vvEPA
              United States
              Environmental Protection
              Agency
              Office of Water
              Regulations and Standards
              Criteria and Standards Division
              Washington, DC 20460
EPA 440/5-86O08
August 1988
Ambient
Water Quality
Criteria
for
              Aluminum - 1988

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AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA  FOR

                   ALUMINUM
    U.S.  ENVIRONMENTAL PROTECTION AGENCY
     OFFICE OF RESEARCH AND DEVELOPMENT
     ENVIRONMENTAL RESEARCH LABORATORY
             DULUTH,  MINNESOTA

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                                     NOTICES
               on for ^ ™lcri:iai Planets does not  constitute  endorsement
NTIS Number - PB88 245 998
                                     11

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                                    FOREWORD
       Section 304(a)(l)  of  the  Clean Water Act of 1977 (P i   QSJ,,,I
  the Administrator  of  the Environmental Prnr^i   A         95~217)  requires

  quality criteria that accurate^ reflect            1"?7 t0 publlsh  "ater
  the kind and extent of  all  idJntiftable
  might  be expected  from  the
  including  ground water
                            presenc  0  Do
                                        poll
                                                   KS°!entlfic  knowled««
                                                          *"* WClfare  that
                                                  -
                                                  in any body  of  water,
          for the same JoTlutJSi")
                                                                          ,
                                                           EPA aquatic life
Watert                ul
program impact in each sect  on.   In

         -
                                     sction 3o   th               a differe"t

                                           ? uji»f.f?.':..r!f"css;1:


 acceptable  pollutant  concentrations' in amb  T' fnforceable •«!"•
 Water  quality  criteria adopted  n              Wate" Within that State.
 same numerical values a      er a
 many situations States mi*ht wan?
 under  section  304 to renfct local
 patterns before incorporation i
                                                               could have  the
                                  o                   on 304.   However,  in  .

                                  env?ronLn\ ?' qU!Ut7 CriterU  d^eloped
                                                 °nd'tl°ns  and human exposure

-ter-reUted programs  of th   Agency
                                                                   °ther
                                 Martha G. Prothro
                                 Director

                                 Office of Water Regulations and Standards
                                                                       AUG 2 3
                                   111

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                                 ACKNOWLEDGMENTS
Larry T. Brooke
(contributor)
University of Wisconsin-Superior
Superior, Wisconsin
Charles E. Stephan
(document coordinator)
Environmental Research Laboratory
Duluth,  Minnesota
                                     i v

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                                     CONTENTS
                                                                           Page

 Foreword ........ . .............
                                ...........................................  111

 Acknowledgments ..............
                                  .........................................   iv

 Tables ....................
 Introduction ...........
                          ................................................    1

 Acute Toxicity to Aquatic Animals .....
                                           ...............................    4-

 Chronic Toxicity to Aquatic Animals ....................
                                                   .......................    D

 Toxicity to  Aquatic Plants ............
                                      ....................................    6

 Bioaccuroulation ...........................


 Other Data ............
                        ..................................................    7

 Unused  Data .........
                      [[[   8

 Summary ...........
                      [[[   9

 National Criteria. . . .
                        ..................................................  10

 Implementation ........

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                                     TABLES
                                                                         Page
 1.  Acute Toxicity of Aluminum to Aquatic Animals	    16
2.  Chronic Toxicity of Aluminum to Aquatic Animals	  19
3.  Ranked Genus Mean Acute Values with Species Mean Acute-Chronic
      Ratios	          21
4.  Toxicity of Aluminum to Aquatic Plants	        23
5.  Bioaccumulation of Aluminum by Aquatic Organisms	        24
6.  Other Data on Effects of Aluminum on Aquatic Organisms	        25
                                     vi

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  Introduct i on




      The  chemistry of  aluminum  in  surface  water  is  complex  because of  five



  properties  (Campbell  et  al.  1983;  Hem  1968a,b;  Hem and Roberson  1967; Hsu




  1968;  Roberson  and  Hem  1969; Smith and Hem  1972).  First,  it  is  amphotenc:



  it  is  more  soluble  in acidic solutions and  in basic solutions than in




  circumneutral solutions.  Second,  such ions as  chloride,  fluoride, nicrate,



  phosphate,  and  sulfate form soluble complexes with aluminum.  Third,   it can



  form strong  complexes with fulvic  and humic acids.  Fourth, hydroxide ions



  can connect  aluminum ions to form  soluble and insoluble polymers.  Fifth,



  under at least some conditions, solutions of aluminum in  water approach



  chemical  equilibrium rather slowly.  This document addresses the toxicity  of




  aluminum to  freshwater organisms in waters in which the pH is between 6.5  and




  9.0,  because the water quality  criterion  for pH (U.S.  EPA 1976)  states that a




  pH range  of  6.5  to 9.0 appears  to  adequately protect  freshwater  fishes and




 bottom-dwelling  invertebrate  fish  food  organisms from  effects of the  hydrogen



  ion.   At  a  PH between  6.5 and 9.0  in fresh water,  aluminum occurs




 predominantly as monomeric,  dimeric,  and  polymeric  hydroxides and as




 complexes with humic acids,  phosphate,  sulfate,  and less  common  anions.  This



 document  does not  contain information concerning the effect of aluminum  on




 saltwater species  because adequate  data and  resources  were  not available.



    Several  investigators have  speculated  about  the toxic  form of aluminum.




 Freeman and  Everhart (1971) found that the toxicity of  aluminum  increased  as




 pH increased  from  8.8 to  8.99.  They concluded that soluble  aluminum  was the




 toxic form.    Hunter et al. (1980) observed the same relationship  with rainbow




trout over a  pH range of  7.0 to  9.0.  However, the opposite  relationship '




resulted in a study with  rainbow trout by Call (1984) and in  studies  with  the

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fathead minnow by Boyd (1979),  Call  (1984),  and Kimball  (Manuscript).   The




tests conducted by Freeman and Everhart (1971),  Hunter et al.  (1980),  and



Kimball (Manuscript) were all renewal  or flow-through and showed the lowest




acute values, whereas the other tests  were static.   In addition,  because the



polymerization of aluminum hydroxide is a relatively slow process  the




chemical form of aluminum might have differed from  test  to test due to the



amount of time the aluminum was in stock and test solutions.




    Driscoll et al.  (1980) worked with postlarvae of brook trout and white




suckers under slightly acidic conditions and concluded that only inorganic




forms of aluminum were toxic to fish.   Hunter et al. (1980) reported that the




toxicity of test solutions was directly related to  the concentration of




aluminum that passed through a 0.45  ^m membrane filter.   In a study of the




toxicity of "labile" aluminum to a green alga,  Chlorella pyrenoidosa.




Helliwell  et al.  (1983)  found that maximum toxicity occurred in the pH range



of 5.8 to 6.2.   This is  near the pH of minimum solubility of aluminum and




maximum concentration of AMOHJg'*'.  They found that the  toxicity of



aluminum decreased as pH increased or  decreased from about 6.0, and they



speculated that the  monovalent hydroxide is  the most toxic form.  Seip et al.



(1984) stated that "the  simple hydroxides (Al(OH)'1'2 and A1(OH)2'1') are




regarded as the most dangerous forms while organically bound Al and polymeric




forms are  less toxic or  essentially harmless."




    In dilute aluminum solutions, formation of particles and the large




insoluble  polynuclear complexes known as floe is primarily a function of  the




concentrations of organic acids and the hydroxide  ion (Snodgrass et al.




1984).  Time for particle formation varies from <  1 min. to  several days




(Snodgrass et al. 1984)  depending upon the source  of aluminum,  the  pH,  and




the presence of electrolytes and organic acids.  When particles  form

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   aggregates Urge enough to  become  visible,  the  floe  is  whitish  and  tends  to
   settle.   Mats have  been reported blanketing  a stream  bed  (Hunter  et  al.
   1980).   Laboratory  studies  conducted at alkaline pHs  have reported  floe in
   the  exposure  chambers  (Brooke  1985; Call 1984; Lamb and Bailey  1981; Zarini
   et  al.  1983).   The  floe  did not appear to affect most aquatic species.
   However,  the  swimming  ability  of Daphnia ma^na was impeded by "fibers"  of
   flocculated aluminum trailing  from the carapaces,  and the movements and
   perhaps feeding of midges was affected,  ultimately resulting in death (Lamb
   and Bailey 1981).  Bottom-dwelling  organisms might be impacted more by
   aluminum floe in the field than in  the  laboratory.
      Aluminum floe might coprecipitate  nutrients,  suspended material,  and
  microorganisms.   Removal  of  phosphorus from  water  has  been observed  in
  laboratory studies  (Matheson 1975;  Minzoni 1984; Peterson  et  al.  1974)  and in
  a lake  (Knapp  and Soltero  1983).  Turbidity due to clay  has been removed from
  pond waters using aluminum sulfate  (Boyd 1979).  Unz and Davis (1975)
  speculated that  aluminum floc might coalesce bacteria  and  concentrate organic
  matter in effluent,, thus assisting the biological sorption of nutrients.
  Aluminum sulfate has been used to flocculate  algae from water (McGarry 1970;
 Minzoni  1984;  Zarini  et  al.  1983).
     An understanding of  the "Guidelines  for  Deriving  Numerical National  Water
 Quality  Criteria  for  the Protection  of  Aquatic Organisms  and  Their Uses"
 (Stephan  et  al.  1935). hereafter referred to  as the Guidelines,  and the
 response  to public comment  (U.S.  EPA 1985a) is  necessary  in order to
 understand  the  following text, tables, and calculations.   Results of  such
 intermediate calculations as  Species Mean Acute Values  are  given  to four
 significant figures to prevent roundoff error  in subsequent calculations, not
to reflect the precision of the value.   Unless otherwise  noted, all
concentrations of aluminum in water reported herein from  toxicity  and
                                       3

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 bioconcentration tests are expected  to  be  essentially  equivalent  to




 acid-soluble aluminum concentrations.   All  concentrations  are expressed  as




 aluminum,  not as the chemical  tested.   The  latest comprehensive  literature



 search for information for this  document was  conducted  in  July,  1986;  some more



 recent information was included.








 Acute Toxicitv  to Aquatic  Animals




     The  earliest study of  the  toxicity  of  aluminum to  aquatic life was




 performed  by Thomas  (1915)  using mummichogs acclimated  to  fresh  water.   His



 report lacks detail  and it  is  unclear whether the aluminum sulfate was



 anhydrous  or hydrated.   Assuming that the  anhydrous form was used, the




 calculated concentrations  of aluminum where all of the  fish died  in  1.5  and  5




 days  were  2,200  and  1,100  fig/l,  respectively.  More recent tests  with  fish




 showing  similar  sensitivities  to aluminum  (Tables 1 and 6) were  conducted with



 brook trout  with a 96-hr LC50  of 3,600  pg/L (Decker and Menendez  1974),




 rainbow  trout with a  72-hr  LC50 of 5,200 pg/L (Freeman  and Everhart  1971),




 and common carp  with  a  48-hr LC50 of 4,000 ng/l (Muramoto  1981).  Other  fish



 species  tested were more resistant to aluminum.




    The  range of  concentrations of aluminum that was acutely toxic to



 freshwater  invertebrate  species was about the same as the  range  of




 concentrations that was toxic  to fish.  The lowest acute values  for



 invertebrates are 1,900 ng/L (McCauley  et al.  1986) and 3,690 ng/L (Call




 1984)  for  ceriodaphnids, whereas the highest acute value is




55.500 fig/I  in a test with a snail  (Call 1984). No data are available




concerning the effect of pH on toxicity of aluminum to  invertebrates.




    Species Mean Acute Values  (Table 1)  were calculated as geometric means of




the available acute values, and then Genus Mean Acute Value.8 (Table  3) were




calculated as geometric means of the available Species Mean Acute Values.




Several species  tested were not exposed to aluminum concentrations high




                                        4

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   enough to  allow calculation  of an LC50.  Although these were ranked in Table



   3  according  to  the  highest concentration used in the test, this does not




   imply  a  true  ranking of sensitivities.  The freshwater Final'Acute Value for



   aluminum at a pH between 6.5 and 9.0 was calculated to be 1,496 ^g/L using



   the procedure described in the Guidelines and the Genus Mean Acute Values in



   Table  3.  Because acute values are available for only fourteen genera,  the



   FAV is about one-half the acute value for the most  sensitive genus.







  Chronic Tnvicitv to Aquatic  Animals




      Chronic toxicity values  for aluminum have  been  determined with three



  freshwater  species  (Table  2).   McCauley et  al.  (1986)  found  that




  2.600  ^g/L  reduced  survival and  reproduction of  CeriodaphnU  dubia  by 23%




  and 92%,  respectively.  An aluminum  concentration of  1,400 fig/L reduced




  survival  by  11%.  but  increased  reproduction.  Although  survival increased  at



  concentrations above 2,600 pg/L, no  reproduction occurred.   In a




  life-cycle test  with Daphnia ma*™,  survival was the same at  540 MS/L as



  in  the  control treatment,  but was reduced about 29% at 1.020 /jg/L




  (Kimball. Manuscript).   Reproduction was about the same at 1,020 pg/L as




  in the  control  treatment.   Biesinger and Christensen (1972) obtained a 21-day



 LC50 of 1.400 ng/L with  D.  ma^na (Table 6).   They estimated that




 320  ,if/L would  reduce  reproduction  by 16%.  but  the concentrations  of



 aluminum were  not measured  in  the test  solutions.




     Kimball  (Manuscript) reported the  results of  an  early  life-stage test



 with fathead minnows.  An aluminum concentration  of  4.700 Mg/L reduced



 weight by  11.4%.  whereas 2,300 Mg/L reduced weight by  7.1%.   Survival  at




 both concentrations was as good or better than in the control  treatment.



These chronic tests indicate that, of the three species tested, the




 invertebrates are more sensitive to  aluminum  than the vertebrate.




                                       5

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    The three available  acute-chronic  ratios  for  aluminum  are 0.9958 with




Oriodaphnia dubia.  51.27  with  Daphnia  magna,  and  10.64 with the fathead



minnow (Table 2).   These values  follow  the  common  pattern  that acutely




sensitive species  have  lower acute-chronic  ratios  (Table 3).  The  Final



Acute-Chronic Ratio is  meant to  apply  to  acutely  sensitive  species,  and.




therefore,  should  be close to 0.9958.   However, according  to the Guidelines.



the Final Acute-Chronic  Ratio cannot  be less  than 2,  because a  ratio lower



than 2 would result in  the Final  Chronic  Value exceeding  the Criterion




Maximum Concentration.   Thus the  Final  Chronic Value  for  aluminum  is equal  to




the Criterion Maximum Concentration of  748.0  ng/L for fresh water  at a  pH




between 8.5 and 9.0 (Table 3).



    Data in Table  6 concerning  the toxicity of aluminum to brook trout  and




striped bass show that  the Final  Chronic  Value should be  lowered to




87 pg/L to protect these two important species.   Cleveland et  al.




(Manuscript) found that  169 ng/L caused a 24% reduction in the weight of




young brook trout  in a  60-day test, whereas 88 A»g/L caused a 4% reduction




in weight.   In a 7-day  test, 174.4 ^g/L killed 58% of the exposed striped




bass, whereas 87.2 ng/L did not kill  any of the exposed organisms (Buckler



et al., Manuscript).  Both of these tests were conducted at a pH of 6.5  to




6.6.








Toxicity to Aquatic Plants




    Single-celled plants were more sensitive  to aluminum  than the other




plants tested (Table 4).  Growth of the diatom, Cvclotella meneghiniana,  was




inhibited at 810 ng/L,  and the species died at 6,480 ng/L  (Rao  and




Subramanian 1982).  The green alga. Selenastrum capri cornutum.  was  about as




sensitive to aluminum as  the diatom.   Effects were found  at concentrations

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      ranging from 460 Mg/l (Call 1984) to 990 ng/L (Peterson et al.  1974).




      Among multice1lular plants, root weight of Eurasian watermi1foi1  was



      significantly decreased at 2,500 Mg/L,  but duckweed was not  affected  at



      45,700 ng/l (Table 4).   A Final  Plant Value,  as  defined in the  Guidelines.



      cannot be obtained because no test in which the  concentrations  of  aluminum



      were measured and the endpoint was biologically  important  has  been conducted



"i      with an important aquatic plant  species.








      Bi oaccunmlat i on




         Cleveland et al.  (1986) found that  young  brook trout contained more




     aluminum after  exposure  for 15 days  than after exposure for  30  days,  and  the



     bioconcentration factors  ranged  from 50 to 231.   No U.S.  FDA action level  or




     other maximum acceptable  concentration  in tissue,  as defined in the




     Guidelines,  is  available  for  aluminum,  and,  therefore,  no  Final  Residue Value



     can be  calculated.








     Other Data




         Additional  data on the  lethal  and sublethal  effects of aluminum on




     freshwater species are presented  in  Table  6.  Bringmann and  Kuhn  (1959a,b)




     found that Scenedesmus quadricauda was  more resistant to aluminum  in  river



     water than C.hlorella pvrenoidosa.  They  did not  find  any toxic  effects on




     Paphnia magna during a 48-h exposure  to  1,000,000 m/L.  Toxicity  might



    have been reduced by naturally occurring  ligands  in  the  river water.




        Birge and coworkers reported that 507.  of the embryos and fry of the




    narrow-mouthed toad,  goldfish, largemouth  bass,   and  rainbow  trout  were killed




    or deformed  by exposure to aluminum concentrations of 50,  150,  170, and




    560 m/L,  respectively (Table 6).  Freeman and Everhart  (1971)  obtained an




    LC50 of  513 m/L with  rainbow trout fingerlings,  but these and other




                                           7

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 investigators also obtained much higher LCSOs  with  embryos,  fry, and



 fingerlinjs of rainbow trout.   Freeman (1973)  studied  the  growth of rainbow



 trout after exposure to aluminum for 4.7 to  45 days.   Growth was reduced  by



 5,200 MgA wnen pH was 7.0. 8.0,  or 9.0.   Normal  growth  resumed within  two



 weeks in control water.








 Unused Data



    Many data on the effects of aluminum on  freshwater organisms were  not



used because the pH of the dilution water used in the  tests  was  less  than 6.5



(Anderson 1948; Baker and Schofield 1982; Brown 1981,1983;  Brown et  al.  1983;



Buckler et al., Manuscript; Clark and LaZerte  1985;  Cleveland et al.  1986;



Cook and Haney 1985; Dickson 1983;  Driscoll  et al.  1980;  Eddy and  Talbot



 1983; Gunn and Keller 1984; Gunn and Noakes  1986; Havas  and Hutchinson



 1982,1983; Hunn et al. 1987; Jones 1940; Ogilvie and Stechey 1983; Orr et al.



1986; Schindler and Turner 1982;  Schofield and Trojnar 1980; Staurnes et  al.



 1984; Tease and Coler 1984; van Dan et al. 1981; Witters et al.  1984).   Data



were also not used  if the studies were conducted with species that are not



resident in North America.



    Burrows (1977), Chapman et al. (1968), Doudoroff and Katz (1953), Howells



et al. (1983). Kaiser (1980),  McKee and Wolf  (1963), Odonnell et  al. (1984),



Phillips and Russo  (1978), and Thompson et al. (1972) compiled data from



other sources.  Test  results (e.g.. Helliwell  et al.  1983)  were not used when



 it was likely that  they would have been  substantially different if they  had



been reported in terms of acid-soluble aluminum.  Data were  not used when



aluminum was a component of an effluent  or a  mixture  (Buckler et  al..



Manuscript; Guthrie et al.  1977; Hall  et  al.  1985;  Hamilton-Taylor et  al.



1984; Havts and Hutchinson  1982; Jay  and  Muncy  1979;  Markarian et al.  1980).

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      Becker and Keller (1983),  Marquis  (1982),  and  Stearns  et  al.  (1978)  were
  not used because the results  were  not  adequately presented  or  could  not  be
  interpreted.   Data were  not  used when  only  enzymes  were  exposed  (e.g.,
  Christensen 1971/72;  Christensen and Tucker  1976).  Tests conducted  by
  McCauley et al.  (1986) at  higher pHs were not  used  because  the organisms were
  not acclimated to  the dilution water before  the beginning of the test.
  Control  mortality  was too  high in  many tests reported by Buckler et  al.
  (Manuscript).
      Reports of  the  concentrations  of aluminum  in wild aquatic organisms
  (e.g., Ecological  Analysts, Inc.  1984;  Elwood et al. 1976;  Wren et al. 1983)
  were not  used  when  the number of measurements of the concentration of
  aluminum  in water was too  small.    Reports of other  field studies were not
  used when they either lacked adequate measurements of aluminum concentrations
  in  the water or reported no specific adverse effects (Berg and Burns 1985;
  Brumbaugh and Kane  1985;  Buergel  and Soltero 1983;  Gibbons et al. 1984; Knapp
 and Soltero 1983; Sonnichsen 1978;  van  Coillie  and Rousseau 1974; Zarini  et
 al.  1983).

 Summary
     Acute tests have been conducted on  aluminum at  PH between 6.5 and 9.0
 with freshwater species  in  fourteen genera.   In many tests,  less  than 50% of
 the  organisms were  affected at  the  highest concentration  tested.   Both
 ceriodaphnids and brook trout were  affected  at  concentrations  below
 4,000 MC/L,  whereas  some  other  fish and invertebrate species  were  not
 affected by  45,000 Mg/L.   Some  researchers found that the acute toxicity
of aluminum  increased with  pH, whereas others found  the opposite  to  be  true.
Three studies have been conducted on the chronic toiicity of aluminum to

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 aquatic  animals.   The  chronic  values  for Daphni a magna. Ceri odaphnia dubia.




 and the  fathead  minnow were  742.2,  1,908, and 3,288 jug/L, respectively.



 The diatom,  Cvclote11 a meneghi ni ana,  and the green alga, Se1enastmm




 capri cornutum. were  affected by concentrations of aluminum in the range of




 400 to  900  ng/L.   Bioconcentration  factors from 50 to 231 were obtained in



 tests with  young  brook trout.  At a pH of 6.5 to 6.6, 169 ng/L caused a



 24% reduction  in  the growth  of young  brook trout, and 174 ng/L killed 58%



 of  the exposed striped bass.








 National Criteria




     The  procedures described in the "Guidelines for Deriving Numerical



 National Water Quality  Criteria for the Protection of Aquatic Organisms and




 Their Uses"  indicate that, except possibly where a locally important species



 is  very  sensitive, freshwater  aquatic organisms and their uses should not be




 affected unacceptably,   when  the pH  is between 6.5 and 9.0, if the four-day




 average  concentration  of aluminum does not exceed 87 p.g/L more than once




 every three years on the average and  if the one-hour average concentration




 does not exceed 750 ng/L more  than once every three years on the average.








 Implementati on




     Because of the variety of  forms of aluminum in ambient water and the  lack




 of definitive information about their relative toxicities to freshwater




 species,  no available  analytical measurement is known to be ideal  for




 expressing aquatic life criteria for  aluminum.  Previous aquatic life




 criteria for metals and metalloids  (U.S. EPA 1980) were expressed  in  terms  of




 the  total recoverable  measurement (U.S. EPA 1983a), but newer criteria for




metals and metalloids  have been expressed in terms of the acid-soluble




measurement (U.S. EPA  1985b).  Acid-soluble aluminum (operationally defined




                                       10

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as the aluminum that passes through a 0.45 ,um membrane filter after the




sample has been acidified to a pH between 1.5 and 2.0 with nitric acid) is



probably the best measurement at the present for the  following reasons:



 1. This measurement is compatible with nearly all  available  data concerning



    toxicity of aluminum to,  and bioaccumulation of aluminum  by,  aquatic



    organisms.   It is expected that  the results  of  tests  used in  the



    derivation of  the criteria would not  have changed substantially  if  thev



    had been reported in terms of  acid-soluble aluminum.




 2.  On samples  of  ambient  water, measurement  of  acid-soluble  aluminum will



    probably measure  all  forms of  aluminum that  are toxic  to  aquatic  life or



    can be  readily converted  to  toxic  forms  under natural  conditions.   In



    addition,  this measurement  probably will  not measure  several  forms, such




    as  aluminum  that  is  occluded in  minerals,  clays,  and  sand or  is strongly
                                                                        B J


    sorbed  to particulate  matter,  that  are not toxic  and  are  not  likely to




   become  toxic under natural conditions.  Although  this  measurement (and




   many others) will measure  soluble complexed forms of  aluminum, such as




   the EDTA complex of aluminum, that probably have  low  toxicities to




   aquatic life,  concentrations of these forms probably are  negligible in



   most ambient water.




3.  Although water quality criteria apply to  ambient water, the measurement



   used to  express criteria is likely to  be  used to measure aluminum in



   aqueous  effluents.   Measurement of acid-soluble  aluminum  is expected to




   be  applicable to effluents  because it  will measure precipitates,  such  as



   carbonate  and hydroxide precipitates of aluminum,  that might exist in  an




   effluent  and  dissolve when  the  effluent is diluted with receiving  water.




   If desired, dilution  of  effluent  with  receiving  water  before measurement




  of acid-soluble  aluminum might  be  used to  determine  whether the  receiving
                                     11

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     water can decrease  the concentration  of  acid-soluble  aluminum  because  of

     sorption.


  4.  The acid-soluble  measurement  is  expected to  be  useful  for  most  metals  and


     metalloids,  thus  minimizing the  number of  samples  and  procedures  that  are

     necessary.  .


  5.  The acid-soluble  measurement  does  not require filtration of  the  sample  at


     the time  of  collection,  as does  the dissolved measurement.


  6.  The only  treatment  required at the time  of collection  is preservation  by


     acidification  to  a  PH between 1.5  and 2.0, similar to  that required  for

     the total  recoverable measurement.


  7.  Durations  of 10 minutes  to 24 hours between  acidification  and  filtration


     of  most samples of  ambient water probably will  not affect  the  result

     substantially.


  8.  Ambient waters have much higher buffer intensities at  a pH between 1.5


     and  2.0 than they do  at a pH  between 4 and 9 (Stumm and Morgan  1981).
                                                                        «

  9.  Differences in pH within the  range of 1.5 to 2.0 probably will  not affect

     the  result substantially.


10.  The  acid-soluble measurement  does not require a digestion step, as does

     the  total  recoverable measurement.


11.  After acidification and filtration of the sample to isolate the


     acid-soluble aluminum, the analysis can be performed using either atomic


     absorption spectrophotometric  or ICP-atomic emission spectrometric


    analysis (U.S.  EPA 1983a),  as  with the total  recoverable measurement.


Thus, expressing aquatic  life criteria  for aluminum in terms of the


acid-soluble measurement has both  toxicological and practical advantages.


The U.S. EPA is considering development and approval of a method for  a

measurement such as acid-soluble.
                                       12

-------
      The 0.45 urn membrane filter is the usual basis for an operational




  definition of "dissolved," at least in part because filters with smaller




  holes often clog rapidly when natural  water samples are filtered.   Some




  particulate and colloidal material,  however, might pass through a  0.45 Mm




  filter.   The intent of the acid-soluble measurement is to measure  the




  concentrations  of  metals and metalloids that are  in true  solution  in a sample




  that has  been appropriately acidified.  Therefore,  material  that does not




  pass through a  filter  with  smaller  holes,  such  as  a  0.1 Mm membrane




  filter, should  not  be  considered acid-soluble even  if  it  passes  through  a




  0.45 Mm membrane filter.   Optional  filtration of appropriately  acidified




  water  samples through  0.1 Mm  membrane  filters should be considered




  whenever the  concentration  of aluminum  that  passes through  a 0.45 Mm




  membrane filter  in  an  acidified water  sample exceeds a  limit specified in



  terms  of acid-soluble  aluminum.




      Metals and metalloids might be measured  using the total recoverable




 method (U.S. EPA 1983.).  This would have two major impacts because this




 method includes a digestion procedure.   First,  certain species of some  metals




 and metalloids cannot be measured because the total recoverable method  cannot




 distinguish between individual oxidation states.   Second,  in some cases  these




 criteria would be overly protective when based  on  the total recoverable




 method because the  digestion procedure  will  probably dissolve  some  aluminum




 that  is not  toxic and cannot be  converted  to  a toxic  form  under natural




 conditions.   This could be  a major  problem  in ambient waters that contain




 suspended clay.   Because  no  measurement  is  known to  be  ideal  for  expressing




 aquatic life criteria for aluminum  or for measuring  aluminum in  ambient water




 or aqueous  effluents, measurement of both acid-soluble  aluminum  and total




 recoverable aluminum  in ambient water or effluent or both  might be useful.




For example,  there might be cause for concern when total recoverable aluminum
                                       13

-------
  is much above an applicable limit, even though acid-soluble aluminum is below



  the limit.




     In addition, metals and metalloids might be measured using the dissolved




 method, but this would also have several  impacts.   First,  in many toxicity




 tests on aluminum the test organisms were exposed  to  both dissolved and




 undissolved aluminum.  If only the dissolved aluminum had been measured,  the




 acute and chronic values would be  lower than if acid-soluble or total




 recoverable aluminum had been  measured.   Therefore, water quality criteria




 expressed as dissolved aluminum would be  lower  than criteria expressed  as




 acid-soluble or  total recoverable  aluminum.   Second,  not  enough data are




 available  concerning the toxicity  of  dissolved  aluminum  to  allow derivation




 of  a  criterion based on dissolved  aluminum.   Third, whatever analytical




 method  is  specified  for measuring  aluminum  in ambient  surface  water will




 probably  also  be  used to  monitor effluents.   If  effluents are  monitored by




 measuring  only the dissolved metals and metalloids, carbonate  and  hydroxide




 precipitates of metals  would not be measured.   Such precipitates  might




 dissolve,  due  to  dilution  or change in pH or  both,  when the  effluent is mixed




 with receiving water.   Fourth,  measurement of dissolved aluminum  requires




 filtration  of  the sample  at the time  of collection.  For these  reasons, it is




 recommended  that  aquatic  life criteria for aluminum not be  expressed as



 dissolved aluminum.




    As discussed  in  the Water Quality Standards Regulation  (U.S. EPA 1983b)




 and the Foreword  to  this document,  a water quality criterion for aquatic life




 has regulatory impact only after it has been adopted in a State water quality




 standard.   Such a standard specifies a criterion for a pollutant that is




consistent with a particular designated use.  With the concurrence of the




U.S.  EPA,  States  designate one  or more uses for each body of water or segment




thereof  and adopt criteria that are consistent with the use(s)  (U.S. EPA




                                       14

-------
1983c,1987).  In each standard a State may adopt the national criterion, if




one exists, or,  if adequately justified, a site-specific criterion.  (If the




site is an entire State, the site-specific criterion is also a State-specific



criterion.)




    Site-specific criteria may include not only site-specific criterion




concentrations (U.S. EPA 1983c),  but also site-specific, and possibly




pollutant-specific, durations of averaging periods and frequencies of allowed




excursions (U.S.  EPA 1985c).  The averaging periods of "one hour" and "four




days" were selected by the U.S. EPA on the basis )f data concerning how




rapidly some aquatic species react to increases in the concentrations of some




pollutants, and "three years" is the Agency's best scientific judgment of the




average amount of time aquatic ecosystems should be provided between




excursions (Stephan et al .  1985;  U.S. EPA 1985c).   However, various species




and ecosystems react and recover at greatly differing rates.  Therefore, if




adequate justification is provided, site-specific and/or pollutant-specific




concentrations,  durations,  and frequencies may be higher or lower than those




given in national water quality criteria for aquatic life.




    Use of criteria, which have been adopted in State water quality




standards, for developing water quality-based per.nit limits and for designing




waste treatment  facilities  requires selection of an appropriate wasteload




allocation model.   Although dynamic models are preferred for the application




of these criteria (U.S.  EPA 1985c), limited data or other considerations




might require the use of a  steady-state  model  (U.S.  EPA 1986).   Guidance on




mixing zones and  the design of monitoring programs  is also  available  (U.S.



EPA 1985c,1987).
                                      15

-------
                                          Table I.   Acute Toxicity of aluminum to Aquatic Animals


Species Method*

Plonorion (odult). S. U
Ouqesi o t igr i no
Snail (adult). S. U
Physo sp
Snail (adult). S. M
Physo sp.
Snail (adult). S. U
Physo sp.
Snail (adult). S, M
Physo sp.
Cladoceran (23.000C >23.000

7 46 55.500d

6 59 >2i.400

7 55 30.600

8 17 >24.700 30.600

74 1.900 1.900

7 68 3.690 3,690

6 5- 3,900e
7 5
7 61 >25.300

7.05 38,200 38,200

7 53 22,000 22.000
                                                                                                                   Reference
                                                                                                                   Brooke  et  al.  1985
                                                                                                                   Call  1984
                                                                                                                   Call  1984
                                                                                                                   Coll  1984
                                                                                                                   Call  1984
                                                                                                                   UcCauley  el  al   1986
                                                                                                                   Call  1984
                                                                                                                   Biesinger  and
                                                                                                                   Christensen  1972

                                                                                                                   Brooke  et  al   1985
                                                                                                                   K imloI I, Uanuscripi
                                                                                                                  Call  1984
Commorus pseudolimnaeus
                                   chloride

-------
Table I.   (continued)
StoneMy (nymph). S, M
Acroneuria sp.
Midge (lorvo), S. U
Tanytorsus dissimi 1 is
Chinook salmon $, u
(juveni le) ,
Oncorhynchus tsho»ytscha
Roinbb* trout S, U
(juveni le) ,
Salmo qoi rdneri
ftainboi trout S, y
(juveni le) ,
So Imo qoi rdneri
Rainboi trout S. U
(juveni le) ,
Salmo qoi rdneri
ftainbo* trout S, U
(juveni le) .
Salmo qoi rdneri
Brook trout F, y
(juveni le) ,
Solvelinus fontinalis
Fathead minnoi S, U
(adult),
Pimephol es prorael as
««'<••« IC50 Species Uea.
( («g/L «s or CC50 Acute Value
«**'ClL CaCOli_ Efi (22.600 >22,600 Call 1984
chloride
"*'""* 7 "- >79.900 >79.900 Lamb and Bailey 1981
sulfate e 85
S*><"U" 28 ° 7 ° >40,000 >40.000 Peterson et al 1974
aluminote
Aluminum 47 4 7 46 8.60011 - Call 1984
chloride
Aluminum 47.4 6 59 7,400 - Call 1984
chloride
Aluminum 47.4 7 31 14,600 - Call 1984
chloride
Aluminum 47 4 817 >24.700e 10.390 Coll 1984
chloride
*'uinint"" - 65 3,600 3,600 Decker ond Menende;
sulFate 1 974
Aluminum - 76 >I8,9UU - Boyd 1979
sul fate

-------
         Table I.  (continued)
oo

Species
Fathead minnon
( j uveni le) .
Pimephol es promelas
Fathead minno*
(juveni 1 e) .
Pimephales promelas
Fathead ainnoi
(juveni le) .
Pimepholes promelos
Channel catfish
(juveni 1 e) ,
Idol urus punc totus
Green sunfish
(juveni le) ,
Lepomi s cvonel 1 us
Yel lo* perch
(juveni le) .
Perca flavescens

Hardness LC50 Species Mean
(•g/L es or EC 50 Acute Value
Method* Chemical CuCO.) pH (/ia/L)b (na/1) Reference
S. M Aluminum 47.4 7.61 >48.200 - Call 1984
chloride

S. U Aluminum 47.4 8 OS > 49, 800 - Call 1984
chloride

F. M Aluminum 220f 7 34 35.000 35.000 Kimball. Manuscript
sul fate

S. U Aluminum 47.4 7 54 > 47. 900 >47.900 Call 1984
chlori de

S. U Aluminum 47.4 7 55 > 50, 000 > 50, 000 Call 1984
chloride

S, U Aluminum 47.4 7.55 > 49. 800 >49,800 Call 1984
chloride

           S = static;  R = renewal; F - fIo«-lhrough,  U = measured;  U =  unmeasured.

           Concentration of aluminum, not the chemical
           48-hr test

           Aluminum chloride was added to Lake Superior »o»er.  the  pH  «as adjusted, and the solution «as aerated for 18 days prior  lo addition
           of  test  organisms, not used in calculations

           Nat  used in calculations

           From Smi Hi  et  al   (I97G)

-------
                                 Table  2.   Chronic Toxicity  of  Aluminum to Aquatic  Aaieials





                                                Hardness
                                                                          Liaits
                                                                                       Chroeic Value
Species Test"
Cladoceran, LC
Ceriodophni a dubio
Cladoceran, LC
Oaphnio maqno
fotheod minnoi, CIS
Pimepholes prgmelos
Chemical CaCO,)
FRESHt
Aluminum 50
chlorida
Aluminum 22UC
sulfate
Aluminum 220°
sulfate
Eft
HATCH SPECIES
715
8 30
7 24-
8 15
1M/1\" (wd/ll
1.400- 1.908
2.600
540- 742 2
1 .020
2.300- 3,288
4.700
Reference
UcCauley et al 1986
Kimbal 1 , Uanuscr ipt
Kimball. Manuscript
LC = life-cycle or partial life-cycle; ELS = early life-stage
Measured concentrations of aluminum
from Smith et a)  (1976).

-------
Table 2.  (co««i»ued)
RaHo
  Cladoceran,
   Cladoceran.
   Paohnio, mat
   fathead •in»o«.
    >i«ephoies  o_roi»»ta£
Hardness
_CaCOjl_
50


220



220

Acut e Val ne

TIC \ 900 '
713"
7 4
742 2
7 05- iBl
8 30

7 24- J5.°UO *'

8 15
e
Ratio
0 9956


51 47


10 64




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

                                                Genus Uean                                Species Uean      Species Uean
                                                Acute Value                               Acute Value       Acute-Chronic
                                                          _     Species                     (null]             Roti oc
                                    14          >79,900         Midge,                    >79,900
                                                                Tonytorsus di ssimiI is

                                    13          >50,QOO         Green sunfish,            >50,000
                                                                Lepomis cyonelI us

                                    12          >49.800         Yello* perch,              >49,800
                                                                Perco fIovescens

                                    II          >47.900         Channel catfish,          >47.900
                                                                Ictolurus punctat us

                                    10          >40,000         Chinook salmon.            >40.00U
N)                                                              Oncorhynchus tshatry tscho
*-•

                                     9           38.200         Cladoceran,                 38.200           51 47
                                                                Oophnia moqno

                                     8           35.000         Fatheod minnow.             35.000           10 64
                                                                Pimepholes promelas

                                     7           30,600         Snail.                     30.600
                                                                Physo sp.

                                     6          >23,000         Planarian.                >23,000
                                                                Dugesig t i qri no

                                     5          >22,600         Stonefly,                  >22,600
                                                                Acroneur i a sp

                                     4           22.000         Amphipod,                   22.000
                                                                Commorus  pseudolimnaeus

                                     3           10,390         Rainbow trout,              10.391)
                                                                Sal mo go i rdner i

-------
                                   Table  3.   (continued)
N>
                                               Genus
                                               Acute Value
»o«k'       	

 2            3.600


 I            2.648
                                                                Brook  trout ,
                                                                SolvelInus  font i nolis

                                                                Cladoceran.
                                                                Ceriodophni o  dubia
                                                               Cladoceran,
                                                               Cer i odophnia  sp
                                                      Species Mean
                                                      Acute Value
                                                        3.60U
                                                          ,9UO
                                                        3,690
Species Uean
Acute-Chronic
   Ratio1
 0 9958
  Ranked fro* Most resistant to Most sensitive based on Genus Mean Acute Value
  Inclusion of "greater than" values does not necessarily  imply a true ranking, but does
  allo* use of all genera for •hich data are available so  that the Final Acute Value is
  not unnecessarily loiered.

b From Table I

0 from Table 2
                                   fresh »oter (pH betneen 6 5 and 9 Q|

                                        Final Acute Value = 1.496 /jg/L

                                        Criterion Maximum Concentration = (1.496 /jg/L) / 2 = 748 0

                                             Final Acute-Chronic Ratio = 2    (see text)

                                        Final Chronic Value - (1,496/jg/L) / 2 = 748 0//g/L

                                        Final Chronic Value = 87 ftq/i (lowered to protect brook trout and striped bass, see text]

-------
u>
                                                      Table 4.   Toxicity al Al«ainum to Aquatic Plants
                                                          Hardness
Spec i es
Diatom.
C y c 1 o t e 1 1 a meneqhi ni ana
Green alga,
Selenastrum copricornut urn

Green alga,
Selenastrum copr i cornut urn
Green alga,
Sel enastrum copri cornut urn
Eurasian latermi 1 f oi 1 .
Mvriophyl 1 urn spicotum
Ouck»eed.
lemno minor
Duckveed,
Lemno minor
Chemical pH

Aluminum 7 9
chloride
Sodium 7 0
aluminate

Aluminum 7 6
chloride
Aluminum 8.2
chloride
-
Aluminum 7 6
chloride
Aluminum 8 2
chloride
(mg/L es Duration
CaCOj]_ (days) Effect
FRESHWATER SPECIES
8 Inhibited gro«th
olgistat ic
algicidal
15 -14 Reduced cell
counts and
dry (eight
14.9 4 ECSO
( bi omass)
14 9 4 ECSO
(biomoss)
32 ECSO
(root Height)
14 9 4 Reduced frond
product ion
14.9 4 Reduced frond
product ion
Concentration
(uQ/L|a Reference

810 Rao and Subramanian
3.240 1982
6.480
990- Peterson et at 1974
1.320

570 Call 1984
460 Call 1984
2.500 Stanley 1974
>45.7QO Call 1984
>45.7QO Call 1984
          Concentration  of  aluminum,  not  the  chemical

-------
                                                 Table 5.  lioaccuaylatio* of Aluaiiua by Aquatic Organisms
                                                                          Hardness
Species
Brook trout (eyed embryo).
Sol vel i nus font i nol is

Brook trout (37 days).
Sal yel i nus font inol is
Concentration
Cheat col i* Voter (ua/ll*
Aluminum 242
sulfote

Aluminum 242
sulfote
(•9/1 as
_£SC°31_ £il Tissue
13 7 24 Whole
body

14 1 35 Whole
body
Durat io«
Post-hatch.
IS days
3Q days
IS days
30 days
BCF or
BAfb

147
SU
231
136
Reference
Cleveland et al 1986


Cleveland et al . 1986

            Ueasured  concentration of
            Bioconcentration factors (BCfs)  and biooccunulotion  factors  (BAfs)  are  based  on  measured concentrations  of  aluminum in Hater and
            i n  I issue
to

-------
                                                Table 6.  01 her Data a* Effects of Aluminum on Aquatic Organises
K)
              Species
                                                    Hardness
                                                    (mg/l as
                                                                                                         Concent rot ion

Green alga,
Chlorel la vul qoris
Green alga.
Chlorel lo vulqor is
Green alga.
Scenedesmus quodr i coudo
Plonktonic communities
Protozoan,
Mi croreqmo heterostoreo
Protozoan ,
Chilomonas paramecium
Protozoan,
Peronemo tr ichoporum
Protozoan ,
Tetrohymeno pyr i I ormis
Protozoan ,
Euql end qroc i 1 i s
Cladoceran (mature),
Oophnio catoirbo

Aluminum
chloride
Aluminum
sul fat*
Aluminum
chlori de
Aluminum
sullate
Aluminum
chloride
Aluminum
chloride
Aluminum
chloride
Aluminum
chloride
Aluminum
chlori de
Aluminum 8 07
chloride
— r"- • «•! »•••»»•• i • I ei I IIJQ/I-I
fBEStUfATER SPECIES
<7 0 3-4 mo Inhibited 4, DUO
grout h
30 days Reduced maximum < 161, DUO
groit h
7 5- 96 hr Incipient 1,500-
^ 8 inhibi I ion 2,000
(river voter)
61- 1 br Decreased pbos- 50
6 9 phote uptake and
photosynthesis
7 5- 28 br Incipient 12,000
78 inhi bi t ion
(river later)
55- 3 hr Some 1 10
7 4 survi val
55- 3 hr Some 62,600
6 5 survival
5 5~> 3 hr Some 1 10
6 5 surv i val
60- 3 hr Some 1 1 1 , 800
7 0 survival
65 72 hr Reduced 1 ,020
surv i val
Hef erence
De Jong 1965
Becker and Keller 1971
Bringmonn and Kuhn
I959a,b
Nelewajko and Paul
1985
Sringmann and Kuhn
I959b
Ruthven and Cairns
1973
Rulhven and Cairns
I97J
Rut hven and Cu i rnv
I97J
Rut hven and Cu i r iii
1971
Huvo:> and I i k e/i%

-------
Table 6.   (continued)


Species
Clodoceran,
Oophni o moqno
Cl odoceran.
Oophni o moono

Cl odoceran ,
Oophni o mogna

Cladoceran ,
Dophni o moono
ro
cr* Cladoceran,
Dophni o moqno
Cladoceran,
Oophni o moqng
Cladoceran,
Dophni o moqno
Cladoceron,
Dophni g moqno
Cladoceron,
Oophni o moqng
Cl adoceran,
Daphni g moqno
Cl odoceran ,
Pophn i o nioqng
Hardness
(•9/1 as
Chemical CaCOJ
Aluminum
swlfate
Ammonium
aluminum
sulfate
Potassium
aluminum
sulfate
Aluminum
chloride
Aluminum 45 3
chloride
Aluminum 45 3
chloride
Sodium 27 0
al umi note
Aluminum 8 26
chloride
Aluminum
chloride
Aluminum 8 26
chloride
Al umi num 33 35
chlor i de

Cokcentrat ion
pH Duration Effect (fia./L)°
16 hr Incipient 21 ,450
immobi 1 i zat i on
16 hr Incipient 21 .620
immobi 1 i zot i on

16 hr Incipient 21.530
immobi 1 i zat i on

75 48 hr Non-toxic 1.000. 000
(river >ater)
6 5- 21 days CCI6 (reduced 320
7 5 reproduction)
6 5- 21 days LC50 1.400
7 5
70 96 hr Mortality > 40, 000

65 48 hr Mortality 320
6.5 48 hr Loss of 1.020
sodi urn
65 24 hr BCf = 18.000 20
BCf = 9,600 320
BCf = II ,000 1 ,020
65 24 hr BCf = 18,000 20
• BCf -- 14.700 1 ,020


Reference
Anderson 1944

Anderson 1944


Anderson 1944


Bringmann and Kuhn
I959o
B i es i nger and
Christensen 1972
Biesinger and
Christensen 1972
Peterson et al 1974

Hovas 1985, Hauas and
Likens I985o
Hovos and Likens
i Sb'ju
Havab 1985
Hovo, ,985

-------
 Table 6.   (continued)
Species
Clodoceron.
Dophni a moqno
Crayfish.
Orconectes viri 1 is
Aquatic beetle (adult),
Tropistermus loterolis
nimbotus
Midge (larva),
Tgnytorsus dissimi 1 is
Roiaboe trout
(f ingerling) ,
Sqlmo qoirdneri
Rainboi trout
(embryo) ,
Sol no qqi rdneri
Rainbo* trout
(embryo, larva),
So Imp qoi rdneri
Rainboi trout
( juveni le) ,
So Imp qoirdneri

Rainbow trout
(embryo, larva) ,
Chemical
Aluminum
sulfate
Alumi a urn
chloride
Aluminum
chloride
Alumi num
sul fate
Al umi num
chloride
Al umi num
chlor i de
Alumi num
chloride
Aluminum
sul fate

A 1 umi num
sul fate
Hardness
(-9/1 as
c.co3i_
220b
II 0
-
17.43
46 8
28 3
28 3
56 6
56 6
-
104
(92-110)
25

14 3
pj
7 05
7 0
7 0
6 63
8.02
8 48
8 99
6.64
6 80
70-
9 0
74
70
8 0
8 5
9 0
6 5
7 2
Durat io»
48 hr
2 hr
14 days
55 days
32 days
7 5 days
3 days
44 days
39 days
Pert i 1 i zo-
t ion to
hatch
28 days
10 days
96 hr
42 hr
42 hr
8 days
[ffect
IC5U
((•*)
Calcium uptake
una I fee ted
Changed the
fat body
37Z dead
SOX dead
SOX dead
SOZ dead
SOZ dead
SOZ dead
No reduced
fert i lity
EC50 (death
and deformity)
OZ dead
40Z dead
IQUZ dead
IUUZ dead
No effect
No effect
Concentre! ion
iwn°
38.200
20U
200
832
5.230
S.I40
5.200
513
5,140
5.200
560
200.000
50,000
50,000
50,000
1 ,000
1 , 000
Reference
Kimbal 1 , Manuscript
Ual ley and Chang 1985
Wooldridge and Wooldridge
1969
Lamb and Bai ley 1981
Freeman and [verhart
19/1
[verhart and freeman
1973
Birge 1978, Birge et al
1978. I960, 1981
Hunter et al (980

Holtze !9Bi
SoImo qoirdner i

-------
Table 6.   (continued)


Species
Roinboi trout
(eyed embryo),
So Imo goif dneri
Roinbo* trout
(juveni le) ,
Sol mo qoi rdneri
Brook trout
(eyed embryo) ,
Solvelinus fontinolis
Brook trout (37 days) .
Solvelinus fontinalis
00
Brook trout
(eyed embryo).
Sol vel inus font inol is
Brook trout (larva),
Solvelinus fontinalis

Brook trout
(embryo, larva),
Solvelinus fontinolis



Goldfish (60-90 mm),
Corassius ourot us

Coldf ish (juveni le) ,
Corassius ouratus
Hardness
(-9/L .s
Chemicel CdCOj)
Aluminum 14 3
sulfate

Aluminum
sulfate

Aluminum 13
sulfate

Aluminum 14
sulfate

Aluminum 
-------
Tokle 6.   (continued)
Species
Goldfish
(embryo, lorvo),
Corossi us ourotus
Common carp (juvenile).
Cyprinus carpi o
fathead minnow (adult) ,
Pimepholes nroroelos

fathead minnow
K> (juveni le) .
Pimephales promelas
Lorgemouth bass
(juveni le) .
Uicropterus solmoides
Uummichog (adult).
f undulus heterocl i tus
Uosqui tof ish
(adult female).
Gombusio a f f j n i s
Threespine stickleback
(adult).
Cast erosteus gcul eat us
Striped bass (159 days),
Uorone saxat i 1 is
Striped bass (195 days),
Uorone saxat ills
Hardness
l-9/l «
Chemical _CoCO,|_
Aluminum 195
chloride
Aluminum
chloride
Aluminum
chloride

Aluminum 220b
sulfate
Aluminum 64-80
sulfate
Aluminum
sul fate
Aluminum
chloride
Aluminum
ni trate
Aluminum
sul fate
Aluminum
sulfate
fjt Pure t ion Effect
74 7 days CC50 (death
and deformity)
65 48 hr JQZ dead
66 ioz dead
5QZ reduction
of acetylchol-
i nesterase
act i vi ty
73 8 days LC50
(fed)
66- 7 days 01 dead
74
36 hr IOOZ dead
120 hr IOOZ dead
43- 4 days LC50 (high
7 7 turbidity)
>7 0 10 days No toxici ty
65 7 days OZ dead
72 OZ dead
65 7 days OZ dead
72 OZ dead
Concentration
fua/Lt Reference
150 Birge 1978
4.000 Muromoto 1981
4,000
18,000 Olson and Christensen
1980

22,400 Kimboll. Manuscript
50,000 Sonborn 1945
2,210° Thomas 1915
I.I 00°
26.900 Wall en et al 1957
18.500
70 Jones 1939
390 Buckler et al . Manuscript
391)
3911 Buckler et al , Manuscript
3911

-------
Table 6.  (continued)
Species
Striped bass (160 days),
Uorone saxat ills

Lorgeaouth bass
(embryo, 1 arva) .
Uicr opterus solmoides
Narro*-Moutbed load
( embryo. 1 arva) ,
Cost rophryne corol i nens is
Marbled salamander
(embryo, larva),
Ambystoma opocum
Hardness
("9/1 «
Chemicel CeCOjl
Aluminum
sulfole
Aluminum 93-105
chloride
AlumJAum 195
chloride
Aluminum 93-105
chloride
pjt Ourot ion
65 7 days
6 5
72
7.2
72- 8 days
7 8
74 7 days
72- 8 days
78
Concentrat ioe
Effect (uq/lV Reference
01 dead 87 2 Buckler et al , Manuscript
58Z dead 174 4
21 dead 174 4
IUOX dead 348.8
CC50 (death 170 Birge et al 1978
and deformity)
EC50 (death) 50 Birge 1978, Birge et al
and deformity) 1979
CC50 (death 2,280 Birge et al 1978
and deformity)
  Concentration of aluminum, not the chemical
b From Smith et ol  (1976)





c If the aluminum sulfate is assumed to  be  anhydrous.

-------
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