&EPA
United States
Environmental Protection
Agency
Office of Water
4304T
EPA 822-R-03-029
December 2003
Ambient Aquatic
Water Quality Criteria
for Nonylphenol - Draft
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AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR
NONYLPHENOL - DRAFT
(CAS Registry Number 84852-15-3)
(CAS Registry Number 25154-52-3)
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
This document has been reviewed by the Health and Ecological Criteria Division, Office of Science
and Technology, U.S. Environmental Protection Agency, and is 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. It is also available on EPA's web site:
http: //www. epa. gov/waterscience/criteria/nony Iphenol/
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FOREWORD
Section 304(a)(l) of the Clean Water Act of 1977 (P.L. 95-217) requires the Administrator of
the Environmental Protection Agency to publish water quality criteria that accurately reflect the latest
scientific knowledge on the kind and extent of all identifiable effects on health and welfare that might
be expected from the presence of pollutants in any body of water, including ground water. This
document is a revision of previous drafts based upon consideration of comments received from US
EPA staff and independent peer reviewers. Criteria contained in this document replace any previously
published EPA aquatic life criteria for the same pollutant.
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 draft 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.
Geoffrey H. Grubbs
Director
Office of Science and Technology
111
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ACKNOWLEDGMENTS
Larry T. Brooke
(author)
University of Wisconsin-Superior
Superior, Wisconsin
Frank Gostomski
(document coordinator)
U.S. EPA
Health and Ecological Criteria Division
Washington, D.C.
IV
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CONTENTS
T
Page
NOTICES ii
FOREWORD iii
ACKNOWLEDGMENTS iv
TABLES vi
FIGURES vi
Introduction 1
Acute Toxicity To Aquatic Animals 6
Chronic Toxicity To Aquatic Animals 8
Toxicity To Aquatic Plants 11
Bioaccumulation 12
Other Data 13
Unused Data 17
Summary . 17
National Criteria .... 18
Implementation 19
References 52
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TABLES
1. Acute Toxicity of Nonylphenol to Aquatic Animals . . . . 24
2a. Chronic Toxicity of Nonylphenol to Aquatic Animals 29
2b. Acute-Chronic Ratios 30
3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic Ratios 31
4. Toxicity of Nonylphenol to Aquatic Plants 34
5. Bioaccumulation of Nonylphenol by Aquatic Organisms 35
6. Other Data on Effects of Nonylphenol on Aquatic Organisms 38
FIGURES
1. Ranked Summary of Nonylphenol GMAVs - Freshwater 21
2. Ranked Summary of Nonylphenol GMAVs - Saltwater 22
3. Chronic Toxicity of Nonylphenol to Aquatic Animals 23
VI
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I
Introduction1
Nonylphenol (C15H240) is produced from cyclic intermediates in the refinement of petroleum
and coal-tar crudes. It is manufactured by alkylating phenol with mixed isomeric nonenes in the
presence of an acid catalyst. The product is a mixture of alkylphenols, predominantly para-substituted
(4-nonylphenol; CAS No. 104-40-5) and occasionally ortho-substituted (2-nonylphenol; CAS No. 136-
83-4), with various isomeric, branched-chain nonyl (nine carbon) groups. (Commercial mixtures
containing specified amounts of nonylphenol isomers and 2,4-dinonylphenol are given specific CAS
Numbers, either 25154-52-3 or 84852-15-3. These products were used for deriving the water criteria
for nonylphenol.) There is little direct use for nonylphenol except as a mixture with diisobutyl
phthalate to color fuel oil for taxation purposes and with acylation to produce oxime as an agent to
extract copper. Most nonylphenol is used as an intermediate chemical which, after etherification by
condensation with efhylene oxide in the presence of a basic catalyst, produces the nonionic surfactants
of the nonylphenol ethoxylate type. The nonionic surfactants are used as oil soluble detergents and
emulsifiers that can be sulfonated or phosphorylated to produce anionic detergents, lubricants,
antistatic agents, high performance textile scouring agents, emulsifiers for agrichemicals, antioxidants
for rubber manufacture, and lubricant oil additives (Reed 1978).
Nonylphenol is produced at a high annual tonnage rate. Its production in the U.S. was 147.2
million pounds (66.8 million kg) in 1980 (USITC 1981), 201.2 minion pounds (91.3 million kg) in
1988 (USITC 1989), 230 million pounds (104 million kg) in 1998 (Harvilicz 1999), and demand is
increasing about 2 percent annually. Nonylphenol has an approximate molecular weight of 215.0 to
220.4 g/mole, is a pale yellow highly viscous liquid with a slight phenolic odor and a specific gravity
of 0.953 g/mL at 20°C (Budavari 1989). It has a dissociation constant (pKa) of 10.7 ±1.0;
octanol/water partition coefficient (Log Kow) of 3.80 to 4.77; pH-dependent water solubility of 4,600
fig/L at pH 5.0, 6,237 ^g/L at pH 7, 11,897 ^g/L at pH 9 and 3,630 /ig/L in seawater; soluble in
many organic solvents; and has a vapor pressure of 4.55 x 10"3 (±3.54 x 10"3) Pa (Roy F. Weston Inc.
1990). Ahel and Giger (1993) measured the solubility of nonylphenol at different temperatures in
distilled water and demonstrated a nearly linear relationship in solubility of 4,600 Mg/L at 2°C to
6,350//g/Lat25°C.
1A comprehension of the "Guidelines for Deriving Numerical National Water Quality Criteria
for the Protection of Aquatic Organisms and their Uses" (Stephen et al. 1985), hereafter referred to as
the Guidelines, is necessary to understand the following text, tables and calculations.
1
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Nonylphenol has been studied for its acute and chronic toxicity to aquatic organisms and
results of many studies are well summarized in a review article (Staples et al. 1998). Additionally, this
review article addresses the ability of nonylphenol to bioaccumulate in aquatic organisms.
Nonylphenol and nonylphenol ethoxylates have been found in the environment and a review of
studies describing their distribution has been published (Bennie 1999). Shackelford et al. (1983)
reported 4-nonylphenol at average concentrations ranging from 2 to 1,617 ^ig/L in eleven water
samples associated with various industrial sources. Bennie et al. (1997) measured water concentrations
from 0.01 to 0.92 yug/L in 25 percent of the sites sampled in the Great Lakes. They found
nonylphenol in all sediment samples and the concentrations ranged from 0.17 to 72 //g/g (dry weight).
Studies have shown the presence of nonylphenol and its ethoxylates in treatment plant wastewaters
(Ellis et al. 1982, Giger et al. 1981) and in sewage sludges (Giger et al. 1984). A study was
conducted of thirty river reaches in the continental U.S. in 1989 and 1990 to determine the frequency
and concentrations of nonylphenol and its ethoxylates in water and sediments. Nonylphenol was found
in approximately 30 percent of the water samples and concentrations in water ranged from about 0.20
to 0.64 jug/L. Approximately 71 percent of the sites had measurable concentrations of nonylphenol in
the sediments and the concentrations ranged from about 10 to 2,960 jug/kg. Various ethoxylates of
nonylphenol were found in 59 to 76 percent of the water samples, varying by extent of ethoxylation
(Naylor 1992, Naylor et al. 1992, Radian Corp. 1990). Keith et al. (2001) measured nonylphenol in
fish tissues of seven species from the Kalamazoo River and the river's mouth at Lake Michigan. They
found 41 percent of the samples had measurable concentrations of nonylphenol with a range of 3.3 to
29.1 ^g/kg, and a mean value of 12.0 Aig/kg.
Most nonylphenol enters the environment as 4-alkylphenol polyethoxylate surfactants which are
degraded to 4-alkylphenol mono- and diethoxylates in active sewage sludges (Giger et al. 1984). It
was theorized by Giger et al. (1984) that further transformation of 4-alkylphenol mono- and
diethoxylates to 4-nonylphenol is favored by anaerobic environments. They conducted experiments
with stabilized (anaerobic) and raw (aerobic) sewage sludge and found that concentrations of 4-
nonylphenol increased four to eight times in the stabilized versus two times in the raw sludge, a
finding which supported their theory.
Persistence of nonylphenol in sewage effluents and the environment has been studied and a
review has been written (Maguire 1999) of published studies. Gaffney (1976) determined that 1 mg/L
nonylphenol did not degrade during a 135-hr incubation with domestic wastewater. He also measured
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no change in nonylphenol concentration at 24 hr in industrial wastewater, but after 135 hr there was a
45 percent degradation of the compound.
Sundaram and Szeto (1981) studied nonylphenol fate in stream and pond waters when
incubated in open and closed containers. They found no degradation of nonylphenol when incubated in
open containers of the pond or stream waters and a half-life of 2.5 days, probably due to volatization.
After three days of incubation in pond or stream waters in closed containers, a breakdown product was
measured and half-lives were estimated of 16.5 and 16.3 days, respectively. The same study
demonstrated that nonylphenol in pond water with sediment present resulted in about 50 percent of the
nonylphenol appearing in the sediment after 10 days. About 80 percent of the nonylphenol in the
sediment was degraded in 70 days. No degradation of nonylphenol occurred when autoclaved water
and sediment samples were used. Staples et al. (1999) measured a half-life of 20 days at 22 °C for
nonylphenol at a concentration of 31 mg/L. They suggested that the temperature of water and the
initial concentration of the nonylphenol both affect the degradation rate of the chemical. Ahel et al.
(1994a,b) studied the fate and transport of alkylphenol polyethoxylates (APrcEO) and their metabolites
in the Glatt River system in Northern Switzerland from the Greifensee to the Rhine River. Water
samples were collected at eight sites along the river hourly and seasonally. They found nonylphenol
concentrations to be lower than other metabolites and nonylphenol concentrations were most common
in the 1 to 3 //g/L range. Metabolite concentrations of APrcEO's varied with time of day reflecting
wastewater treatment plant discharge fluctuations. Metabolite concentrations of APrcEO's also varied
seasonally, and were higher in the winter due to lower water temperature. Nonylphenol had less
season variability than other metabolites of APrcEO's. Sediments were investigated and nonylphenol
was the predominant nonylphenolic compound with concentrations of 364 to 5,100 times that found in
the river water. Treatment conditions within the treatment plants along the Glatt River system were
studied and the abundance of particular metabolites of APrcEO's were dependent on the treatment
conditions (Ahel et al. 1994a; Ahel et al. 2000). Another study by Ahel et al. (1996) demonstrated
that nonylphenol can be reduced in ground water probably by biological processes provided that the
ground water temperature does not become too cold for biological degradation. It has been
demonstrated (Ahel et al. 1994c) that nonylphenol can be degraded by photochemical processes in 10
to 15 hrs (half-life) in bright summer sun when nonylphenol is near the water surface.
Heinis et al. (1999) studied the distribution and persistence of nonylphenol in temperate climate
zone natural pond systems. They reported that nonylphenol partitioned to the pond enclosure wall
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material, macrophytes, and sediments within two days. After 440 days, the primary sink for
nonylphenol was the sediment. Dissipation time from the sediment for 50 and 95 percent were
estimated at 66 and 401 days, respectively. Measurable concentrations of nonylphenol can persist for
many years in sediments. Hale et al. (2000) measured nonylphenol concentrations in sediments below
wastewater outfalls and found one site that had a sediment concentration of 54,400 ,ug/kg more than
twenty years after the treatment plant ceased operation. Bennett and Metcalfe (1998; 2000) found that
nonylphenol was widely distributed in the lower Great Lakes sediments and reached 37,000 Aig/kg in
sediments near sewage treatment plants.
It appears that degradation of nonylphenol in sea water may be slower than in fresh water.
This was observed in both water and sediments. Ekelund et al. (1993) found that initial nonylphenol
degradation was slow in sea water, but after microorganism adaptation occurred, the degradation rate
increased. Approximately 50 percent of the nonylphenol was degraded after 58 days. In marine
sediments, the rate of degradation was initially faster than hi water, but about the same percentage was
degraded in 58 days as in sea water. Ethoxylated nonylphenol, in marine sediments, has a half-life of
60 days similar to nonylphenol (Shang et al. 1999).
Nonylphenol is metabolized by hepatic cytochrome P450 enzymes in the rainbow trout
(Oncorhynchus mykiss), and bile from the fish contained the glucuronic acid conjugates of nonylphenol
(Meldahl et al. 1996; Thibaut et al. 1999). Arukwe et al. (2000) found that bile was the major route of
nonylphenol excretion with a half-life of 24 to 48 hrs in both waterborne and dietary exposures. The
Log P of nonylphenol ranges from 3.80 to 4.77, indicating the possibility of bioaccumulation in
aquatic organisms. Bioconcentration was measured in two saltwater organisms, blue mussel (Mytilus
edulis) and Atlantic salmon (Salmo solar). The estimated bioconcentration factor (BCF) for the blue
mussel ranged from 1.4 to 7.9 (McLeese et al. 1980a), and the Atlantic salmon estimated BCF was 75
(McLeese et al. 1981). Ahel et al. (1993) measured the bioconcentration of nonylphenol in rivers hi
Switzerland. They found that nonylphenol was bioconcentrated approximately 10,000 times in algae,
but this concentration was not further concentrated up the food chain. Instead, they measured lower
bioconcentration factors in fish and ducks than in plants.
Nonylphenol has been tested for its ability to bind to estrogen receptors. There are several
review articles that describe disruption of endocrine function by nonylphenol (Servos 1999;
Sonnenschein and Soto 1998; Sumpter 1998). It has been found to bind to estrogen receptors in cell
cultures (Flouriot et al. 1995; Hewitt et al. 1998; Jobling and Sumpter 1993; Lutz and Kloas 1999;
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Routledge and Sumpter 1996; Soto et al. 1991, 1992; White et al. 1994) and whole animals (Jobling et
al. 1996). Optimal estrogenic activity requires a single tertiary branched alkyl group composed of six
to eight carbons located at the para position on an otherwise unsubstituted phenol ring (Routledge and
Sumpter 1997). Tabira et al. (1999) found that when using human estrogen receptors, the receptor
binding of alkylphenols was maximized when the number of alkyl carbons was nine as it is with
nonylphenol. Nonylphenol is able to stimulate the liver of male and immature female fish to produce
the egg-yolk precursor protein vitellogenin, which is normally found in high concentrations only in
mature female fish. Islinger et al. (1999) estimated the estrogenic potential of nonylphenol to stimulate
vitellogenin production in male rainbow trout at 2,000 to 3,000 times less potent than 17 p-estradiol. It
is also able to cause changes in the spermatogenesis cycle of male fish. Ren et al. (1996a)
demonstrated significant increases in the estrogenic effects in rainbow trout exposed to nonylphenol at
100 Mg/L for 72 hr using vitellogenin production as a biomarker. In another study, Ren et al. (1996b)
demonstrated that nonylphenol could stimulate the production of vitellogenin mRNA in four hr at a
concentration as low as 10 p-g/L. Nonylphenol at concentrations of 50 and 100 /^g/L caused 50 and 86
percent, respectively, of the male Japanese medaka (Oryzias latipes) fish to develop an intersex
condition (both testicular and ovarian tissues in the gonad) with a three month exposure (Gray and
Metcalfe 1997). The sex ratio shifted in favor of females at the highest treatment. Purdom et al.
(1994) found that rainbow trout held in cages in the outfalls of sewage treatment plants had increased
vitellogenin concentrations in the blood. They suggested that the two most likely estrogenic substances
present in the effluents were ethynylestradiol and nonylphenol. Several studies (Allen et al. 1999,
Harries et al. 1997, Lye et al. 1999, Tanghe et al. 1999) conducted in Europe have attempted to
demonstrate that waters in various rivers and estuaries below sewage treatment plants have the ability
to induce estrogenic effects in a yeast assay and in fish. Effects were seen in most areas sampled and
the possibility of mixture effects with nonylphenol, other xenoestrogens, and human estrogens exists.
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 LC50s and 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. The
U.S. Environmental Protection Agency has modified its original intention of requiring testing for
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nonylphenol-mixed isomers (CAS No. 25154-52-3) and now recommends testing to be conducted with
the chemical substance comprised of mostly para-branched C9-alkylphenols with CAS No- 84852-15-3
(Federal Register 1990). 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. Freshwater criteria were derived using nonylphenol of CAS
numbers 25154-52-3 and 84852-15-3; saltwater criteria were derived using only nonlyphenol of CAS
number 84852-15-3. The latest comprehensive literature search for fresh- and saltwater information
for this document was conducted in November, 1999. Some newer information has been included.
Acute Toxicitv To Aquatic Animals
Data that are suitable, according to the "Guidelines," for the derivation of a freshwater Final
Acute Value (FAV) are included hi Table 1. Eighteen species and two subspecies representing fifteen
genera were tested with nonylphenol to determine its acute toxicity to these species. Acute toxicity test
results ranged from 55.72 /zg/L for an amphipod (Hyalella aztecd) to 774 ,ug/L for a snail (Physella
virgata).
The most sensitive freshwater species tested was an amphipod, Hyalella azteca (Tables 1 and
3). Brooke (1993a) and England and Bussard (1995) tested this species under similar conditions,
except for water hardness levels which were 51.5 and 148-154 mg/L as CaCO3, respectively. An
LC50 of 20.7 //g/L.was calculated in the lower hardness water and 150 /ug/L in the higher hardness
water. However, insufficient data exist to demonstrate an effect of water hardness on the toxicity of
nonylphenol. Tadpoles of the boreal toad, Bufo boreas, were ranked second in sensitivity to
nonylphenol (Dwyer et al. 1999a) and had a 96-hr LC50 of 120 Mg/L. Data for one cladoceran species
(Daphnia magna) are available. Brooke (1993a) reported an EC50 of 84.8 /zg/L from a test that had
the solutions renewed daily and Comber et al. (1993) reported an EC50 of 190 /ug/L in a static test.
The Daphnia magna Species Mean Acute Value is 126.9 /^g/L.
Freshwater fish species were in the mid-range of toxicity to nonylphenol. Toxicity test results
are available for eleven species representing eight genera. Their sensitivity to nonylphenol ranged
from 133.9 ^g/L for the fathead minnow (Pimephalespromelas) to 289.3 //g/L for the bonytail chub
(Gila elegans}. Three trout species of the genus Oncorhynchus and two subspecies were tested and had
similar LC50s ranging from 140 to 270 /^g/L. Dwyer et al. (1995, 1999a) exposed nine species offish
that were surrogates of threatened or endangered fish species or were threatened and endangered.
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Acute toxicity test results were based upon static tests with unmeasured nonylphenol concentrations
and the LC50s ranged from 110 ^g/L for the fountain darter, Etheostoma rubrum, to a geometric mean
of 289.3 /zg/L for the bony tail chub.
The least sensitive freshwater species to nonylphenol toxicity were invertebrates. The annelid
worm (Lumbriculus variegatus) had an LC50 of 342 //g/L, nymphs of the dragonfly Ophiogomphus sp.
had an LC50 of 596 //g/L and the least sensitive species tested was a snail, Physella virgata, which
had an LC50 of 774 ,ug/L. The lower sensitivity to nonyphenol occurs even though this species of
snail does not have an operculum and would not be able to completely enclose its body and thus
protect itself against nonylphenol exposure.
Freshwater Species Mean Acute Values (SMAV) and Genus Mean Acute Values (GMAV) were
derived from available acute values (Tables 1 and 3). GMAVs were available for 15 genera; the most
sensitive was the amphipod, H. azteca, which was 13.9 times more sensitive than the least sensitive
species,, a snail P. virgata (Figure 1). The four most sensitive species were within a factor of 2.4 of
one another. The freshwater Final Acute Value (FAV) for nonylphenol is 55.71 //g/L and was
calculated using the procedure described in the "Guidelines" and the GMAVs in Table 3. The FAV is
equal to the lowest freshwater SMAV of 55.72 //g/L for the amphipod H. azteca.
The acute toxicity of nonylphenol to saltwater animals has been tested with seven invertebrate
and three fish species (Table 1). The range of SMAVs extends from 17 ,ug/L for the winter flounder,
Pleuronectes americanus, -to 209.8 /^g/L for the sheepshead minnow, Cyprinodon variegatus (Lussier
et al. 2000; Ward and Boeri 1990b), a difference of 12.3 times. Fish (winter flounder), bivalves (coot
clam, Mulinia lateralis} and crustaceans (the mysid, Americamysis bahia) were all among the most
sensitive species.
Data for nine of the twelve saltwater test values reported in Table 1 were from a single multi-
species test (Lussier et al. 2000). Nonylphenol concentrations were measured in seven of the nine tests
(Table 1), with measurements made at test initiation and at the end of the test (48 or 96 hr). Test
organisms were fed brine shrimp, Anemia sp., during test chemical exposure. Normally this is not
acceptable for data used to derive Final Acute Values. However, the tests reported by Lussier et al.
(2000) were designed to extend beyond the usual 48 or 96-hr acute test interval to 168 hr. The
extended exposure time required feeding to ensure survival of animals not affected by nonylphenol.
The brine shrimp fed during the tests were "reference grade" and not likely to change the exposure to
nonylphenol. Two animal species were tested in two laboratories allowing comparison of results from
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IslMIFT
a study with food added and another without food. In the case of the mysid, 96-hr LC50s were
estimated at 43 and 60.6 //g/L for the non-fed and fed studies, respectively. The sheepshead minnow
had 96-hr LC50s of 310 and 142 /^g/L for the respective non-fed and fed studies. Because feeding
during the tests did not consistently raise or lower the LC50 estimates, feeding is assumed not to have
altered the results in these tests. Therefore, the data from the Lussier et al. (2000) tests were
acceptable for deriving a saltwater Final Acute Value.
GMAVs for the four most sensitive saltwater species differ by a factor of only 3.5 (Table 3
and Figure 2). Using the method of calculation specified in the "Guidelines," the saltwater FAV is
13.35 /ug/L. The FAV is lower than the lowest SMAV of 17 //g/L for the winter flounder.
Chronic Toxicity To Aquatic Animals
The available data that are usable according to the "Guidelines" concerning the chronic toxicity
of nonylphenol are presented in Table 2. England (1995) exposed neonates of a cladoceran,
Ceriodaphnia dubia, to nonylphenol for seven days in a renewal test. The results showed a significant
reproductive impairment at 202 /j-g/L, but not at 88.7 //g/L, and survival was reduced at 377 //g/L, but
not at 202 ^g/L. Based upon reproductive impairment, the Chronic Value for C. dubia was 133.9
//g/L. At the end of 48 hr in the same test, effects were observed and an EC50 of 69 /ug/L was
calculated. However, the animals had received food and according to the "Guidelines," acute tests
with this species must not receive food during an acute toxicity test if the test is to be valid and used to
compute an Acute-Chronic Ratio (ACR).
Fliedner (1993) exposed 4 to 24 hr-old Daphnia magna neonates to nonylphenol for 22 days in
a 20°C life-cycle test. Test solutions were renewed three times each week during which a 52.2 to 65.5
percent decrease in nonylphenol concentration was measured. Mean measured nonylphenol test
concentrations were: 0, 0, 1.55, 1.34, 3.45, 10.70, and 47.81 Aig/L. No effects were observed during
the study on the mortality, the number of offspring per female, or the mean day of the first brood. A
significant effect was measured for the total number of young per concentration on day nine of the
study. Consequently, the No Observed Effect Concentration (NOEC) was 10.7 //g/L and the Lowest
Observed Effect Concentration (LOEC) was 47.8 /j.g/L with a chronic value (geometric mean of the
NOEC and LOEC) of 22.62 ^g/L. An acute test was not conducted to calculate an ACR.
Brooke (1993a) also reported a chronic exposure for the cladoceran Daphnia magna, but for
21-days. Test solutions were renewed three times per week and concentrations of nonylphenol
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declined an average of 57.4 + 5.8 percent between solution renewals. The author concluded that D.
magna were significantly impaired in growth and reproduction at 215 y^g/L, but not at 116 ^g/L.
Survival was reduced to 60 percent at 215 /ug/L; however, this survival rate was not a significant
reduction from the control survival rate because only 80 percent survived in the control group. The
Chronic Value estimated from the geometric mean of the lower (116 //g/L) and upper (215 //g/L)
chronic limits based upon reproductive impairment was 157.9 /^g/L. Division of the chronic value for
this test (157.9 /ug/L) into the 48-hr EC50 from a companion test (84.8 //g/L) resulted in an ACR of
0.5370. The calculated ratio of 0.5370 was changed to 2.000 as suggested in the "Guidelines" because
acclimation to nonylphenol probably occurred during the chronic test.
A third D. magna life-cycle 21-day exposure to nonylphenol was conducted by Comber et al.
(1993). They found no significant effects in survival, reproduction or growth at concentrations <24
//g/L. Reproduction was significantly reduced at concentrations >39 /ug/L when the number of live
young produced was compared to control reproduction. Growth was reduced at concentrations >71
//g/L and survival of adults was reduced at concentrations >130 yug/L. Based upon reduced
reproduction at 39 //g/L but not at 24 //g/L, the Chronic Value was 30.59 yug/L. Division of the
Chronic Value (30.59 /ug/L) for this test into (he 48-hr EC50 of 190 //g/L from a companion study
resulted in an ACR of 6.211.
Because two ACRs were available for D. magna, the geometric mean of the two values was
used as the species-mean ACR. The species-mean ACR for D. magna is 3.524.
The midge, Chironomus teutons, was exposed to five concentrations of nonylphenol and a
control from < 24-hr old larva through emergence (53 days) as adults (Kahl et al. 1997). Nominal
exposure concentrations ranged from 12.5 to 200 //g/L, but mean measured concentrations were lower.
Neither growth or reproductive (sex ratio, emergence pattern, and egg production and viability)
measurements were negatively affected at any of the exposure concentrations. There was a significant
effect upon survival of larvae during the first 20 days of exposure, but none after 20 days. The LOEC
was 91 //g/L, based upon survival at 20 days, and the NOEC was 42 //g/L. The Chronic Value is
61.82 //g/L. An acute exposure was not conducted; therefore, an ACR can not be calculated for this
species.
A 91-day early life-stage test was conducted with embryos and fry of the rainbow trout,
Oncorhynchus mykiss (Brooke 1993a). Five nonylphenol exposure concentrations were tested and they
ranged from 6.0 to 114 //g/L in the flow-through test. Time to hatch and percent survival at hatch
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were not affected by the nonylphenol concentrations; however, nearly all of the larvae were abnormal
at the two highest exposure concentrations (>53.0 //g/L). At the end of the test, survival was
significantly reduced at concentrations >23.1 /^g/L but not at 10.3 Mg/L. Growth (both weight and
length) was a more sensitive chronic endpoint than survival. At the end of the test, the fish were
significantly shorter (14 percent) and weighed less (30 percent, dry weight) at concentrations >10.3
^g/L than the controls, but not at 6.0 //g/L. Based upon growth, the Chronic Value for rainbow trout
was 7.861 /^g/L. A companion acute test was available for this species. Division of the Chronic
Value (7.861 ^g/L) into the Acute Value (221 //g/L) yielded an ACR of 28.11 for rainbow trout.
An early-life-stage toxicity test was conducted with nonylphenol and the fathead minnow,
Pimephales promelas (Ward and Boeri 1991c). Embryos and larvae were exposed for a total of 33
days to five concentrations of nonylphenol that ranged from 2.8 to 23 //g/L. Embryos in the control
and those in the three lowest nonylphenol exposure concentrations (2.8, 4.5, and 7.4 /^g/L) began to
hatch on the third day of exposure, while the two higher concentrations (14 and 23 //g/L) began
hatching on the fourth day. Growth (length or weight) was not significantly different from the control
organisms at an}' of the treatment exposures. Survival of the fish at the end of the test was
significantly reduced at nonylphenol concentrations > 14 //g/L. Fish survival averaged 56.7 percent at
the 23 /ig/L exposure, 66.7 percent at the 14 /^g/L exposure, and 76.7 percent at the 7.4 /^g/L
exposure, only concentrations <7.4 fig/L did not differ from the control that averaged 86.7 percent
survival. Based upon survival, the LOEC for the fathead minnow was 14 //g/L and the NOEC was 7.4
^g/L. The Chronic Value was 10.18 /^g/L (Table 2). No companion acute toxicity test was conducted
with the fathead minnow with which an ACR can be calculated.
The chronic toxicity of nonylphenol to saltwater animals was determined in a 28-day life-cycle
test with mysids, Americamysis bahia (Ward and Boeri 1991b). There was no effect on survival or
reproduction at 6.7 //g/L, but there was a 18 percent reduction in survival and a 53 percent reduction
in reproduction at 9.1 fj-g/L. Effects on survival at the highest concentration tested (21 /^g/L) were
observed before the end of the third week of the test. Test organisms of each sex were measured
separately for length and weight. The data show no obvious difference between the length of male and
female mysids for all of the concentrations tested. The growth analysis was based on combined length
data for both sexes. Growth (length) was the most sensitive endpoint for mysids. There was a 7
percent, but statistically significant, reduction in the length of mysids exposed to 6.7 //g/L of
nonylphenol relative to control mysids. There was not a significant difference in growth for mysids
10
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exposed to 3.9 /zg/L nonylphenol when compared to control animals (Table 2). The Chronic Value,
based on growth, for mysids was the geometric mean of the lower (3.9 /ug/L) and the upper (6.7 //g/L)
Chronic Values and was 5.112 ^g/L. The ACR of 8.412 was calculated using the acute value of 43
Mg/L from a companion study and dividing by the Chronic Value of 5.112 ^g/L.
Three valid ACRs are available for nonylphenol using the third and eighth (Table 3) most
sensitive tested species of freshwater animals and the third most sensitive saltwater animal. Two ACRs
were available for the cladoceranDaphnia magna, which differed by a factor of approximately 3.1
times. The geometric mean of these two values is 3.524. The cladoceran, Ceriodaphnia dubia, had an
ACR ratio of 0.515 when using the tests of England (1995). However, this ratio was derived using the
results of the companion acute test during which the organisms were fed. According to the
"Guidelines," acute tests with this species must be done without food present in the test solutions.
Therefore, the C. dubia ACR was not used. The three valid ACRs (3.524, 8.412 and 28.11) differed
by a maximum of 7.98 times (Table 3). The largest ACR was for a fish (rainbow trout) that
represented the eighth most sensitive genera of the fifteen tested from fresh water. The geometric
mean of the three valid ACRs was 9.410, which is the Final Acute-Chronic Ratio (FACR).
Toxicity To Aquatic Plants
Only a single species of freshwater plant has been tested that meets the requirements for
inclusion in Table 4 according to the "Guidelines." Ward and BoerL(1990a) exposed green algae
(Selenastrum capricomutum) to nonylphenol for four days. They calculated an EC50 of 410 ^g/L
based upon cell counts. At the end of the toxicity test, algae from the highest exposure concentration
(720 //g/L) were transferred to fresh media solution. During the next seven days, cell counts increased
exponentially indicating that nonylphenol treatment at this concentration for four days did not have a
persistent algistatic effect.
Acceptable data on the toxicity of nonylphenol to saltwater plants were available for one
species of marine algae (Table 4). The EC50 value for vegetative growth of the planktonic diatom,
Skeletonema costatum, was 27 ^g/L (Ward and Boeri 1990d). Although this value was lower than
nearly all of the acute values for animals, it is for vegetative growth, which can recover rapidly.
Skeletonema transferred from the highest nominal concentration of nonylphenol with survivors (120
^g/L) into control medium grew to a 76-fold increase in cells/mL within 48 hr (Ward and Boeri
1990d).
11
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Based on the vegetative growth test using the saltwater planktonic diatom, Skeletonema
costatum, the Final Plant Value for nonylphenol is 27 /ig/L. This plant species is more sensitive to
nonylphenol than any tested species of freshwater animal and more sensitive than all but one tested
saltwater animal species.
Bioaccumulation
Three studies were conducted to measure the bioconcentration of nonylphenol in freshwater
animals that, according to the "Guidelines," meet the requirements for inclusion in this section of the
document (Table 5). Ward and Boeri (1991a) measured the whole body burden in juvenile fathead
minnows, with bioconcentration determined at two exposure concentrations (4.9 and 22.7 //g/L) after
27 days of exposure. The bioconcentration factors were not lip id normalized and were similar at 271
and 344 times for the respective lower and higher exposure concentrations.
Brooke (1993b) exposed juvenile fathead minnow (Pimephales promelas) and juvenile bluegill
(Lepomis macrochirus) to nonylphenol each at five concentrations for four and twenty-eight days.
Lipid concentrations were measured (Brooke 1994) for the test fish and the bioconcentration results
were lipid normalized which reduced the bioconcentration factors from 4.7 to 4.9 times. Nonylphenol
concentrations that proved lethal to the organisms were not used to compute bioconcentration factors.
The short-term (4 day) tests showed that plateau tissue concentrations were reached within two days in
both the fathead minnow and the bluegill. Therefore, there was generally good agreement between the
4- and 28-day tests. Normalized bioconcentration factors for the fathead minnow ranged from 128.3 to
209.4 (Table 5). Normalized bioconcentration factors for the bluegill ranged from 38.98 to 56.94.
Giesy et al. (2000) measured me concentration of nonylphenol in the whole bodies of the
fathead minnow following a 42-day exposure. Three sublethal concentrations allowed nonylphenol to
bioaccumulate 203 to 268 times in exposure concentrations ranging from 0.4 to 3.4 ^g/L.
_ Bioconcentration factors are available (Ekelund et al. 1990) for three species of saltwater
animals, Mytilus edulis, Crangon crangon and Gasterosteus aculeatus (Table 5). Dosing was with 14C-
labeled nonylphenol, but the CAS number was not listed. (Crangon crangon is a non-resident species,
but the data are included since very little bioaccumulation data are available.) Exposures lasted 16
days followed by an elimination period of 32 days. Lipid normalized bioconcentration factors based
on wet weight ranged from 78.75 for C. crangon to 2,168 for M. edulis. The steady state tissue
concentration for M. edulis was estimated since it did not reach steady state after only 16 days of
12
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MT
exposure.
No U.S. FDA action level or other maximum acceptable concentration in tissue, as defined in
the "Guidelines," is available for nonylphenol. Therefore, a Final Residue Value cannot be calculated.
Other Data
Additional data on the lethal and sublethal effects of nonylphenol on freshwater species that do
not comply with data requirements described in the "Guidelines" for inclusion in other tables are
presented in Table 6. Three plant species (Chlamydomonas reinhardni, Salvinia molesta, Lemna
minor) were exposed in studies using media solutions that were not described. The results generally
showed the plant species to be less sensitive to nonylphenol than animals. One test with the duckweed,
Lemna minor, was an exception and showed a four-day reduction in vegetative growth at 125 ^g/L
(Prasad 1986). McLeese et al. (1980b) reported LCSOs of 5,000 Aig/L for a clam, Anodonta
cataractae, in a 144-hr exposure and 900 //g/L for the Atlantic salmon, Salmo solar, in a 96-hr
exposure. The values were higher than those reported in Table 1 for similar species. The test
organisms were fed in both tests.
Three long-term (21 day) tests with Daphnia magna (Baer and Owens 1999, Baldwin et al.
1997, LeBlanc et al. 2000) and a single long-term (30 day) test with D. galeata mendotae (Shurin and
Dodson 1997) are included in this section because the tests were conducted without measurement of
nonylphenol concentrations in the test water. The results in the unmeasured tests agree reasonably
well with those measured and reported in Table 2 for D. magna. Negative effects on survival or
reproduction were observed in all three tests between 25 and 200 //g/L. The cladoceran, Daphnia
pulex, was exposed for 48 hr in tests in which nonylphenol concentrations decreased more than 50
percent during the exposures (Ernst et al. 1980), but resulting LC50s ranged from 140 to 190 //g/L,
which agreed with LC50s for other cladoceran species. The cladoceran, Ceriodaphnia dubia, gave
similar LC50 results of 276 and 225 ^g/L for the respective exposure durations of 48 hr and 7 days
(England 1995). The LC50 values reported in this table for the species are slightly higher than the
Chronic Value for the species of 134 ptg/L (Table 2). England and Bussard (1993) reported an EC50
and an LC50 for larva of the midge, Chironomus tentans, of 95 and 119 Aig/L, respectively. These
values were slightly more sensitive than values reported in a similar study in which food was not
available (Table 1). In a pair of tests in which the test organisms were fed, Brooke (1993b) measured
a 96-hr LC50 for the fathead minnow, Pimephales promelas, of 138 /u.g/L and a 96-hr LC50 for the
13
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bluegill, Lepomis macrochirus, of 135 /^g/L. The LC50 values for these species from tests in which
the fish were fed, agree well with data from tests in which the fish were not fed (Table 1).
Five fish species (rainbow trout, lahontan cutthroat trout, apache trout, Colorado squawfish
and fathead minnow) were exposed to nonylphenol for 96 hr to determine if nonylphenol inhibited
brain acetylcholoinesterase enzymes. Response to AchE inhibition was measured by a decrease in the
number of muscarinic cholinergic receptors which is a compensatory response to an acetycholine
buildup (Jones et al. 1998). Responses at exposure concentrations <220 //g/L were observed in the
rainbow trout, lahontan cutthroat trout, and apache trout.
Brooke (1993b) measured the bioconcentration of nonylphenol in the fathead minnow and
bluegill at concentrations near lethality. The fathead minnow BCF was 100.4 and the bluegill BCF
was 35.31. The values were slightly less than the BCFs measured in the fish from lower exposure
concentrations (Table 5). Lewis and Lech (1996) found that bioconcentration of nonylphenol was
highest (BCF=98.2) in the viscera of rainbow trout and 24.21 in the remainder of the carcass. They
also measured the half-life of nonylphenol in various tissues and found that fat and muscle similarly
depurated nonylphenol to half concentrations in about 19 hr. The liver depurated to half
concentrations in about 6 hr.
Mesocosm studies were conducted with nonylphenol in which zooplankton, benthic
macroinvertebrates, and fish were observed for effects. The exposure was for 20 days with four
nonylphenol concentrations. Zooplankt; n populations (O'Halloran et al. 1999) and benthic
macroinvertebrate populations (Schmude et al. 1999) showed no negative effects at the 23 /Lig/L
nonylphenol exposure concentration, and were negatively affected at 76 //g/L. Various species of
zooplankton and macroinvertebrates exhibited differences in sensitivity to nonylphenol. The authors of
the zooplankton study stated that a MATC for the protection of all zooplankton taxa is ~ 10 //g/L. The
fish (bluegill) in the mesocosms (Liber et al. 1999) were unaffected at nonylphenol exposures <76
^g/L, but survival was reduced at 243 /ug/L. In one exposure replicate with a mean nonlyphenol
concentration of 93 ^g/L, survival of the fish was reduced after 20 days of exposure indicating that
concentrations near 100 /ug/L may be maximal for this species. The mesocosm studies demonstrated
that the freshwater Final Chronic Value of 5.920 //g/L should be protective of aquatic life.
Nonylphenol does have estrogen-like qualities. Vitellogenin is a protein produced in the liver
of female oviparous vertebrate species and deposited in the ovaries as the primary material for yolk in
the ova. Male fish normally produce very little vitellogenin. Jobling et al. (1996) demonstrated
14
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significant increases in vitellogenin in male rainbow trout, Oncorhynchus my kiss, at three weeks of
exposure to 20.3 and 54.3 /j.g/L of nonylphenol. Lech et al. (1996) observed a significant increase in
mRNA for the vitellogenin gene in rainbow trout at 14.14 //g/L. A long-term study was conducted
with rainbow trout, Onchorynchus mykiss, exposing female fish immediately after hatch to 1, 10, and
30 or 50 jug/L of nonylphenol (Ashfield et al. 1998). They found reduced growth in fish exposed to 1
Mg/L for 22 days and grown for 86 days beyond treatment. Growth was not reduced in the 10 //g/L
treatment but was in the 50 ^g/L treatment. A second study was conducted and exposure was for 35
days and grow-out was for 431 days beyond the last treatment day. On day 55 of the study, reduced
growth was observed at the 10 and 30 ,ug/L treatments, but not at the 1 ^g/L. At day 466, the fish
exposed to 10 /^g/L recovered the growth reductions seen earlier and only the 30 ^g/L exposed fish
showed reduced (-25 percent) growth. The ovosomatic index (increase in ovary size relative to the
control fish ovaries) increased in the fish exposed to 30 //g/L at day 466. The authors speculated that
the growth reduction may have been caused by the use of energy for precocious sexual development.
A non-resident fish species, Japanese medaka (Oryzias latipes}, was exposed to nonylphenol
for 28 days following hatching (Nimrod and Benson 1998). The survivors were monitored for the
following 55 days. At the highest exposure concentration of 1.93 f^-g/L, survival, growth, egg
production, egg viability, and gonadosomatic index (GSI) were not altered. In another study with the
same species of fish, development of testis-ova, an intersex condition, occurred after a three month
exposure to 50 ^g/L of nonylphenol (Gray and Metcalf 1997). An increase in the number of Sertoli
cells may have occurred in the male fathead minnow exposed to nonylphenol at 1.6 /J.g/L for 42 days
(Miles -Richardson et al. 1999). The evidence was not complete, but indicated the possibility of
increased phagocytic action and Sertoli cell tissue in testes. The condition may negatively affect sperm
production or survival. In a companion study with the fathead minnow, Giesy et al. (2000) found that
nonylphenol exposures of >0.4 //g/L depressed fecundity, concentrations of <3.4 //g/L did not change
vitellogenin concentrations in the blood of males, and raised the 17 p-estradiol liters in the blood of
male and female fish at concentrations >0.05 /ug/L. The characteristic of nonylphenol to induce
estrogenic effects has seldom been reported at concentrations below the freshwater Final Chronic Value
of 5.920 f^g/L. More studies are needed to achieve a better understanding of the role of nonylphenol in
estrogen mimicry.
Additional data on the lethal and sublethal effects of nonylphenol on saltwater species that do
not comply with data requirements described in the "Guidelines" for inclusion in other tables are
15
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presented in Table 6. Results from a sexual reproduction test with red alga species, Champia parvula,
indicated that reproduction was not inhibited at the highest measured concentration tested, 167 ^g/L
(Tagliabue 1993). Cypris larva of the barnacle, Balanus amphitrite, were exposed to nonylphenol for
48 hi and the settlement of the larva was reduced at 1.0 /zg/L (Billinghurst et al. 1998). The soft-shell
clam, My a arenaria, showed no adverse effects on survival from a 360-hr exposure at 700 /^g/L
(McLeese et al. 1980b). Nonylphenol reduced byssus thread strength in the blue mussel Mytilus edulis
(Granmo et al. 1989) at concentrations >56 //g/L. Nonylphenols also show promise as antifouling
agents when compared with other alkyIphenols, copper, and tributyl tin (Takasawa et al. 1990). The
antifouling test results, however, are qualitative. Nonylphenol concentrations extracted from sediments
in the Venice, Italy lagoon were higher in areas with large masses of decomposing macroalgae
(primarily Ulva rigida) than in areas not associated with the decomposition (Marcomini et al. 1990).
This suggests that nonylphenol bioaccumulated by the macroalgae was transferred to trie sediment as
the algae died and decomposed.
McLeese et al. (1980b) reported 96-hr test results for the Atlantic salmon, Salmo solar, that
were in general agreement with freshwater trout test results. In four tests, LC50 values ranged from
130 to 900 jUg/L. Ward and Boeri (1990c) found similar toxicity results for sheepshead minnow,
Cyprinodon variegatus, exposed in brackish water as those reported for salt water (Table 1). In
brackish water, LC50's ranged from >420 ^g/L for a 24-hr exposure to 320 //g/L for a 72-hr
exposure. KUlifish (Kelly -and Di Giulio 2000) were exposed as embryos and larva to nonylphenol for
96 hrs. Even though the solvent concentration used in the exposures exceeded the 0.5 mL/L
recommended limit, the data are included in Table 6 because the results reported for the solvent
controls do not show decreased hatching success or increased abnormalities at 10 days post-hatch.
Embryos exposed to 2,204 /^g/L for 96 hr were all abnormally developed at 10 days post-fertilization.
The LC50 for the same exposure period was 5,444 ^g/L. Killifish larva were similar in sensitivity to
nonylphenol exposures at post hatch ages of 1, 14, and 28 days with LCSO's of 214, 209, and 260,
respectively.
Additional data on the effect of nonylphenol on saltwater species do not indicate greater
sensitivities than indicated previously. Some of the data presented in Table 6 were from the same
acute tests listed in Table 1 (Lussier et al. 2000; Ward and Boeri 1990a,b), but for exposure durations
other than 96 hr.
16
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Unused Data
Some data concerning the effects of nonylphenol on aquatic organisms and their uses were not
used because the tests were conducted in mixtures of chemicals (i.e., Ahel et al. 1993; Amato and
Wayment 1998; Dwyer et al. 1999a; Escher et al. 1999; Larsson et al. 1999; Moore et al. 1987;
Purdom et al. 1994; Sundaram et al. 1980; Turner et al. 1985) or in sediments (i.e., Fay et al. 2000;
Hansen et al. 1999; Ward and Boeri 1992). Andersen et al. (1999); Celius et al. (1999); Jobling and
Sumpter (1993); Knudsen and Pottinger (1999); Lamche and Burkhardt-Holm (2000); Levine and
Cheney (2000); Loomis and Thomas (1999); Milligan et al. (1998); Petit et al. (1997, 1999) exposed
excised cells in tissue cultures. Data were not used when organisms were dosed by injection (i.e.,
Arukwe et al. 1997a,b, 1998; Christiansen et al. 1998a,b,c; Coldham et al. 1997, 1998; Haya et al.
1997; Madsen et al. 1997; Nirnrod and Benson 1996, 1997; Spieser et al. 1998; Yadetie et al. 1999) or
gavage (i.e., Rice et al. 1998; Thibaut et al. 1998). Data were not used when generated in an artificial
medium (i.e., Weinberger et al. 1987). Tsuda et al. (2000) measured tissue concentrations from feral
fish, but water concentrations greatly varied. Some studies were conducted with only the ethoxylated
nonylphenols (i.e., Baldwin et al. 1998; Braaten et al. 1972; Dorn et al. 1993; Maki et al. 1998;
Manzano et al. 1998, 1999; Patoczka and Pulliam 1990). Bearden and Schultz (1997, 1998); Lewis
(1991); Liber et al. (1999); Varma and Patel (1988) and Veith and Mekenyan (1993) compiled data
from other sources. Results were not used when the test organism or the test material were not
adequately described (e.g., Folmar et al. 1998; Hansen et al. 1998; Kopf 1997; Magliulo et al. 1998;
Midler 1980; Palmer et al. 1998; Weinberger and Rea 1981).
Summary
Acute toxicity of nonylphenol was tested in eighteen species and two subspecies representing
fifteen genera of freshwater organisms. Toxicity values ranged from 55.72 //g/L for the amphipod
Hyalella azteca to 774 ^g/L for the snail Physella virgata. For the four most sensitive tested
freshwater species, two were invertebrates and two were vertebrate species (Figure 1). No
relationships have been demonstrated between water quality characteristics (such as hardness and pH)
and toxicity. Eleven species of fish were tested and were in the mid-range of sensitivity (133.9 to
289.3 ,ug/L) of tested species. The freshwater Final Acute Value (FAV) is 55.71 //g/L which is equal
to the LC50 for the most sensitive tested species, Hyalella azteca. Acute toxicity has been tested with
ten species of saltwater organisms (Figure 2). Species Mean Acute Values ranged from 17 //g/L for
17
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the winter flounder, Pleuronectes americanus, to 209.8 //g/L for the sheepshead minnow, Cyprinodon
variegatus. The saltwater FAV is 13.35 //g/L.
Chronic toxicity of nonylphenol was tested in five freshwater species and one saltwater species
(Figure 3). The most sensitive species tested was the mysid Americamysis bahia and it had a Chronic
Value (CV) of 5.112 /^g/L based on reduced growth. Two freshwater fish were tested; the rainbow
trout, Oncorhynchus mykiss, had a CV of 7.861 ^g/L based on growth, and the fathead minnow,
Pimephales promelas, had a CV of 10.18 //g/L based on survival. Two species of freshwater
cladocerans were tested and CVs ranged from 22.62 to 157.9 /ug/L based on reproduction. One
species of freshwater midge was tested and its CV was 61.82 ^g/L. Data were available to calculate a
Final Acute-Chronic Ratio (FACR) for Daphnia magna, a freshwater cladoceran, saltwater mysid,
Americamysis bdhia, and rainbow trout. The FACR for nonylphenol is 9.410.
Two species of aquatic plants were exposed to nonylphenol. Plants were as sensitive as
animals, showing effects that ranged from 27 to 410 /^g/L. Based on the vegetative growth test using
the saltwater planktonic diatom Skeletonema costatum, the Final Plant Value for nonylphenol is 27
/xg/L.
Nonylphenol bioaccumulates in aquatic organisms to low levels. In freshwater fish, lipid-
normalized bioconcentration factors ranged from 39 to 209 times. Bioaccumulation was apparently
greater in saltwater organisms where bioconcentration factors ranging from 78.75 to 2,168 were
measured.
Nonylphenol is considered an endocrine disrupter chemical and induces production of
vitellogenin in male rainbow trout. This is a process normally occurring in female fish in response to
estrogenic hormones during the reproductive cycle. It also induces precocious development of ovaries
and an intersex condition in some fish species.
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 organisms and their uses should not be affected
unacceptably if the four-day average concentration of nonylphenol does not exceed 5.9 /zg/L more than
once every three years on the average and if the one-hour average concentration does not exceed 27.9
fj-g/L more than once every three years on the average. Saltwater organisms and their uses should not
18
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be affected unacceptably if the four-day average concentration of nonylphenol does not exceed 1.4
//g/L more than once every three years on the average and if the one-hour average concentration does
not exceed 6.7 //g/L more than once every three years on the average.
Implementation
As discussed in the Water Quality Standards Regulation (U.S. EPA 1983) 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 1987, 1994). Water quality criteria adopted in State water quality standards
could have the same numerical values as criteria developed under Section 304 of the Clean Water Act.
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. State water quality standards include both numeric and
narrative criteria. A State may adopt a numeric criterion within its water quality standards and apply it
either state-wide to all waters designated for the use the criterion is designed to protect or to a specific
site. A State may use an indicator parameter or the national criterion, supplemented with other
relevant information, to interpret its narrative criteria within its water quality standards when
developing NPDES effluent limitations under 40 CFR 122.44(d)(l)(vi).2
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" and "four
days" were selected by the U.S. EPA on the basis of data concerning how rapidly some aquatic species
react to increases hi 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 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.
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Use of criteria which have been adopted in State water quality standards for developing water
quality-based permit 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 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 available (U.S. EPA
1987, 1991).
20
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Figure 1. Ranked Summary of Nonylphenol GMAVs Freshwater.
Ranked Summary of Nonylphenol GMAVs
_J IUUU -
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Freshwater Rnal Acute Value = 55.7 uo/L Nonylphenol
Criteria Maximum Concentration = 27.9 ug/L Nonylphenol
I I I I I I I I I I
0.0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 0.9 1.0
• Invertebrates
% Rank GMAVs DFisn
A Amphibians
21
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Figure 2. Ranked Summary of Nonylphenol GMAVs - Saltwater.
Ranked Summary of Nonylphenol GMAVs
— IUUU q
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i i 1 1 1 1 1 1
Nonylphenol Effect
-^ 0
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Saltwater Final Acute Value = 13.4 ug/L Nonylphenol
Criteria Maximum Concentration = 6.7 \ig/L Nonylphenoi
I I I I I I I III
0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 0.9 1.0
n/ i-» i ^-«> • •< < • Invertebrate
% Rank GMAVs
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22
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Figure 3. Chronic Toxicity of Nonylphenol to Aquatic Animals.
Chronic Toxicity of Nonylphenol to Aquatic Animals
IUUU -
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D
D
Freshwater Final Chronic Value = 5.B ug/L Nonylphenol
A
Saltwater Final Chronic Value = 1.4 \ig/L Nonylphenol
I I I I I I I I I I
0.0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 0.9 1.0
% Rank Genus Mean Chronic Value ° 'reshwater lnvertebrates
I Freshwater Fish
Saltwater Invertebrates
23
-------
Table 1. Acute Toxicity of Nonylphenol to Aquatic Animals
Species
Annelid (adult),
Lumbriculus variegatus
Snail (adult),
Physella virgata
Cladoceran
(< 24-hr old),
Daphnia magna
Cladoceran
(<24-hr old),
Daphnia magna
Midge (2nd instar),
Chironomus teutons
Dragonfly (nymph),
Ophiogomphus sp.
Amphipod,
(juvenile, 2mm TL),
Hyalella azteca
Amphipod
(juven., 2-3mm TL),
Hyalella azteca
Rainbow trout
(0.67 ±0.35 g),
Oncorhynchus mykiss
Rainbow trout
(1.25 +0.57 g),
Oncorhynchus mykiss
Rainbow trout
(0.27 ±0.07 g),
Oncorhynchus mykiss
Rainbow trout
(1.09 ±0.38g),
Oncorhynchus mykiss
Rainbow trout
(0.48 ±0.08 g),
Oncorhynchus mykiss
Method"
F,M
F,M
R,M
S,M
F,M
F,M
F,M
F,M
S,U
S,U
S,U
s,u
s,u
LC50
or ECso11
Chemical pH (ng/L)
FRESHWATER SPECIES
>90% 6.75 342
>90% 7.89 774
>90% 7.87 84.8
91.8% 8.25 190
>95% 8.0-8.4 160
>90% 8.06 596
>90% 7.80 20.7
>95% 7.9-8.7 150
85% 7.8-7.9 190
85% 7.5-7.7 260
85% 7.9 140
85% 7.7-7.9 270
85% 7.5-7.9 160
Species
Mean Acute
Value
(ng/L) Reference
342 Brooke 1993a
774 Brooke 1993a
Brooke 1993a
126.9 Comber et al.
1993
160 England and
Bussard 1995
596 Brooke 1993a
Brooke 1993a
55.72 England and
Bussard 1995
Dwyer et al.
1995
Dwyer et al.
1995
Dwyer et al.
1995
Dwyer et al.
1995
Dwyer et al.
1995
24
-------
Table I. Acute Toxicity of Nonylphenol to Aquatic Animals (continued)
LL5
Species
Rainbow trout
(0.50 ±0.21 g),
Oncorhynchus mykiss
Rainbow trout
(45 d),
Oncorhynchus mykiss
Apache trout
(0.85 ±0.49 g),
Oncorhynchus apache
Apache trout
(0.38 ±0.18 g),
Oncorhynchus apache
Greenback cutthroat
trout (0.31 ±0.17g),
Oncorhynchus clarki
stomais
Lahontan cutthroat
trout
(0.34 ±0.08 g),
Oncorhynchus clarki
henshawi
Lahontan cutthroat
trout
(0.57 ±0.23 g),
Oncorhynchus clarki
henshawi
Fathead minnow (0.32
±0.16 g),
Pimephales promelas
Fathead minnow (0.56
±0.19 g),
Pimephales promelas
Fathead minnow (0.45
±0.35 g),
Pimephales promelas
Fathead minnow (0.40
+0.21 g),
Pimephales promelas
or
Method" Chemical pJH (Mg/L)
S,U 85% 6.5-7.9 180
F,M
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,U
>90% 6.72 221
85% 7.8-7.9 180
85% 7.3-7.7 160
85% 7.5-7.6 150
85%
7.9
140
85% 7.6-7.7 220
85% 7.7-8.1 210
85% 7.8-8.1 360
85% 7.6-7.8 310
85% 7.5-7.9 330
Species
Mean Acute
Value
(ng/L) Reference
Dwyer et al.
1995
221 Brooke 1993a
Dwyer et al.
1995
169.7 Dwyer et al.
1995
Dwyer et al.
1995
Dwyer et al.
1995
166.6 Dwyer et al.
1995
Dwyer et al.
1995
Dwyer et al.
1995
Dwyer et al.
1995
Dwyer et al.
1995
25
-------
Table 1. Acute Toxicity of Nonylphenol to Aquatic Animals (continued)
Species
Fathead minnow (0.34
+ 0.24 g),
Pimephales promelas
Fathead minnow (0.39
±0.14 g),
Pimephales promelas
Fathead minnow
(32 d),
Pimephales promelas
Fathead minnow (25-
35 d),
Pimephales promelas
Bonytail chub
(0.29 ±0.08 g),
Gila elegans
Bonytail chub
(0.52 ±0.09 g),
Gila elegans
Colorado squawfish
(0.32 ±0.05 g),
Ptychocheilus lucius
Colorado squawfish
(0.34 ±0.05 g),
Ptychocheilus lucius
Razorback sucker
(0.31 ±0.04 g),
Xyrauchen texanus
Razorback sucker
(0.32 + 0.07g),
Xyrauchen texanus
Gila topminnow (0.219
g, 27.2mm),
Poeciliopsis
occidentalis
Method3
S,U
s,u
F,M
F,M
S,U
S,U
S,U
S,U
S,U
s,u
s,u
Chemical pH
85% 7.5-7.6
85% 7.8-8.2
99% 7.29
>90% 7.23
85% 7.7-7.9
85% 7.4-7.6
85% 8.1-8.2
85% 7.8-8.0
85% 7.8-8.1
85% 7.9-8.0
85% 8.0
LC50
or EC50b
Otg/L)
170
290
140
128
270
310
240
270
160
190
230
Species
Mean Acute
Value
(n2/L) Reference
Dwyer et al.
1995
Dwyer et al.
1995
Holcombe et
al. 1984;
University of
Wisconsin-
Superior 1985
133.9 Brooke 1993a
Dwyer et al.
1995
289.3 Dwyeretal.
1995
Dwyer et al.
1995
254.6 Dwyeretal.
1995
Dwyer et al.
1995
174.4 Dwyeretal.
1995
230 Dwyer et al.
1999a
26
-------
Table 1. Acute Toxicity of Nonylphenol to Aquatic Animals (continued)
Species Method"
Fountain darter (0 . 062 S , U
g, 20.2mm),
Eiheostoma rub rum
Greenthroat darter S,U
(0.133 g, 22.6mm),
Elheosloma lepidum
Bluegill (juvenile), F,M
Lepomis macrochirus
Boreal toad S,U
(0.012 g, 9.6 mm),
Bufo boreas
Coot clam S,U
(embryo/larva),
Mulinia lateralis
Copepod (10-12 d), S,U
Acartia lonsa
Mysid ( < 24-hr old), F,M
Americamysis bahia
Mysid (< 24-hr old), F,M
Americamysis bahia
Amphipod (adult), F,M
Leplocheirus
plumulosus
Grass shrimp F,M
(48-hr old),
Palaemonetes vulgaris
American lobster (1st R,U
stage),
Homarus americanus
Mud crab F,M
fdrh anrl Sth sta?esV
Chemical
85%
85%
>90%
85%
SALTW
90%
>95%
90%
90%
90%
90%
90%
LCSO
or EC^
fig Ug/L)
8.0-8.1 110
8.0-8.2 190
7.61 209
7.9-8.0 120
ATER SPECIES
7.8-8.2 37.9
190
7.3-8.2 43
7.8-8.2 60.6
7.8-8.2 61.6
7.8-8.2 59.4
7.8-8.2 71
7.8-8.2 >195
Species
Mean Acute
Value
110
190
209
120
37.9
190
51.05
61.6
59.4
71
>195
Reference
Dwyer et al.
1999a
Dwyer et al.
1999a
Brooke 1993a
Dwyer et al.
1999a
Lussier et al.
2000
Kusk and
Wollenberger
1999
Ward and
Boeri 1990a
Lussier et al.
2000
Lussier et al.
2000
Lussier et al.
2000
Lussier et al.
2000
Lussier et al.
2000
Dyspanopeus sayii
27
-------
Table 1. Acute Toxicity of Nonylphenol to Aquatic Animals (continued)
Species Method3
Winter flounder S,M
(48-hr-old),
Pleuronectes
americanus
Sheepshead minnow F,M
(juvenile) ,
Cyprinodon variegatus
Sheepshead minnow F,M
(juvenile) ,
Cyprinodon variegatus
Inland silversides F,M
(juvenile) ,
Menidia beryllina
LCSO
or EC50b
Chemical pH (jte/L)
90% 7.8-8.2 17
>95% 7.4-8.1 310
90% 7.8-8.2 142
90% 7.8-8.2 70
Species
Mean Acute
Value
(wg/L) Reference
17 Lussier et al.
2000
Ward and
Boeri 1990b
209.8 Lussier et al.
2000
70 Lussier et al.
2000
1 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.
28
-------
Table 2a. Chronic Toxicity of Nonylphenol to Aquatic Animals
Species
Cladoceran,
Ceriodaphnia dubia
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Midge,
Chironomus Tentans
Rainbow trout,
Oncorhynchus mykiss
Fathead minnow,
Pimephales promelas
Mysid,
Americamysis bahia
Test"
LC
LC
LC
LC
LC
ELS
ELS
LC
Chemical
>95%
93.1
>90%
91.8%
95%
>90%
>95%
>95%
pH
8.3-8.6
8.04
8.46
8.25
7.73
6.97
7.1-8.2
7.4-8.3
Chronic
Limits
88.7-202
10.7-47.8
116-215
24-39
42-91
6.0-10.3
7.4-14
3.9-6.7
Chronic
Value
133.9
22.62
157.9
30.59
61.82
7.861
10.18
5.112
Reference
England 1995
Fliedner 1993
Brooke 1993a
Comber et al.
1993
Kahletal. 1997
Brooke 1993a
Ward and Boeri
1991c
Ward and Boeri
1991b
a LC = life-cycle or partial life-cycle; ELS = early life-stage.
b Based upon measured concentrations of nonylphenol.
29
-------
Table 2b. Acute-Chronic Ratios
Acute-Chronic Ratios
Acute Value Chronic Value
Species
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Mysid,
Americamysis bahia
Rainbow trout,
Oncorhynchus mykiss
pH
7.87-8.46
8.25
7.3-8.3
6.72-6.97
(we/L)
84.8
190
43
221
(we/L)
157.9
30.59
5.112
7.861
Ratio
2.000"
6.211
8.412
28.11
Reference
Brooke 1993a
Comber et al. 1993
Ward and Boeri
1990a, 1991b
Brooke 1993a
Acute-Chronic Ratio calculated as 0.5370 but changed to 2.000 (see text).
30
-------
Table 3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic Ratios
Rank8
15
14
13
12
11
10
9
8
denus Mean
Acute Value
(MB/L)
774
596
342
289.3
254.6
230
209
184.2
Species
FRESHWATER SPECIES
Snail,
Physella virgata
Dragonfly,
Ophiogomphus sp.
Annelid,
Lumbriculus variegatus
Bony tail chub,
Gila elegans
Colorado squawfish,
Ptychocheilus lucius
Gila topminnow,
Poeciliopsis occidentalis
BluegiU,
Lepomis macrochirus
Rainbow trout,
Oncorhynchus mykiss
Apache trout,
Oncorhynchus apache
Lahontan cutthroat trout,
Species Mean
Acute Value
(Me/L)b
774
596
342
289.3
254.6
230
209
221
169.7
166.6
Species Mean
Acute-Chronic
Ratioc
28.11
174.4
Oncorhynchus clarki
henshawi, and
Greenback cutthroat trout,
Oncorhynchus clarki stomais
Razorback sucker,
Xyrauchen texanus
174.4
6
5
4
160
144.6
133.9
Midge,
Chironomus tentans
Greenthroat darter,
Etheostoma lepidwn
Fountain darter,
Etheostoma rubrum
Fathead minnow,
160
190
110
133.9
Pimephales promelas
31
-------
Table 3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic Ratios (continued)
Rank"
3
2
1
10
9
8
7
6
5
4
3
2
1
Genus Mean
Acute Value
(us./'L)
126.9
120
55.72
209.8
>195
190
71
70
61.6
59.4
51.05
37.9
17
Species
Cladoceran,
Daphnia magna
Boreal toad,
Bufo boreas
Aruphipod,
Hyalella azteca
SALTWATER SPECIES
Sheepshead minnow,
Cyprinodon variegatus
Mud crab,
Dyspanopeus sayii
Copepod,
Acartia lonsa
American lobster,
Homarus americanus
Inland silversides,
Menidia beryllina
Amphipod,
Leptocheirus plumulosus
Grass shrimp,
Palaemonetes vulgaris
Mysid,
Americarnysis bahia
Coot clam,
Mulinia lateralis
Winter flounder,
Pleuronectes americanus
Species Mean
Acute Value
(ue/L)b
126.9
120
55.72
209.8
>195
190
71
70
61.6
59.4
51.05
37.9
17
Species Mean
Acute-Chronic
Ratioc
3.524
8.412
1 Ranked from the most resistant to the most sensitive based on Genus Mean Acute Value.
b From Table 1.
c From Table 2.
32
-------
Table 3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic Ratios (continued)
Fresh Water
Final Acute Value = 55.71
Criterion Maximum Concentration = 55.71/2 = 27.86 /u.g/L
Final Acute-Chronic Ratio = 9.410 (see text)
Final Chronic Value = (55.71 //g/L)/9.410 = 5.920
Salt Water
Final Acute Value = 13.35 //g/L
Criterion Maximum Concentration = 13.35/2 = 6.675 ,ug/L
Final Acute-Chronic Ratio = 9.410 (see text)
Final Chronic Value = (13.35 ^g/L)/9.410 = 1.419 //g/L
33
-------
Table 4. Toxicity of Nonylphenol to Aquatic Plants
Species
Chemical
Duration
(days)
Effect
Concentration
Qug/L) Reference
FRESHWATER SPECIES
Green algae,
Selenastrum
capricornutum
>95%
7.8
EC50
410 Ward and Boeri
1990a
SALTWATER SPECIES
Diatom,
Skeletonema
costatum
>95%
30a
EC50,
number of
cells
27 Ward and Boeri
1990d
^Salinity (g/kg).
34
-------
Table 5. Bioaccumulation of Nonylphenol by Aquatic Organisms
Cone.
in
Normalized
BCF BCF
Species
Fathead
minnow
(0.5-1 g),
Pimephales
promelas
Fathead
minnow
(0.5-1 g),
Pimephales
promelas
Fathead
minnow
(4-wk old),
Pimephales
promelas
Fathead
minnow
(4-wk old),
Pimephales
promelas
Fathead
minnow
(4-wk old),
Pimephales
promelas
Fathead
minnow
(4-wk old),
Pimephales
promelas
Fathead
minnow
(4-wk old),
Pimephales
promelas
Water Duration Percent or
Chemical (ug/L)' pH (days) Tissue Lipids BAFb
FRESHWATER SPECIES
>95% 4.9 7.0-7.6 27 Whole 271
body
>95% 22.7 7.0-7.6 27 Whole 344
body
99% 18.4 7.62 4 Whole 4.7 + 1.7 751
body
99% 41.9 7.62 4 Whole 4.7±1.7 677
body
99% 82.1 7.62 4 Whole 4. 7 ±1.7 945
body
99% 9.3 7.60 28 Whole 4.7 + 1.7 769
body
99% 19.2 7.60 28 Whole 4.7±1.7 984
body
or
BAF Reference
Ward and
Boeri 1991a
Ward and
Boeri 1991a
159.8 Brooke
1993b
144.0 Brooke
1993b
201.1 Brooke
1993b
163.6 Brooke
1993b
209.4 Brooke
1993b
35
-------
Table 5. Bioaccumulation of Nonylphenol by Aquatic Organisms (continued)
Cone.
in
Water
BCF
Duration Percent or
Normalized
BCF
or
Species Chemical (Mg/L)a pH
Fathead 99% 38.1 7.60
minnow
(4-wk old),
Pimephales
promelas
Fathead 99% 77.5 7.60
minnow
(4-wk old),
Pimephales
promelas
Fathead 0.4
minnow >98% 1.6
(adult), 3.4
Pimephales
promelas
Bluegill 99% 21.6 7.79
(4-wk old),
Lepomis
macrochirus
Bluegill 99% 43.9 7.79
(4-wk old),
Lepomis
macrochirus
Bluegill
(4-wk old), 99% 86.5 7.79
Lepomis
macrochirus
Bluegill 99% 5.6 7.55
(4-wk old),
Lepomis
macrochirus
Bluegill 99% 12.4 7.55
(4-wk old),
Lepomis
macrochirus
Bluegill 99% 27.6 7.55
(4-wk old),
Lepomis
macrochirus
(days) Tissue Lipids BAFb
28 Whole 4. 7 ±1.7 876
body
28 Whole 4.7 + 1.7 603
body
Whole 203
42 body 252
268
4 Whole 4. 9 ±1.5 279
body
4 Whole 4.9±1.5 257
body
4 Whole 4.9±1.5 223
body
28 Whole 4.911.5 231
body
28 Whole 4.9 + 1.5 253
body
28 Whole 4.911.5 250
body
BAF0 Reference
186.4 Brooke
1993b
128.3 Brooke
1993b
Giesy et al.
2000
56.94 Brooke
1993b
52.45 Brooke
1993b
r
45.51 Brooke
1993b
47.14 Brooke
1993b
51.63 Brooke
1993b
51.02 Brooke
1993b
36
-------
Table 5. Bioaccumulation of Nonylphenol by Aquatic Organisms (continued)
Species
Bluegill
(4-wkold),
Lepomis
macrochirus
Bluegill
(juvenile),
Lepomis
macrochirus
Cone.
in
Water
Chemical (^g/L1)'
99% 59.5
1.0
96.4% 3.0
30.0
Duration
pH (days)
7.55 28
7.7 20
BCF
Percent or
Tissue Lipids BAFb
Whole 4.9 + 1.5 191
body
76
Whole 0.72 60
body ±0.46 37
Normalized
BCF
or
BAF
38.98
105.6
83.33
51.39
Reference
Brooke
1993b
Liber et al.
1999
SALTWATER SPECIES
Blue mussel,
Mytikis
edulis
Blue mussel,
Mytihis
edulis
Common
shrimp,
Crangon
crangond
Common
shrimp,
Crangon
crangond
Three-spined
stickleback,
Gasterosteus
aculeatus
Three-spined
stickleback,
Gasterosteus
aculeatus
14C- 5.9
labeled
UC- 6.2
labeled
14C- 6.4
labeled
14C- 7.4
labeled
I4C- 4.8
labeled
14C- 4.9
labeled
16
16
16
16
16
16
Whole 1.6 2,740
body
Whole 1.9 4,120
body
Whole 1.4 110
body
Whole 1.7 900
body
Whole 6.7 1,200
body
Whole 7.8 1,300
body
1,712
2,168
78.75
529.4
179.1
166.7
Ekelund et
al. 1990
Ekelund et
al. 1990
Ekelund et
al. 1990
Ekelund et
al. 1990
Ekelund et
al. 1990
Ekelund et
al. 1990
1 Measured concentration of nonylphenol.
b Bioconcentration factors (BCFs) and bioaccumulation factors (BAFs) are based on measured concentrations of nonylphenol
in water and in tissue.
c When possible, the factors were normalized to 1 % lipids by dividing the BCFs and BAFs by the percent lipids.
d Non-resident species.
37
-------
Table 6. Other Data on Effects of Nonylphenol on Aquatic Organisms
Species
Chemical
Duration
Effect
Concentration
Cug/L) Reference
_ -I
Green alga,
Chlamydomonas
reinhardtii
Floating moss,
Salvinia molesta
Duckweed,
Lemna minor
Duckweed,
Lemna minor
Ciliate protozoan,
Tetrahymena
pyriformis
Ciliate protozoan,
Tetrahymena
pyriformis
Rotifer
(4 to 6 hr-old
female)
Brachionus
calydflorus
Clam (15 g),
Anodonta
cataractae
Zooplankton
Benthic macro-
invertebrates
Cladoceran
(< 24-hr old),
Daphnia magna
Cladoceran
(< 24-hr old and
FRESHWATER
24 days
9 days
5.6 96 hr
4 days
24 hr
7.40 40 hr
Technical 7.5 96 hr
144 hr
96.4% 7.5 8.2 20 days
96.4% 7.5 8.2 20 days
8.0 21 days
'85% 7.8 8.4 96 hr
(fed)
SPECIES
100% algistatic
Reduced frond
production
IC50
Reduced frond
production
EC50
Reduced
population
growth 50%
Sexual
reproduction
reduced
LC50
NOEC
LOEC
NOEC
LOEC
NOEC
LOEC (reduced
fecundity)
MATC (young)
MATC (adults)
6,250
2,500
5,500
125
460
747
50
5000
23
76
23
76
50
100
302
136
Weinberger and
Greenhalgh
1984
Prasad 1986 .
Weinberger and
lyengar 1983
Prasad 1986
Yoshioka 1985
Schultz 1997
Preston et al.
2000
McLeese et al.
1980b
O'Halloran et
al. 1999
Schmude et al.
1999
Baldwin et al.
1997
Gerritsen et al.
1998
adults),
Daphnia magna
38
-------
Table 6. Other Data on Effects of Nonylphenol on Aquatic Organisms (continued)
Concentration
Species
Cladoceran
(< 24-hr old),
Daphnia magna
Cladoceran
(< 24-hr old),
Daphnia magna
Cladoceran
(< 36-hr old),
Daphnia galeata
mendolae
Cladoceran
(> 48-hr old),
Daphnia pulex
Cladoceran
(> 48-hr old),
Daphnia pulex
Cladoceran
(> 48-hr old),
Daphnia pulex
Cladoceran
(< 24-hr old),
Ceriodaphnia
dubia
Cladoceran
(< 24-hr old),
Ceriodaphnia
dubia
Midge
(2nd instar) ,
Chironomus
tentans
Sea lamprey
(larva),
Petromyzon
marinus
Chemical pH Duration
"85% 7.7 + 0.02 21 days
Technical 21 days
30 days
Practical 48 hr
grade
Practical 48 hr
grade
Practical 48 hr
grade
>95% 8.3-8.6 48 hr
>95% 8.3-8.6 7 days
>95% 8.2 14 days
7.5-8.2 14 hr
Effect
No sex ratio
change (high
food rate)
Increased ratio
of males (low
food rate)
50% adult
mortality
NOEC
(deformed
offspring)
NOEC
LOEC
(deformed
offspring)
LC50
LC50
LC50
LC50 (fed)
LC50 (fed)
LC50
EC50
LT100
(UE/D
25
25
200.5
44
10
50-
140
176
190
276
225
119
95
5,000
Reference
Baer and Owens
1999
LeBlanc et al.
2000
Shurin and
Dodson 1997
Ernst etal. 1980
Ernst et al. 1980
Ernst et al. 1980
England 1995
England 1995
England and
Bussard 1993
Applegate et al.
1957
39
-------
IF
Table 6. Other Data on Effects of Nonylpheuol on Aquatic Organisms (continued)
Species
Brook trout
(juvenile),
Salvelinus
fontinalis
Lake trout
(juvenile),
Salvelinus
naymaycush
Brown trout
(fmgerling),
Salmo iruua
Atlantic salmon
(4g),
Salmo salar
Chinook salmon
(juvenile),
Oncorhynchus
tshawytscha
Coho salmon
(juvenile),
Oncorhynchus
kisutch
Rainbow trout
(juvenile),
Oncorhynchus
mykiss
Rainbow trout
(juvenile),
Oncorhynchus
mykiss
Rainbow trout
(juvenile),
Oncorhynchus
mykiss
Rainbow trout
(juvenile),
Oncorhynchus
mykiss
Chemical
Practical
grade
Practical
grade
oH Duration
96 hr
35 days
7.0
7.2
7.2
2hr
96 hr
3hr
3hr
7.5-8.2 4hr
96hr
96 hr
96 hr
Effect
LC50
LC50
(fed)
LT100
LC50
LT100
LT100
LT100
LC50
LC50
LC50
Concentration
(ug/L) Reference
145 Holmes and
Kingsbury 1980
> 40 Holmes and
Kingsbury 1980
5,000 Wood 1953
900 McLeese et al.
1980b
10,000 MacPhee and
Ruelle 1969
10,000 MacPhee and
Ruelle 1969
5,000 Applegate et al.
1957
920 Ernst et al, 1980
560 Ernst et al. 1980
230 Holmes and
Kingsbury 1980
40
-------
Table 6. Other Data on Effects of Nonylphenol on Aquatic Organisms (continued)
Chemical
Rainbow trout
(adult males),
Oncorhynchus
mykiss
Rainbow trout
(adult males),
Oncorhynchus
mykiss
Rainbow trout
(50-200g),
Oncorhynchus
mykiss
Rainbow trout
(50 200 g),
Oncorhynchus
mykiss
Rainbow trout,
(40 - 60 g),
Oncorhynchus
mykiss
Rainbow trout
(40 - 60 g),
Oncorhynchus
mykiss
Rainbow trout
(40 - 60 g),
Oncorhynchus
mykiss
Rainbow trout
(juvenile),
Oncorhynchus
mykiss
Rainbow trout
(juvenile),
Oncorhynchus
mykiss
Rainbow trout
(? juvenile),
Oncorhynchus
mykiss
>99%
>99%
>99%
6.5
Concentration
Duration
3 wk
3 wk
72 hr
72 hr
8hr
2-5hr
12 - 24 hr
4hr
72 hr
22 days
35 days
Effect (w£/L)
Increased 20.3
vitellogenin
production
Increased 54.3
vitellogenin
production
LC50 193.65
Increased 14.14
vitellogenin
mRNA
Tissue half-life 18
fat 19.8hr
muscle 1 8 . 6 hr
liver 5. 9 hr
Eviscerated 1 8
carcass
BAF = 24.21
Viscera 18
BAF = 98.2
Vitellogenin 10
mRNA
production
Vitellogenin 100
production
Reduced growth 50
at 108 days
Reduced growth 30
at 466 days
Reference
Jobling et
1996
Jobling et
1996
Lech et al.
Lech et al.
Lewis and
1996
Lewis and
1996
Lewis and
1996
Ren et al.
Ren et al.
al.
al.
1996
1996
Lech
Lech
Lech
1996a
1996b
Ashfield et al.
1998
41
-------
Table 6. Other Data on Effects of Nonylphenol on Aquatic Organisms (continued)
Concentration
Species
Rainbow trout
(juvenile),
Oncorhynchus
mykiss
Rainbow trout
(35-50 g,
immature),
Oncorhynchus
mykiss
Rainbow trout
(adult males),
Oncorhynchus
mykiss
Rainbow trout
(juvenile, 103-
168 g),
Oncorhynchus
mykiss
Rainbow trout
(adult males) ,
Oncorhynchus
mykiss
Rainbow trout
(598 g; juvenile
females),
Oncorhynchus
mykiss
Chemical pH Duration Effect Cug/L)
96 hr Decreased 220
number of
muscarinic
cholinergic
receptors in
brain
8.0 - 8.4 21 days Increased 50
vitellogenin in
blood plasma
3 wk BCF = 116 63
BCF = 88 81
99% 9 days No vitellogenin 109
induction
Technical 10 days Epidermal 1
per month mucous cell
for 4 granulation
months
99% 18 wk Reduced GSI; 85.6
Reduced HSI; 85.6
Induced 8 . 3
vitellogenin;
Lowered plasma 85.6
estradiol;
Lowered plasma 8.3
FSH
Reference
Jones et al. 1998
Tremblay and
Van Der Kraak
1998
Blackburn et al.
1999
Pedersen et al.
1999
Burkhardt-Holm
et al. 2000
Harris et al.
2001
42
-------
Table 6. Other Data on Effects of Nonylphenol on Aquatic Organisms (continued)
Rainbow trout
(1667 +201.6 g;
F0 3 yr-old
adults),
Oncorhynchus
mykiss
Lahontan
cutthroat trout
(juvenile),
Oncorhynchus
clarki henshawi
Apache trout
(juvenile),
Oncorhynchus
mykiss
Northern
squawfish
(juvenile),
Ptychocheilus
oregonensis
Colorado
squawfish
(juvenile),
Ptychocheilus
lucius
Goldfish
(juvenile),
Carassius
auratus
Concentration
Chemical pH Duration Effect (ME/L)
98% 7.6 4 months Reduced embryo 1
(exposed 10 survival;
days/month) Reduced hatch; 10
F0 Males 1
increased
vitellogenin;
Fj Females 10
increased
vitellogenin and
testosterone;
F! Males 10
increased
estradiol
96 hr Decreased 220
number of
muscarinic
cholinergic
receptors in
brain
96 hr Decreased > 130
number of
muscarinic
cholinergic
receptors in
brain
Reference
Schwaiger et al.
2002
Jones etal. 1998
Jones et al. 1998
7.2
3hr
LT100
96 hr
7.0
5hr
Decreased
number of
muscarinic
cholinergic
receptors in
brain
LT100
10,000
>220
MacPhee and
Ruelle 1969
Jones et al. 1998
5,000
Wood 1953
43
-------
Table 6. Other Data on Effects of Nonylphenol on Aquatic Organisms (continued)
Species
Common carp
(15.2 +3.8g
juvenile),
Cyprinus carpio
Common carp
(50-150 g mature
males),
Cyprinus carpio
Fathead minnow
(4-wk old),
Pimephales
promelas
Fathead minnow
(4-wk old),
Pimephales
promelas
Fathead minnow,
Pimephales
promelas
Fathead minnow
(mature),
Pimephales
promelas
Fathead minnow
(mature),
Pimephales
promelas
Fathead minnow
(mature),
Pimephales
promelas
Fathead minnow
(mature),
Pimephales
promelas
Chemical
Technical
(90% 4-NP)
95%
99%
99%
>98%
>98%
>98%
>98%
pH Duration
7.6 70 days
7.57 28-31
+0.03 days
11 °C
7.62 4 days
7.60 28 days
96 hr
42 days
42 days
42 days
42 days
Effect
Decreased
erythrocytes;
Increased
reticulocytes
BCF = 546.5
No change in
ivp-estradiol,
testosterone, or
vitellogenin
LC50
(fed)
BCF = 100.4
Decreased
number of
muscarinic
cholinergic
receptors hi
brain
Possible
increased
number of
Sertoli cells in
males
Decreased
fecundity
Increased d"
vitellogenin
Increased
17p-estradiol
Concentration
Cug/L) Reference
10 Schwaiger et al.
2000
10
5.36 Villenueve et al.
2002
138 Brooke 1993b
193 Brooke 1993b
> 220 Jones et al. 1998
1.6 Miles-
Richardson et
al. 1999
>0.4 Giesyetal.
2000
>3.4 Giesyetal.
2000
>0.05 Giesyetal.
2000
44
-------
Table 6. Other Data on Effects of Nonylphenol on Aquatic Organisms (continued)
Concentration
Species Chemical pH
BluegiU 7.0
(juvenile),
Lepomis
macrochirus
BluegiU 7.5-8.2
(juvenile),
Lepomis
macrochirus
Bluegill 99% 7.79
(4-wk old),
Lepomis
macrochirus
Bluegffl 99% 7.55
(4-wk old),
Lepomis
macrochirus
BluegiU 96.4% 7.7 7.9
(juvenile),
Lepomis
macrochirus
Southern Technical
platyfish (adult, 85 %
0.62 to 1.15g),
Xiphophorus
maculatus
Green Swordtail Technical
(adult males),
Xiphophorus
helleri
Green Swordtail Technical
(juvenile 30-d-old
males),
Xiphophorus
helleri
African clawed ACS Grade 7.8 - 8.0
frog (larva),
Xenopus laevis
Duration
2hr
14 hr
4 days
28 days
20 days
28 days
96 hr
72 hr
60 days
21 days
Effect CUE/L)
LT100 5,000
LT100 5,000
LC50 135
(fed)
BCF = 35.31 126
NOEC 76
LOEC (survival) 243
Reduced GSI 960
LC50 206
ViteUogenin 4
induced
Reduced sword 0.2
length
NOEC 25
LOEC 50
(increased rate
of tail
resorption)
Reference
Wood 1953
Applegate et al.
1957
Brooke 1993b
Brooke 1993b
Liber et al. 1999
Kinnberg et al.
2000
Kwak et al.
2001
Kwak et al.
2001
Fort and Stover
1997
45
-------
Table 6. Other Data on Effects of Nonylphenol on Aquatic Organisms (continued)
Concentration
Species Chemical
African clawed
frog (larva),
Xenopus laevis
Red alga, >95%
Champia parvula
Barnacle
(cypris larva),
Balanus
amphitrite
Soft-shell clam,
Mya arenaria
Coot clam, 90%
Mulinia lateralis
Coot clam, 90%
Mulinia lateralis
Coot clam, 90%
Mulinia lateralis
Blue mussel,
Mytilus edulis
Blue mussel,
Mytilus edulis
Blue mussel,
Mytilus edulis
Blue mussel,
Mytilus edulis
Blue mussel,
Mytilus edulis
Blue mussel,
Mytilus edulis
Blue mussel,
Mytilus edulis
pH Duration
12 wk
SALTWATER
2 days
48 hr
360 hr
30-311 24 hr
30-3 r 48 hr
30-3 la 72 hr
32a 96 hr
32a 360 hr
32a 13 days
32a 30 days
32a 30 days
32a 32 days
32a 24 hr
Effect
Increased female
phenotypes
SPECIES
No effect on
sexual
reproduction
Reduced cyprid
settlement
No mortality
LC50
LC50
LC50
LC50
LC50
Reduced byssus
strength
Reduced byssus
strength
No byssus
threads formed
Reduction in
growth
No effect on
fertilization
Oig/L)
22
167
1.0
700
-50
-50
-40
3,000
500
56
56
100
56
200
Reference
Kloas et al.
1999
Tagliabue 199:
Billinghurst et
al. 1998
McLeese et al.
1980b
Lussier et al.
2000
Lussier et al.
2000
Lussier et al.
2000
Granmo et al.
1989
Granmo et al.
1989
Granmo et al.
1989
Granmo et al.
1989
Granmo et al.
1989
Granmo et al.
1989
Granmo et al.
1989
46
-------
Table 6. Other Data on Effects
Species Chemical
Blue mussel,
Mytilus edulis
Blue mussel
(40-50 mm
length),
Mytilus edulis
Blue mussel,
Mytilus edulis
galloprovincialis
Mysid, 90%
Americamysis
bahia
Mysid, 90%
Americamysis
bahia
Mysid, 90%
Americamysis
bahia
Mysid, 90%
Americamysis
bahia
Mysid, 90%
Americamysis
bahia
Mysid, 90%
Americamysis
bahia
Mysid, >95%
Americamysis
bahia
Mysid, >95%
Americamysis
bahia
Mysid, >95%
Americamysis
bahia
Copepod
(10-12 d),
Acartia tonsa
of Nonylphenol on Aquatic Organisms (continued)
pH Duration Effect
32a 72 hr No effect on
development
50 days BCF = 350
2 days Repelled
attachment
30-3 r 24 hr LC50
30-3 la 48 hr LC50
30-3 la 72 hr LC50
30-3 la 120 hr LC50
30-3 la 144 hr LC50
30-31* 168hr LC50
20a 24 hr LC50
20a 48 hr LC50
20a 72 hr LC50
18a 48 hr LC50 synthetic
media
Concentration
(we/L)
200
40
22
-114
-82
-66
-60
-60
-60
>47
>47
44
360
280
Reference
Granmo et al.
1989
Granmo et al.
1991a,b
Etoh et al. 199
Lussier et al.
2000
Lussier et al.
2000
Lussier et al.
2000
Lussier et al.
2000
Lussier et al.
2000
Lussier et al.
2000
Ward and Boei
1990a
Ward and Boei
1990a
Ward and Boei
1990a
Kusk and
Wollenberger
1999
47
-------
Table 6. Other Data on Effects of Nonylphenol on Aquatic Organisms (continued)
Concentration
Species
Amphipod,
Lepiocheirus
plumulosus
Amphipod,
Leptocheirus
plumulosus
Amphipod,
Leptocheirus
plumulosus
Amphipod,
Leptocheirus
plumulosus
Amphipod,
Leptocheirus
plumulosus
Grass shrimp,
Palaemonetes
vulgaris
Grass shrimp,
Palaemonetes
vulgaris
Grass shrimp,
Palaemonetes
vulgaris
Grass shrimp,
Palaemonetes
vulgaris
Shrimp,
Crangon
septemspinosa
Shrimp,
Crangon
septemspinosa
Shrimp,
Crangon
septemspinosa
American lobster,
Homarus
americanus
Chemical
90%
90%
90%
90%
90%
90%
90%
90%
90%
>95%
>95%
>95%
90%
pH Duration
30-31a 48 hr
30-312 72 hr
30-3 r 120 hr
30-31a 144 hr
30-3 la 168 hr
30-3 la 24 hr
30-313 48 hr
30-3 la 72 hr
30-31a 120 hr
96 hr
96 hr
96 hr
30-3 la 24 hr
Effect
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
(we/L)
-160
-80
-50
-40
-30
-125
-60
-60
-60
300
300
300
-140
Reference
Lussier et al.
2000
Lussier et al.
2000
Lussier et al.
2000
Lussier et al.
2000
Lussier et al.
2000
Lussier et al.
2000
Lussier et al.
2000
Lussier et al.
2000
Lussier et al.
2000
McLeese et al.
1980b
McLeese et al.
1980b
McLeese et al.
1980b
Lussier et al.
2000
48
-------
Table 6. Other Data on Effects of Nonylphenol on Aquatic Organisms (continued)
Concentration
Species Chemical pH Duration
American lobster, 90% 30-313 48 hr
Homarus
americanus
American lobster, 90% 30-31* 72 hr
Homarus
americanus
American lobster, > 95 % 96 hr
Homarus
americanus
Atlantic salmon, - 96 hr
Salmo salar
Atlantic salmon, 96 hr
Salmo salar
Atlantic salmon, 96 hr
Salmo salar
Atlantic salmon, 96 hr
Salmo salar
Sheepshead 90% 30-3 la 72 hr
minnow,
Cyprinodon
variegatus
Sheepshead 90% 30-3 11 120 hr
minnow,
Cyprinodon
variegatus
Sheepshead 90% 30-3 la 144 hr
minnow,
Cyprinodon
variegatus
Sheepshead 90% 30-31" 168 hr
minnow,
Cyprinodon
variegatus
Sheepshead >95% 15-17* 24 hr
minnow,
Cyprinodon
variegatus
Effect
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
(uzlU
-140
-100
170
190
160
130
900
-150
-125
-120
-120
>420
Reference
Lussier et al.
2000
Lussier et al.
2000
McLeese et al.
1980b
McLeese et al.
1980b
McLeese et al.
1980b
McLeese et al.
1980b
McLeese et al.
1980b
Lussier et al.
2000
Lussier et al.
2000
Lussier et al.
9OOO
Z-VJUVJ
Lussier et al.
9000
^-\j\j\j
Ward and Boeri
1990c
49
-------
Table 6. Other Data on Effects of Nonylphenol on Aquatic Organisms (continued)
Concentration
Species
Sheepshead
minnow ,
Cyprinodon
variegatus
Sheepshead
minnow,
Cyprinodon
variegatus
Killifish
(embryo) ,
Fundulus
hetewclitus
Killifish
(embryo) ,
Fundulus
hetewclitus
Killifish
(1-day old larva),
Fundulus
hetewclitus
KiUifish (14-day
.old larva) , .
Fundulus
hetewclitus
KiUifish (28-day
old larva),
Fundulus
hetewclitus
Three spine
stickleback
Gastewsteus
aculeatus
Inland
silversides,
Menidia beryllina
Inland
silversides,
Chemical pH
>95% 15-17a
>95% 15-17"
85 - 90% 20a
(technical)
85-90% 20a
(technical)
85-90% 20a
(technical)
85 - 90% 20a
(technical) .
85-90% 20a
(technical)
Commercial 32a
(para-
substituted
with branched
nonyl chain)
90% 30-3 T
90% 30-3 la
Duration Effect
48 hr LC50
72 hr LC50
10 days 100% abnormal
development
96 hr LC50
96 hr LC50
(fed)
96 hr LC50
-- (fed)
96 hr LC50
(fed)
96 hr LC50
24 hr LC50
48 hr LC50
Cug/L) Reference
340 Ward and Boeri
1990c
320 Ward and Boeri
1990c
2,204 Kelly and Di
Giulio 2000
5,444 Kelly and Di
Giulio 2000
214 Kelly and Di
Giulio 2000
209 Kelly and Di
... Giulio 2000
260 Kelly and Di
Giulio 2000
370 Granmo et al.
1991a
-120 Lussier et al,
2000
-100 Lussier et al.
2000
Menidia beryllina
50
-------
Table 6. Other Data on Effects of Nonylphenol on Aquatic Organisms (continued)
Species
Inland
silversides,
Menidia beryllina
Inland
silversides,
Menidia beryllina
Inland
silversides,
Menidia beryllina
Inland
silversides,
Menidia beryllina
Chemical
90%
pH
30-31'
Duration
72 hi
90% 30-31° 120 hr
90% 30-31' 144 hr
90% 30-31a 168 hr
Effect
LC50
LC50
LC50
LC50
Concentration
Cug/L) Reference
-80
Lussier et al.
2000
-60 Lussier et al.
2000
-60 Lussier et al.
2000
-60 Lussier et al.
2000
Salinity (g/kg).
51
-------
a IF
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