&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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                                                                                                  TT
        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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                                                                                                  IT
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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                                                                                                   I
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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                                                                                                  I
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.
                                                19

-------
       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

-------
Figure 1. Ranked Summary of Nonylphenol GMAVs  Freshwater.
                 Ranked Summary of Nonylphenol GMAVs
_J IUUU -
*— "
0)
c
0
*m
lv
'c
0)
o
c
o
0 100 :
•4-1
O
£ :
LU
"o
c
0)
^
c
o
z 10 J
Freshwater B
•



D
D
a
D
D D

Q
A '


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

-------
Figure 2. Ranked Summary of Nonylphenol GMAVs - Saltwater.
                Ranked Summary of Nonylphenol GMAVs
— IUUU q
D) :
w
c
o
to
Concent
_i.
§
i i 1 1 1 1 1 1
Nonylphenol Effect
-^ 0
O i . . , i , . , ,i
Saltwater

"
D •
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
DRsh
                                22

-------
Figure 3. Chronic Toxicity of Nonylphenol to Aquatic Animals.
                 Chronic Toxicity of Nonylphenol to Aquatic Animals
IUUU -
5
0 :
3
"r5
'E
o 10-
O :
-
1 -
n
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

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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

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                       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

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                                                                                          a  IF
                                        REFERENCES

Ahel, M. and W. Giger.  1993.  Aqueous solubility of alkylphenols and alkylphenol polyethoxylates.
Chemosphere 26:1461-1470.

Ahel, M., J. McEvoy and W. Giger.  1993. Bioaccumulation of the lipophilic metabolites of nonionic
surfactants in freshwater organisms.  Environ. Pollut. 79:243-248.

Ahel, M., W. Giger and M. Koch.  1994a.  Behaviour of alkylphenol polyethoxylate surfactants in the
aquatic environment-I.  Occurrence and transformation in sewage treatment. Wat. Res. 28:1131-1142.

Ahel, M., W. Giger and C. Schaffner. 1994b.  Behavior of alkylphenol polyethoxylate surfactants in
the aquatic environment-II. Occurrence and transformation in rivers.  Wat. Res. 28:1143-1152.

Ahel, M., F.E. Scully,  Jr., J. Hoigne and W. Giger.  1994c. Photochemical degradation of
nonylphenol and nonylphenol polyethoxylates in natural waters.  Chemosphere 28:1361-1368.

Ahel, M., C. Schaffner and W. Giger. 1996. Behaviour of alkylphenol polyethoxylates surfactants in
the aquatic environment-Ill.- Occurrence and elimination of their persistent metabolites during
infiltration of river water to groundwater. Wat.  Res. 30:37-46.

Ahel, M., E. Molnar, S. Ibric and W. Giger.  2000. Estrogenic metabolites of alkylphenol
polyethoxylates in secondary sewage effluents and rivers.  Wat.  Sci. Technol. 42:15-22.

Allen, Y., A.P. Scott, P. Matthiessen, S. Haworth, J.E. Thain and S. Feist.  1999.  Survey of
estrogenic activity in United Kingdom estuarine and coastal waters and its effects on gonadal
development of the flounder Platichthys flesus. Environ. Toxicol. Chem. 18:1791-1800.
                                             52

-------
Amato, J.R. and D.D. Wayment.  1998. Surfactant toxicity identification with a municipal
wastewater. In: Environmental Toxicology and Risk Assessment.  Little, E.S., A.J. DeLoney and
B.M. Greenberg, Eds.  ASTM STP 1333, Vol. 7, American Society for Testing and Materials,
Philadelphia, PA.  pp. 272-283.

Andersen, H.R., A. Andersson, S.F.  Arnold, H. Autrup, M. Barfoed, N.A. Beresford, P.
Bjerregaard, L.B. Christiansen, B. Gissel, R. Hummel, E.B. Jorgensen, B.  Korsgaard, R. Le Guevel,
H. Leffers, J. McLachlan, A. Moller, J.B. Nielsen, N. Olea, A. Oles-Karasko, F. Pakdel, K.L.
Pedersen, P. Perez, N.E. Skakkeboek, C. Sonnenschein, A.M. Soto, J.P. Sumpter, S.M. Thorpe and
P. Grandjean.   1999.  Comparison of short-term estrogenicity tests for identification of hormone-
disrupting chemicals.  Environ. Health Perspect. 107(Suppl.  1):89-108.

Applegate, V.C., J.H. Howell, A.E. Hall, Jr. and M.A. Smith.  1957. Toxicity of 4,346 chemicals to
larval lampreys and fishes.  Special Scientific Report-Fisheries, No. 207, U.S. Dept. Interior, Fish and
Wildlife Service, Washington, DC. 157pp.

Arukwe, A., T. Celius, B.T. Walther and A. Goksoyr. 1998. Plasma levels of vitellogenin and
eggshell zona radiata proteins in 4-nonylphenol and o,p' nonylphenol treated juvenile Atlantic salmon
(Salmo solar).  Mar. Environ. Res. 46:133-136.

Arukwe, A., L. Forlin and A. Goksoyr.  1997a. Xenobiotic and steroid biotransformation enzymes in
Atlantic salmon (Salmo salar) liver treated with an estrogenic compound, 4-nonylphenol. Environ.
Toxicol. Chem.  16:2576-2583.

Arukwe, A., F.R. Knudsen and A. Goksoyr. 1997b.  Fish zona radiata (eggshell) protein: A sensitive
biomarker for environmental estrogens. Environ. Health Perspect. 105:418-422.

Arukwe, A., R. Thibaut, K. Ingebrigtsen, T. Celius, A. Goksoyr and J-P. Cravedi.  2000.   In vivo and
in vitro metabolism and organ distribution of nonylphenol in Atlantic salmon (Salmo salar).  Aquat.
Toxicol. 49:289-304.
                                              53

-------
AsMield, L.A., T.G. Pottinger and J.P. Sumpter. 1998.  Exposure of female juvenile rainbow trout to
alkylphenolic compounds results in modifications to  growth and ovosomatic index.  Environ. Toxicol.
Chem. 17:679-686.

Baer, K.N. and K.D. Owens.  1999. Evaluation of selected endocrine disrupting compounds on sex
determination in Daphnia magna using reduced photoperiod and different feeding rates. Bull. Environ.
Contain. Toxicol. 62:214-221.

Baldwin, W.S., S.E.  Graham, D. Shea and G.A. LeBlanc. 1997.  Metabolic androgenization of
female Daphnia magna by the xenoestrogen 4-nonylphenol. Environ. Toxicol. Chem.  16:1905-1911.

Baldwin, W.S., S.E.  Graham, D. Shea and G.A. Leblanc. 1998.  Altered metabolic elimination of
testosterone and associated toxicity  following exposure to  Daphnia magna to nonylphenol
polyethoxylate. Ecotoxicol.  Environ. Saf. 39:104-111.

Bearden, A.P. and T.W. Schultz. 1997. Structure-activity relationships for  Pimephales and
Tetrahymena: a mechanism of action approach.  Environ.  Toxicol. Chem.  16:1311-1317.

Bearden, A.P. and T.W. Schultz. 1998. Comparison of Tetrahymena and Pimephales toxicity based
on mechanism of action.  SAR QSAR Environ. Res. 9:127-153.

Bennett, E.R. and C.D. Metcalfe.  1998. Distribution of alkylphenol compounds in Great Lakes
sediments, United States and Canada.  Environ. Toxicol. Chem.  17:1230-1235.

Bennet, E.R. and C.D. Metcalfe. 2000.  Distribution of degradation products of alkylphenol
ethoxylates near sewage treatment plants in the Lower Great Lakes, North America.. Environ.
Toxicol. Chem.  19: 784-792.

Bennie, D.T.  1999.   Review of the environmental occurrence of alkylphenols and alkylphenol
ethoxylates.  Wat. Qual. Res. J. Can.  34:79-122.
                                             54

-------
Bennie, D.T., C.A. Sullivan, H. Lee, I.E. Peart and RJ. Maguire.  1997.  Occurrence of
alkylphenols and alkylphenol mono- and di-ethoxylates in natural waters of the Laurentian Great Lakes
basin and the upper St. Lawrence River. Sci. Total Environ. 193:263-275.

Billinghurst, Z., A.S. Clare, T. Fileman, M. McEvoy, J. Readman and M.H. Depledge.  1998.
Inhibition of barnacle settlement by the environmental oestrogen 4-nonylphenol and the natural
oestrogen 170 oestradiol.  Mar. Pollut. Bull. 36:833-839.

Blackburn, M.A., S.J. Kirby and M.J. Waldock.  1999.  Concentrations of alkyphenol polyethoxylates
entering UK estuaries. Mar. Pollut. Bull.  38:109-118.

Braaten, B., A. Granmo and R. Lange.  1972. Tissue-swelling in Mytilus edulis L. induced by
exposure to a nonionic surface  active agent.  Norw. J. Zool. 20:137-140.

Brooke, L.T. 1993a.  Acute and chronic toxicity of nonylphenol to ten species of aquatic organisms.
Report to  the U.S. EPA for Work Assignment No.  02 of Contract No. 68-C1-0034.  Lake Superior
Research Institute, University of Wisconsin-Superior, Superior, WI.  March 24. 30 pp.

Brooke, L.T.  1993b. Accumulation and lethality  for two freshwater fishes (fathead minnow and
bluegill) to nonylphenol.  Report to the U.S. EPA  for Work Assignment No.  1-12 of Contract No. 68-
Cl-0034.  Lake Superior  Research Institute, University of Wisconsin-Superior, Superior, WI.
September 30. 49 pp.

Brooke, L.T.  1994.  Accumulation and lethality for two freshwater fishes (fathead minnow and
bluegill) to nonylphenol.  Report to the U.S. EPA  for Work Assignment No.  1-15 of Contract No. 68-
Cl-0034.  Lake Superior  Research Institute, University of Wisconsin-Superior, Superior, WI.  May
31. 49pp.

Budavari,  S. (Ed.).  1989. The Merck Index:  An encyclopedia of chemicals, drugs, and biologicals.
llth ed. Merck and Co., Inc. Rahway, NJ.
                                              55

-------
 Burkhardt-Holm, P., T. Wahli and W. Meier.  2000.  Nonylphenol affects the granulation of pattern of
 epidermal mucous cells in rainbow trout,  Oncorhynchus mykiss.  Ecotoxicol. Environ. Safe. 46:34-40.

 Celius, T., T.B. Haugen, T. Grotmol and B.T. Walther.  1999.  A sensitive zonagenetic assay for
 rapid in vitro assessment of estrogenic potency of xenobiotics and mycotoxins.  Environ. Health
 Perspect.  107:63-68.

 Christiansen, T., B. Korsgaard and A. Jespersen.  1998a.  Effects of nonylphenol and 17 p-estradiol on
 vitellogenin synthesis, testicular structure and cytology in male eelpout Zoarces viviparus.  J. Exp.
 Biol. 201:179-192.

 Christiansen, T., B. Korsgaard and A. Jespersen.  1998b.  Induction of vitellogenin synthesis by
 nonylphenol and 17p-estradiol and effects on the testicular structure in the eelpout  Zoarces viviparus.
 Mar. Environ. Res.  46:141-144.

 Christiansen, T., K.L. Pedersen, B. Korsgaard and P  Bjerregaard.  1998c.  Estrogenicity of
 xenobiotics in rainbow trout (Oncorhynchus mykiss} using in vivo synthesis of vitellogenin as a
 biomarker.  Mar. Environ.  Res.  46(1-5):  137-140.

 Coldham, N.G., M.J. Sauer, S.  Sivapathasundaram, L. Ashfield, T. Pottinger and C. Goodall.  1997.
 Tissue distribution, metabolism and excretion of 4-nonylphenol in rainbow trout. J. Vet. Pharmacol.
 Therap. 20(Suppl. 1): 256-257.

 Coldham,  N.G., S. Sivapathasundaram, M. Dave,  L.A. Ashfield, T.G. Pottinger, C.  Goodall and
 M.J. Sauer.  1998. Biotransformation, tissue distribution, and persistence of 4-nonylphenol residues
 in juvenile rainbow trout (Oncorhynchus mykiss).  Drug Metabol. Dispos. 26:347-354.

 Comber, M.H.I., T.D. Williams and K.M. Stewart.  1993. The  effects of nonylphenol on Daphnia
magna.  Wat. Res. 27:273-276.
                                              56

-------
Dorn, P.B., J.P. Salanitro, S.H. Evans and L. Kravetz. 1993.  Assessing the aquatic hazard of some
branched and linear nonionic surfactants by biodegradation and toxicity.  Environ. Toxicol. Chem.
12:1751-1762.

Dwyer, F.J., L.C. Sappington, D.R. Buckler and S.B. Jones. 1995.  Use of surrogate species in
assessing contaminant risk to endangered and threatened species. EPA/600/R-96/029. National
Technical Information Service, Springfield, VA.  71 pp.

Dwyer, F.J., O.K. Hardesty, C.E. Henke, C.G.  Ingersoll, D.W. Whites, D.R. Mount and C.M.
Bridges. 1999a.  Assessing contaminant sensitivity of endandered and threatened species: Toxicant
classes.  EPA/600/R-99/098.  National Technical Information Service, Springfield, VA.  15pp.

Dwyer, F.J., O.K. Hardesty, C.E. Henke, C.G.  Ingersoll, D.W. Whites, D.R. Mount and C.M.
Bridges. 1999b.  Assessing contaminant sensitivity of endangered and threatened species: Effluent
toxicity tests. EPA/600/R-99/099.  National Technical Information Service, Springfield, VA. 9 pp.

Ekelund, R., A. Bergman, A. Granmo, and M. Berggren. 1990.  Bioaccumulation of 4-nonylphenol
in marine animals—A re-evaluation. Environ. Poll. 64:  107-120.

Ekelund, R., A. Granmo, K. Magnusson and M.  Berggren.  1993.  Biodegradation of 4-nonylphenol
in seawater and sediment. Environ. Pollut. 79:59-61.

Ellis, D.D., C.M. Jone, R.A.  Larson and D.J. Schaeffer.  1982. Organic constituents of mutagenic
secondary effluents from wastewater treatment plants.  Arch. Environ. Contain. Toxicol. 11:373-382.

England, D.E.  1995.  Chronic toxicity of nonylphenol to  Ceriodaphnia dubia.  Report No. 41756.
ABC Laboratories, Inc. Columbia, MO. 409 pp.

England, D.E. and J.B. Bussard.  1993. Toxicity of nonylphenol to the midge Chironomus Unions.
Report No. 40597. ABC Laboratories, Inc., Columbia, MO. 2528 pp.
                                             57

-------
England, D.E. and J.B. Bussard.  1995.  Toxicity of nonylphenol to the amphipod Hyalella azteca.
Report No. 41569.  ABC Laboratories, Inc., Columbia, MO.  178 pp.

Ernst, B., G. Mien, K. Doe and R. Parker.  1980.  Environmental investigations of the 1980 spruce
budworm spray program in New Brunswick. Surveillance Report EPS-5-AR-81-3, November 1980.
Environment Canada, Atlantic Region, Halifax, NS.

Escher, M., T. Wahli, S. Buttner, W. Meier and P. Burkhardt-Holm.  1999. The effect of sewage
plant effluent on brown trout (Salmo trutta fario): a cage experiment.  Aquat. Sci. 61:93-110.

Etoh, H., S. Hageshita and K. Ina.  1997.  An improved assay for attachment-promoting substances of
the blue mussel, Mytilus edulis galloprovincialis.  J. Mar. Biotechnol. 5:24-26.

Fay, A.A., F.J. Brownawell, A.A. Elskus and A.E. McElroy. 2000.  Critical body residues in the
marine amphipod Ampelisca abdita: Sediment exposures with nonionic organic  contaminants.
Environ. Toxicol. Chem. 19:1028-1035.

Federal Register.  1990. Testing consent order on 4-nonylphenol, branched. Vol. 55, No.  35,
Wednesday February 21.. pp. 5991-5994.

Fliedner, A.  1993.  Daphnia magna, Reproduction test (OECD No. 202).  Fraunhofer-Institute fur
Umweltchemie und Okotoxikologie, Postfach 1260, W-5948 Schmallenberg - Grafschaft, Germany.
Report No. UBA-002/4-22 February.

Flouriot, G., F. Pakdel, B.  Ducouret and Y. Valotaire.  1995.  Influence of xenobiotics on rainbow
trout liver estrogen receptor and vitellogenin gene expression.  J. Molecular Endocrin. 15:143-151.

Folmar, L., M. Hemmer, N. Denslow, K. Kroll, A. Cheek, H. Meredith, H. Richman and G. Grau.
1998. A comparison of an  in vivo fish VTG assay with YES and E-screen to rank 'relative
estrogenicity' of natural pharmaceutical and xenoestrogens.  Am. Zool. 38:112A.
                                             58

-------
Fort, D.J. and E.L. Stover.  1997.  Development of short-term, whole-embryo assays to evaluate
detrimental effects on amphibian limb development and metamorphosis using Xenopus laevis.  In:
Environmental Toxicology and Risk Assessment: Modeling and Risk Assessment. F.J. Dwyer, T.R.
Doane and M:L. Hinman (Eds.).  ASTM, STP 1317, Vol. 6, American Society for Testing and
Materials, Philadelphia, PA., pp. 376-390.

Gaffney, P.E. 1976. Carpet and rug industry case study II: Biological effects.  J. Water Pollut.
Control Fed. 48:2731-2737.

Gerritsen, A., N. van der Hoeven and A. Pielaat.  1998.  The acute toxicity of selected alkylphenols to
young and adult Daphnia magna. Ecotoxicol. Environ. Safety. 39:227-232.

Giesy, J.P.,  S.L. Pierens, E.M. Snyder, S. Miles-Richardson, V.J. Kramer, S.A. Snyder, K.M.
Nichols and D.A. Villeneuve.  2000.  Effects of 4-nonylphenol on fecundity of biomarkers of
estrogenicity in fathead minnows (Pimephalespromelas). Environ. Toxicol. Chem. 19:1368-1377.

Giger, W., E. Stephanou and C. Schafmer.  1981.  Persistent organic chemicals in sewage effluents:
I. Identifications of nonylphenols and nonylphenol ethoxylates  by glass capillary gas chromatography/
mass spectrometry.  Chemosphere 10:1253-1263.

Giger, W., P.H.  Brunner and C. Schaffner.  1984.  4-Nonylphenol in sewage sludge;  Accumulation
of toxic metabolites from nonionic surfactants. Science 225:623-625.

Granmo, A., R. Ekelund, K. Magnusson and M. Berggren. 1989. Lethal and sublethal toxicity of
4-nonylphenol to the common mussel (Mytilus edulis L.). Environ.  Poll. 59: 115-127

Granmo, A., R. Ekelund, M. Berggren and K. Magnusson.  1991a. Toxicity of 4-nonylphenol to
aquatic organisms and potential for bioaccumulation. Proceedings, Swedish Environmental Protection
Agency Seminar on Nonylphenol Ethoxylates/nonylphenol,  Saltsjobaden, Sweden, February 6-8, pp.
53-75.
                                             59

-------
 Granmo, A., S. Kollberg, M. Berggren, R: Ekelund, K. Magnusson, L. Renberg and C. Wahlberg.
 1991b.  Bioaccumulation of nonylphenol in caged mussels in an industrial coastal area on the Swedish
 west coast.  In: Organic Micropollutants in the Aquatic Environment.  Angeletti, G. (Ed.).
 Proceedings of the 6th European Symposium, pp 71-79.

 Gray, M.A. and C.D. Metcalfe. 1997.  Induction of testis-ova in Japanese medaka (Oryzias latipes)
 exposed to p-nonylphenol.  Environ. Toxicol. Chem. 16:1082-1086.

 Hale, R.C., C.L.  Smith, P.O. de Fur, E. Harvey, E.O. Bush, M.J. La Guardia and G.G. Vadas.
 2000.  Nonylphenols in sediments and effluents associated with diverse wastewater outfalls.  Environ.
 Toxicol. Chem. 19:946-952.

 Hansen, F.T., V.E. Forbes and T.L. Forbes.  1999.  Effects of 4-n-nonylphenol on life-history traits
 and population dynamics of a polychaete. Ecol. Appl.  9:482-495.

 Hansen, P., H. Dizer, B. Hock, A. Marx, J. Sherry, M. McMaster and C. Blaise.  1998. Vitellogenin
 - a biomarker for  endocrine disruptors. Trends Anal. Chem.  17:448-451.

 Harries, I.E., D.A. Sheahan, S. Jobling, P. Matthiessen, P. Neall, J.P. Sumpter, T. Tylor and N.
 Zaman.  1997. Estrogenic activity in five United Kingdom rivers detected by measurement of
 vitellogenesis in caged male trout. Environ. Toxicol. Chem.  16:534-542.

 Harris,  C.A., E.M. Santos, A Janbakhsh, T.G. Pottinger, C.R. Tyler and J.P. Sumpter.  2001.
 Nonylphenol affects gonadotropin levels in the pituitary gland and plasma of female rainbow trout.
Environ. Sci. Technol. 35:2909-2916.

Harvilicz, H.  1999.  NPE demand remains  strong despite environmental concerns in Europe.
Chemical Market Reporter.  October 18, 1999.  p.  15.
                                             60

-------
Haya, K., L.E. Burridge and T.J. Benfey.  1997.  The effect of cortisol and nonylphenol on growth
and ornithine decarboxylase activity of juvenile Atlantic salmon,  Salmo salar  Can. Tech. Rep. Fish.
Aquat. Sci.  2192: 85-86.

Heinis, L.J., M.L. Knuth, K. Liber, B.R. Sheedy, R.L. Tunell and G.T. Ankley.  1999.  Persistence
and distribution of 4-nonylphenol following repeated application to littoral enclosures. Environ.
Toxicol.  Chem.  18:363-375.

Hemmer, M.J., B.L. Hemmer, C.J. Bowman, K.J. Kroll, L.C. Folmer, D. Marcovich, M.D. Hoglund
and N.D. Denstow. 2001.  Effects of p-nonylphenol, methoxychlor and endosulfan on vitellogenin
induction and expression in sheepshead minnow (Cyprindon variegatus).   Environ. Toxicol.  Chem.
20:336-343.

Hewitt, L.M., L. Tremblay, G.J. Van Der Kraak, K.R. Solomon and M.R. Servos. 1998.
Identification of the lampricide 3-trifluoromethyl-4-nitrophenol as an agonist for the rainbow trout
estrogen  receptor.  Environ. Toxicol. Chem.  17:425-432.

Holmes,  S. B. and P. D. Kingsbury. 1980.  The environmental impact of nonylphenol and the
MataciT  formulation.  Part 1: Aquatic ecosystems. Report FPMX-35. Forest Pest Management
Institute,  Canadian Forestry Service, SaultSte. Marie, Ontario.

Holcombe, G.W., G.L. Phipps, M.L. Knuth and T. Felhaber.  1984.  The acute toxicity of selected
substituted phenols, benzenes and benzoic acid esters to fathead minnows (Pimephales promelas).
Environ.  Pollut. (Series A) 35:367-381.

Islinger, M., S. Pawlowski, H. HoUert, A. Volkl and T. Braumbeck.  1999.  Measurement of
vitellogenin-mRNA expression in primary cultures of rainbow trout hepatocytes in a non-radioactive
dot blot/RNAse protection-assay.  Sci. Total Environ. 233:109-122.
                                             61

-------
Jobling, S. and J.P Sumpter.  1993.  Detergent components in sewage effluent are weakly oestrogenic
to fish: An in vitro study using rainbow trout ( Oncorhynchus mykiss) hepatocytes. Aquatic Toxicol.
27:361-372.

Jobling, S., D. Sheahan, J.A. Osborne, P. Matthiessen and J.P. Sumpter.  1996.  Inhibition of
testicular growth in rainbow trout (Oncorhynchus mykiss) exposed to estrogenic alkylphenolic
chemicals. Environ. Toxicol. Chem. 15:194-202.

Jones, S.B., L.B. King, L.C. Sappington, F.J. Dwyer, M. Ellersieck and D.R. Buckler. 1998.
Effects of carbaryl, permethrin, 4-nonylphenol, and copper on muscarinic cholinergic receptors in
brain of surrogate  and listed fish species. Comp. Biochem. Physiol. 120:405-414.

Kahl, M.D.,  E.A.  Makynen, P.A. Kosian and G.T. Ankley. 1997.  Toxicity of 4-nonylphenol in a
life-cycle test with the midge Chironomus tentans.  Ecotoxicol. Environ. Saf. 38:155-160.

Keith, T.L., S.A. Snyder,  C.G. Naylor, C.A. Staples, C. Summer, K. Kannan and J.P. Giesy. 2001.
Identification and quantitation of nonylphenol ethoxylates and nonylphenol in fish tissues from
Michigan.  Environ. Sci. Technol. 35:10-13.

Kelly, S.A. and R.T. Di Giulio. 2000.  Developmental toxicity of estrogenic alkylphenols inkillifish
(Fundulus heteroclitus). Environ. Toxicol. Chem.  19:2564-2570.

Kinnberg, K., B. Korsgaard, P. Bjerregaard and A. Jespersen.  2000.  Effects of nonylphenol and
17p-estradiol on vitellogenin synthesis and testis morphology in male platyfish Xiphorphorus
maculatus. J. Exper. Biol. 203:171-181.

Kitajima, F.,  C.G. Satuito, H. Hirota, I. Katsuyama and N. Fusetani.  1995. A new screening method
for antifouling substances against the young mussels Mytilus edulis galloprovincialis.  Fish. Sci.
61:578-583..
                                              62

-------
Kloas, W., I. Lutz and R. Einspanier. 1999.  Amphibians as a model to study endocrine disrupters:
II. Estrogenic activity of environmental chemicals in vitro and in vivo.  Sci. Total Environ.  225:59-
68.

Knudsen, F.R.  and T.G. Pottinger.  1999. Interaction of endocrine disrupting chemicals, singly and in
combination, with estrogen-, androgen-, and corticosteroid-binding sites in rainbow trout
(Oncorhynchus mykiss). Aquat. Toxicol. 44:159-170.

Kopf, W. 1997.  Wirkung endodriner stoffe in biotests mit wasserorganismen.  In: Stoffe mit
endokriner wirkung in wasser. Bayerisches landesamt fur wasserwirt schaft, Institut fur
Wasserforschung, Munchen.  12pp.

Kusk, K.O.  and L. Wollenberger.  1999. Fully defined saltwater medium for cultivation of and
toxicity testing with marine copepod Acartia tonsa.  Environ. Toxicol. Chem.  18:1564-1567.

Kwak, H., M. Bae, M.  Lee, Y. Lee, B.  Lee, K. Kang, C. Chae, H.  Sung, J. Shin, J. Kim,  W. Mar,
Y. Sheen and M.  Cho.  2001.  Effects of nonylphenol, bisphenol A,  and their mixture on the
viviparous swordtail fish (Xiphophorus helleri).  Environ. Toxicol. Chem. 20:787-795.

Lamche, G.  and P. Burkhardt-Holm. 2000. Nonylphenol provokes  a vesiculation of the golgi
apparatus in three fish epidermis cultures. Ecotoxicol. Environ. Saf. 47:137-148.

Larsson, D.G.J., M.  Adolfsson-Erici, J.  Parkkonen, M. Pettersson, A.H. Berg, P. Olsson and L.
Forlin.  1999.  Ethinyloestradiol - an undesired fish contraceptive? Aquat. Toxicol. 45:91-97.

LeBlanc, G.A., S. Mu and C.V. Rider.  2000.  Embryotoxicity of the alkylphenol degradation product
4-nonylphenol to the crustacean Daphnia magna.  Environ. Health Perspect. 108:1133-1138.

Lech, J. J., S. K.  Lewis and L. Ren.  1996. In vivo estrogenic activity of nonylphenol in-rainbow
trout. Fund. Appl. Toxicol. 30:229-232.
                                              63

-------
Levine, C. and M.A. Cheney. 2000. Metabolic responses to acute toxicity of alkylphenols and
alkylphenol polyethoxylates in Elliptic complanata measured by calorespirometry.  Environ. Toxicol.
Chem. 19:1906-1910.

Lewis, M.A.  1991.  Chronic and sublethal toxicities of surfactants to aquatic animals:  A review and
risk assessment. Wat. Res. 25:101-113.

Lewis, S. K.  and J. J. Lech.  1996.  Uptake, disposition, and persistence of nonylphenol from water in
rainbow  trout (Oncorhynchus mykiss).  Xenobiotica 26:813-819.

Liber, K., J.  A. Gangl, T. D. Corry, L. J. Heinis and F. S. Stay.  1999. Lethality and
bioaccumulation of 4-nonylphenol in bluegill sunfish in littoral enclosures. Environ. Toxicol. Chem.
18:394-400.

Loomis,  A.K. and P. Thomas. 1999. Binding characteristics of estrogen receptor (ER) in Atlantic
croaker (Micropogonias undulatus) testis: Different affinity for estrogens and xenobiotics from that of
hepatic ER. Biol. Reprod.  61:51-60.

Lussier,  S.M., D, Champlin, J. LiVolsi, S. Poucher and RJ. Pruell.  2000. Acute toxicity of para-
nonylphenol to saltwater animals.  Environ. Toxicol. Chem. 19:617-621.

Lutz, I. and W. Kloas.  1999.  Amphibians as a model to study endocrine disrupters: I.
Environmental pollution and estrogen receptor binding. Sci. Total Environ.  225:49-57.

Lye, C.M., C.L.J. Frid, M.E. Gill, D.W. Cooper and D.M. Jones.  1999.  Estrogenic alkylphenols in
fish tissues, sediments, and waters from the U.K. Tyne and Tees estuaries.  Environ. Sci. Technol.
33:1009-1014.

MacPhee, C.  and R. Ruelle.  1969.  Lethal effects of 1888 chemicals upon four species offish from
western North America.  Bulletin No. 3, Forest, Wildlife and Range Experiment Station, University of
Idaho, Moscow, ID.  112 p.
                                              64

-------
                                                                                                   •ll
 Madsen, S.S., A.B. Mathiesen and B. Korsgaard. 1997.  Effects of 17 p-estradiol and 4-nonylphenol
 on smoltification and vitellogenesis in Atlantic salmon (Salmo salar).  Fish Physiol. Biochem.  17:303-
 312.

 Magliulo, L., M.P. Schreibman and J.L. Cepriano.  1998. Disruption of the brain-pituitary-gonad
 axis of platyfish due to hormone mimicking environmental pollutants.  Am. Zool. 38:112A.

 Maguire, R.J.  1999.  Review of the persistence of nonylphenol and nonylphenol ethoxylates in aquatic
 environments.  Wat. Qual. Res. J. Can. 34:37-78.

 Maki, H., H. Okamura, I. Aoyama and M. Fujita. 1998. Halogenation and toxicity of the
 biodegradation products of a nonionic surfactant, nonylphenol ethoxylate. Environ. Toxicol. Chem.
 17:650-654.

 Manzano, M.A., J.A. Perales, D. Sales and J.M.  Quiroga. 1998.  Effect of concentration on the
 biodegradation of a nonylphenol polyethoxylate in river water.  Bull. Environ. Contam. Toxicol.
 61:489-496.

 Manzano, M.A., J.A. Perales, D. Sales and J.M.  Quiroga. 1999.  The effect of temperature on the,
 biodegradation of a nonylphenol polyethoxylate in river water.  Wat. Res. 33:2593-2600.

 Marcomini, A., B. Pavoni, A. Sfriso and A.A. Orio.  1990. Persistent metabolites of alkylphenol
 polyethoxylates in the marine environment. Mar.  Chem. 29:307-324.

 McLeese, D.W., D.B. Sargeant,  C.D. Metcalfe, V Zitko and L.E. Burridge. 1980a. Uptake and
 excretion of aminocarb, nonylphenol, and pesticides diluent 585 by mussels (Mytilus edulis}. Bull.
 Environ. Contam. Toxicol. 24:575-581.

 McLeese, D.W., V. Zitko, C.D.  Metcalf and D.B. Sergeant.  1980b.  Lethality of aminocarb and the
 components of the aminocarb formulation to juvenile Atlantic salmon, marine invertebrates and a
freshwater clam. Chemosphere. 9:79-82.
                                             65

-------
McLeese, D.W., V. Zitko, D.B. Sargeant, L. Burridge and C.D. Metcalfe. 1981.  Lethality and
accumulation of alkylphenols in aquatic fauna.  Chemosphere 10:723-730.

Meldahl, A. C., K. Nithipatikom and J. J. Lech. 1996.  Metabolism of several 14C-nonylphenol
isomers by rainbow trout (Oncorhynchus mykiss): in vivo and in vitro microsomal metabolites.
Xenobiotica 26:1167-1180.

Miles-Richardson,  S.R., S.L. Pierens, K.M. Nichols, VJ.  Kramer, E.M. Snyder, S.A. Snyder, J.A.
Render, S.D. Fitzgerald and J.P. Giesy.  1999.  Effects of waterborne exposure to 4-nonylphenol and
nonylphenol ethoxylate on secondary sex characteristics and gonads of fathead minnows (Pimephales
promelas). Environ. Res. (Series A) 80:S122-S137.

Milligan, S.R., 0.  Khan and M. Nash. 1998.  Competitive binding of xenobiotic estrogens to rat
alpha-fetoprotein and to sex steroid binding proteins in human and rainbow trout ( Oncorhynchus
mykiss) plasma. Gen.  Comp. Endocrinol. 112:89-95.

Moore, S.B., R.A. Diehl, J.M. Earnhardt and G.B. Avery.  1987.  Aquatic toxicities of textile
surfactants.  Text. Chem. Color. 19:29-32.

Muller, R. 1980.  Fish toxicity  and surface tension of non-ionic surfactants: investigations of antifoam
agents. J. Fish. Biol.  16:585-589.

Naylor, C.G.  1992.  Environmental fate  of alkyIphenol ethoxylates.  Soap Cosmetics Chemical
Specialities. August.

Naylor, C.G., J.P.  Mieure, W.J. Adams, J.A. Weeks, F.J. Castaldi, L.D.  Ogle and R.R. Romano.
1992.  Alkylphenol ethoxylates  in the environment.  J. Am. Oil Chem. Soc. 69:695-708.

Nimrod, A.C. and W.H. Benson.  1996.  Estrogenic responses to xenobiotics in channel catfish
(Ictaluruspunctatus).  Mar. Environ. Res. 42:155-160.
                                             66

-------
 Nimiod, A.C. and W.H. Benson. 1997.  Xenobiotic interaction with and alteration of channel catfish
 estrogen receptor. Toxicol. Appl. Pharmacol.  147:381-390.

 Nimrod, A.C. and W.H. Benson. 1998. Reproduction and development of Japanese medaka following
 an early life stage exposure to xenoestrogens. Aquat. Toxicol. 44: 141-156.

 O'Halloran, S. L., K. Liber, J. A. Gangl  and M. L. Knuth.  1999. Effects of repeated exposure to 4-
 nonylphenol on the zooplankton community in littoral enclosures. Environ. Toxicol. Chem. 18:376-
 385.

 Palmer, B.D., S.K. Palmer, C. Burch, J.  Danyo and K.W. Selcer. 1998. Effects of endocrine
 disrupting chemicals on amphibians. Am.  Zool. 38(5): Abstract No.  177A.

 Patoczka, J. and G.W. Pulliam.  1990.  Biodegradation and secondary effluent toxicity of ethoxylated
 surfactants.  Wat. Res. 24:965-972.

 Pedersen, S.N., L.B. Christiansen, K.L. Pedersen, B. Korsgaard and P. Bjerregaard.  1999. In vivo
 estrogenic activity of branched and linear  alkylphenols in rainbow trout (Oncorhynchus mykiss). Sci.
 Tot. Environ. 233:39-96.

 Petit, F., P. Le Goff, J.P. Cravedi, Y. Valotaire and F. Pakdel.  1997.  Two complementary bioassays
 for screening the estrogenic potency of xenobiotics: recombinant yeast for trout estrogen receptor and
 trout hepatocyte cultures. J. Mol. Endocrinol.  19:321-335.

Petit, F., P. Le Goff, J.P. Cravedi, 0. Kah, Y. Valotaire and F. Pakdel.  1999.  Trout estrogen
receptor sensitivity to xenobiotics as tested by different bioassays.  Aquaculture.  177:353-365.

Prasad, R.  1986.  Effects of nonylphenol  adjuvant on macrophytes.  In: Adjuvants and
Agrochemicals,--Ch0w, P.N.P. (Ed.).  Vol. 1, Mode of action  and physiological activity  First
International Symposium. Brandon,  Manitoba, Canada.  August 5-7. XIV+ 207 pp.
                                              67

-------
 Preston, B.L., T.W  Snell, T.L. Robertson and BJ. Dingmann.  2000.  Use of freshwater rotifer
 Brachionus calyciflorus in screening assay for potential endocrine disrupters. Environ. Toxicol.
 Chem. 19:2923-2928.

 Purdom, C.E., P.A.  Hardiman, V.J. Bye, N.C. Eno,  C.R. Tyler and J.P. Sumpter.  1994. Estrogenic
 effects of effluents  from sewage treatment works.  Chem. and Ecol. 8:275-285.

 Radian Corp.  1990.  Nonylphenol and nonylphenol ethoxylates in river water and bottom sediments-
 January 1989-August 1990.  Final Report to Alkylphenol and Ethoxylates Panel, Chemical
 Manufacturers Association.

 Reed, H.W.B.  1978. ALkylphenols.  In: Kirk-Othmer:  Encyclopedia of chemical technology.
 Grayson M. and EcKroth D. (Eds.).  3rd ed., Vol. 2,  John Wiley and Sons, New York.  pp. 72-96.

 Ren, L., D. Lattier and J. J. Lech.  1996a.  Estrogenic activity in rainbow trout determined with a
 new cDNA probe for vitellogenesis, pSGSVgl.l. Bull. Environ. Contam. Toxicol. 56:287-294.

 Ren, L., S.K. Lewis  and J.J. Lech.  1996b. Effects of estrogen and nonylphenol on the post-
 transcriptional regulation of vitellogenin gene expression.  Chemico-Biol. Interact. 100:67-76.

 Rice, C.D.,  L.E. Roszell, M.M. Banes and R.E. Arnold.  1998.  Effects of dietary PCBs and nonyl-
 phenol on immune  function and CYP1A activity in channel catfish, Ictalurus punctatus.  Mar.
 Environ. Res.  46:351-354.

 Rouuedge, E.J. and J.P. Sumpter. 1996. Estrogenic activity of surfactants and some of then-
 degradation products  assessed using a recombinant yeast screen.  Environ. Toxicol. Chem. 15:241-
 248.

 Roufledge, E.J. and J.P. Sumpter. 1997. Structural features of alkylphenolic chemicals associated
with estrogenic activity. Jour. Biol. Chem.  272:3280-3288.
                                             68

-------
Roy F. Western Inc.  1990.  Determination of the vapor pressure of 4-nonylphenol.  Final Report Study
No. 90-047.  Roy F. Weston Inc., Environmental Fate and Effects Laboratory, 254 Welsh Pool Road,
Lionville, PA.  15 August 1990.

Schmude, K. L., K. Liber, T. D. Corry and F S. Stay.  1999.  Effects of 4-nonylphenol onbenthic
macromvertebrates and insect emergence in littoral enclosures.  Environ. Toxicol. Chem. 18:386-393.

Schultz, T.W.  1997.  Tetratox: Tetrahymena pyriformis population growth impairment endpoint   A
surrogate for fish lethality.  Toxicol. Methods. 7:289-309.

Schwaiger, J., O.K. Spieser, C. Bauer, H. Ferling, U. Mallow, W. Kalbfus and R.D. Negele.  2000.
Chronic toxicity of nonylphenol and ethinylestradiol: haematological and histopathological effects in
juvenile common carp (Cyprinus carpio).  Aquat. Toxicol. 51:69-78.

Schwaiger, J., U. Mallow, H. Ferling, S.  Knoerr, T.  Braunbeck, W.  Kalbfus and R.D. Negele. 2002.
How estrogenic is nonylphenol: A trans generational study using rainbow trout ( Oncorhynchus mykiss)
as a test organism.  Aquat. Toxicol. 59:177-189.

Servos, M.R.  1999.  Review of the aquatic toxicity, estrogenic responses and bioaccumulation of ,
alkylphenols and alkylphenol polyethoxylates.  Wat. Qual. Res. J. Can. 34:123-177.

Shackelford, W.M., D.M. Cline, L. Faas  and G. Kurth. 1983.  Evaluation of automated spectrum
matching for survey identification of wastewater components by gas chromatography-mass
spectrometry.  PB83-182931.  National Technical Information Service, Springfield,  VA.

Shang, D.Y., R.W. MacDonald and M.G. Ikonomou.  1999.  Persistence of nonylphenol ethoxylate
surfactants and their primary degradation products in sediments from near a municipal outfall hi the
Strait of Georgia, British Columbia, Canada.  Environ. Sci. Technol.  33:1366-1372.
                                             69

-------
                                                                                  i
Shurin, J.B. and S.I. Dodson. 1997.  Sublethal toxic effects of cyanobacteria and nonylphenol on
environmental sex determination and development in Daphnia. Environ. Toxicol. Chem. 16:1269-1276.

Sonnenschein, C. and A.M. Soto.  1998. An updated review of environmental estrogen and androgen
mimics and antagonists.  J. Steroid Biochem. Molec. Biol. 65:143-150.

Soto, A.M., H. Justicia, J.W. Wray and C. Sonnenschein.  1991.  £>-nonylphenol: An estrogenic
xenobiotic released from modified polystyrene. Environ. Health Perspect. 92:167-173.

Soto, A.M., T.M. Lin,  H. Justicia, R.M. Silvia and C. Sonnenschein. 1992.  An "in culture"
bioassay to assess the estrogenicity of xenobiotics (E-SCREEN). In: Advances in Modern
Environmental Toxicology.  Volume XXI.  Chemically-induced alterations in sexual and functional
development: The wildlife/human connection.  T. Colburn and C. Clement (Eds.).  Princeton
Scientific Publishing Co., Inc., NJ.  403 pp.

Spieser, O.K., J. Schwaiger, H. Ferling, W. Kalbfus and R. Negele.  1998. Effects of nonylphenol
and ethinyl-estradiol on swimming behavior of juvenile carp.  Abstract for Annual Meeting.
International Association for Great Lakes Research. Hamilton, Ontario, Canada,  pp. 37-38.

Staples, C.A., J. Weeks, I.E. Hall and C.G. Naylor. 1998. Evaluation of aquatic toxicity and
bioaccumulation of C8- C9-alkylphenol ethoxylates.  Environ. Toxicol. Chem. 17:2470-2480.

Staples, C.A., J.B. Williams, R.L. Blessing and P.T. Varineau. 1999.  Measuring the
biodegradability of nonylphenol, ether carboxylates, octylphenol, ether carboxylates, and nonylphenol.
Chemosphere 38:2029-2039.

Stephan, C.E., D.I. Mount, D.J. Hansen, J.H.  Gentile, G.A.  Chapman and W.A. Brungs.  1985.
Guidelines for deriving numerical national water quality criteria for the protection of aquatic organisms
and their uses. PB85-227049. National Technical Information Service, Springfield, VA.
                                             70

-------
                                                                                                   TT
Sumpter, J.P  1998.  Xenoendocrine disrupters — environmental impacts.  Toxicol. Lett.  102-103:
337-342.

Sundaram, K.M.S. and S. Szeto.  1981.  The dissipation of nonylphenol in stream and pond water
under simulated field conditions. J. Environ. Sci. Health (Part B) B16(6):767-776.

Sundaram, K.M.S., S. Szeto, R. Kindle and D. MacTavish.  1980.  Residues of nonylphenol in spruce
foliage, forest soil, stream water and sediment after its aerial application.  J. Environ.  Sci. Health (Part
B)B15(4):403-419.

Tabira, Y., M. Nakai, D. Asai, Y. Yakabe, Y. Tahara, T.  Shinmyozu, M. Noguchi, M. Takatsuki and
Y. Shimohigashi.  1999.  Structural requirements of para-alkyIphenols to bind to estrogen receptor.
Eur. J. Biochem.  262:240-245.

Tagliabue, M.D.  1993.  Nonylphenol Champia results. Memo dated February 23 to S. Poucher,
Science Applications International Corporation, Narragansett, RI. 6 pp.

Takasawa, R., H. Etoh, A. Yagi, K. Sakata and K. Ina. 1990. Nonylphenols as promising antifouling
agents  found by a simple bioassay  method using the blue mussel, Mytilus edulis. Agric. Biol. Chem.
54:1607-1610.

Tanghe, T., G. Devriese and W. Verstraete.  1999.  Nonylphenol and estrogenic activity  in aquatic
environmental samples. J. Environ. Qual.  28:702-709.

Thibaut, R., L. Debrauwer, D. Rao and J. Cravedi.  1998.  Characterization of biliary metabolites of
4-n-nonylphenol in rainbow trout (Oncorhynchus mykiss). Xenobiotica. 28:745-757.

Thibaut, R., L. Debrauwer, D. Rao and J.P Cravedi.  1999.   Urinary metabolites of 4-n-nonylphenol
in rainbow trout (Oncorhynchus mykiss).  Sci. Total Environ. 233:193-200.
                                             71

-------
                                                                                                  TT
Tsuda, T., A. Takino, M. Kojima, H. Harada, K. Muraki and M. Tsuji. 2000.  4-Nonylphenols and
4-tert-octylphenol in water and fish from rivers flowing into Lake Biwa.  Chemosphere 41:757-762.

Tremblay, L. and G. Van Der Kraak. 1998. Use of a series of homologous in vitro and in vivo
assays to evaluate the endocrine modulating actions of p-sitosterol in rainbow trout. Aquat. Toxicol.
43:149-162.

Turner, A.H:, F.S. Abram, V.M. Brown and H.A. Painter.  1985. The biodegradability of two
primary alcohol ethoxylate nonionic surfactants under practical conditions, and the toxicity of
biodegradation products to rainbow trout. Wat. Res. 19:45-51.

University of Wisconsin-Superior.  1985. Acute toxicities of organic chemicals to fathead minnows
(Pimephales promelas). Volume II.  D.L. Geiger, C.E. Northcott, DJ. Call and L.T. Brooke (Eds.).
Center for Lake Superior Environmental Studies, University of Wisconsin-Superior, Superior, WI.
 326pp.

U.S. EPA.  1983. Water quality standards regulation.  Federal Regist. 48:51400-51413.  Novembers.

U.S. EPA.  1985. Appendix B - Response to public comments on "Guidelines for deriving numerical
national water quality criteria for the protection of aquatic organisms and their uses." Federal Regist.
50:30793-30796.  July 29.

U.S. EPA.  1986. Chapter 1-Stream design flow for steady-state modeling. In: Book VI-Design
conditions. In: Technical guidance manual for performing waste load allocation. Office  of Water,
Washington, DC.  August.

U.S. EPA. 1987. Permit wriiers guide co water quality-based permitting for toxic pollutants. EPA-
440/4-87-005. Office of Water, Washington, DC.
                                             72

-------
 U.S. EPA. 1991. Technical support document for water quality-based toxics control. EPA-505/2-90-
 001 Office of Water, Washington, DC, March; or PB91-127415,  National Technical Information
 Service, Springfield, VA.

 U.S. EPA. 1994. Water Quality Standards Handbook: 2nd ed.  EPA-823-B-94-005a,b.  Washington,
 DC.

 USITC.  1981. Synthetic organic chemicals:  United States production and sales,  1980.  United States
 International  Trade Commission Publication No.  1183. U.S. Govt. Printing Office, Washington,  DC
 20402.  327 p.

 USITC.  1989. Synthetic organic chemicals:  United States production and sales,  1988.  United States
 International  Trade Commission Publication No. 2219. U.S. Govt. Printing Office, Washington,  DC
 20402.

 Varma, M.M. and D. Patel.  1988. Nonionic surfactants inperspecitive. J. Environ. Systems
 18:87-96.

 Veith, G.D. and O.G. Mekenyan. 1993. A QSAR approach for estimating the aquatic toxicity of soft
 electrophiles  (QSAR for soft electrophiles).  Quant. Struct. Act. Relat.  12:349-356.

 ViUenueve, D.L., S.A. Villalobos, T.L. Keith, E.M. Snyder, S.D. Fitzgerald and J.P. Giesy.  2002.
 Effects of waterborne exposure to 4-nonylphenol on plasma sex steroid and vitellogenin concentrations
 in sexually mature male carp (Cyprinus carpio). Chemosphere 47:15-28.

 Ward, T.J. and R.L. Boeri. 1990a. Acute  static  toxicity of nonylphenol to the freshwater alga
 Selenastrum capricomutum. EnviroSystems Study No. 8969-CMA. Resource Analysts, Inc.,
 Hampton, NH.  41 pp.

 Ward, T.J. and R.L. Boeri. 1990b. Acute flow through toxicity of nonylphenol to the mysid,
Mysidopsis bahia. Study Number 8974-CMA. EnviroSystems, Hampton, NH.  35 pp.
                                             73

-------
 Ward, TJ. and R.L. Boeri. 1990c. Acute flow through toxicity of nonylphenol to the sheepshead
 minnow, Cyprinodon variegatus. Study Number 8972-CMA. EnviroSystems, Hampton, NH. 34 pp.

 Ward, TJ. and R.L. Boeri. 1990d. Acute static toxicity of nonylphenol to the marine alga Skeletonema
 costatum. Study Number 8970-CMA. EnviroSystems, Hampton, NH. 42 pp.

 Ward, TJ. and R.L. Boeri.  1991a.  Bioconcentration test with nonylphenol and the fathead minnow,
 Pimephales promelas.  Study Number 8975-CMA.  Envirosystems, Hampton, NH.  72pp.

 Ward, TJ. and R.L. Boeri. 1991b. Chronic toxicity of nonylphenol to the mysid, Mysidopsis bahia.
 Study Number 8977-CMA. EnviroSystems, Hampton, NH. 61 pp.

 Ward, T J. and R.L. Boeri. 1991c. Early life stage toxicity of nonylphenol to the fathead minnow,
 Pimephales promelas. Study Number 8979-CMA. EnviroSystems, Hampton, NH. 59 pp.

 Ward, TJ. and R.L. Boeri. 1992. Toxicity  of nonylphenol to the tadpole Rana  catesbiana. Study
 Number 8981-CMA. EnviroSystems, Hampton, NH. 78 pp.

 Weinberger, P  and R.  Greenhalgh.  1984.  Some adjuvant effects on die fate of fenitrothion and
 aminocarb. Environm. Toxicol. Chem. 3:325-334.

 Weinberger, P.  and S. lyengar.  1983.  Effects  of aminocarb, fuel oil 585 and nonylphenol on the
 growth and development ofLemna minor L. Dev. Ecol. Environ. Qual.  Shuval, H. I. (Ed.). Proc.
 Int. Meet. Isr. Ecol. Soc. PP 595-607.

 Weinberger, P. and M. Rea. 1981.  Nonylphenol: A perturbant additive.  Canadian Tech. Rep. Fish
 Aquat. Sci. 990:370-381.

Weinberger, P., C. DeChacin and M. Czuba.  1987. Effects of nonyl phenol, a pesticide surfactant,
on some metabolic processes of Chlamydomonas segnis.  Can. J. Bot. 65:696-702.
                                            74

-------
White, R., S. Jobling, S.A. Hoare, J.P. Sumpter and M.G. Parker.  1994. Environmentally persistent
alkylphenolic compounds are estrogenic.  Endocrinology 135:175-182.

Wood, E. M. ' 1953.  The toxicity of 3400 chemicals to fish.  Report of Fish and Wildlife Service,
Kearneysville, West Virginia.  EPA 560/6-87-002  Office of Toxic Substances, Washington, DC,
August; or PB87-200-275  National Technical Information Service, Springfield, VA.

Yadetie, F.,  A. Arukwe, A. Goksoyr and R. Male. 1999.  Induction of hepatic estrogen receptor in
juvenile Atlantic salmon in vivo by the environmental estrogen, 4-nonylphenol. Sci. Total Environ.
233:201-210.

Yoshioka, Y.  1985.  Testing for the toxicity of chemicals with Tetrahymena pyriformis.  Sci. Total
Environ.  43:149-157.
                                             75

-------