AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR
ACROLEIN
(CAS Registry Number 107-02-8)
July 1, 2009
U.S. ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF WATER
OFFICE OF SCIENCE AND TECHNOLOGY
HEALTH AND ECOLOGICAL CRITERIA DIVISION
WASHINGTON D.C.
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NOTICES
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.
in
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FOREWORD
Section 304(a) (1) of the Clean Water Act of 1977 (P.L. 95-217) requires the
Administrator of the Environmental Protection Agency to publish water quality criteria that
accurately reflect the latest scientific knowledge on the kind and extent of all identifiable effects
on health and welfare that might be expected from the presence of pollutants in any body of
water, including ground water. 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. Alternatively, states may use
different data and assumptions than EPA in deriving numeric criteria that are scientifically
defensible and protective of designated uses. It is not until their adoption as part of state water
quality standards that criteria become regulatory. Guidelines to assist the states and Indian tribes
in modifying the criteria presented in this document are contained in the Water Quality Standards
Handbook (U.S. EPA 1994). This handbook and additional guidance on the development of
water quality standards and other water-related programs of this agency have been developed by
the Office of Water.
This final document is guidance only. It does not establish or affect legal rights or
obligations. It does not establish a binding norm and cannot be finally determinative of the
issues addressed. Agency decisions in any particular situation will be made by applying the
Clean Water Act and EPA regulations on the basis of specific facts presented and scientific
information then available.
Ephraim S. King
Director
Office of Science and Technology
IV
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ACKNOWLEDGMENTS
Gregory J. Smith
Great Lakes Environmental Center
Columbus, Ohio
Frank Gostomski
(document coordinator)
U.S. EPA
Health and Ecological Criteria Division
Washington, D.C.
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CONTENTS
Page
NOTICES iii
FOREWORD iv
ACKNOWLEDGMENTS v
TABLES vii
FIGURES vii
Introduction 1
Acute Toxicity To Aquatic Animals 5
Chronic Toxicity To Aquatic Animals 6
Toxicity To Aquatic Plants 8
Bioaccumulation 9
Other Data 9
Unused Data 11
Summary 12
National Criteria 14
Implementation 14
References 31
VI
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TABLES
1. Acute Toxicity of Acrolein to Aquatic Animals 19
2a. Chronic Toxicity of Acrolein to Aquatic Animals 22
2b. Acute-Chronic Ratios 23
3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic Ratios 24
4. Toxicity of Acrolein to Aquatic Plants 26
5. Bioaccumulation of Acrolein by Aquatic Organisms 27
6. Other Data on Effects of Acrolein on Aquatic Organisms 28
FIGURES
1. Ranked Summary of Acrolein GMAVs - Freshwater 16
2. Ranked Summary of Acrolein GMAVs - Saltwater 17
3. Chronic Toxicity of Acrolein to Aquatic Animals 18
vn
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Introduction1
Acrolein, also known as acrylaldehyde, allyl aldehyde and 2-propenal, has a wide-variety
of applications. It is used directly as a biocide for aquatic weed control, and is currently
registered under the trade name MAGNACIDE® H primarily for use in irrigation canals. This
product is commonly applied to surface waters at a rate of 1-15 mg/L, which is much higher than
the acutely toxic levels for most aquatic animals tested (Fritz-Sheridan 1982; U.S. EPA 2007).
Acrolein is also used for algae, weed and mollusk control in recirculating process water systems;
for slime control in the paper industry; to protect liquid fuels against microorganisms; and to
control sulfate reducing bacteria that produce corrosive hydrogen sulfide in oilfield water
systems (IARC 1985; U.S. EPA 2007). It is also used for cross-linking protein collagen in
leather tanning and for tissue fixation in histological samples.
Different forms of acrolein are widely used as an intermediate in the chemical industry
(ATSDR 1989). The dimmer, which is prepared by a thermal, uncatalyzed reaction, has several
applications including use as an intermediate for cross-linking agents, humectants, plasticizers,
polyurethane intermediates, copolymers, and homopolymers and creaseproofing cotton. The
monomer is utilized in synthesis via the Diels-Alder reaction as a dienophile or a diene. Acrolein
is widely used in copolymerization, but its homopolymers do not appear commercially
important. The copolymers of acrolein are used in photography, for textile treatment, in the paper
industry, as builders in laundry and dishwasher detergents, and as coatings for aluminum and
steel panels, as well as other applications.
Isolated acrolein is produced in a closed system by heterogeneously catalyzed gas-phase
oxidation of propene. Acrolein is also produced as a non-isolated intermediate during the
manufacture of acrylic acid. In the 1990's, worldwide production was about 120,000 tons.
Worldwide capacity was estimated at 125,000 tons/year, of which U.S. capacity was 35,000
tons/year (WHO 2002).
A comprehension of the "Guidelines for Deriving Numerical National Water Quality Criteria for
the Protection of Aquatic Organisms and their Uses" (Stephan et al. 1985), hereafter referred to as the
Guidelines, is necessary to understand the following text, tables and calculations.
1
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Acrolein is a colorless liquid at room temperature with a structural formula of
CH2=CHCHO and a molecular weight of 56.06 g/mol. It melts at -86.95 °C, boils at 52.5 to
53.5°C and has a density of 0.8410 at 20°C (Weast 1975). The vapor pressure at 20°C is 29.3 to
36.5 KPa, and its water solubility is 206 to 270 g/L at 20°C (Standen 1967; WHO 2002). It has
an octanol/water partition coefficient (Log Kow) range of-0.01 to 0.90 (-0.01 is recommended by
Karickhoff and Long 1995), and an organic carbon/water partition coefficient (Log Koc) of-2.19
to 2.43 (WHO 2002).
A flammable liquid with a pungent odor, acrolein is an unstable compound that
undergoes polymerization to the plastic solid disacryl, especially under light or in the presence of
alkali or strong acid (Windholz 1976). It is the simplest member of the class of unsaturated
aldehydes, and the extreme reactivity of acrolein is due to the presence of a vinyl group
(H2C=H~) and an aldehyde group on such a small molecule (Standen 1967). Additions to the
carbon-carbon double bond of acrolein are catalyzed by acids and bases. The addition of
halogens to this carbon-carbon double bond proceeds readily (Standen 1967).
Acrolein is released into the environment as a product of natural fermentation (WHO
2002), as a volatile component of essential oils extracted from the wood of oak trees (Slooff et
al. 1994), as a product of the incomplete combustion of organic matter (Lipari et al. 1984), and
by photochemical oxidation of hydrocarbons in the atmosphere (Ghilarducci and Tjeerdema,
1995). As a product of the incomplete combustion of organic matter, acrolein is released by
waste incinerators, furnaces, fireplaces, power plants, burning vegetation (e.g., forest fires),
combustion of polyethylene plastics, and the cooking of food (WHO 2002).
Potential routes of acrolein degradation are via volatilization, microbial metabolism, and
absorption into plants by cross-linking of protein. Degradation products include 3-
hydroxypropanol, acrylic acid, allyl alcohol, propanol, propionic acid and oxalic acid. A unique
feature of 3-hydroxypropanol is that it is in equilibrium with acrolein, and thus does not fully
degrade via hydrolysis. Data are not available to characterize the rate of acrolein photolysis in
water (U.S. EPA 2007).
Bowmer et al. (1974) described the loss of acrolein by volatilization and degradation in
sealed bottles and tanks of freshwater. The amounts of acrolein dissipated after eight days were
34 percent from the tank and 16 percent from the bottles. The lack of turbulence in the tank
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reduced acrolein loss by volatilization to 1/20 of what would be expected if volatilization were
controlled only by resistance in the gas phase and any discrete surface layers. The primary
degradation reaction is reversible hydrolysis to p-hydroxypropionaldehyde, which is less volatile
than acrolein (Geyer 1962).
Acrolein can enter the aquatic environment by its use as an aquatic herbicide, from
industrial discharge, and from the chlorination of organic compounds in wastewater and drinking
water treatment. It is often present in trace amounts in foods and is a component of smog, fuel
combustion, wood, and possibly other fire and cigarette smoke.
The fate of acrolein in freshwater was observed in buffered solutions and in natural
channel waters (Bowmer and Higgins 1976). Equilibrium between acrolein and its degradation
products was reached in the buffered solution following dissipation of 92 percent of parent
compound, but in the natural channel waters there was no indication of equilibrium, with the
dissipating reaction apparently continuing on to completion. Also, in the natural channel waters,
the accumulation of a reaction (degradation) product was greater at higher initial acrolein
concentration, and decay was rapid when acrolein concentrations fell below 2 to 3 mg/L. The
initial period of slow decline preceding the rapid dissipation period was thought to be the result
of microbiological processes. Unlike earlier works (Bowmer et al. 1974), there was an 8- to 10-
fold increase in the observed dissipation rate as compared to the expected rate in two of four
flowing water channels, suggesting major losses in volatilization and absorption. A half-life of
approximately seven hours was observed for acrolein in freshwater by Nordone et al. (1998), but
the authors noted that the dissipation rate was both concentration and temperature dependent.
The presence of viable microbial populations also heavily influences the acrolein degradation
rates in freshwater systems (Smith et al. 1995).
In the marine environment, acrolein undergoes hydrolysis and oxidation to form P-
hydroxypropanol and p-hydroxy propionic acid (Smith 1962). A half-life of less then 20 hours
was reported by Rustenbil (1981).
Limited studies are available reporting the concentrations of acrolein in freshwater, and
saltwater occurrence data are lacking. Analysis of Dayton, Ohio municipal effluents showed the
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presence of acrolein in 6 of 11 samples, with concentrations ranging from 20 to 200 //g/L (U.S.
EPA 1977). During the 1980s, acrolein was not detected in raw or treated Canadian water
supplies, with the limit of detection ranging from 0.1-2.5 //g/L (Environment Canada
1989a,b,c,d; Otson 1987). For 798 well or surface water samples collected from unspecified
locations in the United States, acrolein was detected (detection limit not reported) in only 2
samples, and the median concentration of acrolein in these samples was <14 //g/L (Staples et al.
1985).
Monitoring studies conducted after field application show that acrolein can be transported
up to 61 miles from the point of application. Reported half-lives ranged from 2 to 20 hours
based on concentrations measured downstream of application. Field studies also determined that
acrolein volatilizes from treated waters and represents a source of exposure to non-target animals
through inhalation (U.S. EPA 2007).
The mechanism of toxic action of acrolein, observed in mammalian and other systems,
includes cell wall degradation and disrupting the cell's ability to inactivate toxic chemicals
(Siemering et al. 2008). Other effects on cell energetics include reduction in intracellular ATP
levels in tissue culture (Monteil et al. 1999), and reduced beating activity of myocytes (Toraason
etal. 1989).
A comprehension of the "Guidelines" for Deriving Numerical National Water Quality
Criteria for the Protection of Aquatic Organisms and Their Uses" (Stephan et al. 1985),
hereinafter referred to as the "Guidelines," and the response to public comments concerning that
document (U.S. EPA 1985) is necessary to understand the following text, tables and calculations.
Results of such intermediate calculations as recalculated LCSOs and Species Mean Acute Values
(Table 1) and chronic values (Table 2) are given to four significant figures to prevent roundoff
error in subsequent calculations, not to reflect the precision of the value. The criteria presented
herein are the agency's best estimate of maximum concentrations of the chemical of concern to
protect most aquatic organisms, or their uses, from any unacceptable short- or long-term effects.
Whenever adequately justified, a national criterion may be replaced by a site-specific criterion
(U.S. EPA 1983a), which may include not only site-specific criterion concentrations (U.S. EPA
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1983a), but also site-specific durations of averaging periods and site-specific frequencies of
allowed excursions (U.S. EPA 1991). The latest comprehensive literature search for this
document was conducted in June, 2009, with some new information also included.
Acute Toxicity to Aquatic Animals
Data that are suitable, according to the "Guidelines," for the derivation of a freshwater
Final Acute Value (FAV) are included in Table 1. Fifteen species representing fourteen genera
were tested with acrolein to determine its acute toxicity to these species (Table 3). Species Mean
Acute Values (SMAV) ranged from 7 //g/L for the African clawed frog (Xenopus laevis) to
5,920 //g/L for an insect (Peltoperia mar id). The white sucker (Catostomus commersonf) was
the second most sensitive species tested, with a SMAV of 14 //g/L. Rainbow trout
(Oncorhynchus mykiss) and the bluegill sunfish (Lepomis macrochirus) were the third and fourth
most sensitive species tested, with SMAVs of 16 and 27.19 //g/L, respectively.
The least sensitive group of freshwater species to acrolein toxicity was invertebrates. The
insect (Peltoperia maria) was the most tolerant to acrolein with a SMAV of 5,920 //g/L,
followed by the midge (Chironomus riparius) with a SMAV of 510 //g/L, the snail (Physa
heterostrophd) with a SMAV of 368 //g/L, and the scud (Gammarus minus) with a SMAV of
180 //g/L. The snail (Aplexa hypnorum) and midge (Tanytarsus dissimilis) had SMAVs of >151
Mg/L acrolein each. The planktonic crustacean, Daphnia magna, was the most acutely sensitive
invertebrate to acrolein with an SMAV of <39.76.
Freshwater SMAVs and Genus Mean Acute Values (GMAV) were derived from
available acute values (Tables 1 and 3). GMAVs were available for 14 genera; the most
sensitive was the amphibian, Xenopus, which was 846 times more sensitive than the least
sensitive species, an insect, Peltoperia (Figure 1). The four most sensitive genera were within a
factor of 4.1 of one another. The freshwater FAV for acrolein is 5.920 //g/L and was calculated
using the procedure described in the "Guidelines" and the GMAVs in Table 3. The FAV is
slightly lower than the lowest freshwater SMAV of 7 //g/L for the African clawed frog, X laevis.
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The acute toxicity of acrolein to saltwater animals has been tested with only four species
(Table 1). The most sensitive was the brown shrimp (Penaeus aztecus) with a SMAV of 100
fj-g/L, followed by the eastern oyster (Crassostrea virginica), with a SMAV of 106 //g/L. The
two most tolerant species were the mysid (Americamysis bahid) and the sheepshead minnow
(Cyprinodon variegatus), with SMAV values of 500 and 428 //g/L acrolein, respectively
(Figure 2).
Since SMAVs are available for only three of the eight required families as specified in
the Guidelines (Stephan et al. 1985), a saltwater FAV cannot be calculated for acrolein at this
time.
Chronic Toxicity to Aquatic Animals
The available data that are usable according to the "Guidelines" concerning the chronic
toxicity of acrolein are presented in Table 2a. All tests were conducted with measured
concentrations of acrolein. Macek et al. (1976) conducted the only freshwater invertebrate
chronic test. Based on the cumulatively reduced survival of/), magna through three generations,
a chronic value of 23.83 //g/L was obtained from chronic limits of 16.9 and 33.6 //g/L (Table
2a). The acute value for this species by the same investigators was 57 //g/L, and this results in
an acute-chronic ratio (ACR) of 2.392 (Table 2b).
Macek et al. (1976) also conducted a life cycle toxicity test with acrolein and the fathead
minnow, P. promelas, that resulted in a chronic value of 11.4 //g/L based on an EC20 analysis of
the data (Table 2a). Survival of newly-hatched second generation fathead minnow fry was
significantly reduced at 41.7 //g/L. A dilutor malfunction killed or severely stressed the fish at
an intermediate concentration (20.8 Mg/L), so no second generation fish were produced. A 6-day
incipient LC50 value of 84 //g/L was the only acute value reported for this species by the same
authors using a flow-through test with unmeasured concentrations (Table 6).
Two additional chronic tests have been conducted with acrolein and the fathead minnow.
Sabourin (1986, 1987) conducted a flow-through measured early life-stage (ELS) toxicity test
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with acrolein and P. promelas in a reverse osmosis-treated and well water blended mixture.
Embryos and larvae were exposed in a continuous-flow diluter for a total of 32 days to five
concentrations of acrolein that ranged from 3.8 to 66.8 //g/L. The no-observed-effects-
concentration (NOEC) and lowest-no-observed-effects-concentration (LOEC) for survival were
recorded at 9.1 and 30.8 //g/L, respectively, with a resultant chronic value of 16.74 //g/L (Table
2a). The ACR of 1.774 was calculated using the acute value of 29.7 //g/L from a companion
study and dividing by the chronic value of 16.74 //g/L (Table 2b).
Spehar (1989) conducted a 32-day flow-through measured ELS toxicity test with acrolein
and P. promelas in filtered Lake Superior water. Survival, the most sensitive endpoint, was
significantly reduced at 35 //g/L compared to controls, but not at acrolein concentrations of 14
Mg/L and lower. Based upon survival, the chronic value was 22.14 //g/L. Spehar (1989) also
determined an acute value of 27 //g/L for this species, and when divided by the chronic value of
22.14 //g/L, yields an ACR of 1.220 (Table 2b).
A 32-day ELS test was also conducted with embryos and fry of the flagfish, Jordanella
floridae in filtered Lake Superior water (Spehar 1989). Five acrolein exposure concentrations
were tested which ranged from 1.4 to 42 //g/L in the flow-through measured test. Percent hatch
was not affected by any of the acrolein concentrations. At the end of the test, survival was not
significantly reduced in any of the exposure concentrations; however, growth (weight) was
significantly reduced in the highest exposure concentration (42 //g/L) relative to the controls.
Based upon growth, the chronic limits were 16 and 42 //g/L, and the resultant chronic value for
flagfish was 25.92 //g/L. A companion acute test was conducted in the study, and division of the
acute value (51 //g/L) by the chronic value (25.92 //g/L) yields an ACR of 1.968 for flagfish
(Table 2b).
Three valid freshwater ACRs are available for acrolein using the fourth, sixth and seventh
most acutely sensitive tested species of freshwater animals (Table 3). Two ACRs were available
for the fathead minnow, P. promelas., which differed by a factor of approximately 1.5 times. The
geometric mean of these two values is 1.471. Since the three valid ACRs (1.471, 1.968 and
2.392) differed by only a factor of 1.6 (Table 3), the Final Acute to Chronic Ratio (FACR) is
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calculated as the geometric mean of the three values, or 1.906. These data show that there is
little difference in concentrations between the acute and chronic effects of acrolein on D. magna
and the tested fish species. As stipulated in the Guidelines (Stephan et al. 1985), if the most
appropriate species mean ACRs are less than 2.0, acclimation has probably occurred during the
chronic test, and the FACR should be assumed to be 2.0. Thus the FACR for acrolein is 2.0. It
appears from available data (Figure 3) that all tested freshwater species will be protected from
adverse effects due to chronic acrolein exposure by the freshwater Chronic Value (3.0 //g/L).
Toxicity to Aquatic Plants
Four acceptable tests are available with freshwater plant species exposed to acrolein in
tests lasting from 5 to 14 days (Table 4). Even though the exposures were measured in the
studies conducted by Hughes and Alexander (1992a,b,c,d,e), the authors reported nominal effect
concentrations because the acrolein concentrations at test termination was less than the detection
limit. Based on this approach, the adverse effect concentrations from these freshwater tests
ranged from 36 //g/L for Anabaena flos-aquae to 72 //g/L for the duckweed, Lemna gibba.
Toxicity tests with acrolein have been conducted using a single saltwater plant species
(Table 4). The diatom, Skeletonema costatum, had a five-day ECso value of 28 //g/L acrolein
based on cell density.
Additional fresh- and saltwater plant information is included with "Other Data." These
published studies describe the use of acrolein to control aquatic macrophytes and algae (see
Table 6); no appropriate plant effect data are available. In some cases, test methods were
insufficiently described to evaluate reported results. In others, because of the methods used, no
actual exposure concentration under field conditions could be calculated. In a few instances,
results were reported where acrolein was used in the control of the weeds, but no quantitative
measurements were made (Ferguson et al. 1965, Unrau et al. 1965, van Overbeek et al. 1959).
A Final Plant Value, as defined in the Guidelines, cannot be obtained because no test in
which the endpoint was biologically important and the concentrations of acrolein were
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sufficiently measured has been conducted with an important aquatic plant species.
Bioaccumulation
One study was conducted to measure the bioconcentration of acrolein in freshwater
animals that, according to the "Guidelines," meet the requirements for inclusion in this section of
the document (Table 5). Barrows et al. (1978) measured the whole body burden in juvenile
bluegill (Lepomis macrochirus) exposed to 13.1 //g/L acrolein for 28 days. The half-life in
tissue was greater than seven days, and thin-layer chromatography was used to verify
concentrations. Lipid concentrations were measured (Johnson 1980) for the test fish and the
bioconcentration results were lipid normalized, which increased the bioconcentration factor from
344 to 7,167.
No bioconcentration factors are available for saltwater species based on the literature
search conducted.
No U.S. FDA action level or other maximum acceptable concentration in tissue, as
defined in the "Guidelines," is available for acrolein. Therefore, a Final Residue Value cannot
be calculated.
Other Data
Additional data on the lethal and sublethal effects of acrolein on freshwater species that
do not comply with the data requirements described in the "Guidelines" for inclusion in other
tables are presented in Table 6. Reduced DNA synthesis of the green alga, Dunaliella bioculata,
was observed at 100 //g/L (Marano and Puiseux-Dao 1982), and various species of aquatic
weeds were damaged or destroyed following treatment with 500 to 25,000 //g/L of acrolein
(Ferguson et al. 1965; Fritz-Sheridan 1982; Unrau et al. 1965; van Overbeek et al. 1959).
Bringmann and Kuhn (1978) determined that the 72-hour toxic concentration to the protozoan,
Entosiphon sulcatum, was 850 //g/L of acrolein.
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Ninety-eight percent of Australorbis glabratus adult snails and 100 percent of snail
embryos died after a 24-hour exposure to 10,000 //g/L (Ferguson et al. 1961), and the 24-hour
EC50 of acrolein exposed Asiatic clams (Corbicula flumined) was 300 //g/L (Foster 1981).
Acutely fed and chronic unmeasured toxicity values were determined for the cladoceran,
Ceriodaphnia dubia (Union Carbide Corporation 1997), yielding a ACR value of 2.857
(400^-140 //g/L), which is very similar to the ACR value of 2.392 determined for Daphnia
magna (Macek et al. 1976). Mayfly nymphs (Ephemerella walkerf) were observed to avoid
acrolein concentrations greater than 100 //g/L (Folmar 1978).
Ten short-term exposures (either 24 or 48 hours) with seven fish species yielded acute
toxicity values in the range of 46 to 140 //g/L. Static tests with unmeasured concentrations were
run by Bond et al. (1960), Folmar (1976), Louder and McCoy (1962) and Bridie et al. (1979).
The studies of Burdick et al. (1964) and Macek et al. (1976) were performed under flow-through
conditions with unmeasured concentrations. The value from Bartley and Hattrup (1975), who
reported 32 percent mortality of rainbow trout in 48 hours at 48 //g/L, was the only value based
on a flow-through exposure with measured acrolein concentrations. Because of differences in
test methods and the volatility of acrolein, no meaningful comparison of relative sensitivity
among the fish species is possible.
The avoidance response of rainbow trout at 100 //g/L is above reported acute levels
(Folmar 1976). Folmar (1980) reported flavor impairment of rainbow trout flesh for up to four
days after a four-hour exposure to 90 //g/L.
Additional data on the lethal and sublethal effects of acrolein on saltwater species that do
not comply with data requirements described in the "Guidelines" for inclusion in other tables are
presented in Table 6. The 48-hour LC50 values for three saltwater species are in the range from
240 to 2,100 //g/L, with the juvenile longnose killifish, Fundulus similis, being the most
sensitive. Rustenbil (1981) observed detachment of the mussel, Mytilus edulis., at a
concentration of 600 //g/L acrolein.
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Unused Data
Based on the requirements set forth in the guidelines (Stephan et al. 1985), the following
studies are not acceptable for the following reasons and are classified as unused data. Some data
concerning the effects of acrolein on aquatic organisms and their uses were not used because the
tests were conducted in mixtures of chemicals (i.e., Albarino et al. 2007; Blondeau 1959;
Bowmer and Smith 1984; Corbus 1982; Donohue et al. 1966; Hayworth and Melwani 2004;
McLarty 1960; Power 1982; Snyder-Conn 1997) or a control was not included with the study
(i.e., Bowmer and Sainty 1977; Bowmer et al. 1979).
Results were not used when the test organism or the test material were not adequately
described (i.e., Baker Performance Chemical 1991; Hopf and Muller 1962; Juhnke and
Luedemann 1978; Mayer 1974; Tchan and Chiou 1977), the organism tested is not resident to
North America (i.e., Alabaster 1969), the site was previously contaminated (i.e., Underwood and
Paterson 1993), or the test material was just sprayed on the plants (i.e., Blackburn 1963;
Siemering et al. 2008).
Baker Performance Chemical (1991), Beauchamp et al. (1985), Butler (1965a,b), Eisler
(1994), Epstein and Legator (1971), Folmar (1977), Freidig et al. (1999), Grahl (1983), McKim
(1977), Russom (1997), Seward et al. (2001), Siemering et al. (2003) and Yarbrough and Schultz
(2007) compiled data from other sources, and non-English studies were not translated (i.e.,
Baran-Marano and Izard 1968; Bringmann and Kuhn 1980, 1981; Bringmann et al. 1980). Data
were not used if there were no interpretable concentration, time, or response data, or if the
toxicity test evaluated only a limited number of test organisms (
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Johnson and Epel 1983; Rebhun and Ben-Amotz 1986; Union Carbide Chemical and Plastics Co.
1991; Woodiwiss and Fretwell 1974; Yarzhombek et al. 1991). Dypbukt et al. (1989), Horton et
al. (1997), Minko et al. (2008), Seiner et al. (2007), Szadkowski and Myers (2008) and
Thompson and Burcham (2008) only exposed enzymes, excised or homogenized tissue, or cell
cultures.
Summary
Sufficient data are available to derive freshwater criteria for acrolein, but the lack of data
precludes the estimation of saltwater criteria, a final plant value and a residue value. Additional
studies are needed to provide the necessary data to satisfy the criteria derivation requirement as
currently specified in the Guidelines.
Acute toxicity of acrolein was tested in fifteen species representing fourteen genera of
freshwater organisms. Toxicity values ranged from 7 //g/L for the African clawed frog Xenopus
laevis to 5,920 //g/L for the insect Peltoperia maria. Of the four most sensitive freshwater
species tested, one was an amphibian and three were fish species (Table 3 and Figure 1). No
relationships have been demonstrated between water quality characteristics (such as hardness
and pH) and toxicity. The least sensitive group of freshwater species to acrolein toxicity was
invertebrates. The freshwater Final Acute Value (FAV) is 5.920 //g/L, which is slightly lower
than the LC50 for the most sensitive tested species, X. laevis. Acute toxicity has been tested with
only four species of saltwater organisms (Table 1 and Figure 2). Species Mean Acute Values
ranged from 100 //g/L for the brown shrimp (Penaeus aztecus) to 500 //g/L for the mysid
(Americamysis bahid). Since SMAVs are available for only three of the eight required families
as specified in the Guidelines (Stephan et al. 1985), a saltwater FAV cannot be calculated for
acrolein at this time.
Chronic toxicity of acrolein was tested in three freshwater species, but no saltwater
species (Table 2a and Figure 3). More studies are needed for marine animals in order to estimate
acute and chronic saltwater criteria for acrolein. The most chronically sensitive freshwater
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species tested was the fathead minnow, Pimephalespromelas, with a Chronic Value (CV) of
11.4 //g/L based on reduced survival (Macek et al. 1976). Two additional studies with this
species had measured CVs of 16.74 //g/L (Sabourin 1986) and 22.14 //g/L (Spehar 1989), also
based upon a survival endpoint. The remaining freshwater fish tested, the flagfish Jordanella
floridae, had a CV of 25.92 //g/L based on growth (Spehar 1989). The only freshwater
invertebrate tested chronically was the cladoceran Daphnia magna, with a CV of 23.83 //g/L
based on survival (Macek et al. 1976). Data were available to calculate a Final Acute-Chronic
Ratio (FACR) using three freshwater species: D. magna, the fathead minnow and the flagfish.
Since the three valid ACRs (2.392, 1.471 and 1.968) differed by only a factor of 1.6, the FACR
is calculated as the geometric mean of the three values, or 1.906. These data show that there is
little difference in concentrations between the acute and chronic effects of acrolein on D. magna
and the tested fish species. As stipulated in the Guidelines (Stephan et al. 1985), if the most
appropriate species mean ACRs are less than 2.0, acclimation has probably occurred during the
chronic test, and the FACR should be assumed to be 2.0. Thus the FACR for acrolein is 2.0. It
appears from available data that all tested freshwater species will be protected from adverse
effects due to acrolein by the freshwater Chronic Value (Figure 3).
Acceptable data on the toxicity of acrolein to freshwater and saltwater plants are
available for five species. Freshwater algae are affected by concentrations of acrolein as low as
36 //g/L, based on data for three species. The duckweed, Lemna gibba, was similarly affected at
72 //g/L acrolein, as was the marine diatom, Skeletonema costatum, with a ECso value of 28
//g/L.
One study estimated the bioconcentration of acrolein in bluegill, with a lipid normalized
freshwater bioconcentration factor of 7,167 (Barrows et al. 1978). Bioconcentration factors are
not available for saltwater species based on the literature search conducted. No U.S. FDA action
level or other maximum acceptable concentration in tissue, as defined in the "Guidelines," is
available for acrolein. Therefore, a Final Residue Value cannot be calculated.
13
-------
National Criteria
The procedures described in the "Guidelines for Deriving Numerical National Water
Quality Criteria for the Protection of Aquatic Organisms and Their Uses" (Stephan et al. 1985)
indicate that, except possibly where a locally important species is very sensitive, freshwater
aquatic organisms and their uses should not be affected unacceptably if the one-hour average
concentration of acrolein does not exceed 3.0 //g/L more than once every three years on the
average, and if the four-day average concentration of acrolein does not exceed 3.0 //g/L more
than once every three years on the average.
Since SMAVs are available for only three of the eight required families as specified in
the Guidelines (Stephan et al. 1985), a saltwater FAV cannot be calculated at this time for
acrolein. Likewise, the lack of chronic data precludes the development of a saltwater chronic
criterion at this time.
Implementation
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 or tribal 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 and tribes 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 1987, 1994). In each
standard a state or tribe 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 1994), but also site-specific, and possibly pollutant-specific, durations of averaging periods
and frequencies of allowed excursions (U.S. EPA 1991). The averaging periods of "one hour"
14
-------
and "four days" were selected by the U.S. EPA on the basis of data concerning how rapidly some
aquatic species react to increases in the concentrations of some 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 1991). However, various
species and ecosystems react and recover at greatly different 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 into state or tribal water quality standards, for
developing water quality-based permit limits requires selection of an appropriate wasteload
allocation model. Although dynamic models are preferred for the application of these criteria
(U.S. EPA 1991), 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 1987, 1991).
15
-------
Figure 1. Ranked Summary of Acrolein GMAVs - Freshwater.
O)
C
o
"•£
2
*j
c
0)
o
c
o
o
+rf
u
0
t
UJ
8
10000
1000 .
100 :
10 -
Summary of Ranked Acrolein GMAVs
Freshwater
D D
0.0 0.1
Freshwater Final Acute Value = 5.9 20ug/L Acrolein
CriteriaMaximum Concentration = 3.0ug/L Acrolein
0.2 0.3 0.4 0.5 0.6 0.7
Genus Mean Acute Values
(Cumulative Fraction)
0.8 0.9
1.0
n Freshwater Invertebrates
• Freshwater Fish
/\. Freshwater Amphi bian
16
-------
Figure 2. Ranked Summary of Acrolein GMAVs - Saltwater.
c
o
0)
o
c
o
O
+•«
I
lil
2
1000
100
10
Summary of Ranked Acrolein GMAVs
Saltwater
0.0 0.1
0.2
0.3
0.4
0.5
0.6
0.7
0.8 0.9
1.0
Genus Mean Acute Values
(Cumulative Fraction)
O Saltwater Invertebrates
O^altwater Fish
17
-------
Figure 3. Chronic Toxicity of Acrolein to Aquatic Animals.
1000
c
O
to
is
o
o
o
"o
£
HI
_0)
2
o
100
10
Chronic Toxicity of Acrolein to Aquatic Animals
Freshwater Final Chronic Value = 3.0 ug/L Acrolein
0.0 0.1 0.2 0.3 0.4 0.5 0.6 0.7
Genus Mean Chronic Values
(Cumulative Fraction)
0.8 0.9
1.0
D Freshwater Invertebrate
l^reshwater Fish
18
-------
Table 1. Acute Toxicity of Acrolein to Aquatic Animals.
Species
Method3
Chemical
LC50
or ECSO
(U2/L)
Species Mean
Acute Valueb
fUE/U
Reference
FRESHWATER SPECIES
Snail (adult),
Aplexa hypnorum
Snail (juvenile),
Physa heterostropha
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran
(<24-hr old),
Daphnia magna
Cladoceran
(<24-hrold),
Daphnia magna
Cladoceran,
Daphnia magna
Scud (juvenile),
Gammarus minus
Insect (juvenile),
Peltoperia maria
Midge (juvenile),
Chironomus riparius
Midge (3rd and 4th instar),
Tanytarsus dissimilis
Coho salmon
(12-17 months old),
Oncorhynchus kisutch
Rainbow trout
(45.7 mm),
Oncorhynchus mykiss
Rainbow trout (juvenile),
Oncorhynchus mykiss
F,M
S,U
s,u
s,u
s,u
s,u
F, M
F,M
s,u
s,u
s,u
F,M
s,u
s,u
s, u
-
-
99%
-
-
>80%
-
96.4%
-
-
-
-
-
-
-
>151
368
57
80
93
83
11
SJl
180
5.920
510
>151
68
74
180
>131
368
-
-
-
-
-
<39.76
180
5,920
510
>131
68
-
-
Holcombetal. 1987
Home and Oblad
1983
Maceketal. 1976
USEPA 1978
Randall and Knopp
1980
LeBlanc 1980
Holcombetal. 1987
Blakemore 1990
Home and Oblad
1983
Home and Oblad
1983
Home and Oblad
1983
Holcombetal. 1987
Lorzetal.1979
Birgeetal. 1982
Home and Oblad
1983
19
-------
Table 1. Acute Toxicity of Acrolein to Aquatic Animals (continued).
Species
Method3
Chemical
LC50
or ECSO
fus/L)
Species Mean
Acute Valueb
fus/L)
Reference
FRESHWATER SPECIES
Rainbow trout (juvenile),
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout (2.5 g),
Oncorhynchus mykiss
Fathead minnow (adult),
Pimephales promelas
Fathead minnow
(43.2mm),
Pimephales promelas
Fathead minnow
(42-46 day old),
Pimephales promelas
Fathead minnow
(32-day old),
Pimephales promelas
Fathead minnow
(43.2mm),
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow
(1-day old & 30-day old),
Pimephales promelas
Fathead minnow (0.4 g),
Pimephales promelas
White sucker (3. 9 g),
Catostomus commersoni
Flagfish (1-day old),
Jordanella floridae
Flagfish (30-day old),
Jordanella floridae
R,M
F, M
F,M
S,U
S,M
S,U
R,M
F, M
F,M
F, M
F,M
F,M
F, M
F,M
-
96.4%
-
-
-
99%
99%
-
-
97%
-
-
97%
97%
38
<31
16
320
45
14.0
19.5
61
29.7
27
14
14
60
11
-
-
16
-
-
-
-
-
-
-
28.77
14
-
55.32
Venturino et al. 2007
Bowman 1990a
Holcombetal. 1987
Union Carbide Corp.
1974
Birgeetal. 1982
Geigeretal. 1986
Geigeretal. 1986
Birgeetal. 1982
Sabourin 1986
Spehar 1989
Holcombetal. 1987
Holcombetal. 1987
Spehar 1989
Spehar 1989
20
-------
Table 1. Acute Toxicity of Acrolein to Aquatic Animals (continued).
Species
Method3
Chemical
LC50
or ECSO
fus/L)
Species Mean
Acute Valueb
fus/L)
Reference
FRESHWATER SPECIES
Bluegill(l.Og),
Lepomis macrochims
Bluegill,
Lepomis macrochims
Bluegill (young of year),
Lepomis macrochims
Bluegill,
Lepomis macrochims
Bluegill,
Lepomis macrochims
Largemouth bass (1.5 g),
Micropterus salmoides
African clawed frog
(tadpole),
Xenopus laevis
S,U
s,u
s,u
F, M
F, M
s,u
F, M
-
>80%
-
96.4%
-
-
100
90
90
33
22.4
160
7
-
-
-
-
27.19
160
7
Louder and McCoy
1962
USEPA 1978
Buccafusco et al.
1981
Holcombetal. 1987
Bowman 1990b
Louder and McCoy
1962
Holcombetal. 1987
SALTWATER SPECIES
Eastern oyster,
Crassostrea virginica
Mysid,
Americamysis bahia
Brown shrimp (adult),
Penaeus aztecus
Sheepshead minnow,
Cyprinodon variegatus
F, M
F,M
F,U
F, M
94.7%
94.7%
-
94.7%
106
500
100
428
106
500
100
428
Bettencourt 1994a
Bettencourt 1994b
Butler 1965a
Bettencourt 1994c
a S = static; R = renewal; F = flow-through; M = measured; U = unmeasured.
b Each Species Mean Acute Value was calculated from the associated underlined number(s) in the preceding
column based on recommendations in the Guidelines (e.g., a flow -through measured test value takes
precedence over static tests).
21
-------
Table 2a. Chronic Toxicity of Acrolein to Aquatic Animals.
Species
Test3
Chemical
Chronic
Limits
Ol2/L)b
Chronic
Value
fus/L)
Reference
FRESHWATER SPECIES
Cladoceran,
Daphnia magna
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Flagfish,
Jordanella floridae
LC
LC
ELS
ELS
ELS
99%
99%
-
97%
97%
16.9-33.6
-
9.1-30.8
14-35
16-42
23.83
11. 4C
16.74
22.14
25.92
SALTWATER SPECIES
Maceketal. 1976
Maceketal. 1976
Sabourin 1986, 1987
Spehar 1989
Spehar 1989
a LC = life-cycle or partial life-cycle; ELS = early life-stage.
b Based upon measured concentrations of acrolein.
0 Based on EC20 analysis of data (see text)
22
-------
Table 2b. Acute-Chronic Ratios.
Acute-Chronic Ratios
Species
Cladoceran,
Daphnia magna
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Flagfish,
Jordanella floridae
Acute Value
fu2/L)
57
29.7
27
51
Chronic Value
fus/L)
23.83
16.74
22.14
25.92
Ratio
2.392
1.774
1.220
1.968
Reference
Maceketal. 1976
Sabourin 1986, 1987
Spehar 1989
Spehar 1989
23
-------
Table 3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic Ratios
Rank3
Genus Mean
Acute Value
fus/L)
Species
Species Mean
Acute Value
Ol2/L)b
Species Mean
Acute-Chronic
Ratio0
FRESHWATER SPECIES
14
13
12
11
10
9
8
7
6
5
4
3
2
1
5,920
510
368
180
>151
>151
160
55.32
<39.76
32.98
28.77
27.19
14
7
Insect,
Peltoperia maria
Midge,
Chironomus riparius
Snail,
Physa heterostropha
Scud,
Gammams minus
Snail,
Aplexa hypnorum
Midge,
Tanytarsus dissimilis
Largemouthbass,
Micropterus salmoides
Flagfish,
Jordanella floridae
Cladoceran,
Daphnia magna
Coho salmon,
Oncorhynchus kisutch
Rainbow trout,
Oncorhynchus mykiss
Fathead minnow,
Pimephales promelas
Bluegill,
Lepomis macrochirus
White sucker,
Catostomus commersoni
African clawed frog,
Xenopus laevis
5,920
510
368
180
>151
>151
160
55.32
<39.76
68
16
28.77
27.19
14
7
-
-
-
-
-
-
-
1.968
2.392
-
-
1.471
-
-
-
a Ranked from the most resistant to the most sensitive based on Genus Mean Acute Value.
b From Table 1.
c From Table 2b.
24
-------
Table 3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic Ratios (continued).
Rank"
4
3
2
1
Genus Mean
Acute Value
(us/L)
500
428
106
100
SALTWATER SPECIES
Species
Mysid,
Americamysis bahia
Sheepshead minnow,
Cyprinodon variegatus
Eastern oyster,
Crassostrea virginica
Brown shrimp,
Penaeus aztecus
Species Mean
Acute Value
(ug/L)b
500
428
106
100
Species Mean
Acute-Chronic
Ratio0
-
-
-
-
a Ranked from the most resistant to the most sensitive based on Genus Mean Acute Value.
b From Table 1.
c From Table 2b.
Fresh Water
Final Acute Value = 5.920 //g/L
Criterion Maximum Concentration = 5.920/2 = 3.0
Final Acute-Chronic Ratio = 2.0 (see text)
Final Chronic Value = (5.920 /^g/L)/2.0 = 3.0 (j.g/L
Salt Water
Final Acute Value = cannot be calculated
Criterion Maximum Concentration = cannot be calculated
Final Acute-Chronic Ratio = NA
Final Chronic Value =cannot be calculated
25
-------
Table 4. Toxicity of Acrolein to Aquatic Plants.
Species
Chemical
Method3
Duration
(davs)
Effect
Concentration1"
Ol2/L)
Reference
FRESHWATER SPECIES
Blue green alga,
Anabaena flos-aquae
Green alga,
Pseudokirchneriella
subcapitata
Diatom,
Navicula pelliculosa
Duckweed,
Lemna gibba
95%
95%
95%
95%
Diatom,
Skeletonema costatum
95%
S,M
S,M
S,M
S,M
5
5
5
14
EC50
(cell density)
EC50
(cell density)
EC50
(cell density)
ECso
(frond #)
SALTWATER SPECIES
S,M
5
ECso
(cell density)
36
44
47
72
Hughes and
Alexander
1992a
Hughes and
Alexander
1992b
Hughes and
Alexander
1992c
Hughes and
Alexander
1992d
28
Hughes and
Alexander
1992e
a S = static; R = renewal; F = flow-through; M = measured; U = unmeasured.
b Effect based on nominal concentration of active ingredient at test initiation. Concentration of test material
decreased to non-detectable levels by test termination.
26
-------
Table 5. Bioaccumulation of Acrolein by Aquatic Organisms.
Species
Chemical
Cone.
in
Water
(usfLf
Duration
fdavs)
Tissue
Percent
Linid
BCF"
Normalized
BCFC
Reference
FRESHWATER SPECIES
Bluegill
(0.37-0.94 g),
Lepomis
macrochirus
-
13.1
28
Whole
body
4.8
344
7,167
Barrows etal. 1978,
Veithetal. 1980
Johnson 1980
SALTWATER SPECIES
a Measured concentration of acrolein.
b Bioconcentration factor (BCF) is based on the measured concentration of acrolein in water and in tissue.
0 BCF was normalized to 1% lipid by dividing the BCF by the percent lipid.
27
-------
Table 6. Other Data on Effects of Acrolein on Aquatic Organisms.
Species
Chemical
Duration
Effect
Concentration
f«E/U
Reference
FRESHWATER SPECIES
Blue-green alga,
Anabaena sp.
Green alga,
Cladophora glomerata
Green alga,
Cladophora glomerata
Green alga,
Cladophora glomerata
Green alga,
Cladophora glomerata
Green alga,
Dunaliella bioculata
Green alga,
Enteromorpha intestinalis
Green alga,
Enteromorpha intestinalis
Aquatic macrophytes,
Najas sp., Ceratophyllum
sp. and Ipomea sp.
Pondweed,
Potamogeton crispus
Aquatic macrophyte,
Elodea densa
Protozoan,
Entosiphon sulcatum
Snail (adult),
Australorbis glabratus
Snail (embryo),
Australorbis glabratus
Asiatic clam (veliger),
Corbicula fluminea
Cladoceran,
Ceriodaphnia dubia
92%
92%
92%
92%
92%
-
92%
92%
-
-
-
-
-
-
-
-
24hr
24hr
24hr
24hr
24hr
48hr
24 hr
24 hr
-
5hr
24hr
72hr
24hr
24hr
24 hr
48 hr
IC50@25°C
(photosynthesis)
IC50@15°C
(photosynthesis)
IC50@20°C
(photosynthesis)
IC50@25°C
(photosynthesis)
IC50@30°C
(photosynthesis)
Reduced DNA
synthesis
IC50@20°C
(photosynthesis)
IC50@25°C
(photosynthesis)
Destroyed or badly
scorched one week
after application
Decayed in 6 days
Cell deterioration
Toxic
concentration
98% mortality
100% mortality
EC50
LC50
(fed)
690
680
1,070
1,000
760
100
2,500
1,800
25,000
20,000
500
850
10,000
10,000
300
400
Fritz-Sheridan
1982
Fritz-Sheridan
1982
Fritz-Sheridan
1982
Fritz-Sheridan
1982
Fritz-Sheridan
1982
Marano and
Puiseux-Dao 1982
Fritz-Sheridan
1982
Fritz-Sheridan
1982
Ferguson et al.
1965
Unrauetal. 1965
van Overbeek et al.
1959
Bringmann and
Kuhn 1978
Ferguson et al.
1961
Ferguson et al.
1961
Foster 1981
Union Carbide
Corporation 1997
28
-------
Table 6. Other Data on Effects of Acrolein on Aquatic Organisms (continued).
Species
Chemical
Duration
Effect
Concentration
fwE/U
Reference
FRESHWATER SPECIES
Cladoceran,
Ceriodaphnia dubia
Mayfly (nymph),
Ephemerella walkeri
Midge (T'instar),
Chironomus sp.
Black fly (last instar),
Simulium sp.
Coho salmon
(12-17 months old),
Oncorhynchus kisutch
Chinook salmon
(fingerling),
Oncorhynchus
tshawytscha
Rainbow trout
(fingerling),
Oncorhynchus mykiss
Rainbow trout (fry),
Oncorhynchus mykiss
Rainbow trout (fry),
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Brown trout (fingerling),
Salmo trutta
Goldfish (6.2 cm),
Carassius auratus
Fathead minnow,
Pimephales promelas
-
-
-
-
-
-
-
-
-
92%
-
-
-
-
7 days
Ihr
24hr
24hr
96hr
24 hr
24 hr
24 hr
Ihr
48 hr
4hr
24hr
24 hr
6 days
Chronic value
(reproduction)
Avoidance
LC50
LC50
Adverse
histological effects
on gill, kidney and
liver
LC50
LC50
LC50
Avoidance
32% mortality
Tainted flesh at 1
and 4 days post
exposure
Mean time to death
LC50
(aerated)
Incipient LC50
140
>100
2,830
600
50
80
65
140
100
48
90
46
<80
84
Union Carbide
Corporation 1997
Folmar 1978
Venturino et al.
2007
Venturino et al.
2007
Lorzetal.1979
Bondetal. 1960
Bondetal. 1960
Folmar 1976
Folmar 1976
Bartley and
Hattrup 1975
Folmar 1980
Burdick et al. 1964
Bridie etal. 1979
Maceketal. 1976
29
-------
Table 6. Other Data on Effects of Acrolein on Aquatic Organisms (continued).
Species
Chemical
Duration
Effect
Concentration
fWE/U
Reference
FRESHWATER SPECIES
Fathead minnow,
Pimephales promelas
Bluegill (fingerling),
Lepomis macrochirus
Bluegill (92 ± 9mm),
Lepomis macrochirus
Mosquitofish,
Gambusia affmis
-
-
-
-
Barnacle (adult),
Balanus eburneus
Barnacle (adult),
Balanus eburneus
Eastern oyster,
Crassostrea virginica
Mussel (1.5 mm),
Mytilus edulis
Longnose killifish
(juvenile),
Fundulus similis
92%
92%
-
-
-
48hr
24hr
Ihr
48 hr
LC50
Mean time to death
Adverse effect on
cough frequency
LC50
SALTWATER SPECIES
48hr
48hr
96hr
24 hr
48 hr
LC50
(aerated)
LC50
(aerated)
55
(shell growth)
Detachment
LC50
115
79
70
61
Louder and
McCoy 1962
Burdick et al. 1964
Carlson 1990
Louder and
McCoy 1962
2,100
1,600
55
600
240
Dahlberg 1971
Dahlberg 1971
Butler 1965a
Rustenbil 1981
Butler 1965b
Mayer 1987
30
-------
References
Agency for Toxic Substances and Disease Registry (ATSDR). 1989. Toxicological profile for
acrolein. U.S. Public Health Service, U.S. Department of Health and Human Services, Atlanta,
GA. ATSDR website accessed July 2006. http://www.atsdr.cdc.gov/MHMI/mmgl24.html
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