Draft
2/18/86
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
This document has been reviewed by Che Criteria and Standards Division,
Office of Water Regulations and Standards, U.S. Environmental Protection
Agency, and approved for publication.
Mention of trade names or commercial products does not constitute
endorsement or recommendation for use.
This document is available to the public through the National Technical
Information Service (NTIS), 5285 Port Royal Road, Springfield, VA 22161
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FOREWORD
Section 304(a)(l) of Che Clean Water Act of 1977 (P.L. 95-217)
requires the Administrator of the Environmental Protection Agency to
publish water quality criteria that accurately reflect the latest scientific
knowledge on the kind and extent of all identifiable effects on health
and welfare that might be expected from the presence of pollutants in any
body of water, including ground water. This document is a revision of
proposed criteria based upon a consideration of comments received from
other Federal agencies, State.agencies, special interest groups, and
individual scientists. Criteria contained in this document replace any
previously published EPA aquatic life criteria for the same pollutant(s).
The term "water quality criteria" is used in two sections of the
Clean Water Act, section 304(a)(l) and section 303(c)(2). The term has a
different program impact in each section. In section 304, the term
represents a non-regulatory, scientific assessment of ecological effects.
Criteria presented in this document are such scientific assessments. If
water quality criteria associated with specific stream uses are adopted
by a State as water quality standards under section 303, they become
enforceable maximum acceptable pollutant concentrations in ambient waters
within that State. Water quality criteria adopted in State water quality
standards could have the same numerical values as criteria developed
under section 304. However, in many situations States might want to
adjust water quality criteria developed under section 304 to reflect
local environmental conditions and human exposure patterns before incorporation
into water quality standards. It is not until their adoption as part of
State water quality standards that criteria become regulatory.
Guidelines to assist States in the modification of criteria presented
in this document, in the development of water quality standards, and in
other water-related programs of this Agency, have been developed by EPA.
James M. ConIon
Acting Director
Office of Water Regulations and Standards
Lll
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ACKNOWLEDGMENTS
Larry T. Brooke
(author)
University of Wisconsin-Superior
Superior, Wisconsin
Charles E. Stephan
(document coordinator)
Environmental Research Laboratory
Duluth, Minnesota
Clerical Support: Terry L. Highland
Shelley A. Heintz
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CONTENTS
Page
Foreword ....................... .- ...... iii
Acknowledgments .......................... iv
Tables ............................... vi
Introduction ..... ....................... 1
»
Acute Toxicity to Aquatic Animals ................. 6
Chronic Toxicity Co Aquatic Animals ................ 8
Toxicity to Aquatic Plants ........ . ............ 8
Bioaccumulation .......................... 9
Other Data ............................. 9
Unused Data ............................ 10
Summary ....... .• ...................... H
National Criteria . ........................ 11
References ............................. 23
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TABLES
Page
1. Acute Toxicity of Aluminum to Aquatic Animals 13
2. Chronic Toxicity of Aluminum To Aquatic Animals 15
3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic
Ratios 16
4. Toxicity of Aluminum to Aquatic Plants 18
5. Other Data on Effects of Aluminum on Aquatic Organisms 19
VI
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Introduction*
The aquatic toxicology of aluminum is complex because of three chemical
characteristics. First, it is amphoteric with minimum solubility at a pH
of about 5.5. Solubility increases as pH increases and as pH decreases.
Second, a variety of ions form soluble complexes with aluminum. Third, it
polymerizes in the presence of hydroxide to form a visible whitish colored
precipitate. Detailed explanations of the behavior of aluminum in natural
waters are presented by Hem (1968), Hem and Robertson (1967), and Robertson
and Hem (1969). This document addresses the toxicity of aluminum to
freshwater** aquatic organisms in waters with a pH from 6.5 to 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 hydrogen ion.
The polymerization, hydrolysis, and solubility of aluminum are all markedly
affected by pH. At pH greater than 6.5, aluminum occurs predominantly in
the forms of monoraeric, dimeric, and polymeric hydroxides, and complexes with
sulphates, phosphates, humic acids, and less common anions.
The toxic forms of aluminum are thought to be the soluble inorganic
forms. Driscoll et al. (1980) worked with postlarvae of brook trout and
white suckers under slightly acidic conditions and concluded that only
inorganic forma of aluminum were toxic. Hunter et al. (1980) found that
toxicity of aluminum was directly related to the concentration of the
*An understanding of the "Guidelines for Deriving Numerical National Water
Quality Criteria for the Protection of Aquatic Organisms and Their Uses"
(Stephan et al. 1985), hereafter referred to as the Guidelines, is necessary
in order to understand the following text, tables, and calculations.
**EPA feels that the need for a saltwater criterion is not great enough to
warrant devoting resources to it.
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soluble (able to pass through a 0.45 pm membrane filter) portion. Seip
et al. (1984) stated that "simple hydroxides Al(OH)*2 and A1(OH)2* are
regarded as the most dangerous forms while organically bound aluminum and
polymeric forms are less toxic or essentially harmless." Freeman and
Everhart (1971) found that, in alkaline conditions, toxicity to rainbow
trout increased with increasing pH, indicating that soluble aluminum is
the toxic form.
In a study of the toxicity of "labile" aluminum to the 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 the pH range of minimum
solubility of aluminum and maximum concentration of AKOHK • 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.
In dilute aluminum solutions, formation of particles and the large
polynuclear complexes known as floes is primarily a function of the
organic acid and hydroxyl ion concentration (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 aggregates large enough to become visible, the
floe is whitish in color and tends to settle. Mats have been reported
blanketing a stream bed (Hunter et al. 1980). Laboratory studies
conducted at alkaline pHs have reported floes in the exposure chambers
(Brooke et al. 1985; Call 1984; Lamb and Bailey 1981; Zarini et
al. 1983). The floes had no known effects on toxicity to most aquatic
species but did impede the swimming ability of Daphnia magna. J>. magna
were noticed to have "fibers" of flocculated aluminum trailing from their
2
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carapaces. Midges were impeded in their movements and perhaps feeding,
ultimately resulting in death (Lamb and Bailey 1981).
Aluminum floes might eoprecipitate nutrients, suspended material, and
microorganisms. Phosphorus removal from water has been observed in
laboratory studies (Matheson 1975; Minzoni 1984; Peterson et al. 1974)
'and in a lake (Knapp and Soltero 1983). Clay turbidity has been removed
from pond waters using aluminum sulfate (Boyd 1979). Unz and Davis
(1975) speculated that aluminum floes may coalesce bacteria and concentrate
organic matter in effluents, thus assisting the biological adsorption of
nutrients. Aluminum sulfate was used to flocculate algae from water
(McGarry 1970; Minzoni 1984; Zarini et al. 1983). Bottom dwelling species
or certain life stages of other species that are associated with the
bottom might be impacted by the aluminum floe or its coprecipitates.
Because of the variety of forms of aluminum (Hem 1968; Hem and
Robertsqn 1967; Robertson and Hem 1969) and lack of definitive information
about their relative toxicities, no available analytical measurement is
known to be ideal for expressing aquatic life criteria for aluminum.
Previous aquatic life criteria for metals (U.S. EPA 1980) were expressed
in terms of the total recoverable measurements (U.S. EPA 1983a), but newer
criteria for metals have been expressed in terms of the acid-soluble measurement
(U.S. EPA 1985a). Acid-soluble aluminum (operationally defined as the
aluminum that passes through a 0.45 pra membrane filter after the sample
is acidified to pH » 1.5 to 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 aquatic organisms. Few test results were
rejected just because it was likely that they would have been substantially
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different if they had been reported in terns of acid^soluble aluminum.
For example, results reported in terms of labile aluminum (Helliwell et
al. 1983) were not used.
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 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 probably will
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 water can decrease the concentration of acid-soluble
aluminum because of sorption.
4. The acid-soluble measurement is probably useful for most metals, thus
minimizing the number of samples and procedures that are necessary.
5. The acid-soluble measurement does not require filtration at the time
of collection, as does the dissolved measurement.
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6. The only treatment required at the time of collection is preservation
by acidification to pfl « 1.5 to 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. The carbonate system has a much higher buffer capacity from pH * 1.5
to 2.0 than it does from pH » 4 to 9 (Weber and Stumm 1963).
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. On
the other hand, 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 if total recoverable
aluminum is much above an applicable limit, evea though acid-soluble
aluminum is below the limit.
Unless otherwise noted, all concentrations reported herein are
expected to be essentially equivalent to acid-soluble aluminum concentrations.
All concentrations are expressed as aluminum, not as the chemical tested.
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Whenever adequately justified, a national criterion may be replaced by a
site-specific criterion (U.S. EPA 1983b), which may include not only site-
specific criterion concentrations (U.S. EPA 1983c), but also site-specific
durations of averaging periods and site-specific frequencies of allowed excursions
(U.S. EPA 1985b). The latest literature search for information for this document
was conducted in February, 1985; some newer information was also used.
Acute Toxicity to Aquatic Animals
An extensive review of the literature on the toxicity of aluminum to
aquatic organisms was published by Burrows (1977), but most of the studies were
conducted at pH less than 6.5. Durations of exposures reported in the
literature varied and test endpoints were diverse.
The earliest study of the toxicity of aluminum to fish was performed
by Thomas (1915) using mummichogs acclimated to fresh water. His report
lacked detail and it is unclear whether the aluminum sulfate was anhydrous
or hydrated. If the anhydrous form was used, 100% mortality of the
mummichog occurred in 1.5 and 5 days at 2,200 and 1,100 pg/L, respectively.
The pH was not reported and could have been depressed by the aluminum
salt present at the lethal test concentrations. More recent tests with
fish showing similar sensitivities to aluminum were conducted with brook
trout with a 4-day LC50 of 3,600 ng/L (Decker and Menendez 1974), rainbow
trout with a 3-day LC50 of 5,200 pg/L (Freeman and Everhart 1971), and common
carp with a 2-day LC50 of 4,000 pg/L (Muraraoto 1981). Other fish species
were less sensitive to aluminum.
The effect of pH on aluminum toxicity has been studied by several
investigators. In a study of the median time to death of rainbow trout,
Freeman and Everhart (1971) found an increase in aluminum toxicity as pH
increased from 6.8 to 8.99. Hunter et al. (1980) observed the same
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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 fathead minnow by Boyd (1979), Call (1984),
and Kimball (Manuscript). The studies by Freeman and Everhart (1971),
Hunter et al. (1980), and Kimball (Manuscript) were all flow-through or
daily renewal of test solutions and showed the highest toxicities,
whereas the other tests were static tests. The chemical forms of aluminum
might have been different due to the time the aluminum was in solution
and was able to form precipitate, thus becoming less available to organisms.
Acute toxicity of aluminum to invertebrate species occurred in about
the same range of concentrations as to fish. A 48-h EC50 of 3,690 pg/L
for Ceriodaphnia sp. (Call 1984) was the lowest reported acute value, whereas
the ECSOs with Daphnia magna ranged from 3,900 to 38,200 pg/L. The highest
LCSO was 55,500 pg/L in a test with a snail (Call 1984). No pH-dependent
trends were evident due to an insufficient number of tests with any species.
Species Mean Acute Values (Table 1) were calculated as geometric means of
the available acute values, and then Genus Mean Acute Values (Table 3) were
calculated as geometric means of the available freshwater Species Mean Acute
Values. Because data are available for only one species in each genus,
the species and genus mean acute values are identical. Several species
tested were not exposed to aluminum concentrations high enough to allow
calculation of an LCSO. 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. Measured acute values are available for the
four most sensitive genera. The freshwater Final Acute Value for aluminum
was calculated to be 1,894 pg/L using the procedure described in the
Guidelines and the Genus Mean Acute Values in Table 3.
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Chronic Toxicity to Aquatic Animals
Chronic toxicity values have been determined for aluminum with two
freshwater species (Table 2). Daphnia magna had a chronic value of 1,388
iJg/L after 28 days of exposure to aluminum sulfate (Kimball, Manuscript).
This value was based upon survival of the adult. Reproduction was impaired
at 2,840 Mg/L- Biesinger and Christensen (1972) obtained a 21-day LC50 of
1,400 Mg/L with]), magna, and they found 16% reproductive impairment at
320 Mg/L (Table 5), but the concentration of aluminum was not measured in
the test solutions.
Fathead minnows (Kimball, Manuscript) differed significantly in weight
and length from the controls after exposure to 7,100 Mg/L for the period
of embryonic development and 28 days posthatch. The chronic value was
5,777 Mg/L. Survival was affected at 9,200 Mg/L (Table 5). The chronic
tests indicate that, of the two species tested, the invertebrate was more
sensitive to aluminum than the vertebrate.
The only two available acute-chronic ratios are 27.52 with Daphnia magna
and 6.059 with the fathead minnow (Table 3). The Final Acute-Chronic
Ratio of 12.91 was calculated as the geometric mean of these two. Division
of the Final Acute Value by the Final Acute-Chronic Ratio results in a
Final Chronic Value of 146.7 Mg/L for fresh water at pH » 6.5 to 9.0.
Toxicity to Aquatic Plants
Single-celled plants were more sensitive to aluminum (Table 4) than
the other plants tested. Growth of a diatom was inhibited at 810 Mg/L,
and the diatom died at 6,480 Mg/L (Rao and Subramanian 1982). The green
alga, Selenastrum capricornutum, was about as sensitive to aluminum as
the diatom. Effects were found (Table 4) at concentrations ranging from
460 Mg/L (Call 1984) to 990 Mg/L (Peterson et al. 1974).
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Among multicellular plants, root weight of Eurasian watennilfoil was
significantly decreased at 2,500 ng/Lt but duckweed was not affected at
45,700 ng/L (Table 4).
Bioaccumulation
No bioaccumulation data are available because none of the reported
tissue concentrations had measured water concentrations for comparison.
Also, no U.S. FDA action level or other maximum acceptable concentration in
tissue is available for aluminum.
Other Data
Bringmann and Kuhn (1959a,b) found that Scenedesmus quadricauda was
more tolerant of aluminum than Chlorella pyrenoidosa in river water
(Table 5). They also did not find any toxic effects on Daphnia magna
during a 48-h exposure to 1,000,000 ug/L. Toxicity might have been reduced
by naturally occurring ligands in the river water.
Birge et al . (1980,1981) killed or deformed 102 of the embryos and
fry of rainbow trout during a 28-day exposure to 369 pg/L, but Hunter et al .
(1980) found no effect after a 10-day exposure of juveniles to 200,000 ug/L.
Freeman (1973) studied the growth of rainbow trout after exposure to aluminum
for 8 to 11 days.
Embryos and larva of the narrow-mouthed toad were very sensitive to
aluminum exhibiting 50% death and deformity during a 7-day exposure to 50
Mg/L (Birge 1978; Birge et al . 1979). Marbled salamander embryos and
larva showed the same effect after an 8-day exposure to 2,280 Mg/L (Birge
et al. 1978).
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Unused Data
Many data on the effects of aluminum on aquatic 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; Dickson 1983; Driscoll et al. 1980; Eddy and Talbot 1983; Gurm and
Keller 1984; Havas and Hutchinson 1982,1983; Jones 1940; Ogilvie and Stechey
1983; Staurnes et al. 1984; Schindler and Turner 1982; Schofield and
Trojnar 1980; Tease and Coler 1984; van Dam 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), Howells et al. (1983), Kaiser
(1980), McKee and Wolf (1963), Phillips and Russo (1978), and Thompson et
al. (1972) only present data that have been published elsewhere. Data were
not used if aluminum was a component of a mixture (Hamilton-Taylor and
Willis 1284; Havas and Hutchinson 1982; Markarian et al. 1980). Becker
and Kellor (1983), Marquis (1982), and Stearns et al. (1978) were not
used because the results were not adequately presented or could not be
interpreted. Also, data were not used if only enzymes were exposed (e.g.,
Christensen 1971/72; Christensen and Tucker 1976).
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 if the number of measurements of the concentration in
water was too small.
Field studies were not used because they either lacked aluminum con-
centrations in the water or reported no specific adverse effects (Buergel and
Soltero 1983; Gibbons et al. 1984; Knapp and Soltero 1983; Sonnichsen 1978;
Zarini et al. 1983).
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Summary
Acute tests have been conducted on aluminum with 14 freshwater species
at pH - 6.5 to 9.0. Quantitative LCSOs or ECSOs are available for only
seven of these species; the other tests resulted in effects on less than
50% of the organisms at the highest concentrations tested. The tested
species that was most sensitive to aluminum was the brook trout with a
96-h LC50 of 3,600 ug/L. Some studies found that the toxicity of aluminum
increased with pH, whereas other studies found the opposite. Two studies
have been conducted on the chronic toxicity of aluminum to aquatic animals.
An acute-chronic ratio of 27.52 was obtained with Daphnia magna, and a
ratio of 6.059 was obtained with the fathead minnow. The diatom, Cyclotella
meneghiniana. and the green alga, Selenastrum capricornutum, were affected
by concentrations of aluminum in the range of 400 to 900 pg/L. No biocon-
centration or bioaccumulation factors are available for aluminum because in
none of the studies were the concentrations in both tissue and water adequately
measured.
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 pH is between 6.5 and 9.0, if
the four-day average concentration of aluminum does not exceed 150 Mg/L
more than once every three years on the average and if the one-hour average
concentration does not exceed 950 pg/L more than once every three years
on the average.
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EPA believes that "acid-soluble" is probably the best/measurement
at present for expressing criteria for metals and the criterion for
aluminum was developed on this basis. However, at this time, no EPA
approved method for such a measurement is available to implement
criteria for metals through the regulatory programs of the Agency and the
States. The Agency is considering development and approval of a method
for a measurement such as "acid-soluble." Until one is approved, however,
EPA recommends applying criteria for metals using the total recoverable
method. This has two impacts: (1) certain species of some metals cannot
be measured because the total recoverable method cannot distinguish
between individual oxidation states, and (2) in some cases these criteria
might be overly protective when based on the total recoverable method.
The allowed average excursion frequency of three years is the Agency's
best scientific judgment of the average amount of time it will take an
unstressed aquatic ecosystem to recover from a pollution event in which
exposure to aluminum exceeds the criterion. Stressed systems, for example
one in which several outfalls occur in a limited area, would be expected
to require more time for recovery. The resiliencies of ecosystems and
their abilities to recover differ greatly, however, and site-specific
criteria may be established if adequate justification is provided.
Use of criteria for developing water quality-based permit limits and
for designing waste treatment facilities requires selection of an appropriate
wasteload allocation model. Dynamic models are preferred for the applica-
tion of these criteria. Limited data or other considerations might make
their use impractical, in which case one must rely on a steady-state
model. The Agency recommends the interim use of 1Q5 or 1Q10 for the
Criterion Maximum Concentration (CMC) design flow and 7Q5 or 7Q10 for the
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Criterion Continuous Concentration (CCC) design flow in steady-state
models for unstressed and stressed systems respectively. These matters
are discussed in more detail in the Technical Support Document for Water
Quality-Based Toxics Control (U.S. EPA 1985b).
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Table 1. Acute Toxiclty of Aluminum to Aquatic Animals
Species
Planar I an (adult) ,
Dugesla tlgrlna
Snail (adult),
Physa sp.
Snail (adult),
Physa sp.
Snail (adult),
Physa sp.
Snail (adult),
Physa sp.
Cladoceran «24 hr old),
Cerlodaphnia sp.
Cladoceran,
Daphnla tnagna
Cladoceran,
Paphnla magna
Cladoceran,
Daphnla magna
Amphipod (adult),
Gaimarus pseudol Imnaeus
Stonafly (nymph),
Acroneurla sp.
Midge ( larva),
Tanytarsus disslmills
Chinook salmon (juvenile),
Oncorhynchus tshawytscha
Method*
S. M
S. M
S, M
S. M
S, M
S, M
S. U
S, M
S, M
S. M
S. M
s, u
S, M
Chemical
Aluminum
chloride
Aluminum
chloride
Aluminum
chlor Ide
Aluminum
chloride
Aluminum
chlor Ide
Aluminum
chlor Ide
Aluminum
chloride
Aluminum
chloride
Aluminum
sul fate
Aluminum
chloride
Aluminum
chlor Ide
Aluminum
sul fate
Sodium
aluminate
Hardness
23,000t >23,000
55,500tf
>23,400
30,600
>24,700 30,600
3,690 3,690
3,900tn
>25,300
38,200 38,200
22,000 22,000
>22,600 >22,600
>79,900 >79,900
>4 0,000 >4 0,000
Reference
Brooke et al . 1 985
Call 1984
Call 1984
Call 1984
Call 1984
Call 1984
Blesfnger and
Chrlstensen 1972
Brooke et al . 1985
Klmball, Manuscript
Call 1984
Call 1984
Lamb and Bailey 198
Peterson et al . 197'
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Table 1. (continued)
Species Method*
Rainbow trout (juvenile). S, M
Salfflo galrdnerl
Rainbow trout (juvenile), S, H
Salmo galrdnerl
Rainbow trout (juvenile), S, M
Salmo gairdnerl
Rainbow trout (juvenile). S. H
Sal mo galrdnerl
Brook trout (juvenile), F, M
Salvellnus fonTlnalls
Fathead minnow (adult). S, U
Plmephatos promelas
Fathead minnow (juvenile), S, M
Pinephales pronelas
Fathead minnow (juvenile), S, M
Plmephales promelas
Fathead minnow (juvenile), F, M
Plmophales prone) as
Channel catfish (juvani)e), S, M
Ictalurus punctatus
Green sunflsh (juvenile). S, M
Cepomls cyaneltus
Yellow parch (juvenile), S, M
Perca f lavescens
Che* leal
Aluminum
chloride
Aluminum
chloride
Aluminum
chloride
Aluminum
chloride
Aluminum
suit ate
Aluminum
sul fata
Aluminum
cnlorlde
Aluminum
chloride
Aluminum
sul fate
Aluminum
chloride
Aluminum
chloride
Aluminum
chloride
Hardness LC50 Species Mean
(•g/L as or EC50 Acute Value
CaOOjl pH " (Mg/L>«» Reference
47.4 7.46 e,600ft - Call 1984
41.4 6.59 7,400 - Call 1964
47.4 7.31 14.600 - Call 1984
47.4 8.17 >24,700m 10,390 Call 1984
6.5 3,600 3,600 Decker and Menendez
1974
7.6 >18.900 - 8oyd 1979
47.4 7.61 >48,200 - Call 1984
47.4 8.05 >49,800 - Call 1984
7.34 35,000 35,000 Kimbal 1 , Manuscript
47.4 7.54 >47,900 >47,900 Call J984
47.4 7.55 >50,000 >50,000 Call 1984
47.4 7.55 >49,800 >49,800 Call 1984
* S = static; F = flow-through; H = measured; U = unmeasured.
** Results are expressed as aluminum, not as the chemical.
tt
48-hr test.
Aluminum chloride was added to Lake Superior water, the pH s adjusted, and the solution was aerated for 18 days
prior to addition of test organisms; not used in calculations.
Not used in calculations.
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Table 2. Chronic Toxlclty of AluMlnun to Aquatic Anlaals
Species
Cladoceran,
Daphnla magna
Fathead minnow
(embryo, larva),
Plmephales pronelas
Hardness
(•g/L as Halts Chronic Value
Test* Chemical CaCO,) pH
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Table 3. Ranked Canus Mean Acute Values with Species Mean Acute-Chronic Ratios
\l
lank*
14
13
12
11
10
9
a
7
6
5
4
3
2
Genus Mean
Acute Value
C^sA)
>79,900
>50,000
>49.aoo
>47,900
>40,000
38,200
35,000
30,600
>23,000
>22,600
22,000
10,400
3,690
Spec las
FRESHWATER SPECIES
Midge,
Tanytarsus dlsslnltls
Green sun fish,
Lepomis cyanel lus
Yellow perch,
Parca flavescens
Channel catfish,
Ictalurus punctatus
Chinook salmon,
Oncorhynchus tshaxytscha
Ctadoceran,
Daphnla maqna
Fathead minnow,
P Imephales prometas
Snail,
Physa sp.
Planar i an,
Dugasla tlqrjna
Stonet ly,
Acronurla sp.
Am phi pod,
Gammarus pseudol Imnaeus
Rainbow trout,
Salmo gairdnerl
Cladoceran,
Species Mem Species Mean
Acute Value Acute-Chronic
(Mg/L>" Ratio*"
>79,900
>50,000
>49,600
>47,900
>40,000
33,200 27.52
35,000 6.059
30,600
>23,000
>22,600
22,000
10,390
3.690
Carlodaphnla sp.
-------
TabU 3. (Continued)
Rank*
1
Genus Mean
Acute Value
3,600
Species
Brook trout,
Salvellnus fontlnalls
Species Mean
Acute Value
(nflA)**
3,600
Species Mean
Acute-Chronic
Ratio""
—
* Ranked from most resistant to most sensitive based on Genus Mean Acute Value.
Inclusion of "greater than" values In the rankings does not necessarily Imply a true
ranking, but does allow use of all genera for xhlch data are available so that the
Final Acute Value Is not unnecssartly lowered.
** From Table 1.
•••From Table 2.
Fresh mater (pH = 6.5 to 9.0)
Final Acute Value = 1,894 Mg/L
Crlterton Maximum Concentration = (1,894 ug/L) /2 = 947 ng/L
Flnal Acute-Chronic Rat lo = 12.'9I
Final Chronic Value = (1,894 Mg/L) / 12.91 = 146.7 Mg/L
-------
Table 4. Toxic I ty of Aluminum to Aquatic Plants
Species
Diatom,
Cyclotelia menegh 1 n 1 ana
Green alga,
Selenastrum capr Icornutum
Green alga,
Selenastrum capr icornutum
Green alga,
Selenastrum capr Icornutum
Eurasian watermll fol 1,
Hyrlophylium spicatum
Duckweed,
Lemna minor
Duckweed.
Lemna minor
Chemical
Aluminum
chloride
Sodium
alumlnate
Aluminum
chloride
Aluminum
chloride
Aluminum
Aluminum
chloride
Aluminum
chloride
Hardness
(mg/L as
pH CaCO,)
FRESHWATER
7.9
7.0 15
7.6 14.9
8.2 14.9
7.6 14.9
8.2 14.9
Duration
(days)
SPECIES
8
14
4
4
32
4
4
Effect
Inhibited
growth
alglstatic
algae Ida 1
Reduced cell
counts and
dry weight
EC50
(blomass)
EC50
(blomass)
EC50
(root weight)
Reduced frond
production
Reduced frond
production
Result
810
3,240
6,480
990-
1,320
570
460
2,500
>45,700
>45.700
Reference
Rao and Subramanian
1932
Peterson at al. 1974
Call 1984
Call 1984
Stanley 1974
Call 1984
Call 1984
* Results are expressed as aluminum, not as the chemical.
-------
Table 5. Other Data on Effects of Aluminum on Aquatic Organ ISMS
Species
Green alga.
Chloral la vuigarls
Green alga,
Chloral la vulgarls
Green alga,
Scenedesmus quadrlcauda
Protozoan,
Microregma heterostoma
Protozoan ,
Chilomonas paramecfum
Protozoan,
Peranema trichoporutn
Protozoan,
Tetrahymana pyrlformls
Protozoan,
Euqlena graci 1 is
Cladoceran,
Oaphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladocaran,
Daphn la matjna
Hardness
(•g/L as
Chemical CaC03>
Aluminum
chloride
Aluminum
sulfate
Aluminum
chloride
Aluminum
chloride
Aluminum
chloride
Aluminum
chloride
Aluminum
chloride
Aluminum
chloride
Aluminum
sulfate
Anmon 1 um
aluminum
suj fate
Potassium
aluminum
sutfate
Aluminum
chloride
_£H_
FRESHW
«
<7.0
7.5-
7.8
7.5-
7.8
5.5-
7.4
5.5-
6.5
5.5-
6.5
6.0
7.0
7.5
Duration
tfER SPECIES
3-4 mo
30 days
96 hr
28 hr
3 hr
3 hr
3 hr
3 hr
16 hr
16 hr
16 hr
48 hr
Effect
Result
(MS/LI*
Growth 4 ,000
inhibition
Maximum < 163, 000
growth reduced
Incipient 1,500-
Inhlbltlon 2,000
(river water)
Incipient 12,000
Inhibition
(river water)
Some 110
survival
Some 62,600
survival
Some UO
surv Ival
Some 111,800
survival
Incipient 21,450
Immobl 1 izatlon
Incipient 21,620
Immobl 1 ization
Incipient 21,530
Immobilization
Non- toxic 1,000,000
(river water)
Reference
Dejong 1965
Becker and Keller 1973
Bringmann and Kuhn
1959a,b
Bringmann and Kuhn
1959b
Ruttwen and Cairns
1973
Ruthven and Cairns
1973
Ruthven and Cairns
1973
Ruthven and Cairns
1973
Anderson 1944
Anderson 1944
Anderson 1944
Brlngraann and Kuhn
1959 a
-------
Table 5. (Continued)
Species Chemical
Cladoceran, Aluminum
Oaphnla magna chloride
Cladoceran, Aluminum
Daphnla magna chloride
Ctadoceran, Sodium
Daphnla magna alunlnate
Aquatic beetle (adult). Aluminum
Troplsterrous tat era i Is chloride
nlmbatus
Midge (Carva) , Aluminum
Tanytarsus dlsslrollls sulfate
Rainbow trout ( finger [ Ing), Aluminum
Salmo galrdnerl chloride
Rainbow trout (tIngerl Ing), Aluminum
Salmo gairdneri chloride
Rainbow trout ( f Ingerl Ing), Aluminum
Salmo galrdnerl chloride
Rainbow trout ( f Inqert ing) , Aluminum
Salmo galrdnerl chloride
Rainbow trout (fingerling). Aluminum
Salmo galrdnerl chloride
Rainbow trout (embryo), Aluminum
Salroo galrdnerl chloride
Rainbow trout Aluminum
(embryo and fry), chloride
Salmo galrdnerl
Rainbow trout Aluminum
(embryo and fry), chloride
Salmo gairdneri)
Hardness
(•g/L as
CnCOj)
45.3
45.3
27.0
pH Duration
17.43
46.8
28.3
28.3
56.6
56.6
104
(92-110)
102
(92-110)
6.5-
7.5
6.1-
7.5
7.0
7.0
8.99
6.64
6.80
7.0-
9.0
7.4
7.4
21 days
21 days
96 hr
Effect
EC16 (reduced
reproduction)
LC50
Mortality
Result
320
1,400
>40,000
14 days Changed fat 200
body
6.63 55 days 37* mortality 832
8.02 32 days 501 dead 5,230
8.48 7.5 days 50* dead
3 days 50* dead
44 days 50* dead
39 days 50* dead
Fertiliza-
tion to
hatch
28 days
No reduced
fertility
EC50 (death
and deformity)
5.140
5,200
513
5,140
5,200
560
28 days EC10 (death 369
and deformity)
Reference
Bleslnger and
Christensen 1972
Bleslnger and
Christensen 1972
Peterson et ol. 1974
Wootdrldge and Mooldrldge
1969
Lamb and Bailey 1981
Freeman and Everhart
1971
Freeman and Everhart
1971
Freeman and Everhart
1971
Freeman and Everhart
1971
Freeman and Everhart
1971
Everhart and Freeman
1973
Blrge 1978; Bfrge et al,
1973, I960
Birge et al. 1980, 198)
-------
Table 5. (continued)
Species
Rainbow trout (juvenile),
Salcno galrdnerl
Rainbow trout (juvenile),
Sal mo galrdnerl
Rainbow trout (juvenile).
Sal mo galrdnerl
Rainbow trout (juvenile),
Salmo qalrdnerl
Goldfish (60-90 mm) ,
Carasslus auratus
Goldfish
(embryo and fry),
Carasslus auratus
Common carp (juvenile),
Cyprlnus carplo
Common carp (juvenile),
Cyprlnus carplo
Fathead minnow (adult),
P Imephaias promelas
Fathead minnow (juvenile),
Plmephales promelas
Mummlchog (adult),
Fundu 1 us heteroc H tus
Mummlchog (adult),
F undu 1 us heteroc 1 1 tu s
Hardness
Img/L as
Chemical CaCO,)
Aluminum 25
sul fate
Aluminum 25
sul fate
Aluminum 25
su( fate
Aluminum 25
sul fate
Aluminum
potassium
sul fate
Aluminum 195
chloride
Aluminum
en lor Ida
Aluminum
chloride
Aluminum
chloride
Aluminum
chloride
Aluminum
sul fate
Aluminum
sut fate
pH Duration
7.0 10 days
8.0 96 hr
8.5 42 hr
9.0 42 hr
6.8 4 days
7.4 7 days
6.5 48 hr
6.6 48 hr
7.24- 28 days
8.15
36 hr
120 hr
Effect
No toxic Ity
40* mortal Jty
100* mortal Ity
100* mortal Ity
Reduced
survival time
EC50 (death
and deformity)
30* dead
10* dead
50* reduction
of acetylcho-
1 Inasterase
activity
Incipient
lethal
100* mortality
100* mortal Ity
Result
200,000
50.000
50 ,000
50,000
5,700
150
4,000
4,000
18,000
9,200
2,210
1,100
Reference
Hunter et al,
Hunter et al .
Hunter at al .
Hunter et al .
EHls 1937
Blrge 1978
Muramoto 1981
Muramoto 1981
1980
1980
1980
1980
Olson and Chrlstensen
1980
KImbaM Manuscript
Thomas 1915
Thomas 1915
-------
Table 5. (continued)
Species
Mosquitoflsh (adult female).
Gambusia afflnls
Mosquitoflsh (adult female),
Gambusia at finis
Threes pine stickleback
(adult),
Gasterosteus aculeatus
Larqemouth bass
(embryo, larva) ,
Mlcropterus salmoides
Narrow-mouthed toad
(embryo, larva),
Gastrophryne carolInensls
Marbled salamander
(embryo, larva),
Ambystoma opacuro
Hardness
(mg/L as
Chemical CaC03j
Aluminum -
chloride
Aluminum
chloride
Aluminum
nitrate
Aluminum 93-105
chloride
Aluminum
chloride
Aluminum
chloride
195
93-105
_EH_
4.3-
7.2
1.4-
7.7
>7.0
7.2-
7.8
7.4
7.2-
7.8
Duration
4 days
4 days
10 days
Effect
LC50 (high
turbidity)
LC50 (high
turbidity)
No toxlcity
Result
(|»g/L)* Reference
26,900
18,500
70
8 days EC50 (death 170
and deformity)
7 days EC 50 (death 50
and deformity)
8 days EC50 (death 2,280
and deformity)
Wai I en et al. 1957
Wai I en et al. 1957
Jones 1939
Blrge et al . 1978
Blrge 1978; Blrge at at.
1979
Birge et al . 1978
V)
* Results are expressed as aluminum, not as the chemical.
-------
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