DRAF
                                                                    8/19

       Revised Section B of Anbianc Water Quality Critarla far Arsenic

                             AQUATIC TOXICOLOGY*



Introduction

     Arsenic is found  in all living organisms, including  chose  in  aquatic

379terns.  Little is known about the mechanisms of arsenic toxicity to aquatic

organisms; however, arsenic readily foras stable bonds  to sulfur and carbon

in organic compounds.  Like mercury, trivaleat arsenic  reacts with sulfhydryl

groups of proteins; enzyne inhibition by this mechanism may  be  the primary

mode of  toxicity.  Pentavalent arsenic does not react with sulfhydryl groups

as readily but nay uncouple oxidative phosphorylation (Towler,  et  al. 1977;

Schiller, et al. 1977).

     The chemistry of  arsenic  in  water  is complex,  consisting  of  chemical',

biochemical, and geocheaical  reactions  which  together control  the  concentra-

tion,  oxidation  state, and form of arsenic  in water (Callahan,  et  al. 197S;

Holm,  et al.  1979;  Scudlark and Johnson, 1982).   Four  arsenic  species common

in natural  waters  are  arsenate (-1-5),  arsenite (+3), methanearsonic acid and

dlmethylarslnic  acid.   In aerobic water,  arsenite  is slowly  oxidized to

 arsenate at neutral  pB,  but  the  reaction proceeds measurably in several days

 in strongly alkaline or acidic conditions.   Because the chemical and

 toxicological properties of the forms appear to  be quite different and  the
 *An understanding of the Guidelines for Deriving Numerical National Water

 Quality Criteria for the Protection of Aquatic Life and Its Uses (Stephan, et

 al. 1983) is necessary in order to understand the following text, tables, and

 calculations.

-------
eoxicicies of  Che  forms  have  not  been shown co  be  additive,  che  data  for



crlvalenc Inorganic arsenic,  pentavalent  Inorganic arsenic,  nonosodium




methanearsonate  (MSMA) and other  arsenic  compounds will be creaced



separately.  Methods  have  been developed  for separately measuring these forms



of arsenic in  water (Grabinski, 1981; Irgollc,  1982).



     Because of  the variety of the forms  of arsenic and lack of  Information



about  their relative  toxicities,  no available analytical method  is  known  to



be ideal  for expressing  aquatic life criteria for  arsenic, but dissolved



arsenic (operationally defined as the arsenic chat passes through a 0.45  uo



membrane  filter)  is probably  che  best available method.  Measurement  of



dissolved arsenic is  compatible with all of the data used to derive criteria



for  arsenic because precipitate was not observed in any of the seats- On



samples of ambient water this method is intended to measure all* forms of



arsenic that are toxic  to  aquatic life or can be readily converted to toxic



foras  under  natural conditions.  In addition, this method is intended to



exclude several  forms,  such as arsenic that is part of minerals, clays, and



sand or  is  strongly  sorbed to partlculate matter,  that are not toxic  and  are



not  likely  to  become  toxic under  natural conditions.  Measurement of



dissolved arsenic does  not require special effort or equipment.   Measurement



of dissolved arsenic  probably does not require immediate analysis in  che



field because  the ratio of dissolved to undlssolved arsenic probably  will not



change substantially  in short periods of time.  This is also che least



rigorous  of the measurements (a)  which are compatible with the available



toxicological data without using hypothetical extrapolations and (b)  for



which it is usually acceptable to assume that no harm will result from



measured or calculated concentrations in ambient water that are below



national criteria.

-------
                                                                               3
     Dissolved arsenic should also be a useful measurement for raonicoring




effluents and dilution of effluent with receiving water before aeasurement




should demonstrate whether the receiving water can decrease the concentration




of dissolved arsenic because of sorptioa.  Measurement of both dissolved




arsenic and total recoverable airsenic (U.S.  EPA., 1979) in ambient water or




effluent or both can be useful.  For example, there  is aore cause for concern




if total recoverable arsenic is above the appropriate criterion, even though




dissolved arsenic Is below the criterion, than there is if both are below  the




criterion.  If a national criterion is possibly unacceptable  for a particular




situation, a site-specific criterion (U.S.  SPA, 1982) can be derived.




     Unless otherwise noted, all concentrations reported herein are expected




to be essentially equivalent to dissolved arsenic concentrations.  All




concentrations are expressed as arsenic, not as che  chemical  tested.  The




criteria presented herein supersede previous aquatic life water quality




criteria for arsenic (U.S. EPA, 1976a, I960) because these new criteria were




derived using improved procedures and additional information.  The literature




search  for  this document was conducted in October,  1981; some newer




information vas also used.








Acute Toxicity to Aquatic Animals




     Data are available on  the acute  toxicity of crivalenc  Inorganic  arsenic




to  fourteen species  in ten  families (Tables  1 and 3).  Two crustacean




families, Gammaridae and Daphnidae, are  much more sensitive  than  the other




tested  invertebrate  and fish families, with  the acute  sensitivities ranging




from 379 ug/1 for Gammaridae to 97,000 ug/1  for Chlronomidae.  Inglis and




Davis  (1972) found  that hardness did  not affect the toxicity  of  trivalent

-------
inorganic arsenic  co  the  bluegill.   Fachead minnows  were much less  sensitive




Co arsenic crlsulfide (Table 6)  Chan co  sodium arsenice (Table 1).




     Family Mean Acute Values (Table 3)  were calculated as  geometric means  of




Che available  Species Mean Acute Values  (Table 1).   For trivalent inorganic



arsenic, Che Species  Mean Acute  Values  for daphnids  were within a factor of 6




and those for  saLnonids and cyprinids were within a  factor  of 2.   Of the



fourteen families  for which acute values are available, the two crustaceans,



Gammaridae and Daphnidae, are ouch more  sensitive than the  others.   Both the




most sensitive family, Gammaridae, and  the most resistant  family,



Chironomidae,  are  invertebrates, but the one is 110  times aore sensitive Chan



the other.  A.  freshwater Final acute Value of 273.7  
-------
aore than 400 times  aore  sensitive  than.  Che  lease  sensicive  family,




Ictaluridae.



     Not enough  acute  values  are  available  for  calculation of  freshwater




Final Acute Values  for pentavalent  inorganic  arsenic  or MSMA.



     Data are available on the  acute  toxicity of  trivalent inorganic  arsenic




to saltwater species in three fish  and six  invertebrate  families  (Tables  I




and 3).  The fish species tested  were the least sensitive with a  range of



LCSOs from 12,700 ug/1 for the  sheepshead minnow  to 16,033 ag/1 for the




Atlantic silverside.  Among the invertebrates,  the copepod,  Acartia clausi,




was the most sensitive (LC50  =  508  ug/1) and  the  polychaete  worm, Neanthes



arenaeeodentata, was the  least  sensitive (10,120  ug/1).  In  addition,




Alderdice and Brett (1957) obtained a 48-hour LC50 of 3,300  -ig/1  wich arsenic



crioxide to chum salmon (Table 6).   Holland,  et al. (1960) decarained a



10-day LC54 of  3,787 ug/1 for the pink salmon,  whereas Curtis, et al. (1979)




reported a 96-hour IC50 of .24,700 ug/1 for  arsenic trisulfide  in  tests with



juvenile white  shrimp (Table 6).   A saltwater Final Acute Value of 242.3  ag/1



was calculated  for trivalant inorganic arsenic  (Table 3)..



     Data  are available for pentavalent  arsenic vlch  cvo salcwacer species.




Pentavalent  arsenic was less toxic to a aysid (LC50 = 2,319  ug/1) Chan



trivalent  (LCSO • 1,740 ag/1),  but more  toxic to the  scud whose Species Mean



Acute  Values  are 2,957 ug/1  for pentavalent arsenic and  8,204  ag/1  for



trivalent  arsenic.  Not enough data are available to  calculate a  saltwater



Final  Acute Value for pentavalent inorganic arsenic.








Chronic Toxicity to Aquatic Animals



      Three chronic  tests  have been conducted on trivalent  inorganic  arsenic



with  freshwater  species  (Table 2).  A life-cycle test with Daphnia magna

-------
(Lima, et al. Manuscript) resulted in a chronic value of 912.8 ng/1  based  on




chronic limits of 633.4 and 1,315.4 ug/L.  The 96-hour LCSO  for  this species




la the same study was 4,340 ug/1, resulting in an acute-chronic  ratio  of




4.755.  The chronic values for the fathead oinnow and flagfish exposed  to




sodium arsenite were approximate!? the same.  The 96-hour L.C50 values  Ear  the




two species were also similar and the acute-chronic ratios were  4.636  and




4.395, respectively.




     Data on  the chronic toxicity of arsenic  to saltwatar species  are




available for only one species, Mysldopais bahia.  In a 35-day life-cycle




test on  sodiua arsenite, no effaces were observed at 530 Mg/1, whereas 1,270




affected reproduction and significantly reduced survival.  These results




provide  chronic  limits for crivalant  inorganic arsenic of 630-1,270  
-------
1,400 ug/1 and Che comparable acute value was 7,400 ig/1, resulting in  an




estimated acute-chronic ratio of 8.7.




     The fathead minnow vas approximately 3 times aore sensitive on a chronic




basis to pentavalent than to crivalent arsenic, but Daphnia magna appeared  co




be equally sensitive to both forms of inorganic arsenic.  No chronic tests




have been conducted vith MSMA or any other organic arsenic compound.








Toxieity to Aquatic Plants




     Adverse effects were observed at concentrations  ranging from 2,320 ug/1




for  3 species of algae and one  submerged plane  co over 59,000 ag/1  for  the




alga Selenascrum eapricornutum  (Table 4).  Except for S_. eapricornutum,




values  reported for aquatic planes exposed to  sodium  arsenite are comparable




to  Che  acute values for some of che  more sensitive  invertebrate  species




(Table  L) and  co che chronic values  reported  for the  fathead minnow and




flagfish  (Table 2).



     Concentracions of  pencavalent  inorganic  arsenic  which  caused  adverse




effects on  six species  of  freshwater algae ranged from 43  to 202,000 iig/1




(Table  4).  A  L4-day EC50  value of  48 ug/1 obtained  foe  che most sensitive




alga, Scenedesmus  obliquus, was 13  cimes  lower than  Che  lowest  acute value




and approximately  L9 tiaes lower Chan che only chronic value available for




pencavalent inorganic  arsenic.   Data on the  sensitivity  of  S_.   eapricornutum




co  both pencavalenc and crivalenc inorganic  arsenic  is widely  variable and




appears co  depend  on  che  kind  of coxicicy  test used  (Richcar,  1982).




      Data on the  toxicity of  crivalenc  arsenic co  saltwater plants  is




available for  four species of  microalgae and two  species of macroalgae (Table

-------
4).  Growth of  Che  saltwater diatoms, Skeleconema coscacum  and Thalassiosera



aestivalis, was affected  at 20  >ig/l  and 22 'ig/1, respectively, and




photosynthesis  of S." costatua vas  reduced at  5 ug/1.   3oney, et al. (1959)




showed that trivalent arsenic inhibited the development of  sporelings in the



red oacroalga,  Plumana elegaas, at 577 ug/1.  In addition,  formation of mature




cystocarps by another red macroalgae, Champia parvula, was  prevented at 95




•ig/1 and growth of  female plants was reduced  at 145 ug/l.



     Data on the  toxicity of pentavalent arsenic to saltwater plants is




available for four  species of oicroalgae and  one species of nacroalgae (Table




4).  Based upon these data, there  is no significant differences between the



toxicity of pentavalent and trivalent arsenic to the  plant  species  tested.




Thursby and Steele  (Manuscript) found that  phosphate  decreased the  toxicity




of pentavalent  arsenic to Champia  parvula,  but did not affect the  toxicity of




trivalent arsenic.








Bioaecumulation



     Bioconcentration tests have been conducted on trivalent and pentavalent




inorganic arsenic and a number of  organic arsenic compounds with a  variety of




freshwater  fish and invertebrates  (Table 5).  Ho bioconcentration  factor



(BCF)  was greater than 10 except that a value of 17 was obtained for  trivalent



inorganic  arsenic with a snail  (Spehar, et  al. 1980). An early life-stage




cast with  the  fathead minnow on sodium  arsenate (Deroe, 1982) showed  that  the



3CF decreased  with, increased exposure concentrations  in the water.  BCFs were




slightly  lower  (down to 1.2) in exposure concentrations that caused adverse




effects  than  that reported for a no  effect  concentration  (Table 5).

-------
     One acudy by Oladimeji, et al. (1982) showed chat Che pretreanaent of




rainbow trout to sodium arsenite enhanced che elimination of a subsequent



dose of arsenic.  Additional results indicated that fish retained less



arsenic after 4 weeks of exposure  Chan after 2 weeks.



     In the one bioconcentration test on arsenic with a saltwater species,  a



3CF of 350 was obtained with the oyster, Craasostrea vlrginica, after 112




days of exposure (Zaroogian, 1982).  In a 4-day test Nelson, et al.  (1976)



obtained a BCF of IS with the bay  scallop.



     No Final Residue Value could  be determined because no maximum




permissible tissue concentration is available cor arsenic.








Other Data



     Comparison of data  for fish in Tables 1 and 6  indicates that in almost



all cases, arsenic toxicity increased with increased duration of exposure.



One value for the bluegill (Hughes and Davis, 1967) was an exception



resulting in a low 48-hour LC50 of 290 ug/1.  A specialized pallatized  form



of sodium arsenite was used which  aay have accounted for  its high toxicity.



The invertebrate data were too variable  Co indicate a  trend in toxtcity in



regard  to duration of exposure.



     Spehar, et al. (1980) compared  the  coxicitles  of  different foras of



arsenic in the same water.  In 28-day tests, trivalent inorganic arsenic



(arsenic  trioxide) was more  toxic  to  the  scud, Gammarus pseudolianaeus, than



arsenic pentoxide, sodium dimethyl arsenate and disodium methyl arsenate.



Survival  of stoneflies,  snails and rainbow trout was not  adversely  affected



when exposed to any of the compounds at  the concentrations tested.

-------
                                                                               /o
     Two studies on  the  efface  of  environmental  factors on  the  toxieity of




arsenic Co  freshwater  organisms have  been  reported.  Sorenson  (1976c)  shoved




chat increased  water temperature decreased the median  lethal  time  of green




sunfiah after exposure Co two concentrations of  sodium arsenate  (Table 6).



Lima, et al. (Manuscript) found that  che toxicity of tcivlent  inorganic




arsenic to  Daphnia nagna was decreased  by  about  a factor of 3  when food was



added in 43- hour  tests  compared to exposures Ln uhich food was  not added.



Additional  exposures showed that trivalent arsenic did not  affect  additional




unfed animals  from 48  to 96 hours, indicating that the lack of food in these



tests was  not  too  stressful.  Sodium arsenite' increased albinism in channel




catfish (Wester-nan, and Birge, 1973).



     Exposures  of  eabryos and larvae of rainbow  trout  and  goldfish to



trivalent  inorganic  arsenic resulted in values that were  several cines Lower



•than those for older juvenile stages of these species  (Tables  L  and 6), and



these values were  lower than the chronic values  in Table  2.  The lowest value



obtained  in any test on arsenic, however,  was 40 ug/l  from a  7-day exposure



of embryos and larvae of che toad, GasErjohryne  earolinensis,  to trivalent




inorganic arsenic  (Birge, 1973).  This value is  nearly a  factor of 2  lower



than the  freshwater Final Chronic Value for trivalent  inorganic arsenic..



      Bryan (1976)  exposed che  saltwater polychaete  wora,  Nereis diversieolor,



 to sodium arsenite  and estimated  che 192-hour LC50  to  be  greater than 14,500



•ig/1 (Table 6).   Sodium  arsenite  caused other effects  which include depressed



oxygen consumption  rate  and behavioral changes  in mud  snails  exposed  to



 sodium arsenite at  concentrations of arsenic greater  than 2,000 ug/L  far  72




 hours (Haclnnes and Thurberg,  1973).

-------
Uauaed Data



     Much infomaclon on Che effects of arsenic on aquatic life could ROC be




used because Che studies were not conducted with species chat ace resident in




North America.  Papers by Dabrovski (1976), Faladino (1976), and Paladino and




Spotila  (1978) were not used because control survival was too low.  Studies



by Anderson (1944), Grindley (1946), Eipper (1959), Stanley (1974), Ingrolic,



et al. (1977), and Spotila and Paladino (1979) were not used because




Insufficient detail was reported about such items as use of controls and



control  survival or because methodology problems occurred in che cescs which



made  Che results questionable.  Tests by Jones (1940), Jones (1941), Heir and




Sine  (1970), Schaefer and Pipes (1973), and Devisprased and Chowdary (1981)



were  not included because an unacceptable dilution wacar was used.



      Papers by Belding (1927), Surber (1943), The Ontario Water Resourcas




Commission (1959), Lawrence (1958), Hllcibran (1967), Chriscensen (1971),



Penrose  (1975), Christen3en and Tucker (1976), Conway (1973), Oladiaeji, ec



al. (1979), Brunsklll, et al. (1980) and Chrlstensen and Zielski (1980) were




not used because the concentrations causing effects or che effact endpoincs



were  noc clearly reported or defined.  One paper by Johnson (1978) was not



Included because the fish were not acclimated to che test water for a



sufficient amount of time after collection from  che field.  A study by



Passino  and Kramer (1980) on Che effects of arsenic on Lake Superior Cisco



fry was  noc used because  fry were obtained from  eggs and spera of two




different species.



      Reviews by Chapman, et al. (1968), Thompson, ec al. (1972), U.S. EPA



 (1975, 1976b), and Phillips and Russo (1978) only contain data chat were




published  elsewhere.  Several papers dealing with che accumulation of arsenic




 in aquatic organisms, including those by Wiebe,  ec al. (1931), Ellis (1937),

-------
Ellis, at al. (1941),  Oupree (I960),  Sohacki  (1968), Re ay (1972),  Co pel and,




ee al. (1973),  Harden  (1976),  Sandhu  (1977),  Foley, ec al.  (1978), Uagemann,



ec al. (1978),  Sorenson,  ec al.  (1979,  1980), were not used because wacer




concentrations  during  Che test varied unaccepcably or were  unknown.   3CFs




calculated  by Isensee, ec al.  (1973), Schuch, ec  al.  (1974),  Wool son, ec  al.



(1976),  and Anderson,  ec  al.  (1979)  were not uaed because  chey were




calculated  from microcosm or model ecosystem  studies in  which  water




concentrations  decreased  with time or were obtained after shore exposures



before steady-state was reached.  Results eeported by Thomas,  ec  al.  (1980)




were  noc used because  arsenic was one of ten  metals in a mixture.








Summary



      The chemistry of  arsenic in wacer  is complex and  the  fora present  in




solution is dependent  on such environmental conditions as Eh,  pH,  organic



content, presence of suspended solids,  and sediment.  The  relative coxicicies




of  the various  forms of arsenic  apparently vary from species to species.   For



 crivaletit Inorganic arsenic acute values for  fourteen  freshwater  animal




 species  ranged  from 879 ig/1 for a scud co 97,000



 4g/l for a midge, but the three acute-chronic ratios only  ranged  from 4.68 co




 4.90.  The five acute values for pentavalent  inorganic arsenic covered  about



 the same range, but the single acute-chronic  ratio was 28.7.  The six acute




 values  for MSMA ranged from 3,243 ug/1 to 1,403,000 ag/1.   The freshwater



 residue data indicated that arsenic  is not bloconc en traced  to  a high  degree



 but Chat lower forms of aquatic life may accumulate higher  arsenic residues



 than fish.  The low bioconcencration and short half-life of arsenic in  fish

-------
tissue suggest that residues should not be a problem to predators of  aquatic




life.



     The  freshwater plant data  indicate that aquatic plants differ  a  great




deal as to their sensitivity to trivalenc and pentavalenc arsenic.  In



comparable tests,  the alga, Selenastrum capricornutun, was 45  times more



sensitive to  sodium arsenate than  to sodium, arsenite, although other  data




present conflicting information on the sensitivity of this alga to  sodium



arsenate. For trivalent  inorganic arsenic, many plant values  were  in the



same  range as the  available chronic values  for  freshwater animals;  for



pentavalent  arsenic several plant  values were lover  than the one available




chronic value.



      The  other toxicological data  revealed  a wide range of  toxicity based on



casts  with a variety  of  freshwater specias  and  endpoints.   Tests wich earl'/



"  "   -::--;  --nasred  ca  be  che  raosc sensitive indicator of  arsenic  toxicity.



'.a_-da ooc^inad  froa  this type  of  test with trivalent  inorganic arsenic were



lower than  chronic values obtained in Table 2 for  this  compound.  The lowest



effect concentration  for arsenic  and  freshwater organisms was  40 ig/1 and was




reported  for trivalent inorganic  arsenic.



      Mine species of  saltwater  animals gave acute values  for  trivalent



inorganic arsenic from 508  tig/1 to 16,030  ug/1  and  the  single  acute-chronic



ratio was 1.945.  The only values available for pentavalent  inorganic arsenic



were for cwo invertebrates and were between 2,000  and 3,000 -ig/1.  Trivalenc



 and pentavalent inorganic arsenic are equally toxic to various species of



 saltwater algae, but the sensitivities of the species range from 5 to more



 than 1,000 -ig/I.  In a test with an oyster, a BCF  of 350 was  obtained for




 trivalent inorganic arsenic.

-------
                                                                                 ' '-j
                                                                               f   I
National Criteria


     To protect  freshwater  aquatic  life  and  its uses,  In each 30 consecutive



days:  (a)  the average concentration of  dissolved trivalent inorganic  arsenic



(operationally defined as the trivalent  inorganic arsenic that passes  through



a 0.45 am membrane filter)  should not exceed 72 ug/1;  (b) Che maximum



concentration should not exceed UO ug/l;'and (c) the  concentration say be



betveen 72  and 140 ug/1 Cor up to 96 hours.   This criterion will be too high



wherever  the toad, Gastrophryae carolinensis, is an Important species.



     To protect  saltwater aquatic life and ics uses,  La. each 30 consecutive



days:   (a)  the average concentration of  dissolved trivalent inorganic  arsenic



should  not  exceed 63 'ig/1;  (b) the  maximum concentration should not exceed



120 ug/1;  and (c) the concentration aay be between 63  and 120 ug/1 for up Co



96  hours.   This  criterion will be too high wherever Steelstoneaa costatua,



Thalassiosira aestivalis, or Champla parvula are important species.


      Hoc  enough data are available  to allow derivation of numerical national



water quality criteria  for freshwater aquatic  life for pentavalent inorganic



arsenic or any organic  arsenic compound.  ?entavalent inorganic arsenic Is


acutely toxic to  freshwater  aquatic  animals ae concentrations as Low as 350



•ig/1 and an acute-chronic ratio of 25 was obtained with  Che fathead minnow.



Pentavalent arsenic aay be toxic to  freshwater aquatic plants at concentra-



 tions as low as  43 ug/1.  Honosodium aethanearsenate (MSMA) is acutely toxic



 co aquacic  animals at  concentrations as lov as 1,900 ug/1  but no data are



 available concerning chronic toxicicy to animals or toxiclcy  to plants.



      Very  few data  are available concerning the  toxicity of any fora of



 arsenic other than  trivalent Inorganic  arsenic to  saltwater aquatic life.



 The available data do show that  pentavalent inorganic  arsenic  is acutely

-------
coxic to salcwacer aniaals ac concentrations as low as  2,319 ag/1  and nay  be



coxic :B 3altva:er plants at 5-50 ug/1.  No data are  available  concerning  che



chronic toxicity of any fora of arsenic other than trivalent inorganic




arsenic to saltwater aquatic life.

-------
Table 1.  fccute toxlclty
.-senlc to aquatic animals
Species

Snail.
Aploxa hypnoruia
Cladoceran.
Cerlodaphnla retlculata
Cladoceran,
Daphnla nagna
Cladocaran,'
Daplmld reagnd
Clailocuran,
Daphnla magna
C 1 adoceran ,
Oapluila put ox
Clacoduran,
Dapltnla pulox
Cladocaran.
Oaphula pulox
Cladocardn.
Slmocophalus sarruldlus
Claductormi,
Slmocoplmlus vatulus
Scud,
Gatnnarus pseudol linnocus
Stonof ly,
Pf-oronitrcys call torn led
Mldija,
Tanytarsus dlsslmlllb
Method*

s,
s,
s.
s.
s.
s.
s.
s.
s.
s.
FT.
s.
s.

H
U
U
U
M
U
U
U
U
U
M
U
H
Chemical
FRESJI
Trlvdlonl i
Arsenic
trloxldo
Sodium
arson ltd
-
Sodium
arsonllu
Sod 1 um
ursunlto
-
Sodium
ar sen 1 to
Sodium
ar son 1 to
Sodium
arsenlle
Sodium
arsenlte
Arsenic
trloxlde
LC50
or EC50
(jjg/l)"
SPECIES
ijanlc Arson Ic
24. SOU
1,700
5.27fl
3,600
4,340
1.044
I.BOO
1.740
UI2
1.800
B79
22,040

-------
Table I.  (ContinuedI
Species

Rainbow trout,
Sdlmo galrdnurl
Brook Irout,
Sdl vol Inns I on t Ilia I Is

GoldMsh (Juvenile).
Car ass I us aurat us

Fathead  minnow,
(Juvenile)
Plmapha | es promul as

Fathuad  minnow
IJuvonl Id),
Plmopliales proinqldS

Channel  catfish
(f lnyorllny),
jctdhiTus punctattn»

Channel  catfish
(Juvoitl la),
IetaIorus punctatus

Flagflsli (try),
jjgrd^anel^la I[lorjdaa

Flaijflsn (Juvonlla),
Jordanulla H or I dag

Bluei)!!!.
Lojiomls  macrochlrus

Bluuglll,
Lajioinljs  macroch Irus

Blueglll,
Lepomls  macrochlrus
Blueylll.
Lepomls  macrochlrus
                             Mat nod*

                              S,  U


                             Ff,  M


                             ri.  M


                             FT.  M



                             Ff,  M



                              S.  U



                             Ff.  M



                             Ff.  M


                             FT,  M


                              S.  U


                              S,  U


                              S,  U


                              S,  U
                                           ChamleaI

                                            Sod luu
                                                 iro
                                            Soil 1 uin
                                           drsonl ta

                                            Sod 1 uu
                                           drsunl tti

                                            Sod luii
                                           arsunlta
                                            Sod 1 uit
                                           ar sun 1 ta
                                            Sodium
                                           dr sun 1 to
                                            Sodium
                                           dfsonlte
                                            Sodium
                                           ctrsanlta

                                            Sodium .
                                           arson Ita

                                            Sod 1 um
                                           dTbonl ta

                                            Sodium
                                           ar son 1 to

                                            Sodium
                                           dTSUnltb

                                            Sodlun
                                           drsenl Id
LC3II
or £CM
M.J40
N.'JbO
26,040
15,660
14, IUO
15,022
18.096
2U.I30
14.500
15,370
16,240
15,406
17,400
Species Mean
Acute Value
(uq/l)" Reference
13,340 Johnson & F Inlay,
1980
14.960 Card wall, et al. 1976
26,040 CdTdwell, et al. 1976
Cardwell. et al. 1976
14.900 Lima, et al.
Manuscript
Clemens & Sneed. 1959
18,100 Cardwell. et dl. 1976
Cardwell, et al. 1976
20,200 Lima, et al.
Manuscr Ipt
Ing Ms & Davis. 1972
Ing Us & Ddvls, 1972
Inglls & Davis. 1972
Johnson & Flnley,
                                                                                              1980

-------
Tobl« I.  (Continued)
                                                              LC50        Spacles Moan
                                                             or IIC50       Acute Value
Species
Bluecjlll (Juvanllo),
L spools nacrocnlrus
Cladoceran,
Daptmla magna
Cladocwan,
Oaphnla pulex
Clddocoran,
Bosailna lontjlrostrls.
Rainbow trout (2 roost.
Sal mo gdlrdnorl
Fttthaud nlttnow
(Juvanl la),
Plroaphdles promo las
Mosqiiltotl&h,
GdinUusId afllnls
Scud.
Gamroarus fascist us
Cray II ah,
Procambdrus sp.
Cutthroat trout.
Sal mo clarkl
Gotdllih.
Carasblus aural us
Fdthodd mlnnoM,
Hutliod* Chum leal (|ii]/l)"
FT, M ioJIura 41. /cO
ariu/ttto
Hoii1dV4lnu!*o<}| uu ^illu.OOO
** t
ui(>tlijnojrboiiat6
St U Moiio^oJIuin >I6,OIO
S, U Mjni>!,otl 1 um 4.9JU
mullidiiuor soiid ta
S, U MoiiOiOdliiin 2,129
(fiq/IJ-"
41,760
7,400
3,600
050
10.800
25.600
49,000
> 16 .010
506,000
>I6,OIO
4.978
2,129
iwrerance
Cord-oil, at dl. 1976
Bleslnger &
Chrlstensan, 197^
JurwlC2 A Bulkb.ua,
1980
Pass 1 no & Novak,
1962
lldlo, 1977
OaFoo, I9B2
JuroMlci & Qulktuiia,
1900
Johnson 4 FJnley,
I9UO
Andurson. et al. t97S
Johnson & F Inlay,
I9UO
Johnson & F Inlay.
I9UO
Johnson & Flnlay,
IQHA

-------
Table 1.  (Continued)
Spec las
Channul cattish,
Ictalurus punctatus
Bljaglll,
Lopomls macroclilrus
Small mouth bass
(f Ingorllngl,
Hlcropterus dolomlaul

Method11
S. U
S. U
S, U
Cliaalcal
Monosod 1 urn
moth anaar sonata
Honosod 1 UN
mothaiiodriionata
Monosod 1 urn
umth
-------
Table  I.   IContinued)
Species Method"
Four spine stick lebacK, S, U
Ape It oa quadracus
Mysld, FT. H
M/sldopsls bdhla
Amphlpod, FT, M
Ampul Isca abdlta
Aiaphlpod, FT, M
Amp&l Isca abdlta

Cll(MlC4l
Sod IUN
Htintdvdlbii
Sodliui
bodluin
Sodium
1(30 Species Mean
or EC50 Acute Value
M/J5i 14.950
t Inorganic Arson Ic
2,3»9 2,319
2,100
4,1'jU 2,95ft
Reference
Card In, 1982
Gent He, 196 1
Scott, 1981
Scott, 1981
"  S = static, ft  = roriutfal, FT - f lox-lttruujli,  U •• uummiburoJ, H -

'• Hasults 
-------
Tablw 2.  Chronic toxlclty of  arson Ic to aquatic  animals
                                    Limits     Chronic Value
      Test"
Clunlcal
                    4,340
                 912. B
4.75S
                                                                Refaranca
Clailoceran, LC
Oaphnla nagna
Fathead minnow, ELS
Plmephales promelas
Flagtlsh. ELS
Jordana 1 1 a H or 1 duo
Fathead minnow, ELS
Plmophalas promo las
Mysld, LC
Mysldopsls t>ah la

" LC = Ufa eye la or partial Ufa
"Results aro expressed as organic
Spaclas
FRESHWATER SPECIES
Trlvulant Inorganic Arsonlc
Sodium 633.4-1,315.4 912.6 Lima, et al.
arson Ho Manuscript
Sodium 2,130-4,300 3,026 Lima, at al.
arsanlta Manuscript
Sodium 2,130-4,120 2,962 Lima, ef al.
arsonlta Manuscript
Pontavalont Inoryanlc Arsonlc
Sodlun 530-1. !>00 091.6 OeFoa, 1982
ar sana re
SALTWAltK SPECIES
Trlvdlant lnori|iiiilc Ar sonic
Sodium 610-1,270 094. S Gontlltt, at al.
arsunlla 1961
cyclo, ELS - uiirly Illo slafjo.
, nol as the clioml. > .
Acuta-Chn Kat lo
Acute Vale- Chronic Valua
(jjg/l) (fiQ/ll Katlo
frlvalont li>-> , ilc Arsunlc

-------
Tabl* 2.  (Continued)
                                         Acute-Chronic Ratio
Acute Value 'Chronic Value
Spocles l|ig/l) (Jjg/l)
Fathead minnow. 14.100 3,026
Plmephales promaUi.
Hagflsh. 14,500 2,962
Jordanella llorlUaa
Hysld. 1.740 894.5
Mysldopsls bah la
Panl aval ant Inorganic Arsenic
Ratio
4.636
4.695
1.945
                   FathaaJ minnow,        25.600             091.6     20.71
                   Pjmaphdlas promo Us

-------
Table 3.  Sunnary of data In Tables I and 2 on acuto and chronic toxlclty of arsenic to aquatic animals
lank". FiMlly
Farol ly Mean
Acuto Value
dig/It
Species Neon
Acute Value
Spoclus (iig/lt
Species Mean
Acute-Chronic
Retlu
FKKSHWAfLft SPCCIES
10 Chlronoinldae
9 Contrarclildae
8 Physldad
7 Ptoronarcldae
6 Cyprlnodontlddi)
5 Cyprlnlddit
4 Ictdlurldae
3 Salmonldcia
Trlvalont
91.000
41.760
24,500
22,040
20,200
19,700
18,100
14,130
1,748
Inorganic Arson Ic
Midge,
Tanytarsus dlsblnillls
Lt»L>amls niacrochlrus
Snail.
Aplctxa hyi>normn
Stonolly,
Pluronarcyb Cdllfornlca
Fldgllbli.
Jorddnelld Horldaa
Goldfish.
Carasslus durntus
FdthOdd minnow,
Plniu|ihdlos prone las
Channul catfish,
Ictalunib punctatus
Cirook trout.
Salve) liuib funtlnal Is
Rdlnliow trout ,
SdlnM Qdlrdnurl
Cladocoritn,
Curludtipluild rotlculata
Cliidocuran,
()
-------
Tabla 3.   (ConlInued)
ink1 Family
1 Gdiwidrldae
5 Poeclllldda
4 Cyprhiluae
3 Salmonldaa
2 Oaphnldae
1 BoMiilnldae
Fdmlly Moan
Acute Valua
(i/g/n
879
PantdVdlent
49,000
25,600
10,800 '
5,161
050
•Spec 1 o&
Cladocuran,
Slmocoplidluii sorruldtus
Clddocurdn,
Slniocophdlui volulus
Scud,
GdHimarus pseudol Imnduus
Inoicjanlc Ar sonic
Mosqullof Ish,
Gdinbusla df finis
Fattiedd minnow,
Plmapdales promulds
KdlnboM trout,
Salino gdlrdnorl
CldJoceraii,
Ddphnld magna
Cladoceran,
Oaphnla pulux
ClddOCufdll,
Bosmlna loiiQlrostrls
Species Haan
Acuta Valua
812
I.BOO
879
49,000
25.600
10.800
7,400
3,600
850
Spec! as Haan
Acute-Chronic
Ratio
26.71
Moaosodlum Mdllidiiudi ionnto (MbMA)
6 Ictdlurldde
5 Ailacldaa
1.403,000
506,000
28,200
Channul cdlflsh,
1 c 1 d 1 in us puncta tuS
CiMyl Ish,
UllllKjl II.
1.403,000
506,000
1.921
-
                                                               injci'ocli 11 us

-------
Table 3.  (Continued)
ank« Family
3 Ganinurldaa
2 Salmonliiaa
1 Cyprlnldaa
Family Mean Species Mean Species Maan
Acute Value Acute Value Acute-Chronic
(iig/l) Species (fjg/D Ratio
> 16. 010
> 16. 010
3,255
Smdl 1 mou ll» bjiS,
Mlcroptuni!> dolomlaul
Scud,
Garnmarus tasclatus
Cutthrout trout,
Sdlmo clarkl
Goldfish,
Carassltis auratus
Fathead mlnnoM,
Plmapttdlus pr ana lab
SALTWATER SPECIES
414,000
>I6,OIO
>I6,OIO
4.97B
2,129
Trlvdlant Inorganic Ar^unlc
9 Atharhtldaa
a Gastorostaldaa
7 Cyprlnodontldaa
6 Nurolddu
5 Ampal Uchldaa
4 Oslrulddd
3 Pocllnlil.ia
16,033
14.950
12,700
10.120
a, 204
7,500
3.4'JO
I./40
Art antic si Ivors Ida,
Manldld inonldla
Foursplna stickleback,
Apoltes quadracus
SlioupshtaoJ minnow,
Cyprlnodon varlugalub
Polychdiitu Morin,
Hoanthob aronacaodantatd
Ainphlpod,
Anijiul IbCd abJI ta
Edbtunt oyslur,
Crassobliua vlri|lnli.d
Day scallop,
Aryupuciun Irradldii^
Mybld,
16,030
14,950
12,700
10.120
8. 204
7,500
3,490
1,740 1.945

-------
TabIa 3.  (Continued)



Rank*     Family

  I       Acartlldcui
Family Moan
Acute Value
Specl** Mean
Acut* Value
Specl«s Mean
Acute-Chronic
    Ratio
                Copopod,
                Acartla clausl
                                               508
• Hanked  from most resistant to mast  uinsltlvo bused at Family Mean Acute Value.

Trlvalent Inorganic Arsenic

     Final Acute-Chronic Ratio =• 3.816

     Fresh Mater
          Final Acute Value = 275.7

          Criterion Maximum Concentration =  (275.7  |g/l) / 2 »  137.8

          Final Chronic Value =  (275.7 jjg/l> / 3.816 =»  72.25 pg/l
     Salt water
          Final Aculo Vdluo = 242.3 jjy/l

          Criterion M^xlmun Concentrot Ion =•  (242.3 jjg/l)  /2  = 121.2

          Final Chronic  Value >  (242. J jjg/l>  / 3.UI6  »  63.50

-------
                           Tabla 4.  Toxlclty of arsenic to aquatic plants
Secies
Clicwlcal
                                                                       Result
                                                                                   Reference
FUCSIIWATEH SPECIES
Trlvolunt Inorganic Arsenic
Alga,
Cladophora sp.
Alga,
Splrogyra sp.
Alga,
Zycjriama sp.
Alga,
Salonastriun cofir Icornutum
Alga,
5 a t ana s tr un c a p r 1 cor n ut mi
Submerged plant,
Potainqfla ton t>p.
Alga,
Anklstrodesmus fjlcatus
Alga,
ScertatJasmus obllqiius
Alga,
Chlamydomonas re liihar d 1 1
A(Qtt,
Ch laiaydoingnas r al nhard j I
Alya.
Salenastriim cajirlcornutum
Alga,
Selonastrtim cnyr Icornutuni
Sodium
arbonlto
Sodlun
itrsunl ta
Sodium
ar sun 1 lu
Sodlun
arsenlta
Sodlun
or sun 1 to
Sodium
arsanlte
Pantavalunt
Sodium
Sodlun
or s anal a
Sod 1 utn
arsiinatu
Sodium
Sodium
ar scna to
Suiilum
or stinato
100< kill In
2 wks
100| kill In
2 wks
100* kill In
2 uks
Mf InliJbl t\3,000
Cowall, 1963
CoweM, I96S
Cowall. 1965
Rl chter, 1982
Rlcttter, I9B2
Cowed, 1965
Vocfca. et al. 1980
Vocka, at al. I960
Jurbwlcz & Bulkoma,
I960
PJanas & Haal«y,
1918
Rlchtar, 1962
Rlchtor, 1982

-------
TabI* 4.  (Contlnuod)
Spacles
Alga,
Sulonastruo caprlcornuluin
Alga.
Huloslro granulata
Alga,
Ochromonas vullaslaca
Bluu alga,
Mlcrocvstls aaruglnosa
Gruui alga,
Sconodasnus i^uadrlcduua

Chaalcal
Sodlun
arsanata
Sodium
arseiidtu
Sodlun
arsanata
Sodium
ar senate
Sodlun
arsanata
Ettoct
14-day EC50
Uocraasad
grouth
Decreased
Incipient
Inhibition
1 nc 1 p 1 ont
Inhibition
SALT MAI LI* SPECIES
Rasult
30.761
75
75
11,000
4.100
Reference
Vocka, at al. I9UO
PI anas & Heal ay,
1978
PI anas & Healey,
1978
Bringraami, 1915;
Brlngmami & Kuhn. 1976,
)97Ba.b
Brlngiaam. & Kuhn. I977a,
I97aa.b. 1979, tdOOb
Trlvalant Inorganic Arsenic
Alya.
SKolatonaoa costatum
Alga,
Skotetonema costatum
Alga,
Thai ass los Ira aostlvalls
Rod alga.
Champla parvula
Rod alga.
Champ la parvula
Rod alga,
P lunar la elegdns
Alga,
Totraselnils chul
llyfwjnomondi cartarou
Sodlun
ar sen Ito
Sodium
ar sen It a
Sodlun
. arson 1 ta
Sodlun
arsanlta
Sodlun
arsanlta
Sodlun
arson Ito
Sodlun
arsonlta
Sodlun
arson 1 ta
GI-UM th
Inhibition
50| decrease
C-14 uptaka
Growth
Inhibition
Pravantud matura-
tion of cystocarps
Roducud feoiala
growth
Arrastod davalop-
inoitt ut sporallngs
No grottth
tnhlbltlon
Iki growth
Inhibition
20
5
22
60-95
95-145
577
1,000
10.000
Sanders. 1979.
Sanders. 1979
Moll Ibaugh, at al.
1980
Thursby & Staala,
Manuscript
Thursby & Steal u.
Manuscript
Honey, at al. 1959
Bottlno. at al. 1978
Bottlno, at al. 1978

-------
Table 4.  (Conllnuad)
                                                                      Result
Species
Alga.
Skelatoneina cost a turn
Alga,
Skalatonema coslutuin
Alga,
Thalassloslra austlvdlls
Alga,
Te t rase 1 mis chul
Alga,
Uymanomonas carlurae
Red alga,
Chainpla parvula
Chimlcdl
Pent ova lent
bod lull
arsandla
Sod lun
ar sonata
Sod 1 un
ursuiiato
Sod lun
ursonato
Sod lun
drsoruifu
Sod lun
Effoct
Inorganic Arson Ic
Growth
Inhibition
50J dacroasu
C-14 uptako
Growth
Inhibition
ML) growth
Inhibition
No growth
Inhibition
RoduCuJ fund la
growth
13
5
22
1,000
ISO, 000
<56
Reference
Sanders. 1979
Sanders, 1979
Holllbaugh. at al.
1979
Bottlno, et al. 1976
Oottlno, at al. I97B
Thursby & Staala,
Manuscript
• Results aro expressed as arson Ic, not as the chemical.
•"Highest concentration that would nut have killed a slgnlt leant  nunibor  of  cells  In  five days.
                                                                                                                              -G

-------
                               Table 5.  Bloaccunulatlon of 'arsenic  by aquatic ergon I sax
                                Tissue
Chemical
Duration    Blocancentratlon
 (days)          Factor"        Reference
FRESHWATER SPECIES
Trlvalant Inorqqnlc Arsenic
Snail,
Staflnlcola aroarfllftata
Snail,
Ital Isoma catnpanulatum
Cladocaran,
Daplinla magna
Stor.elly,
Ptoronarcys Ucvsata
Rainbow trout.
Sal mo (jalrdnerl
Olueglll,
lepoml 5 macrochlrus

Snail.
Stafln Icola emarc] Inata
Snail,
Mellsonia campanula turn
CladocLran,
Daphhla maqna
Scud,
Gammarus pseudol Imnaeus
S tonally,
Pteronarcys dorsata
Kalntio>< trout,
balmo <]alrdnuT 1
Fathead uilnnow.
Whole
Whole
Whole
Whole
Whole
Whole

Whole
Whole
Whole
Whole
Whole
Whole
Whole
body
body
body
body
body
body

body
body
body
body
body
body
Uxly
Arsenic
trloxlde
Arsanlc
trloxlde
Arsenic
trloxlde
Ar sunk
tr loxlde
Arsanlc
trloxldo
Arsenic
trloxlde
PonTava 1 ant 1 l_n_qr>|iin_ 1 _c_
Arsenic
pentoxlde
Arsanlc
pantoxlde
Arsanlc
pen loxlde
Arsonlc
pentoxlde
Arsanlc
pentaxlde
Arsanlc
puntoxldu
Arsanlc
28
28
21
28
28
28
Arsenic
28
28
21
28
28
20
30
3
17
10
9
0
4

3
6
4
0
7
0
3
Spehar,
Spehar,
Spehar,
Spahar,
Spehar.
Barrows

Spahar,
Spehar ,
Spahar.
Spahar.
Spehar,
Spehar,
OeFoe,
at al.
at al.
at al.
at al.
et al.
. et al.

et al.
at al.
et ai.
at al.
et al.
et al.
1982
1980
I960
1980
1980
1980
1980

1980
1980
1980
1980
1980
I960
_P|raophcil6s  pr onio las
pout ox Ida
                                                                                                                                     O

-------
Table 5.  (Continued)
Species
Herb.
Hydrophlla lacustrU
Hattr hyacinth,
Clchhcrnla crasslpus
Tissue
Mho la
Whole
Alligator wood. Whole
Altornanthera phi loxoroldes
Duck wued.
Lemma minor
Snail,
Stajjnlcola oinarqlnala
Snail,
Staqnlcola emarglnala
Snail.
Met Isotna carnpatuilatuii
Snail,
Hal Isoma campanula run
Cladoceran,
Daphnja roagna
Cladocoran,
Daphnla maqna
Scud,
Gamnarus p^saudol Inuumus
Scud,
Gammarus jtsoudpl lamauus
Stoned y.
Ptu-oiitircys dor sat a
Stonolly.
Whole

Whole

Whole

Whole

Whole

Wholo

Whale

Whul a

Whole

Whole

Whole
body
body
body
body

body

body

body

body

body

body

body

body

budy

body
Choral cal
Organic AT sonic Con
Munosodlum
u» thdnotirsonate
Moiiosodlum
Monosod 1 un
uiulhaitear sonata
Mono^od 1 un
ntuthdnearbonata
Dlbodlua methyl
ar senate
Sodium dimethyl
ar senate
Dl sodium methyl
ar senate
Sodium dimethyl
or senate
DlsuJlum inuthyl
of sonate
Sodluin dlinothyl
dTbenatu
Dl sodium muhiyl
ar sona 1 o
Sodium dimethyl
urseiMte
Ulsodluio methyl
arsonule
Sod luiu dl inuthyl
Duration Bloconcantratlon
idays) Factor* Refarmc*
iipoiiiuls
42
42
42
42

28

28

28

28

21

21

28

28

2U

28

2
2
3
5

3

2

4

5

4

4

0

0

9

7




Anderson, at al.
1980
Anderson, at al .
I960
Anderson, at al.
I960
Anderson, et al.
1580
Spahar.

Spehar ,

Spehar .

Spehar,

Spehar,

Spehar,

Spohar ,

Spahar ,

Spehar ,

Spehar,

at

et

et

et

at

at

at

At

at

et

al.

al.

al.

al.

al.

al.

al.

al.

al.

al.

I9DO

1980

I9UO

1980

1900

1900

1980

I960

1980

1980
Plorondrcys dorsafa

-------
Tab la 5.  (Continued)
Spec las
Rainbow trout,
Salmo galrdnorl
Rainbow trout,
Salmo golrdnorl
Eastern oyster,
Crassobtrea virgin leu

Tissue
Whole body
Whole body
Soft parts
Chuulcal
Duration.
(days)
Dl sodium mathyl 26
ar senate
Sodium dimethyl 26
ac senate
SALTWATER SPECIES
Trl volant Inorganic
Sodluio
arsenlte
Ar sonic
112
B 1 oconcentrat 1 on
Factor*
0
0
350
Reference
Spaliar, at
Spehar, et
Zarooglan,
al. 1900
al. I960
1982
•Results are based  en  arsenic,  not thu cliunlcdl.
                                                                                                                                          o
                                                                                                                                          X

-------
labla 6.  Other data on effects of arsenic on aquatic organisms

Species

Chemical


Duration
FRESHWATER

Effect
SPECIES
Result
fog/I )"

Reference

Irlvalent Inorganic Arsunlc
Green alga,
Scenodesmus quadrlcauda
Bacteria,
Eschar Ich la coll
Protozoan,
Mlcroregma heterostoma
Rotifer,
(unidentified)
Rotifer,
(unidentified)
Cladocoran,
Daphnla mogna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla nuigna
Cladoceran,
Daphnla magna
Cladoceran.
(unidentified)
Cladoceran,
(unidentified)
Copepod (ailult)',
(unidentified)
Sodium
arsen 1 te
Sodium
arsen Ite
Sodium
arsen Ite
Sod 1 urn
arsen Ite
Sodium
arson! to
Sodium
arsen Ite
Sodium
ar sen Ite
Sodium
arsen Ite
Sodium
drsunlto
SoJIum
ar:>anlte
Sodium
dr sen 1 te
Sodium
arson! fe
96 hr
28 hrs
1 wk
16 wks
26 hrs
48 hrs
48 hrs
48 hrs
1 wk
16 wks
16 wks
Incipient
Inhibition
Incipient
Inhibition
Incipient
Inhibition
Slgnll leant popu-
Idtlut reduction
Roducud population
(monthly treatments)
EC5U
(IninoMllzatlon)
EC50
EC50 (tod)
EC50
Significant pop-
ulation reduction
Rutlucod population
(onu Iroatniont)
Reducud population
(wuokly trodtmenlb)
35.000-
46,000"
290.000
5.000
2.320
690""
3.770
1.540
4.830
4.600"
2.320
690
690""
Brlngmann & Kuhn.
I959a,b
Brlngmann & Kuhn,
I959a
Brlngmann & Kuhn, I959b
Cowell. 1965
Gllderhus. 1966
Crosby & Tucker. 1966
Lima, et al.
Manuscript
Lima, et al.
Manuscript
Brlngmann & Kuhn. I959a,
I959b
Cowell, 1965
Gllderhus, 1966
Glldorhus, 1966

-------
Table 6.  (Continued)
SpecIas

Copepod,
(unidentified)

Scud,
Gaiumarus pseudo1I ntnanus

Scud.
llyaleMa kiUckarbqckgrl

Mayfly.
Calllbaatls sp.

May My (nymph).
Caen Is dimI nota

Mayfly (nymph).
CaonIs dIm1nota

Coho salmon.
Oncorhynchus klsutch

Rainbow  trout
(embryo, larva),
Sal mo flalrdnerl

Rainbow  trout,
SaImo fla IrdnerI

Rainbow  trout (Juvenile),
Sal nip flajrdnarl

Brook trout,
SaIvolInus fontIna11s

Goldfish (Juvunllo),
          auratus
Goldfish (embryo, larva),
Car ass | us aoratos

Spottdll shlnor,
Motropls hudsonlus
                                 Choalcal

                                  Sod I urn
                                 ar sun I ta

                                  Arsonlc
                                 trloxlde

                                  Arsonlc
                                 trloxldo

                                  Arsenic
                                 trloxlde

                                  Arsonlc
                                 trloxldo

                                  V sonic
                                 trloxlde

                                  Arsonlc
                                 trlux Ida

                                  Sod I urn
                                 arsen lie
                                  Arsonlc
                                 tr 1 ox I de

                                  Arson Ic
                                 trloxlde

                                  bod 1 mil
                                 arsonl le

                                  Sod 1 urn
                                 ar sun 1 to

                                  Sodium
                                 or sun 1 re

                                  Sod 1 ma
                                 drsunl to
Duration
1 uk
7 days
• 5 days
5 days
5 days
5 days
5 mo
28 days
144 hrs
21 days
262 hrs
336 hrs
Effect
Significant popu-
lation reduction
60* mortality
70* mortality
94* mortality
25* mortality
62* mortality
riiyslologlcal
alterations.
EC50 (death and
deformity)
LC50
Ducruase In fat
wolglit yaln
LC50
LC50
Result
2.320
961
4,469
4.469
2.234
5,958
300
550
13.300
1.000
10.440
18.618
Reference
Cowell. 1965
Spehar. et al. I98(
Surber A Meehean.
1931
Surber & Meehean,
1931
Sir bar & Meehean,
1931
Sir bar & Meuhean,
1931
Nichols. 1981
Blrge. et al. 1980
Dlxon, 1980; Dlxon
Sprague, 1981
Speyer, I974j
Spoyar & Loduc, 19'
Cardwell, et al. l<
Car dwell, et al. If
                                                   7 days     ECiO (duath and
                                                              dutorml ly)
                                                  72 hrs
                                                              IC50
   490     Blrga. 1978
27.000     Boschettl &
           McLoughlln. 1957
                                                                                                                                  I/O

-------
Table 6.  (Continued)
                                                                                  Result
Species
Fathead minnow (juvenile),
Plroaphales promo las
fathead minnow (adult),
Phnophalos promo las
Fathead minnow,
Plmjtphalos jgr omglas
Blueglll (Juvenile).
Lepomls macrochlrus
Blueglll (adult),
Lepomls macrochlrus
Blueglll (Juvenile),
Lopomls macrochlrus
Blueglll (f Ingurllng),
Lepomls roacrochlrus

Largunouth bass
(embryo, larva).
Ml crop tor us salmolUus
Narrow-mouthed load
(embryo, larva),
Gastrophryne carol Inens Is
Marbled salamander
(embryo, larva),
Ambystuna opacum
Chemical
Sodium
ar sen 1 to
Sodium
ar son 1 la
Ar sonic
tribal fide
Sodium
ar son 1 to
Sodium
ar sen ltd
Sodium
arsenltu
Sodium
ar sen! to
(pellutlzod)
Sodium
arsenlte
Sodium
ar sen 1 ta
Sodium
ar sen 1 to
OurajMo.
336 hrs
-
96 hr
16 Ml '.
16 ut-.
336 1.
U .
7 u
b U../.
Lltect
^m,mmf imfm ••
I.C50
50* reduction In
AChE _hi vitro
LC'JO
Reduced survival
(ono Irualinunt)
Illblopathologltal
dltoratlons
(weekly Ireatinunts)
LC50
LCiO
tC50 (duath anil
dutcrmlly)
EC50 (doath and
deformity)
EC50 (dodth and
delormlty)
fug/0*
10,536
2,400
82,400
690
690* •••
18,328
290
42, 100
40
4,450
Reference
Cardwell, et al. 1976
Olson A Chrlstensen,
I960
Curtis, et al. I979j
Curtis & Mard, 1981
Gllderhus. 1966
Gllderhus. 1966
Car dwell, et al. 1976
Hughes & Davis, 1967
Blrge. et al. 1978
Blrge, 1978
dirge, et al. 1978
Pantayalunr hiij <|anlc Arsar>lc_
BdCtorla,
Psautionionas put Ida
Protozoan,
Chios Iplion sulcatum
Sodium
arsenatu
Sod Inn
arsondlu
16 Irs
72 hrs,
Inclplunt
Inhibition
Incipient
Inhibition
10.000
4.600
Brlngmann & Kuhn, 1976,
I977a. 1979, I980b
Brlngmann, 1978;
Brlngmann & Kuhn, 1979,
ioonk

-------
Table 6.   (Continued)
Species
Protozoan,
Chi lomonas j>aramec 1 urn
Protozoan,
Uronoma parduezl
Cladoceran,
Daujm la inaflna
Cladoceran,
Pafihnla ma;ina
Cladocoran,
Daphnla magna
Channel catfish,
Ictdlurus jiunctatus
Chdnnel catfish,
Ictdlurus punctatus
Fathead minnow (adult),
PI map t>a las jprom&las
Green sunfl&h (Juvenile),
Lepomls cvane|tus
Green sunllsh,
Lepomls cyanel lus
Green sun fish,
Louomls cyanel lus
Green suntlsh,
Lepomls cyanel lus
Green sunflsh,
Lepomls cyanel lus
Croon sunflsh,
Lepomls cvantillus
Cheat cal
Sodium
ar send la
Sodium
ar senate
Sodium
ar send 1 e
Sod luu
ar sena fa
Sod 1 KB
ar sena la
Load
ar sena ta
Sod Inn
ar send IB
Sod 1 mil
ar send to
Sodium
dr senate
Sodium
arsenal a
Sodium
dr son a to
Sodium
ar sena lo
Sod 1 urn
arsenal a
Sod 1 urn
ar sun a re
Duration
48 hrs
20 hrs
24 hrs
3 Hk!i
3 Mks
96 hrs
6 nos
39 hrs
2 wks
678 hrs
210 hrs
124 hrs
527 Irs
Effect
Incipient
Inhibition
Incipient
Inhibition
LC50
LC50
Chronic limits
LC50
UltrdStructuTdl
changes In liver
Mtf reduction In
AChE In vMro
LT50
infrastructure)
changes In 1 Ivor
LT50 (10 C)
Lf50 (20 C)
LT50 (30 C)
LI 50 (20 Cl
Result
(iig/U«
45,000
144,000
17.000
2,650
520-
1,400
>22,000
13,000
262,500
40.000
31,700
60,000
60,000
60,000
30,000
Reference
Brlngnann, et at.
Brlngmann & Kuhn,
Qrlngmann & Kuhn,
Bleslnger 4
Chrlstensen, 1972
Uleslnger &
Chrlstensen, 1972
1980
I980a
19771)


Johnson t Flnley,
1900
Sorenson A Solth,
1981
Olson A Chrlstonsen,
I960
Sorenson. I976n
Sorenson, I976b
Sorenson, I976c
Sorenson. I976c
Sorenson, I976c
Sorenson, I976c





                                                                                                                         GJ

-------
Table 6.   IContinued)
Species
Greon sunflsh,
Lopomls cyanollus
Polycbdbte norm,
Ntrols dlyerslcolor
Hud snail,
Nassarlus obsolatus
Bay scallop IJuvonlla),
Arqapectln Irradlans
Mill to shrimp
(Juvanl la),
Penaaus sat 1 turns
Pink salmon,
Oncorhyncluis florhuschd
Pink salmon,
Oncorhynchus jjpr busclm
Pink salnion.
Chun) salmon,
Oncorhynchus keta

Gnomical
Sodium
ar sonata
Sodliuu
arsuiil tu
Sod 1 imi
arsunl lu
Sod 1 mil
arsbitl lu
AT sonic
trlsuMlde
Ar sonic
Ir loxldo
Irloxldu
Arsenic
Irloxldo
Arsunlc
fr loxlJo
Result
Duration EMoct (|M|/I)*
209 hrs UT50 (30 C> 30.000
SALTWATCK bl'CCltb
Trlvaluut fncri|iin(c Arsontc
192 lirs LC50 >M,500
72 lirs 0., consumpl Ion >2,000
rjlo Uuprussod and
aluioriiiiil behavior
4 days liCK^IS
96 hrs LC50 24,700
96 hrs LCIUU 12,307
7 days 1-l'HlO 7,195
10 days IC^4 3,787
48 Irs LC50 8.330
Refer onca
Sorenson, I976c
ft-yan. 1976
Mac 1 ones A Thurbarg
1973
Nelson, et al. 1916
Curtis, et al. 1979
Holland, at al . I960
Hal land, et al. I960
Holland, et al . I960
Aldurdlca & Drutt,
1957
*   Itasults  are express*! «s arsonic,  nor  <>s the
*"  In  rlwor Mcitu*.
""• Moasurod concoiilral Ion attar  16  wuuKs  MJS 2.2UO |iij/l.
•ni'Huatiurud coiicuiHrallon alter  16  wook-  w»s 9,04(1 \uj/\.
                                                                                                                                      00

-------
                                    REFERENCES
Alderdice, D.F.  and  J.R.  Brett.   1957.   Toxic icy  of  sodium arsenice  to  young




chum saloon.   Prog.  Rep.  Pacific  Coast  Scat.  Fish.  Res.  3d.  Canada.   108:  27.








Anderson, A.C. ,  et al.   1975.   The  acute toxic icy of MSMA. to black bass (Mi-




cropcerus doloaieu) ,  crayfish  (Procambarus  so.),  and channel catfish (Ictal-




urus lacustris).  Bull.  Environ.  Contain. ToxicoL.  14:  330.








Anderson, A.C.,  ec al.   1979.   Face of  Che  herbicide MSMA in microcosms.   In:




D.D. He-sphill  (ad.),  Trace Substances in Environmental  HeaLth-XlII.   University




of Missouri,  Colvsbia,  "•  •-•v.ri..   ••  ""'-








Anderson, A.C.,  et al..  1980.   Screening of four  vascular plants for uptake  of




monosodium methanearsonate (MSMA).   Sci. Total Environ.  16:  95.








Anderson,  B.C.  1944.  The toxicity thresholds of various substances found in




industrial wastes as deterined by the use of Daohnia magna.   Sewage  Works  Jour.




16:  1156.








Anderson,  B.C.  1946.  The Coxicity thresholds of various sodium salts  de-




termined by  the use  of Daohnia magna.  Sewage Works Jour.  18: 82.








Barrows, M.E., ec al.  1980.  Bioconcentration and  elimination of selected water




pollutants by bluegill sunfish (Lepomis macrochirus).  In: R. Hague  (ed.),

-------
Dynamics, Exposure and Hazard Assessment of Toxic Chemicals.  Ann Arbor Science




Pub., Inc., Ann Arbor, Mich.  p. 379.








BeIding, O.L.  1927.  Toxicicy experiments with fish in reference co trade waste




pollution.  Trans. Am. Fish. Soc. 57:  100.









Biesinger, K.E. and G.M. Christensen.   1972.  Effects of various metals on




survival, growth, reproduction, and metabolism of Daphnia magna.  Jour.




Fish. Res. Board Can.  29: 1691.








Birgs, W.J.  1973.  Aquatic Toxicology of Trace Elements of Coal and Fly




Ash.  In: J.H. Thorn and J.W. Gibbons  (eds.1, Energy and Environmental Stress  in




Aquacic Systems.  CONF-77111&, Mational Technical Information Service,




Springfield, Virginia,  p. 219.








Birge, W.J., et al.  1973.  Embryo-larval bioassays on inorganic coal elements




and in situ biomonitonng of coal-waste effluents.  In: D.S. Samuel, et al.




(eds.), Surface Mining and Fish/Wildlife Needs in the Eastern United States,




P3 298 353.  National Technical Information Service, Springfield, Virginia, p.




97.








Birge, W.J., et al.  1980.  Aquatic toxicity tests on inorganic elements




occurring in oil shale.  In; C. Gale (ed.), Oil Shale Symposium: Sampling,




Analysis  and Quality Assurance.  EPA-600/9-80-022.  National Technical




Information  Service, Springfield, Virginia,  p. 519.

-------
Boney, A.D., ec  al.   1959.   The effects of various poisons  on  che  growth and



vitality of sporellogs  of  the red alga Plumarla elegans (Sonnem.).  Biochea.




Pharaacol.  2: 37.








Soschetti,  M.M.  and  T.F.  McLoughlin.  1957.  Toxicity of sodium arsenite co




minnows.  Sanitalk.  5:  14.








Sottino,  5T.R., et al.  1978.  The effects of arseaate and arsenite on the  growth




and morphology of the marine unicellular algae Tetraselmis chui (Cilorophyta)




and Hymenomonas  earterae (Chrysophyta).  J. Exp. Mar. Biol. Ecol.   33:  153.








Bringmann,  G.   1975.  Detecninacion of the biologically harmful efface  of  water



pollutants  by means of the retardation of cell proliferation of the blue algae




Xlcrocystls.   Gesundheits-Iag. 96: 238.








Bringmann,  G.   1978.  Determination of che biological  toxicity of vaterbound



substances  towards protozoa. I.  Bacteriovorous flagellates (model organisa:




3nto3iphon suleatunt Steia) .  Z.  Wasser Abwasser Forsch. 11: 210.








 Bringmann,  G. and R. Kuhn.   1959a.  The  toxic  effects  of waste vatar on aquatic



 bacteria, algae, and small  crustaceans.   Gesundheics-Ing. SO:   115.








 Bringmann, G. and EL. Kuhn.   I959b.  Water toxicology studies with protozoans  as




 test organisms.  Gesundheits-Ing. 30:  239.








 Bringmann, G. and R.. Kuhn.   1976.   Comparative results of  the  damaging effects



 of water pollutants against bacteria  (P'seudomonas putlda)  and  blue algae




 (Mlcrocystls  aeruglnoaa) .   Gas-Wasserfach,  Wasser-Abwasser 117: 410.

-------
Bringmann, G. and R. Kuhn.  1977a.  Limiting values for Che damaging  action  of




water pollutants to bacteria (Pseudomonas putida) and green algae  (Scenedesmus




quadrieauda) in the cell multiplication inhibition test.  Z. Wasser Abwasser




Forsch. 10: 87.









Briagmann, G. and R. Kuhn.  1977b.  Results of the damaging effect of water




pollutants on Daphnia aagna.  Z. Wasser Abwasser Forsch. 10: 161.








Bringmann, G. and R. Kuhn.  1978a.  Limiting values for the noxious effects  of




water pollutant material to blue algae (Microcystis aeruginosa) and green algae




(Scenedesmus quadricauda) in cell propogation inhibition tests.  Vom Wasser  50:




4.5.









Bringmann, G. and R. Kuhn.  1978b.  Testing of substances for  cheir toxicity




threshold: model organisms Microcystis (Diplocystis) aeruginosa and Scenedesmus




Quadricauda.  Mitt. Int. 7er. Theor. Angew. Liranol. 21: 275.








Bringmann, G. and R. Kuhn.  1979.   Comparison of toxic limiting concentrations




of water contaminants toward bacteria, algae, and protozoa in  the  cell-growth




inhibition test.  Raustech. Bauphys. Umwelttech. 100: 249.








Bringmann, G. and R. Kuhn.  1980a.  Determination of the harmful biological




effect of water pollutants on protozoa. II. Bacteriovorous ciliates.  Z. Wasser




Abwasser Forsch. 13: 26.









Bringmann, G. and R. Kuhn.  1980b.  Comparison of the toxicity thresholds of




water pollutants to bacteria, algae, and protozoa in the cell multiplication



inhibition test.  Water Res. 14: 231.

-------
Bringmann, G., et al.   1980.   Determination of  biological damage  froa water




pollutants to protozoa.  III.  Saprozoic  flagellates.   2.  Wasser Abwasser Forsch.




13: 170.








Brunskill, G.J., et  al.   1980.  Sxperineatal studies on  the  effect of arsenic on




taicrobial degradation  of organic natter and algal growth.  Can. J. Fish. Aquae.




Sci. 37: 417.








Bryan, G.W.   1976.   Heavy Metal Contamination in the Sea.  In; R. Johnson (ed.)>




Marine Pollution,  Part 3.  Academic Press.   Mew York.  p.  135.








Calabrese,  A.,  et  al.   1973.  The toxicicy of heavy necals co embryos of  the




American oyster,  Crassostrea virginica.  Mar. 3iol.  IS: 162.








Callahan,  M.A.,  et al.  1979.  Water-related environmental face  of  L29  priority




pollutants.   Vol.  I.  *PA-4AO/4-79-G29a.  National Technical Information




Service, Springfield,  Virginia.








Cardin,  J.A.  1982.  Memorandum  ca John 3. Gentile,  'J.S. Z?A., Marragansec:,




 Rhode Island.








 Cardwell, R.D., et  al.   1976.   Acute coxicity  of  seleccad toxicants co  six




 species of  fish.  SPA 600/3-76-008.  National  Technical Information Service,




 Springfield, Virginia.-

-------
Chapman, W.H., et al.  1968.  Conceatracion  factors  of  chemical  elements  in




edible aquatic organisms.  UCS.L-50564.  Lawrence Livenaore  Laboratory,




Livermore, California.








Christensen, G.ti.  1971.  Effects of metal cations and  other  chemicals  upon  the



in vitro activity of two enzymes in the blood  plasma of the white  sucker,



Catostomus commersoni (Lacepede) .  Chem.-Biol.  Interact.  4: 351.








Christensen, G.M.., and J.H. Tucker.  1976.   Effects  of  selected  water toxicants



on the  in vitro activity of fish carbonic anhydrase. Chem.-3iol.  Interact.  13:



131.








Christensen, E.R., and P.A. Zielski.   1980.  Toxicity of arsenic and PC3  co  a



green alga (Chlamydomonas).   Bull. Environ.  Contain.  Toxicol.  25:  43.








Clemens, H.P.  and K.S. Sneed.  1959.   Lethal doses of several commercial



chemicals for  fingerliag channel catfish.  U.S. Fish Wlldl. Serv.  Sci.  Repc.



Fish. Mo. 316, Washington,  O.C.








Cotiway, H.L.   1978.   Sorption of arsenic  and cadmium and their effects  on



growth, nacroautrient utilization, and photosynthetic pigment composition of



Ascarionellas  fornosa.   J.  Fish.  Res.  Board  Can.  35: 236.








Copeland, R.A.,  et al.   1973.  Trace  element distributions  in Lake Michigan



fishi A baseline study with calculations  of  concentration factors and



equilibrium radioisotope distributions.   Environ.  Res.  Group  Spec. Kept.  No. Z.

-------
Cowell, B.C.   1965.  The  effects  of  sodium  arsenice  and  silvex on the plankton




populations in farm ponds.  Trans. Am.  Fish.  Soc.  94: 371.









Crosby, O.G. and R.K. Tucker.   1966.  Toxicity of  aquatic herbicides Co Daphnia




magna.  Science  154: 289.








Curtis, M.W.,  et al.  1979.  Acute toxicity of 12  industrial  chemicals to




freshwater and saltwater  organisms.   Water  Res.   13:  137.








Curtis, M.W.,  and  C.H.  Ward.   1981.   Aquatic  toxic icy of forcy  industrial




chemicals.  Testing  in  support  of hazardous substance spill prevention




regulation.  Jour. Hydrology 51:  359.








Dabrowski, K.R.   1976.  The effect of arsenic and  embryonal development -of




rainbow trout  (Salmo gairdneri).  Water Res.  10:  793.








DeFoe, D.L.   1982.   Memorandum Co R. L. Soehar.   U.S. EPA,  DuLuch,  Minnesota.




July  9.








Devisprasad,  P.7.,  and  Y.B.K.  Chowdary.  1981.  Effects  of  metabolic inhibitors




on  the calcification of a freshwater green  algae.  Gloeotaenium




 loitlesbergarianum Hansgirg.   I.  Effects of some phocosynthecic  respiratory




 inhibitors.   Ann.  Bot.  47:  451.








 Dixon,  D.G.,  and J.3.  Sprague.  1981.  Acclimation-induced  changes  in coxicicy




of  arsenic  and cyanide  to rainbow trout, Salmo gairdneri Richardson.  J. Fish




 Biol. 18:  579.

-------
Dupree, H.K.   1960.  The arsenic concent  of  water,  plankton,  soil  and fish from




ponds created  with sodium  arsenice  for  weed  control.   Proc.  14th  Ann. Conf.,  S.




E. Assoc. Game Fish Comm.,  Columbia,  South  Carolina,   p.  132.








Zipper, A.W.   1959.  Effects  of  five  herbicides on  farm pond  plants and fish.




N.Y.  Fish Game Jour.   6: 46.








Ellis,  M.M.   1937.  Detection and  measurement of stream pollution.  Bull. Bur.




Fish. 48: 365.








Ellis,  M.M.,  ec al.   1941.. Arsenic Ln freshwater fish.  Ind. Eng. Chesn.  33:




1331.








roley,  R.E.,  ec al.   1978.  Arsenic concentrations in wacer and fish  from




Chaucauqua Lake, Mew York.  Environ. BioL.  Fish. '3: 361.








 Fowler, B.A., ac al.   1977.  Ulcrascruccural and biochemical affects  of




 prolonged oral arsenic exposure on Liver nucociondr la of racs.  Environ.  Healch




 Perspecc. 19:  197.








 Gencile, S.M.   1981.  Memorandum Co  Jonn H.  Gencile,  U.S. E?A, Narragansec:,




 Rhode  Island.








 Gencile, S.M.,  et al.   1981.  Memorandum Co John H. Gencile, U.S. EPA,




 Narragansecc,  Rhode Island.

-------
Gllderhus, P.A.   1966.   Some effects  of  sublethal concentrations of sodium




arsenite on bluegills  and  the aquacic environment.  Trans. Am. Fish. Soc.  95:




239.








Grabinski, A.A.   1981.   Determination of arsenic (III), arsenic (V),



aonooiethylarsonate,  and dlmethylarsinate by ion-exchange chroma cog raphy with




flameless atomic absorption spectromecric detection.  Anal. Cham- S3: 966.








Grindley, J.   1946.   Toxicity to rainbow trout and  minnows of  some substances



known  to  be  present in waste water discharged to rivers.  Ann. Appl. BioL. 33:




103.








Hale,.J.G.   1977.  Toxleity of metal mining wastes.  Bull. Environ.  Contam.




Toxicol.  17:  66.








Harden, J.M.  1976.  Arsenic  in water and  fish  from Lakes  Harcweell, Keowee,  and




Jocassee, South Carolina.   PB 367 571.  National Technical Information Service,




Springfield, Virginia.








 Hiltlbran, R.C.   1967.  Effects of some herbicides on fertilized fish  eggs and




 fry.  Trans. Am.  Fish.  Soc.  96: 414.








 Eolcombe, G.W.,  et  al.  Manuscript.   The  toxicity  of selected priority




 pollutants to various  aquatic organisms.   U.S.  EPA, Duluth,  Minnesota.

-------
                                                                                 H7
Holland, A.A., ec al.  I960.  Toxic effects of organic and inorganic pollu-
tants OQ young salmon and trout.  State of Washington, Oept. Fish. Res. Bull.
Mo. 5.


Hollibaugh, J.T., et al.  1980.  A comparison of Che acute toxicities of Ions of
ten heavy metals to phytoplankton from Saanick. Inlet, B. C. Canada.  Est. Coast.
Mar. Science  10: 93.


Holm, T.R., et al.  1979.  Hetergeneous  interactions of arsenic  in aquatic
systems.   la: E.A. Jenne (ed.), Chemical Modeling of Ecosystems, American
Chemical Society Symposium Series Mo. 93.  Washington, D.C.  p.  712.


Hughes, J.S.  and J.T. Davis.  1967.  Effects of  selected herbicides on  blue-
gill  sunfish. ?roc. 18th Ann.  Conf., 3.S. Assoc- Game "ish Coom., Colisibia,
South Carolina,  p. 430.


Inglis, A. and 2.L. Davis.   1972.   Effects of -water  hardness on  the  toxicity  or
several organic  and  inorganic herbicides  to  fish.  Bur. Sport  Fish Wild!. Tech.
Paper 67.   (J.S.  Qept. of Interior.


Igrolic, X.J., et  al.   1977.  Characterization  of arsenic  compounds  formed  by
Daphnia aagna and  Tetraseliia chuii from inorganic arsenate.   Environ.  Health
Perspect.  19: 61.


Igrolic, K.J.  1982.   Speciation of arsenic  compounds  in  water supplies.
EPA-600/1-82-010.   National Technical  Information Service,  Springfield,
Virginia.

-------
Isensee, A.R.,  ec  al.   1973.   Distribution  of alkyl  arsenical3  in model




ecosystem,   environ.  Sci.  Tech.   7:  841.









Johnson, C.R.   1978.   Herbicide  coxicicies  ia the  mosquieofish  (Ganbusia




affinis).  ?TOC. R.  Soc.  qd.  89:  23.








Johnson, W.W.,  and M.T.  Finley.   1980.   Handbook of  acute  toxicity of chemicals




Co fish  and  aquatic  invertebrates.   Summaries of toxicity  tests  conducted  at




Columbia National  Fisheries  Research Laboratory, 1965-1978.   U.S. Oepc. of




Interior,  Fish  & Wildlife Service,  Resource Publication 137,  Washington, O.C.








Jones, J.R.E.   1940.   A further  study of the relation  between  EoxicLty  and




solution pressure, with Pol^calis nigra as  test  animal. Jour.  Expel. 3iol.  17:




408.








Jones, J.R.E.   1941.   A study of the relative Eoxicity of  anions, with  Polycalis




nigra as test  animal.   Jour.  Expel.  3iol. 13: 170.








Jurevicz,  S.,  and  A.L. Suikeiaa.   L980.   Effects  of arsenate  on  algae, Oaohnia,




and mosquito fish.  Virginia Jour.  Sci. 31: 124.








Lawrence,  J.M.   1958.   Recent investigations on  the  use oc sodium arsenite as  an




algacide and its  effects on fish production ia ponds.   ?roc.  llth Ann.  Con;.,  S.




Z. Assoc.  Game Fish  Comm., Columbia, South  Carolina,  p. 281.








Lima, A.R.,  ec al.  Manuscript.   Acute and  chronic toxicities  of arsenic to




selected freshwater  organisms.  University of Wisconsin-Superior, Superior,




Wisconsin.

-------
Maclnnes, J.R. and R.P. Thurberg.  1973.  Effects of metals on  Che  behavior  and




oxygen consumption of Che mud snail.  Mar. Poll. Bull.  4:  185.








Mount, O.I. and T.J. Norberg.  Manuscript.  A seven-day life-cycle  cladoceran




toxicity cesc.  U.S. EPA.  DuluCh, Minnesota.








Nelson, D.A., et al.   1976.  Biological effects of heavy  metals on  juvenile  bay



scallops, Argooecten irradiana,  in short-term exposures.   Bull. Environ.  Concam.




Toxicol.  16: 275.








Michols,-J.W.   1981.   Effects of chronic  exposure  to  arsenic  crioxide on



smoLtifieat ion, downstream migration,  and seawacer  adaptation of caho saLaon




(Oncorhynchus kiauteh).   Mascara Thesis,  University of «ashi.-igcon.








 Haa-.ae;, I,  A.A.,  et  al.   1979.   Metabolism of  inorganic  arsenic to




organoarsenicals  in  rainbow  crout (Salmo  gairdne'ri) .   Ecotox. Environ. Safety 3:




349.








Oladimeji,  A.A.,  et  al.   1982.   Effect of acclimation of  rainbow trout (Salao



gairdneri)  co arsenic  on retention of a subsequent dose of arsenic.  ECocox. and




Environ.  Safety 6:  196.








Olson, O.I,.-,  and G.M.  Christensen.  1980.  Effects of water  pollutants on other



chemicals  on fish acetylcholinesterase (iji vitro).  Environ. Res. 21: 327.








 Ontario Water Resources Commission.  19S9.   Cladophora investigations.  A report




 of observation on Che nature and control of excessive growth of Cladoohora so.




 in Lake Ontario.

-------
Paladino, ?.V.  1976.  The effect of  arsenic on che  thermal  tolerance and




survival of newly hatched miskellunge  fry  (Esox maaquinongy).  Masters thesis,




State University College, Buffalo,  Mew York.








Paladino, F.V., and J.R. Spotila.   1978.   The effecc of arsenic on che thermal




tolerance of newly hatched muskellunge (Ssox oasquinongy).   Jour. Thermal 3iol.




3: 223.








Passino, D.R.,  and J.M.  Kramer.   1980.  Toxicity  of  arsenic  and PCBs to fry of




deepwater ciscoes (Coregonus).   Bull.  Environ.  Concan. ToxicoL. 24: 527.








Passino, D.R.M., and  A..J. Movak.   1982.   Letter  to  R.  L.  Spehar, Michigan DNR.




February 4.








Penrose, M.R.  .1975.   Biosynthesis  of organic  arsenic  compounds in brown crout




(Salmo  trutea). Jour. Fish.  Res.  Board  Can.  32:  2385.








Phillips, G.R.  and  R.C.  Ruaso.   1973.  Mecal  bioaccumulat ion in  fishes  =r.d




aquatic invertebrates:  a literature  review.   EPA-600/3-78-L03.  National




Technical  Information Service,  Springfield, Virginia.








Planas, 0.,  and F.P.  Healey.   1978.  Effects  of arsenate  on  growth and




phosphorus  metabolism of phytoplankton.   J. Phycol.. L4:  337.








Reay, ?.?.   1972.   The accumulation of arsenic from arsenic-rich natural waters




by aquatic plants.   Jour. Appl. Ecol. 9: 557.

-------
                                                                               si



Richter, J.c.  1982.  Memorandum to C.E. Stephan, U.S. EPA, Duluth, Minnesota.



June 30.







Sanders, H.O. and O.B. Cope.  1966.  Toxic icies of several pesticides to two



species of cladocerans.  Trans. Am. Fish. Soc.  95: 165.







Sanders, H.O. and 0.3. Cope.  1968.  The relative coxici.ci.es of several pes-



ticides co naiads of three species of stoneflies.  Limnol. Oceanogr.



13: 112.







Sanders, J.C.  L979.  Effects of arsenic speciacion and phosphate concentration



on arsenic vnhi.bi.cion of Skeleconena costatua (3acilLar-.s phyceae) .  J. PhycoL.



15:
Sandu, S.S.   1977.  Study of the post-mortem  identification o£ pollutants  In




fish killed by wacsr pollution: detection of  arsenic.  Bull. Environ. Con cam.




Toxicol.  17:  373.








Schaefer, E.O.,  and M.O. Pipes.  1973.  Temperature  and the toxicity of chromate




and  arsenate  co  the Rotifer, Philodina roseola.  Water ^es . 7: 1731.








Schiller, C.M. ,  at  al.   L977.  affects of arsenic on  syruvaca aanydrogenase




activation.   Environ. Health Perspecc.  19: 205.








Schuth ,  C.K. ,  eC al.  1974.  Distribution of  ^*C-arsenic derived  from




I  C  Cacodylic  acid  in an aquatic ecosystem.   Jour. Agric.  Food Chea. 22:




999.

-------
Scocc, K.J.   1981.  Memorandum Co  John H.  Gencile.   U.S.  EPA,  Narragansecc,




Rhode Island.








Scocc, K.J.,  and C.E.  Peach.   1981.   Memorandum Co  John H.  Gencile.   U.S.  EPA,




Narragansecc, Rhode Island.








Scudlark, J.R.  and O.L.  Johnson.   1982.  Biological oxidacion  of  arsenice  in




seawacer.   Escuarine,  Coascal, and Shelf Science 14:  693.








SohacSci, L.P.   1968.   Dynamics of  arsenic in Che aquaeic  environment.



Dissercacion, Michigan Scace Univ.  Ease Lansing, Michigan.








Sorenson, E.M.3.   1976a.  Toxic icy and accumulacion of  arsenic in ?rsen  sun-



-'--  ".»•"•--  £---•.••  -,   t::rosad  to  arsenace in -acar.  3ulL.  Environ.  Con-
Sorenson,  E.M.3.   19766.   Ulcrascruccural changes Ln che hepacocyces  oc  green




sunfish,  Leoomis  cyanellus Racinesque, exposed Co solutions of sodium arse-




nace.   Jour.  Fish 3iol.  3:  229.








Sorenson,  E.M.3.   L976c.   Thermal affects on che accumulacion oc arsenic in




green  sunfish,  Lepomis cyanellus.  Arch. Environ. Concam. ToxLcol.   4: 8.









Sorenson,  S.M.3., and N.K.R. Smich.   1981.  Heraosiderin granules:  cycoxic




responses  Co arsenic exposure in channel eacfish.  Bull. Environ.  Concam.




Toxicol.  27:  645.

-------
Sorenson, E.M.3., ec al.  1979.  Arsenic accumulation, tissue distribution and




cytotoxicicy ia teleosts following indirect aqueous exposures.  Bull. Environ.




Coneam. Toxicol. 21: 162.








Sorenson, E.M.B., ec al.  1980.  Cytological changes in fish  liver following




chronic, environmental exposure.  Bull. Environ. Contara. Toxicol. 25: 93.








Spehar, R.L., et al.  1980.  Comparative toxicity of arsenic  compounds and their




accumulation in  invertebrates and fish.  Arch.  Environ. Coneam. Toxicol.  9:




55.








Speyer, X.R.  1974.  Some effects of  combined  chronic  arsenic  and cyaniae




poisoning on the physiology of  rainbow  trout.   M.S. Thesis, Concordia Univ.,




Montreal, Canada.








Soever, M.S.  and C.  Leduc.   1975.   Effects of  Arsenic  Trioxide on Growth of




Rainbow Trout.   In:  International Conference on Heavy  Metals  in the  Environ-




aent.   Toronto,  Ontario,  Canada,  p.  C.17.








 Spotila,  J.l.,  and  F.V.  ?aladino.   1979.   Toxicity  of  arsenic Co developing




amskeilunge £ry (Eaox masquinongy).  Corap. Biochen. PhysioL.  62: 57.








 Stanley,  R.A.   1974.  Toxic icy or heavy metals and  salts  co Eurasian




 watermilfoil (Xyriophyllun soicatum L.).  Arch. Environ.  Contarn. Toxicol.  2:




 331.

-------
                                                                             5-y
Scephan, C.Z., et al.   1983.   Guidelines  for  deriving  numerical national via car




quality criteria, for  the  protection of aquatic  life and its uses.  U.S. SPA.




Duluth, Minnesota.  July  5.








Surber, E.W.   1943.   Weed coatrol  in  hard-water ponds  with copper sulphate and



3odium arsenate.  In; E.M. Quee  (ed.), Transactions of the Eighth North American




Wildlife Conference,  1943.  Washington, D.C.: American Wildlife Institute 3:




132.








Surber, E.W.  and O.L. Meehean.  L931.  Lethal concentrations of arsenic for




certain aquatic organisms.  Trans. Am. Fish.  Soc.  61: 22S.








Thoaas, W.H.,  et  al.   1930.   Toxicity of  a mixture of  ten uetais to




phytoplankton.  Marine  Ecology Progress Series  2: 213.








Thompson,  S.Z., et  al.   1972.   Concentration  faccors of the chemical elsaents  In




edible aquatic organisms. UCRL-50564.  Rev.  i.  Lawrence Liveraore Laboratory,



Livemora,  California.








Thursby,  G.3. and R.L.  Steele.  Manuscript.  Toxicity  of arsenide and  arsenata



to  Che marine macroalga Champia parvula  (Rhodophyta).  U.S. SPA, Narragansett,



RJiode Island..








U.S.  EPA.   1975.   Initial Scientific  Review of  MSMA/DSMA.  EPA-540/1-75-020.



National  Technical  Information Service,  Springfield, Virginia.

-------
U.S. i?A.  1976a.  Quality criteria for water.  055-001-01049-4.  Government




Printing Office.  Washington, D.C.








U.S. EPA.  I976b.  Arsenic.  E?A-600/l-76-036.  National Technical Information




Service, Springfield, Virginia.








U.S. SPA.  1979.  Methods for chemical analysis of vater and wastes.



EPA-600/4-79-020.  National Technical Information Service, Springfield,




Virginia.








U.S. EPA.  1980.  Ambient water quality criteria for arsenic.  E?A-4iO/5-30-02L.




National Technical Information Service, Springfield, Virginia.








U.S. SPA.  1982.  Watar Quality Standards Regulation.   Federal Register. 47:




49234.  October 29.








Vocke,  R.y.,  ec ai.   L980.  Growth  responses  af  selected  freshwater  algae  :o




trace  elements  aid scrubber ash slurry generated by coal-fired power  plants.




Wacer  Res. 14:  141.








Vageoann,  8.., at  al.   1978.   .Arsenic  in sediments, water  and aquatic  biota  from




lakes  in the  vicinity of  Yellowknife, Northwest  Territories, Canada.   Arch.



Environ.  Contarn.  Toxicol. 7:  169.








Weir,  P.A.,  and C.H.. Hine.   1970.  Effects  of various  metals on behavior  of



conditioned goldfish.  Arch.  Environ. Health 20: 45.

-------
Westeraan,  A.G.,  and  W.J.  3irge.   1978.   Accelerated  race  of  albinism  in channel




catfish exposed  Co metals.   Prog.  Fish-Colt.  4-0:  143.








Wlebe, A.R.,  et  al.   1931.   The arsenic  content of largemouth bass  (Micropterus




sal™ ides)  flngerlings.   trans. Am.  Pish. Soc.  61:  150.








Woolson,  F.A.,  et al.  1976.  Distribution and  Isolation of radioactivity  froa




7*As-arsenate and l4C-«ethanearsonic acid in an aquatic  model ecosystem.




Pest.  Biochem.  ?hys.  6:  Z61.








Zaroogian,  G.S.   1982.  Meraorandurn to John H. Gentile, U.S. EPA, Marragansett,




Rhode  Island.

-------