FINAL DRAFT
United States ECAO-CIN-G081
Environmental Projection September , 1989
Research and
Development
HEALTH AND ENVIRONMENTAL EFFECTS DOCUMENT
BUTYL BENZYL PHTHALATE
Prepared for
0 HCE OF SOLID WASTE AND
E URGENCY RESPONSE
Prepared by
Environmental Criteria and Assessment Office
C fice of Health and Environmental Assessment
I 3. Environmental Protection Agency
Cincinnati, OH 45268
DRAF1: DO NOT CITE OR QUOTE
NOTICE
This document 1s a preliminary draft. It has not been formally released
by the U.S. Environmental Protection Agency and should not at this stage be
construed to represent Agency policy. It Is being circulated for comments
on Us technical accuracy and policy Implications.
HEADQUARTERS UBRARY
ENVIRONMENTAL PROTECTION AGENCY
WASHINGTON, D.C. 20460
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UNITED STATES ENVIRONMENTAL PROTECTION AGENCY
WASHINGTON, D.C. 20460
«*?*
nr,T 5 9 138G
OFFICE OF
RESEARCH AND DEVELOPMENT
S'CfB JECT:
FROM:
Health and Environmental Effects Document for Butyl
Benzyl Phthalate
TO:
H. Fatland, Ph.D.
Director
Office of Health and Environmental
Assessment (RD-689)
Matthew Straus
Chief, Waste Characterization Branch
Office of Solid Waste (OS-330)
I am forwarding copies of the Health and Environmental
Effects Document (HEED) for Butyl Benzyl Phthalate.
The HEEDs support listings under RCRA, as well as provide
health-related limits and goals for emergency and remedial
actions under CERCLA. These documents represent scientific
summaries of the pertinent available data on the environmental
fate and mammalian and aquatic toxicity of each chemical at an
extramural effort of about $10K. The attached document has been
reviewed within OHEA, by staff in OPP and OTS, and by two
external scientists.
Should you wish to see any of the files related to the
development of the HEEDs, please call Chris DeRosa at
F"S: 684-7531.
Attachment
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DISCLAIMER
This report 1s an external draft for review purposes only and does not
constitute Agency policy. Mention of trade names or commercial products
does not constitute endorsement or recommendation for use.
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PREFACE
Health and Environmental Effects Documents (HEEOs) are prepared for the
Office of Solid Waste and Emergency Response (OSHER). This document series
Is Intended to support listings under the Resource Conservation and Recovery
Act (RCRA) as well as to provide health-related limits and goals for
emergency and remedial actions under the Comprehensive Environmental
Response, Compensation and Liability Act (CERCLA). Both published
literature and Information obtained for Agency Program Office files are
evaluated as they pertain to potential human health, aquatic life and
environmental effects of hazardous waste constituents. The literature
searched for In this document and the dates searched are Included In
"Appendix: Literature Searched." Literature search material Is current up
to 8 months previous to the final draft date listed on the front cover.
Final draft document dates (front cover) reflect the date the document 1s
sent to the Program Officer (OSWER).
Several quantitative estimates are presented provided sufficient data
are available. For systemic toxicants, these Include: Reference doses
(RfD's) for chronic and subchronlc exposures for both the Inhalation and
oral exposures. The subchronlc or partial lifetime RfO, Is an estimate of
an exposure level which would not be expected to cause adverse effects when
exposure occurs during a limited time Interval I.e., for an Interval which
does not constitute a significant portion of the llfespan. This type of
exposure estimate has not been extensively used, or rigorously defined as
previous risk assessment efforts have focused primarily on lifetime exposure
scenarios. Animal data used for subchronlc estimates generally reflect
exposure durations of 30-90 days. The general methodology for estimating
subchronlc RfO's Is the same as traditionally employed for chronic
estimates, except that subchronlc data are utilized when available.
In the case of suspected carcinogens, RfD's are not estimated. Instead,
a carcinogenic potency factor, or qi (U.S. EPA, 1980} 1s provided.
These potency estimates are derived for both oral and Inhalation exposures
where possible. In addition, unit risk estimates for air and drinking water
are presented based on Inhalation and oral data, respectively.
Reportable quantities (RQs) based on both chronic toxlclty and
cardnogenlclty are derived. The RQ 1s used to determine the quantity of a
hazardous substance for which notification Is required In the event of a
release as specified under the Comprehensive Environmental Response,
Compensation and Liability Act {CERCLA). These two RQs (chronic toxlclty
and carclnogenldty) represent two of six scores developed (the remaining
four reflect IgnltablHty, reactivity, aquatic toxlclty, and acute mammalian
toxlclty). Chemical-specific RQ's reflect the lowest of these six primary
criteria. The methodology for chronic toxldty and cancer based RQs are
defined 1n U.S. EPA, 1984 and 1986b, respectively.
Ill
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EXECUTIVE SUMMARY
Butyl benzyl phthalate Is a colorless, oily, nonvolatile, combustible
liquid with a slight odor (Sax and Lewis, 1987). It Is probably soluble In
most organic solvents and Is only sparingly soluble In water (Howard et al.,
1985). During 1977, between 101 and 510 million pounds of butyl benzyl
phthalate was produced In the United States at two locations of the Monsan-
to Company (TSCAPP, 1989); as of January 1988, the Bridgeport, NJ location
of this company was the sole producer of this chemical (SRI, 1988). Current
production data were not located. Butyl benzyl phthalate 1s produced by
reacting butyl alcohol with phthallc anhydride In the presence of an acid
catalyst and by reacting the resulting ester with benzyl chloride under
neutral aqueous or alcoholic solutions. Butyl benzyl phthalate Is used
almost exclusively as a plastlclzlng agent; more than half goes Into PVC
plastics used as flooring materials. Smaller amounts of butyl benzyl phtha-
late are used In other household products. Butyl benzyl phthalate Is also
used as a plastlclzer for polyvlnyl acetates, which are used as adheslves In
the packaging of food (Gledhlll et al., 1980; IARC, 1982).
In the atmosphere, butyl benzyl phthalate 1s expected to exist both In
the vapor phase and In the partlculate form In the ambient atmosphere
(Cautreels and van Cauwenberghe, 1978; Elsenrelch et al., 1981). Both dry
and wet deposition may be significant atmospheric fate processes for this
compound. Destruction by ozone and by direct photolysis are not expected to
be significant. The destruction of vapor-phase butyl benzyl phthalate by
the reaction with photochemlcally produced hydroxyl radicals Is expected to
be a rapid fate process with an estimated half-life of 1.5 days (Atkinson,
1985); however, It may not be significant for the partlculate form. If
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released to water, the dominant fate processes are expected to be mlcrobUl
degradation and bloconcentratlon In fish and aquatic organisms. Hydrolysis,
volatilization to the atmosphere, oxidation and photolysis are not expected
to be significant fate processes In water (Gledhlll et a!., 1980). If
released to soil, butyl benzyl phthalate can be strongly adsorbed. B1ode-
gradation 1n soil may occur under the proper conditions. Volatilization of
butyl benzyl phthalate from the soil surface to the atmosphere Is not
expected to be significant.
Butyl benzyl phthalate 1s a nonvolatile, organic compound caused by
anthropogenic sources. It enters the environment during Us manufacture,
and also through the processing, use and disposal of plastic products
containing H. In general, the majority of phthalate esters Incorporated
Into plastic products are ultimately deposited 1n landfills (Perwak et al.,
1981).
Data were lacking regarding exposure to butyl benzyl phthalate.
Occupational exposure to butyl benzyl phthalate may occur by Inhalation and
dermal contact during Its manufacture or formulation Into polymers. For the
general population, exposure to butyl benzyl phthalate may be the same as
that believed to be occurring for other phthalate esters, which are also
used as plastlclzers. These routes of exposure Include dermal contact.
Inhalation and Ingestlon through drinking water. It has been detected In
surface water, groundwater, rainwater, Industrial effluent and drinking
water. The general population can be exposed through Ingestlon of contamin-
ated water. Sufficient data were not located to estimate the exposure of
the general population to butyl benzyl phthalate through Inhalation, Inges-
tlon of food and drinking water and dermal contact. Butyl benzyl phthalate
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can also be present In certain foods as a result of migration from plastic
packaging material.
Butyl benzyl phthalate has been assessed for acute toxldty In at least
four freshwater fish species (Buccafusco et al., 1980; EG&G, 1983a,b,c;
Gledhlll et al., 1980; Knle et al., 1983), and three marine fishes (Gledhlll
et al.. 1980; Heltmuller et al., 1981; Ozretlch et al., 1983; Randall et
al.. 1983; Sprlngborn Bionomics Inc., 1984) L05QS were reported at con-
centrations as low as 0.82 mg/i In freshwater (EG&G, 1983a) and 0.51
mg/8. In saltwater (Ozretlch et al., 1983).
Acute toxldty data for fresh and saltwater Invertebrates Indicate that
mysld shrimp, M. bahla, are slightly more sensitive than other forms, but
all LCgo values fell within the range of 0.9-92 mg/i (Analytical Blochem
Labs, 1981; Gledhlll et al.. 1980; LeBlanc, 1980; Monsanto Co., 1983a,b,;
Sprlngborn Life Sciences, 1988; SRI, 1981).
Chronic toxldty of butyl benzyl phthalate has been assessed In fathead
minnows, £. promelas and water fleas, 0. magna (Gledhlll et al., 1980;
Monsanto Co., 1983c; LeBlanc et al., n.d.) and In five species of aquatic
flora (Gledhlll et al., 1980; Monsanto Co., 1983e; Sprlngborn Bionomics
Inc., 1985b). With the exception of one plant species (the bluegreen alga,
Hlcrocystls aeruglnosa). sensitivity was similar between tested algal
species and fell within the narrow range of 0.2-1 rog/l. M. aeruglnosa was
considerably more resistant, with a 96-hour LC5 of 1000 mg/8, and a NOEC
of 560 mg/i (Gledhlll et al., 1980).
Bloaccumulatlon and uptake studies of butyl benzyl phthalate with blue-
gill sunflsh, l^. roacrochlrus. and English sole, P_. vetulus. Indicate that
this chemical bloaccumulates 1n tissues of freshwater or marine fauna but Is
rapidly depurated (Barrows et al., 1980; Monsanto Co., 1983d). A 30-m1nute
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EC,Q of 10 mg/l was reported for the bacterium, £.. putlda (Knle et al.
(1983).
The lack of adequate pertinent data regarding toxldty of butyl benzyl
phthalate prevented the development of freshwater or saltwater criteria by
the method of U.S.EPA/OWRS (1985).
Studies where rats were orally and Intravenously administered
14C-butyl benzyl phthalate (Elgenberg et al., 1986) Indicate that
gastrointestinal absorption Is rapid and virtually complete; however, at
very high doses (2000 mg/kg), the extent of gastrointestinal absorption may
be reduced. Distribution 1s rapid and widespread, but no tissue appears to
preferentially accumulate the compound or Its radioactive metabolites.
Although butyl benzyl phthalate Is llpophlllc, accumulation 1n fat does not
occur, probably because the compound 1s rapidly metabolized.
Following absorption, butyl benzyl phthalate undergoes very rapid
metabolism and excretion (Elgenberg et al., 1986). The principal metabolic
pathway appears to be hydrolysis of the ester linkages followed by conjuga-
tion with glucuronlc acid. Peak levels of monophthalates are measured In
the blood within 5 minutes of an Intravenous dose. The benzyl ester linkage
appears to be more labile than the butyl ester linkage. There Is evidence
that glucuronlde conjugation becomes saturated at higher dosages.
Experiments with bile duct-cannulated rats showed that metabolites of
butyl benzyl phthalate are excreted to a larger extent In the bile than In
the urine (Elgenberg et al., 1986); however, In Intact rats, urinary excre-
tion exceeded fecal excretion. Indicating that substantial reabsorptlon of
biliary excretion products occurs. Excretion Is very rapid following Intra-
venous or oral treatment. An overall half-life of =6 hours was estimated
for removal of butyl benzyl phthalate and the monophthalate esters from all
tissues.
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An acute toxlclty study Indicated that the testes and accessory sex
organs appear to be Important target organs of butyl benzyl phthalate toxlc-
Uy (Agarwal et al., 1985). Exposure of male F344 rats to diets containing
2.5 or 5.0% butyl benzyl phthalate for 14 days resulted In decreased weights
of testes, epldldymus, seminal vesicle and thymus and hlstopathologlcal
evidence of a dose-dependent atrophy of the testes, prostate and seminal
vesicles {Agarwal et al., 1985). Atrophy of the thymus and decreased body
weight were observed only at the 5.0% level. Bone marrow cellularlty was
reduced at the 2.5 and 5.0% levels.
Testlcular degeneration was observed In male F344 rats fed a diet
containing 25,000 ppm butyl benzyl phthalate for 91 days (NTP, 1982). Mice
fed a similar diet did not exhibit signs of testlcular degeneration.
Atrophy of the seminiferous tubules of the testicles and aspermla were seen
In rats fed a 2.5% diet for 26 weeks (NTP, 1985). The kidneys of 6/15 rats
on the 2.5% diet exhibited areas of atrophy. In an unpublished 90-day
toxlclty study (Honsanto, 1972), an Increase In liver weight was observed In
rats fed diets containing 1.0. 1.5 or 2.0% butyl benzyl phthalate. No
adverse effects were observed among dogs exposed to similar doses.
The male rat appears to be more sensitive to butyl benzyl phthalate
toxlclty than female rats and male and female mice (NTP, 1982). Groups of 50
males fed diets containing 6000 or 12,000 ppm butyl benzyl phthalate experi-
enced high mortality within 28 weeks. Internal hemorrhaglng was the sus-
pected cause of the mortality. Mortality was not seen In female rats or
male and female mice after 103 weeks exposure to these diets.
Female rats fed a diet containing butyl benzyl phthalate at a con-
centration of 12,000 ppm demonstrated a significantly Increased Incidence of
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leukemia or lymphoma (NTP, 1982); however, a high Incidence of tumors In
control rats was noted (Kluwe et al., 1982). There was no evidence of
cardnogenlcHy In mice. Evidence suggests that butyl benzyl phthalate 1s
not mutagenlc (see Table 6-3) .
Butyl benzyl phthalate was assigned to U.S. EPA Group C, Possible Human
Carcinogen, as has been done In previous evaluations (U.S. EPA, 1986c,
1987a,b,c). Data were Inadequate for quantitative estimation of cancer
potency. The chemical was administratively assigned to Potency Group 2,
which resulted 1n a LOW hazard ranking and an RQ based on cardnogenlclty of
100. The NTP (1989) has scheduled butyl benzyl phthalate for additional
testing 1n rats by oral administration.
An RfD for subchronlc oral exposure of 2 mg/kg/day was derived by
applying an uncertainty factor of 100 to the NOEL of 159 mg/kg/day for
elevated liver weight, hematologlcal and testlcular effects In the 26-week
dietary study using male rats by NTP (1985). Application of an uncertainty
factor of 1000 allowed derivation of an RfD of 0.2 mg/kg/day for chronic
oral exposure. An RQ of 1000 for chronic (noncancer) toxldty was based on
early mortality In male rats 1n the 103-week study by NTP (1982).
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TABLE OF CONTENTS
Page
1. INTRODUCTION 1
1.1. STRUCTURE AND CAS NUMBER 1
1.2. CHEMICAL AND PHYSICAL PROPERTIES 1
1.3. PRODUCTION DATA 2
1.4. USE DATA 2
1.5. SUMMARY 3
2. ENVIRONMENTAL FATE AND TRANSPORT 4
2.1. AIR 4
2.1.1. Reaction with Hydroxyl Radicals 4
2.1.2. Reaction with Ozone 4
2.1.3. Photolysis 4
2.1.4. Physical Removal Processes 5
2.2. WATER 5
2.2.1. Hydrolysis 5
2.2.2. Oxidation 5
2.2.3. Photolysis 5
2.2.4. Mlcroblal Degradation 6
2.2.5. 81oconcentrat1on 7
2.2.6. Adsorption 7
2.2.7. Volatilization 8
2.3. SOIL 8
2.3.1. Mlcroblal Degradation 8
2.3.2. Adsorption 8
2.3.3. Volatilization 9
2.4. SUMMARY 9
3. EXPOSURE 11
3.1. WATER 12
3.2. FOOD 14
3.3. INHALATION 14
3.4. DERMAL 14
3.5. OTHER 15
3.6. SUMMARY 15
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TABLE OF CONTENTS (cont.)
Page
4. ENVIRONMENTAL TOXICOLOGY 16
4.1. AQUATIC TOXICOLOGY 16
4.1.1. Acute Toxic Effects on Fauna 16
4.1.2. Chronic Effects on Fauna 16
4.1.3. Effects on Flora 22
4.1.4. Effects of Bacteria 22
4.2. TERRESTRIAL TOXICOLOGY 22
4.2.1. Effects on Fauna 22
4.2.2. Chronic Effects on Flora 22
4.3. FIELD STUDIES 24
4.4 AQUATIC RISK ASSESSMENT 24
4.5. SUMMARY 27
5. PHARMACOKINETICS 29
5.1. ABSORPTION 29
5.2. DISTRIBUTION 29
5.3. METABOLISM 31
5.4. EXCRETION 32
5.5. SUMMARY 33
6. EFFECTS 35
6.1. SYSTEMIC TOXICITY 35
6.1.1 Inhalation Exposures 35
6.1.2. Oral Exposures 35
6.1.3. Other Relevant Information 39
6.2. CARCINOGENICITY 41
6.2.1. Inhalation 41
6.2.2. Oral 41
6.2.3. Other Relevant Information 43
6.3. NUTAGENICITY 45
6.4. TERATOGENICITY 45
6.5. OTHER REPRODUCTIVE EFFECTS 45
6.6. SUMMARY 46
7. EXISTING GUIDELINES AND STANDARDS 48
7.1. HUMAN 48
7.2. AQUATIC 48
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TABLE OF CONTENTS (cont.)
Page
8. RISK ASSESSMENT 49
8.1. CARCINOGENICITY 49
8.1.1. Inhalation 49
8.1.2. Oral 49
8.1.3. Other Routes 49
8.1.4. Weight of Evidence 50
8.1.5. Quantitative Risk Assessment 50
8.2. SYSTEMIC TOXICITY 50
8.2.1. Inhalation Exposure 50
8.2.2. Oral Exposure 51
9. REPORTABLE QUANTITIES 54
9.1. BASED ON SYSTEMIC TOXICITY 54
9.2. BASED ON CARCINOGENICITY 56
10. REFERENCES 60
APPENDIX A A-l
APPENDIX B B-l
APPENDIX C C-l
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LIST OF TABLES
No. Title Page
4-1 Acute ToxIcUy of Butyl Benzyl Phthalate to Aquatic Fauna.. 17
4-2 Acute Toxlclty of Butyl Benzyl Phthalate to Aquatic Flora.. 23
5-1 Percent of Radioactive Dose 1n Tissues or Excreta In
Hale F344 Rats Given a Single Intravenous Dose of Ring
Labeled "C-Butyl Benzyl Phthalate 30
6-1 Oral LD50 Values for Butyl Benzyl Phthalate 40
6-2 Hematopoletlc Neoplasms In F344/N Rats and B6C3F1 Mice Fed
n-Butyl Benzyl Phthalate 1n the Diet for 103 Weeks 42
6-3 Genotoxlclty Summary Table for Butyl Benzyl Phthalate 44
9-1 Toxlclty Summary for Butyl Benzyl Phthalate 55
9-2 Composite Scores for Butyl Benzyl Phthalate 57
9-3 Butyl Benzyl Phthalate: Minimum Effective Dose (MED) and
Reportable Quantity (RQ) 58
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LIST OF ABBREVIATIONS
ADI Alcohol dehydrogenase
BCF Bloconcentratlon factor
bw Body weight
CAS Chemical Abstract Service
CS Composite score
ECgg Concentration effective to 50% of recipients (and all other sub-
scripted concentration levels)
FEL Frank effect level
FSH Follicle stimulating hormone
GMAV Genus mean acute values
GHCV Genus mean chronic values
Koc Soil sorptlon coefficient
Kow Octanol/water partition coefficient
LC5Q Concentration lethal to 50% of recipients
1059 Dose lethal to 50% of recipients
LH Lute1n1z1ng hormone
LOAEL Lowest-observed-adverse-effect level
MATC Maximum allowable toxicant concentration
MCH Mean cell hemoglobin
MCV Mean cell volume
MCHC Mean cell hemoglobin concentration
MEO Minimum effective dose
NOEC No-observed-effect concentration
NOEL No-observed-effect level
ppb Parts per billion
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LIST OF ABBREVIATIONS (cont.)
ppm Parts per million
ppt Parts per trillion
PVC Polyvlnyl chloride
RfO Reference dose
RQ Reportable quantity
RV(j Dose-rating value
RVe Effect-rating value
SCAS Semi-continuous activated sludge
SE Standards error
UV Ultraviolet
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1. INTRODUCTION
1.1. STRUCTURE AND CAS NUMBER
Butyl benzyl phthalate 1s also known by the synonyms benzyl butyl phtha-
late; benzyl n-butyl phthalate; l,2-benzened1carboxcy!1c add, butyl phenyl-
methyl ester; by the tradenames Santldzer 160, Palatlnol BB and S1col 160;
and the acronym BBP (Chemline, 1989; SANSS, 1989). The structure, CAS
Registry number, empirical formula and molecular weight are as follows:
CAS registry number: 85-68-7
Empirical formula: c-|gH2o04
Molecular weight: 312.36
1.2. CHEMICAL AND PHYSICAL PROPERTIES
Butyl benzyl phthalate Is a clear, oily, combustible liquid with a
slight odor (Sax and Lewis, 1967). It Is sparingly soluble In water (Howard
et al., 1985). Selected physical properties of butyl benzyl phthalate are
given below:
Melting point:
Boiling point:
Density (25"C):
Vapor pressure (25°C):
Water solubility (25°C):
-35°C
377°C
1.119
8.25X10'6 mm Hg
2.69 mg/l
IARC, 1982
IARC, 1982
Dean, 198S
Howard et al., 1985
Howard et al.. 1985
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Log Kow: 5.50 Howard et al.. 1985
Conversion factor {25°C): 1 mg/m3 = 0.0783 ppm;
1 ppm = 12.76 mg/m3
1.3. PRODUCTION DATA
Data from the U.S. EPA TSCA production file (TSCAPP, 1989) Indicate that
during 1977, between 101 and 510 million pounds of butyl benzyl phthalate
was produced In the United States at two locations of the Monsanto Company;
as of January, 1998, the Bridgeport, NJ location of this company was the
sole producer of this chemical In the United States (SRI, 1988). More
current production data were not located.
Butyl benzyl phthalate Is produced by a two-step reaction Involving the
Initial formation of the mono butyl ester of phthallc acid by the reaction
of butyl alcohol with phthallc anhydride using an acid catalyst. The mono
ester Is reacted with benzylchlorlde under neutral aqueous or alcoholic
solutions to form the desired product (1ARC, 1982).
1.4. USE DATA
Butyl benzyl phthalate Is used almost exclusively as a plastlclzlng
agent. The major end use (>50%) for butyl benzyl phthalate Is 1n the
synthesis of PVC used as flooring materials. Smaller amounts of butyl
benzyl phthalate are used In other household products. Butyl benzyl
phthalate Is also used as a plastlclzer for polyvlnyl acetate emulsions,
which are used as adheslves In the food packaging Industry. Other polymers
that can be plastlclzed using butyl benzyl phthalate Include acrylic resins,
ethyl cellulose, polyvlnyl formal and polyvlnyl butyral (Gledhlll et al.,
1980; IARC, 1982).
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1.5. SUHMARY
Butyl benzyl phthalate Is a colorless, oily, nonvolatile, combustible
liquid wHh a slight odor (Sax and Lewis, 1987). It Is probably soluble In
most organic solvents and Is only sparingly soluble 1n water (Howard et al.,
1985). During 1977, between 101 and 510 million pounds of butyl benzyl
phthalate was produced 1n the United States at two locations of the Monsan-
to Company (TSCAPP, 1989); as of January 1988, the Bridgeport, NO location
of this company was the sole producer of this chemical (SRI, 1988). Current
production data were not located. Butyl benzyl phthalate Is produced by
reacting butyl alcohol with phthalate anhydride In the presence of an acid
catalyst and by reacting the resulting ester with benzyl chloride under
neutral aqueous or alcoholic solutions. Butyl benzyl phthalate Is used
almost exclusively as a plastlclzlng agent; more than half goes Into PVC
plastics used as flooring materials. Smaller amounts of butyl benzyl phtha-
late are used In other household products. Butyl benzyl phthalate Is also
used as a plastlclzer for polyvlnyl acetates, which are used as adheslves In
the packaging of food (Gledhlll et al., 1980; IARC, 1982).
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2. ENVIRONMENTAL FATE AND TRANSPORT
2.1. AIR
Based on the known vapor pressure, 8.25xlO~» mm Hg at 25°C (Howard et
al., 1985), butyl benzyl phthalate Is expected to exist both In the partlcu-
late form and In the vapor phase In the ambient atmosphere (Elsenrelch et
al.. 1981). In urban air samples over Belgium, 1t was found In both of
these physical states (Cautreels and van Cauwenberghe, 1978).
2.1.1. Reaction with Hydroxyl Radicals. Using the method of Atkinson
(1985), an estimated rate constant for the vapor-phase reaction of butyl
benzyl phthalate with photochemlcally produced hydroxyl radicals Is
l.OSxlO11 cm3/molecule-sec. If an average atmospheric hydroxyl radical
concentration 1s 5x10* molecule/cm3, the half-life for this reaction Is
1.5 days. Since butyl benzyl phthalate will also exist In the partlculate
phase In the ambient atmosphere, and the OH radical reaction 1s expected to
be slower with the partlculate form, the actual rate of destruction of butyl
benzyl phthalate through this reaction 1s expected to be slower.
2.1.2. Reaction with Ozone. Butyl benzyl phthalate Is not expected to
react with ozone 1n the ambient atmosphere (Atkinson, 1985).
2.1.3. Photolysis. Since butyl benzyl phthalate adsorbs UV light In the
environmentally significant range of >290 nm, It Is a candidate for direct
photochemical degradation; however, exposure of aqueous solutions of this
compound In sealed quartz tubes with natural sunlight showed that photochem-
ical reaction 1s not significant (Gledhlll et al., 1980). Therefore, photo-
chemical reaction In the atmosphere may also be Insignificant compared with
other atmospheric removal processes.
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2.1.4. Physical Removal Processes. Butyl benzyl phthalate was found In
the rain-dissolved phase in 7/7 rainfalls in Portland, OR, but not In gas
phase ambient air samples taken at the same time (Ligocki et al., 1985).
These data suggest that rain washout may be a significant process. It was
found in participate matter in indoor air samples, but not In concurrent
samples obtained outdoors (Weschler, 1984). The known ability of phthalate
esters to adsorb to particulate matter (Weschler, 1984), combined with its
expected occurrence of butyl benzyl phthalate partially in the condensed
form in the ambient atmosphere (see Section 2.1), suggests that dry deposi-
tion may occur for particulate (both adsorbed and condensed) butyl benzyl
phthalate.
2.2. WATER
2.2.1. Hydrolysis. Pertinent data regarding the hydrolysis of butyl
benzyl phthalate were lacking in the literature cited in Appendix A;
however, from their dark photolysis experiment, Gledhill et al. (1980)
observed <57. chemical degradation, which included hydrolysis in 28 days.
The authors estimated the half-life for hydrolysis to be >100 days; there-
fore, hydrolysis is not expected to be an important fate process.
2.2.2. Oxidation. Pertinent data regarding chemical oxidation of butyl
benzyl phthalate in water were not located in the available literature cited
in Appendix A. Based on the dark photolysis experiment of Gledhill et al.
(1980), it is not expected to be a significant process.
2.2.3. Photolysis. Since butyl benzyl phthalate adsorbs UV light 1n the
environmentally significant range of >290 nm, it has the potential for
direct photochemical degradation. Gledhill et al. (1980) exposed butyl
benzyl phthalate in sealed quartz tubes to sunlight for 28 days and observed
6203H -5- 07/24/89
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<5% photodegradation. They estimated the photolysis half-life for butyl
benzyl phthalate to be >100 days; therefore, this process is not expected to
be significant.
2.2.4. Mkrobial Degradation. At an Initial concentration of 1 ppm, butyl
benzyl phthalate was found to undergo *99% primary aerobic degradation in
7 days in a river die-away study (Saeger and Tucker, 1973). Other authors
(Gledhill et al., 1980) have shown that between >95 and 100% primary degra-
dation of this compound will occur in 7-9 days in natural river and lake
water. The half-life of primary biodegradatlon In natural waters was esti-
mated to be 2-4 days; however, only 51-65% of the compound underwent
complete mineralization in lake water in 28 days (Gledhill et al., 1980).
Between 92 and 99% primary degradation was also observed in 1 day in a
screening test using a SCAS reactor (Gledhill et al., 1980; Saeger and
Tucker, 1973). Again, =96% complete mineralization occurred in 28 days
with the SCAS (Gledhill et al., 1980; Saeger and Tucker, 1976). In another
screening study, butyl benzyl phthalate, at an initial concentration of 5
and 10 mg/^, was listed as undergoing 100% aerobic degradation within 7
days using settled domestic wastewater as microbial inoculum (Tabak et al.,
1981). In a shake flask test using an activated inoculum from soil and
sewage microorganisms under aerobic conditions, butyl benzyl phthalate
underwent 77.7% primary biodegradation and 43% complete mineralization in 28
days after a short initial acclimation period (Sugatt et al., 1984).
Using sludge from municipal digestors of two different treatment plants,
butyl benzyl phthalate underwent slow anaerobic degradation in one experi-
ment and no observable degradation in the other. After 4 weeks, a 24%
theoretical methane production was measured in the former case, as opposed
6203H -6- 07/24/89
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to no significant methane production in an 8-week experiment in the latter
case (Horowitz et al., 1982). In another anaerobic screening test'using a
digester sewage sludge inoculum, butyl benzyl phthalate underwent between 30
and 75% of the theoretical methane production in 8 weeks with sludge from a
secondary digester and 75% methane production in 4 weeks with sludge from a
primary digester (Shelton and Tiedje, 1984). A related study showed that 20
|ig/m^ butyl benzyl phthalate underwent 90% mineralization to CH«
within 40 days with primary anaerobic sludge from a sewage treatment plant
(Shelton et al., 1984).
2.2.5. Bioconcentration. Based on the Kow value of 5.50 (Howard et al.,
1985), a BCF of 8900 can be calculated using the regression equation log
BCF - 0.76 log Kow - 0.23 (Bysshe, 1982). A BCF of 663 was observed for
butyl benzyl in bluegills exposed to 9.73 ppb "C-labelled compound for 21
days (Gledhill et al., 1980). From the Kow, Gledhill et al. (1980)
calculated a BCF of 510 for butyl benzyl phthalate. Therefore, this com-
pound has a moderate to significant bloaccumulation potential in aquatic
organisms.
2.2.6. Adsorption. The K0w of butyl benzyl phthalate (concentration in
soil to concentration in water) containing 1.2-3.4% organic matter ranged
from 68-350 (Gledhill et al., 1980). The experimental Koc for butyl
benzyl phthalate in a compost soil was 17,000 (Section 2.3.2). These values
suggest that butyl benzyl phthalate should be sorbed at least moderately to
suspended particles and sediment, yet, butyl benzyl phthalate was found in
the sediment of the inner harbor navigation channel of Lake Pontchartrain,
LA, at an average concentration of 0.8 ppb (dry weight) (McFall et al.,
1985a); water concentrations in the area ranged from 0.1-0.3 ppb (McFall et
6203H -7- 07/24/89
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al., 1985b). It was found In 16/16 participate samples obtained In the
Hersey Estuary, United Kingdom, at concentrations ranging from 3.4-18 ng/g.
These figures represent 27.7-259% of the concentration of butyl benzyl
phthalate measured 1n the water (Preston and Al-Omran, 1986). These data
suggest that adsorption to sediment and suspended organic matter may be
different from adsorption to soil.
2.2.7. Volatilization. Butyl benzyl phthalate was listed as undergoing an
estimated zero percent removal during the air stripping process at a sewage
treatment plant (Petrasek et al., 1983). Using the bond method of Hlne and
Mookerjee (1975), a Henry's Law constant of 2.87xlO"8 l-atm/mol at 25°C
1s obtained. Using this value, the estimated volatilization half-life for a
model river 1 m deep, flowing at 1 m/sec, with wind velocity of 3 m/sec 1s
2254 days (Thomas, 1982). Volatilization of butyl benzyl phthalate from
water to the atmosphere Is therefore not expected to be a significant fate
process.
2.3. SOIL
2.3.1. Mlcroblal Degradation. In a biological soil reactor, butyl benzyl
phthalate, added as a component of a wood preserving sludge, underwent aero-
bic blodegradatlon. At an Initial loading of 117 mg/kg, 24 mg/kg remained
after 135 days, corresponding to a half-life of 59.2 days. At higher
loading concentrations, the half-life Increased (Klncannon and Lin, 1985).
In a field study where butyl benzyl phthalate had entered soil from the
application of spent treatment plant sludge, this compound was listed by the
author as not undergoing blodegradatlon (DemirjIan et al., 1984).
2.3.2. Adsorption. An experimental K value of 17,000 was obtained for
butyl benzyl phthalate using a composite soil from Broome County, NY (1.89%
6203H -8- 10/17/89
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organic carbon) (Russell and McDuffle, 1986). This value suggests that
butyl benzyl phthalate will be Immobile In soil (Swann et al., 1983). In a
field study, butyl benzyl phthalate added as a component of spent treatment
_2
plant sludge (application rate equal to 1.51x10 kg/ha) was soon found In
the underlying soil (3.51x10 kg/ha). It was also found In underlying
groundwater wells at a concentration ranging from <0.1-4 yg/l (Dem1rj1an
et al., 1984). The presence of butyl benzyl phthalate In these groundwater
samples may be due to the leaching of this plastlclzer from pipes, drainage
tiles, liners, etc., which are all present at the experimental site rather
than the result of spent sewage sludge.
2.3.3. Volatilization. The known vapor pressure, 8. 25x10 ~ mm Hg at
25°C (Howard et al., 1985), suggests that volatilization from the soil
surface to the atmosphere Is not expected to be significant.
2.4. SUMMARY
In the atmosphere, butyl benzyl phthalate Is expected to exist both In
the vapor phase and 1n the partlculate form In the ambient atmosphere
(Cautreels and van Cauwenberghe, 1978; Elsenrelch et al., 1981). Both dry
and wet deposition may be significant atmospheric fate processes for this
compound. Destruction by ozone and by direct photolysis are not expected to
be significant. The destruction of vapor-phase butyl benzyl phthalate by
the reaction with photochemical ly produced hydroxyl radicals 1s expected to
be a rapid fate process with an estimated half-life of 1.5 days (Atkinson,
1985); however, It may not be significant for the partlculate form. If
released to water, the dominant fate processes are expected to be mlcroblal
degradation and bloconcentratlon 1n fish and aquatic organisms. Hydrolysis,
6203H -9- 10/17/89
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volatilization to the atmosphere, oxidation and photolysis are not expected
to be significant fate processes in water (Gledhill et al., 1980). If
released to soil, butyl benzyl phthalate can be strongly adsorbed. Biode-
gradation in soil may occur under the proper conditions. Volatilization of
butyl benzyl phthalate from the soil surface to the atmosphere is not
expected to be significant.
6203H -10- 07/24/89
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3. EXPOSURE
Butyl benzyl phthalate may enter the environment during Us manufacture,
and through the processing, use and disposal of plastic products containing
H. In general, the majority of phthalate esters that are Incorporated Into
plastic products are ultimately deposited In landfills (Perwak et a!., 1981).
The National Occupational Exposure Survey conducted between 1981 and
1983 estimated that 89,644 workers are potentially exposed to butyl benzyl
phthalate (NIOSH, 1984). Occupational exposure may result from Inhalation
or dermal contact during the manufacture of butyl benzyl phthalate or during
Its formulation Into polymers.
Phthalate esters used as plastlclzers can be present 1n concentrations
up to 60% of the total weight of the PVC plastic. The plastldzer Is not
linked by primary chemical bonds to the PVC resin. Rather, It Is locked
Into the structure of Intermeshlng polymer molecules and held by van der
Waals forces. The result Is that the plastlclzer Is easily extracted.
Plastlclzers are responsible for the odor associated with new plastic toys
or flexible sheet that has been contained In a sealed package.
Although the phthalate esters are not soluble or are only very slightly
soluble 1n water, they do migrate Into aqueous solutions placed In contact
with the plastic. Thus Industrial facilities with tank linings, wire and
cable covering, tubing and sheet flooring of PVC are expected to discharge
some phthalate esters 1n their raw waste. In addition to their use as
plastlclzers, phthalate esters are used In lubricating oils and pesticide
carriers. These also can contribute to Industrial discharge of phthalate
esters.
Butyl benzyl phthalate was detected 1n approximately two-thirds of the
subjects studied In the National Human Adipose Tissue Survey (U.S. EPA,
1986a).
6203H -11- 10/17/89
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Exposure to butyl benzyl phthalate by the general population may occur
through Ingest Ion of contaminated waters. Although there Is little Informa-
tion regarding specific exposure to butyl benzyl phthalate, exposure to
phthalate esters by the general population may result from use 1n plastlcl-
zers (Perwak et al., 1981). The resulting routes of exposure may Include
Ingestlon of food contaminated from the use of the chemical 1n packaging,
exposure by the use of plastic medical products, such as tubing and storage
containers containing phthalate esters as a plastldzer, dermal contact with
plastics containing these compounds as plastlclzers and Inhalation of vapors
or partlculates that have volatilized from plastics (Perwak et al., 1981).
3.1. HATER
Butyl benzyl phthalate has been found In surface water, groundwater,
rainwater and wastewater. It 1s not known to be a naturally occurring
compound; It appears to be associated with Industrial activity.
Butyl benzyl phthalate was not detected at the source of the Mississippi
River, Lake Itasca, MM, but was found at a concentration of 34 ppt at a
point 25 miles below where It meets the Ohio river. The compound was found
at 59 ppt, 25 miles below the dty of Memphis, TN. It was not found at the
Intake of the Carrolton Street water Intake In New Orleans (Deleon et al.,
1986). Butyl benzyl phthalate was found 1n the Influent of a sewage treat-
ment plant 1n Philadelphia serving both Industrial and residential sources
at a concentration of 40 ppb. The effluent from this plant had a measured
concentration of 100 ppb. Two miles upstream In the Delaware River, the
concentration was 0.6 ppb. The concentration 2 miles further upstream from
the plant was 0.3 ppb. The concentration of butyl benzyl phthalate 1n the
Intake water of Phlladephla's Torresdale water treatment plant was 0.3 ppb
and the concentration In the effluent from this plant was 0.1 ppb (HHes,
1979; Sheldon and HUes, 1979).
6203H -12- 10/17/89
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Butyl benzyl phthalate was found 1n 9/31 sampling sites taken from
surface waters throughout the United States during 1980-1982 at concentra-
tions <0.9 ng/i (Michael et al., 1984). It was found In 16/16 water
samples obtained from the Mersey Estuary, United Kingdom, at concentrations
ranging from 5.8-28.5 ng/l (Preston and Al-Omran, 1986). It was found In
5/11 summer samples and 11/11 winter samples taken from the Delaware River
during 1976-77 at concentrations of 0.4-1 ppb and 0.3 ppb, respectively
(Sheldon and H1tes, 1978). It was also Identified In the River Lee, United
Kingdom, at concentrations >1 pg/fc (Waggott, 1981).
In a recent review of the literature on landfill sites, H was detected,
but not quantified, In the leachate from 58 municipal landfills. (Brown and
Donnelly, 1988). Butyl benzyl phthalate has been Identified In the leachate
from a sanitary landfill In Barcelona, Spain (Albalges et al., 1986).
Butyl benzyl phthalate has been quantitatively detected 1n drinking
water wells In New York State at a concentration of 38 pg/a, (Burmaster,
1982; Kopfler et al., 1977). It has also been detected In drinking water
from New Orleans at concentrations ranging from 0.08-1.8 vq/i (Keith et
al., 1976; Kool et al., 1982).
Butyl benzyl phthalate was Identified In 1454 of 30 water samples taken
from Industrial effluent, water treatment works and fjords In Norway at
concentrations >1 ng/l (Sporstoel et al., 1985). An analysis of the
STORE! data base shows that butyl benzyl phthalate was found in 7.2% of 1337
effluent samples at a median concentration of <6 yg/l and 3.0% of 1220
surface water samples at a median concentration of <10 vg/l (Staples et
al., 1985).
It was found In 1/86 samples In the national urban runoff program, at a
concentration of 10 vg/8, (Cole et al., 1984). Butyl benzyl phthalate
6203H -13- 10/17/89
-------
was not found In the sludge of three publicly owned water treatment plants;
however, It was found 1n two of four combined sludges at different plants at
concentrations ranging from 1161-3975 ^g/l (Feller et al., 1980). Butyl
benzyl phthalate was found In the rainwater In 7/7 rainfalls In Portland,
OR, In 1984 at concentrations ranging from 20-74 ng/st (Llgock! et al.,
1985). It has been found In sediment samples In 6/31 sites at concentra-
tions <1.2 v»g/g dry weight (Michael et al.. 1984).
3.2. FOOD
Pertinent data regarding exposure to butyl benzyl phthalate In food were
not located In the available literature cited In Appendix A; however, butyl
benzyl phthalate Is used as a plastldzer for adheslves approved for food
packaging. The potential for the chemical to migrate from the packaging
material Into food Is high.
3.3. INHALATION
Butyl benzyl phthalate has been Identified 1n the participate form and
In the gas phase of urban air samples In Belgium (Cautreels and van Cauwen-
berghe, 1978). Butyl benzyl phthalate was found on Indoor participate
matter at a concentration of 1-20 ng/m3 but not on outdoor partlculates
obtained concurrently (Weschler, 1984). It was also Identified 1n the fly
ash from municipal Incinerators (Tong et al., 1984). Data are not suffi-
cient to predict Inhalation exposure of the general population to this
compound.
3.4. DERMAL
Pertinent data regarding dermal exposure to butyl benzyl phthalate were
not located In the available literature cited In Appendix A.
6203H -14- 10/17/89
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3.5. OTHER
Pertinent data regarding other sources of exposure to butyl benzyl
phthalate were not located In the available literature cited In Appendix A.
3.6. SUMMARY
Butyl benzyl phthalate Is a nonvolatile, organic compound produced by
anthropogenic sources. It enters the environment during Its manufacture,
and also through the processing, use and disposal of plastic products
containing H. In general, the majority of phthalate esters Incorporated
Into plastic products are ultimately deposited In landfills (Perwak et al..
1981).
Data were lacking regarding exposure to butyl benzyl phthalate. Occupa-
tional exposure to butyl benzyl phthalate may occur by Inhalation and dermal
contact during Us manufacture or formulation Into polymers. For the
general population, exposure to butyl benzyl phthalate may be the same as
that believed to be occurring for other phthalate esters, which are also
used as plastlclzers. These routes of exposure Include dermal contact,
Inhalation and Ingestlon through drinking water. It has been detected 1n
surface water, groundwater, rainwater, Industrial effluent and drinking
water. The general population can be exposed through Ingestlon of contamin-
ated water. Sufficient data were not located to estimate the exposure of
the general population to butyl benzyl phthalate through Inhalation, Inges-
tlon of food and drinking water and dermal contact. Butyl benzyl phthalate
can also be present In certain foods as a result of migration from plastic
packaging material.
6203H -15- 10/17/89
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4. ENVIRONMENTAL TOXICOLOGY
4.1 AQUATIC TOXICOLOGY
4.1.1. Acute Toxic Effects on Fauna. Acute toxldty Information regarding
butyl benzyl phthalate Is available for at least four freshwater Inverte-
brates, four freshwater fish, a saltwater Invertebrate and three marine fish
(Table 4-1). The 48-hour LC™ ranged from 1.64-92 mg/l for freshwater
Invertebrates, with the midge, Chlronomus tentans, the most sensitive
species. For freshwater fish, similar LC5Qs have been reported, ranging
from 0.82-43 mg/1. The toxlclty of butyl benzyl phthalate Increased
slightly In fathead minnows, Plmephales promelas. when hardness (expressed
as CaC03 content) Increased from 40-160 mg/l (96-hour LC5Q=2.1 and 5.3
mg/l, respectively) (Gledhlll et al., 1980).
Sensitivity to butyl benzyl phthalate among saltwater forms was Indica-
ted by LC5Qs ranging from 0.51-440 mg/l. The 96-hour LC<. of 440
mg/l (Heltmuller et al., 1981) for the sheepshead minnow, Cyprlnodon
varleqatus. exceeds the solubility of *2.69 mg/l (Howard et al., 1985)
for butyl benzyl phthalate and may therefore be Inaccurate. All other
LC,-n values for saltwater species fell within the narrow range of 0.51-3.0
mg/l.
4.1.2. Chronic Effects on Fauna.
4.1.2.1. TOXICITY -- The chronic toxlclty of butyl benzyl phthalate
has been Investigated In Daphnla magna and Plmephales promelas. Chronic
exposure for <21 days to concentrations of 1.4 and 2.4 mg/l butyl benzyl
phthalate resulted In significantly lower survival and reproduction rates
6203H -16- 08/08/89
-------
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