, and the value presented is based upon residues in the fish tor the exposure period indicated.




1    The study was conducted with fish at several lipid content levels, and a single overall lipid-normalized BCF was reported.




9   The hexachlorobenzene concentration had not equilibrated between water and fish at 28 days, and the value presented is based upon residues in the fish on day 28.




"   Reported by Veith (1980).

-------
                                      Table 6. Other Data on Effects of Hexachlorobenzene on Aquatic Organisms
Species
            Hardness
            (mg/L as
Chemical     CaCOJ
                                                                                                    Result
                                                           Duration
Effect
FRESHWATER SPECIES
Green alga.
Ankistrodesmus falcatus
Green alga,
Chlorella pyrenoidosa
Green alga,
Chlorella pyrenoidosa
Green alga,
Chlorella pyrenoidosa
Green alga,
Oedogonium cadiacum
Diatom,
Cyclotella meneghiniana
Protozoan.
Colpidium campylum
Protozoan,
Tetrahvmena pyriformis
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran (<24 hr),
Daphnia manna
Cladoceran ( - 5 days),
Moina macrocopa
Mussel,
Elliptic complanate
Amphipod,
-
-
-
-
-
Reagent
grade
-
Analytical
grade
Analytical
grade
Analytical • . - 	
grade
134
Analytical
grade
-
25 35
4 hf
46 hr
90 days
76 hr
7 days
48 hr
43 hr
24 hr
24 hr
• 14 days •
28.3 hr
3hr
11 days
28 days
EC50
Reduced
chlorophyll
Increased
chlorophyll
Reduced growth
BCF
EC50
(DNA reduction)
No effect
EC50-
EC50
EC50 • - •-. .
EC10
(immobilization)
LC50
BCF = 3,650
40% mortality
>3
1
1
10,000
623
2
10,000
> 50,000
>27
- 16
>6«
>6*
-0.28
3.3"
Reference
                                                                                                                 Wong et al. 1984
                                                                                                                 Geike and Parasher 1976
                                                                                                                 Geike and Parasher 1976
                                                                                                                 Parasher et al. 1978
                                                                                                                 Laseter et al. 1976
                                                                                                                 Figueroa and Simmons
                                                                                                                 1991

                                                                                                                 Dive et al. 1980
                                                                                                                 Yoshioka et al.  1985
                                                                                                                 Calamari et al. 1983
                                                                                                                 Calamari et al. 1983
                                                                                                                 Sugatt et al. 1984
                                                                                                                 Yoshioka et al.  1986
                                                                                                                 Russell and Gobas 1989
                                                                                                                 Nebeker et al. 1989
Gammarus lacustris

-------
Table 6.  (Continued)
                                            Hardness
(mg/L as
Species Chemical CaCO,)
Crayfish (juvenile),
Procambarus clarki
Crayfish (male),
Procambarus clarki
Crayfish (female),
Procambarus clarki
Crayfish (male),
Procambarus clarki
Crayfish (juvenile),
Procambarus clarki
Rainbow trout. Analytical 320
Oncorhynchus mvkiss grade
Atlantic salmon,
Salmo salar
Fathead minnow (juvenile), - 25-35
Pimephales promelas
Guppy (2-3 mo), - 25
Poecilia reticulata
Largemouth bass,
Micropterus salmoides
Largemouth bass,
Micropterus salmoides
Largemouth bass,
Micropterus salmoides
Largemouth bass/ ' '• - -
Micropterus salmoides
Largemouth bass,
Micropterus salmoides
Duration
10 days
1 0 days
1 0 days
1 0 days
1 0 days
24 hr
96 hr
28 days
1 4 days
1 0 days
1 0 days
1 5 days
1 5 days
1 5 days
Effect
Damaged the
hepatopancreas
Whole body
BCF = 149
Whole body
BCF = 83
Whole body
BCF - 112
Whole body
BCF = 75
LC50
Accumulation
coefficient = 753
No mortality or
effects upon
growth
LC50
Damaged the liver
and kidney
Damaged the
gallbladder
Whole body
BCF - 44,000
Whole body
BCF - 33,800
Whole body
BCF = 18.200
Result
u/g/U
5
27.3
27.3
36.1
36.1
>27
6.6
3.8
>320
3.5
25.8
2
2
2
Reference
Laseter et al. 1976
Laseter et al. 1976
Laseter et al. 1976
Laseter et al. 1976
Laseter et al. 1976
Calamari et al. 1983
Zitko 1977
Nebeker et al. 1 989
Konemann 1979. 1981
Laseter et al. 1976
Laseter et al. 1976
Laseter et al. 1976
Laseter et al. 1976
Laseter et al. 1976

-------
            Table 6.  (Continued)
Species
Largemouth bass,
Micropterus salmoides
Hardness
(mg/L as
Chemical CaCO,l
-
Duration
1 5 days
Effect
Whole body
BCF = 32.500
Result
t^g/U
2
Reference
Laseter et al.

1976
            ' The tested concentration was at saturation, which was estimated to be pg/L based on Metcalf et al. (1973).

            " See text.
ro
-j

-------
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                                       40

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