NTP-CERHR Monograph on the 

Potential Human Reproductive and 

Developmental Effects of

1-Bromopropane

October 2003 NIH Publication No. 04-4479

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iii

Table of Contents

Preface .............................................................................................................................................v

Introduction.................................................................................................................................... vi

NTP Brief on 1-Bromopropane .......................................................................................................1

References........................................................................................................................................4

Appendix I. NTP-CERHR Bromopropanes Expert Panel 

Preface ..............................................................................................................................I-1

Expert Panel......................................................................................................................I-2

Appendix II. Expert Panel Report on 1-Bromopropane .............................................................. II-i

Table of Contents........................................................................................................... II-iii

Abbreviations...................................................................................................................II-v

List of Tables................................................................................................................ II-viii

List of Figures................................................................................................................ II-ix

Preface .............................................................................................................................II-x

A Report of the Bromopropanes Expert Panel .............................................................. II-xi

Chemistry, Usage and Exposure ......................................................................................II-1

General Toxicological and Biological Effects.................................................................II-7

Developmental Toxicity Data........................................................................................II-28

Reproductive Toxicity ...................................................................................................II-36

Summaries, Conclusions and Critical Data Needs .......................................................II-47

References.....................................................................................................................II-51

Appendix III. Public Comments on 1-Bromopropane Expert Panel Report

EnviroTech International, Inc......................................................................................... III-1

United States Environmental Protection Agency........................................................... III-7
iv

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v

The National Toxicology Program (NTP) 

established the NTP Center for the Evaluation 

of Risks to Human Reproduction (CERHR) 

in 1998. The CERHR is a publicly accessible 

resource for information about adverse reproductive and/or developmental health effects 

associated with exposure to environmental 

and/or occupational chemicals. The CERHR 

is located at the National Institute of Environmental Health Sciences (NIEHS) of the 

National Institutes of Health and Dr. Michael 

Shelby is the director.1

The CERHR broadly solicits nominations of 

chemicals for evaluation from the public and 

private sectors. The CERHR follows a formal 

process for review and evaluation of nominated 

chemicals that includes multiple opportunities 

for public comment. Chemicals are selected for 

evaluation based upon several factors including 

the following: 

• potential for human exposure from use 

and occurrence in the environment.

• extent of public concern.

• production volume.

• availability of scientific evidence for 

reproductive and/or developmental toxicity. 

The CERHR convenes a scientific expert 

panel that meets in a public forum to review, 

discuss, and evaluate the scientific literature 

on the selected chemical. Public comment 

is invited prior to and during the meeting. 

The expert panel produces a report on the 

chemical’s reproductive and developmental 

toxicities and provides its opinion of the degree 

to which exposure to the chemical is hazardous to humans. The panel also identifies areas 

of uncertainty and where additional data are 

needed. The CERHR expert panels use explicit 

guidelines to evaluate the scientific literature 

and prepare the expert panel reports. Expert 

panel reports are made public and comments 

are solicited. 

Next, the CERHR prepares the NTP-CERHR 

monograph. The NTP-CERHR monograph 

includes the NTP brief on the chemical evaluated, the expert panel report, and all public 

comments on that report. The goal of the NTP 

brief is to provide the public, as well as government health, regulatory, and research agencies, 

with the NTP’s interpretation of the potential for 

the chemical to adversely affect human reproductive health or children’s health. The NTPCERHR monograph is made publicly available 

electronically on the CERHR web site and in 

hard copy or CD-ROM from the CERHR.

Preface

1 Information about the CERHR is available on the 

web at <http://cerhr.niehs.nih.gov> or by contacting the director:

NIEHS, P.O. Box 12233, MD EC-32,

Research Triangle Park, NC 27709 

919-541-3455 [phone] 

919-316-4511 [fax]

shelby@niehs.nih.gov [email] 

Information about the NTP is available on the web 

at <http://ntp-server.niehs.nih.gov> or by contacting the NTP Office of Liaison and Scientific Review at the NIEHS:

liaison@starbase.niehs.nih.gov [email]

919-541-0530 [phone]
vi

In 1998, the CERHR Core Committee, an advisory committee composed of representatives 

from NTP member agencies, recommended 

1-bromopropane and 2-bromopropane for expert panel review. 1-Bromopropane was selected for evaluation because it is produced in 

large volumes, there are documented cases of 

occupational exposures, and it exhibits reproductive toxicity in rodent studies.

1-Bromopropane is used as a solvent for fats, 

waxes, or resins and in spray adhesives, in precision cleaning, and as a degreaser. It also is used 

as an intermediate in the synthesis of pharmaceuticals, insecticides, flavors, and fragrances. 

Based on documented evidence of worker exposure and published evidence of reproductive 

and developmental toxicity in rodents, there is 

concern about the safety of 1-bromopropane. 

As part of the evaluation of 1-bromopropane, 

the CERHR convened a panel of scientific 

experts (Appendix I) to review, discuss, and 

evaluate the scientific evidence on the potential reproductive and developmental toxicities 

of the chemical. A public meeting of the Bromopropanes Expert Panel was held on December 5-7, 2001 in Herndon, VA. The CERHR 

received numerous public comments throughout the evaluation process. 

The NTP has prepared an NTP-CERHR monograph for 1-bromopropane. This monograph includes the NTP brief on 1-bromopropane, a list 

of the expert panel members (Appendix I), the 

expert panel’s report on 1-bromopropane (Appendix II), and all public comments received 

on the expert panel report on 1-bromopropane 

(Appendix III). The NTP-CERHR monograph 

is intended to serve as a single, collective source 

of information on the potential for 1-bromopropane to adversely affect human reproduction or 

development. Those interested in reading this 

monograph may include individuals, members 

of public interest groups, and staff of health and 

regulatory agencies. 

The NTP brief included within this monograph 

presents the NTP’s interpretation of the potential for exposure to 1-bromopropane to cause 

adverse reproductive or developmental effects 

in people. The NTP brief is intended to provide 

clear, balanced, scientifically sound information. It is based on the expert panel report, the 

public comments on that report, and additional 

scientific information available since the expert 

panel meeting. 

Introduction
1

NTP Brief

What is 1-Bromopropane?

1-Bromopropane (1-BP) is a bromine-containing hydrocarbon with the chemical formula 

C3H7Br and the structure shown in Figure 1. 

Most of the 1-BP manufactured is used as a 

solvent for fats, waxes, or resins. Some is used 

to synthesize pharmaceuticals, insecticides, flavors and fragrances. 1-BP is also used in some 

spray adhesives and in cleaning metal and electronic components. 

1-BP is produced by reacting n-propyl alcohol 

with hydrogen bromide and then removing water that is formed. 1-BP also can be produced 

by dehydration of propanol with bromine or 

hydrogen bromide in the presence of a sulfur 

catalyst. Recent information indicates that 

in the year 2000, approximately 1.5 million 

pounds of 1-BP were produced in the United 

States and 2.8 million pounds were imported. 

It is worth noting that 1-BP is typically contaminated with small amounts of 2-bromopropane 

(2-BP). 2-BP is the subject of a separate NTPCERHR Monograph. The expert panel report 

cited OSHA-determined contamination levels 

of 0.1 to 0.2%. Industry comments on the 

1-BP expert panel report state that improved 

manufacturing methods have reduced the 2-BP 

contamination level to 0.05% or less.

1-BP is currently under review by the EPA as 

a possible replacement for ozone-depleting 

substances such as CFC-113 and methyl chloroform in non-aerosol solvent cleaning of metals 

and electronics. It is also being considered as a 

replacement for methyl chloroform, CFC-113, 

and HCFC-141b in aerosol solvents and adhesive applications.

Are People Exposed to 1-BP?*

Yes. While no information was available to 

the panel on exposure of the general public to 

1-BP, information was available on exposures 

in the workplace. 

The most complete information available on 

current 1-BP exposures in the U.S. is based on 

occupational surveys that show a wide range of 

exposure levels in the workplace. 1-BP levels 

in worker breathing zones were 18-381 ppm 

(parts per million in the air) in plants where 

spray adhesive containing 1-BP was used, 

and 0.04 to 0.63 ppm where 1-BP was used 

as a vapor degreaser. It is likely that workers 

were exposed to 1-BP through inhalation and 

dermal contact. However, no measurements on 

the contribution of dermal exposure to the total 

dose have been conducted to date. Additionally, 

these few surveys should not be considered to 

represent a cross-section of occupational exposures across the U.S.

Recently, additional case reports and biological 

monitoring studies have become available. One 

survey, where 1-BP was used as a solvent with 

a glue spray gun, showed that the daily time 

weighted average (TWA) air concentrations 

ranged from 60 to 261 ppm (Ichihara et al., 

2002). Another study, where workers cleaned 

and painted metal surfaces with preparations 

containing 1-BP and other solvents, showed a 

geometric mean exposure of 1.42 ppm with a 

maximal exposure of 27.8 ppm (Kawai et al., 

2001). These exposure levels are consistent 

with the surveys described above. 

Occupational exposure limits have not been 

NTP Brief on 1-Bromopropane

Br

Figure 1. Chemical structure of 1-BP

* Answers to this and subsequent questions 

may be: Yes, Probably, Possibly, Probably 

Not, No or Unknown
2

NTP Brief

established at this time.

The lack of information on levels of 1-BP in 

the general environment prohibits development 

of an estimated exposure level for the general 

U.S. population. The occupational exposure 

data discussed above are too limited to be considered an accurate representation of occupational exposures nationwide.

Can 1-BP Affect Human Development or 

Reproduction?

Possibly. Although there is no direct evidence 

that exposure of people to 1-BP adversely affects 

reproduction or development, studies reviewed 

by the expert panel and more recent studies in 

rats show that exposure to 1-BP can adversely 

affect reproduction and development (Fig. 2). 

Scientific decisions concerning health risks are 

generally based on what is known as a “weightof-evidence” approach. Recognizing the lack 

of data on 1-BP toxicity in humans, the NTP 

judges the scientific evidence of effects in laboratory animals sufficient to conclude that 1-BP 

may adversely affect human development and 

reproduction if exposures are sufficiently high.

Supporting Evidence 

As presented in the expert panel report (see 

Appendix II for details and literature citations), 

the panel concluded that 1-BP produces reproductive and developmental toxicity in rats. 

The critical study of developmental effects in 

animals showed that when pregnant rats inhaled 

1-BP at concentrations of 500 ppm or greater, 

fetal weights were decreased and incidences of 

skeletal variations were observed. Benchmark 

dose analysis of the fetal weight data estimated 

a 5% decrease in fetal weight would result from 

exposure to 561 ppm (central estimate with a 

lower 95th confidence limit of 305 ppm).

The critical reproductive toxicity study in animals was a two-generation, inhalation study. It 

showed exposure of rats to 250 ppm or greater 

altered numerous reproductive endpoints in both 

females and males. These included decreased 

prostate weight, decreased sperm motility and 

percent normal sperm in males and decreased 

litter size, decreased numbers of implantation 

sites, increased ovarian follicular cysts, and 

increased estrous cycle length in females. The 

panel determined that no adverse reproductive 

effects were observed at an exposure concentration of 100 ppm.

The expert panel noted that data were not available to permit a comparison of how laboratory 

animals and humans absorb and metabolize 

Figure 2. The weight of evidence that 1-BP causes adverse developmental or 

reproductive effects in laboratory animals 

Clear evidence of adverse effects

Some evidence of adverse effects

Limited evidence of adverse effects

Insufficient evidence for a conclusion

Limited evidence of no adverse effects

Some evidence of no adverse effects

Clear evidence of no adverse effects

Developmental and reproductive toxicity
3

NTP Brief

1-BP. Therefore, exposure concentrations from 

animal studies were used to directly predict 

exposure concentrations that might adversely 

affect humans. 

A recent case report, not available to the panel, 

discussed symptoms experienced by three women occupationally exposed to 1-BP (Ichihara et 

al., 2002). Workers who used 1-BP as a solvent 

experienced neurological, intestinal, and reproductive effects. Two of the workers experienced 

altered menstrual periods and decreased sexual 

desire. Passive sampling of the environment 

indicated daily TWAs ranging from 60 to 261 

ppm. The average daily value was 133 ppm. 

These findings provide some evidence that 

exposure to 1-BP may adversely affect human 

reproduction in females. Because of the small 

sample size and the unique exposure circumstances in this study, these data would be of 

limited use in predicting possible adverse reproductive effects in the general population.

A recent study in rats showed that exposure to 

concentrations ranging from 50 to 1000 ppm 

1-BP for 8 hours a day for at least 20 consecutive days did not significantly alter estrous 

cycle, ovulation, or ovary and uterus weights 

(Sekiguchi et al., 2002). The use of a short time 

course (20 days) compared to the critical reproductive animal study (greater than 10 weeks 

exposure) limits its utility in assessing possible 

human health effects.

Another recent study showed that female rats 

exposed 8 hours per day to 200, 400, or 800 

ppm 1-BP for 7 to 12 weeks showed a significant, dose-dependent increase in the number of 

irregular estrous cycles, with extended diestrus 

at 400 ppm (Yamada et al., 2003). Additionally, 

examination of the ovaries showed a dosedependent reduction in the number of normal 

antral (or mature) follicles at doses of 200 and 

400 ppm. This effect is consistent with reduced 

fertility and litter sizes reported in earlier studies. Interestingly, the number of primordial follicles was not significantly reduced in any of 

the 1-BP exposure groups. The authors suggest 

that antral follicle counts may provide a more 

sensitive indicator of 1-BP-induced female 

reproductive dysfunction than other endpoints 

such as estrous length. 

Are Current Exposures to 1-BP High 

Enough to Cause Concern?

Possibly. More data are needed to better unFigure 3. NTP conclusions regarding the possibilities that human development 

or reproduction might be adversely affected by exposure to 1-BP

1 based on the upper end of the occupational exposures range (18 to 381 ppm)

 2 based on exposures that are intermittent and well controlled (0.04 to 0.63 ppm)

Serious concern for adverse effects

Concern for adverse effects

Some concern for adverse effects

Minimal concern for adverse effects

Negligible concern for adverse effects

Insufficient hazard and/or exposure data

Developmental and reproductive effects 2

Developmental and reproductive effects 1
4

NTP Brief

derstand human 1-BP exposure levels and how 

these exposures vary across the population. 

There are no data on 1-BP exposure of the 

general U.S. population but there are some data 

available on occupational exposures. Based on 

the occupational exposure data and studies in 

humans and laboratory animals, the NTP offers 

the following conclusions (Figure 3):

The NTP concurs with the CERHR Bromopropanes Expert Panel that there is serious 

concern for reproductive and developmental 

effects at the upper end of the human occupational exposure range (18-381 ppm).

Additional support for the expert panel’s conclusion is found in more recent rodent and 

limited but consistent human studies showing 

that exposure to 1-BP can lead to adverse developmental and/or reproductive effects. Such 

effects are reported in animal studies at exposure levels of 200 ppm or greater. 

The NTP concurs with the CERHR Bromopropanes Expert Panel that there is minimal 

concern for reproductive and developmental 

effects when humans are exposed at the lower 

end of the human occupational exposure 

range (0.04-0.63 ppm). 

This exposure range is far below the “No Observed Adverse Effect Concentrations” identified by the expert panel.

These conclusions are based on 

the information available at the 

time this brief was prepared. As 

new information on toxicity and 

exposure accumulate, it may form 

the basis for either lowering or 

raising the levels of concern expressed in the conclusions.

Ichihara G, Miller JK, Ziolkowska A, Itohara 

S, Takeuchi Y. Neurological disorders in three 

workers exposed to 1-bromopropane. Journal 

of Occupational Health 44:1-7 (2002).

Kawai T, Takeuchi A, Miyama Y, Sakamoto 

K, Zhang ZW, Higashikawa K, Ikeda M. Biological monitoring of occupational exposure 

to 1-bromopropane by means of urinalysis for 

1-bromopropane and bromide ion. Biomarkers

6:303-312 (2001).

Sekiguchi S, Suda M, Zhai YL, Honma T. Effects of 1-bromopropane, 2-bromopropane, and 

1,2-dichloropropane on the estrous cycle and 

ovulation in F344 rats. Toxicology Letters 126:

41-49 (2002).

Yamada T, Ichihara G, Wang H, Yu X, Maeda 

K, Tsukamura H, Kamijima M, Nakajima T, 

Takeuchi Y. Exposure to 1-bromopropane 

causes ovarian dysfunction in rats. Toxicological Sciences 71:96-103 (2003).

References
I-1

Appendix I

Appendix I. NTP-CERHR Bromopropanes Expert Panel

A 9-member panel of scientists covering dis-

ciplines such as toxicology, epidemiology, 

and medicine was recommended by the Core 

Committee and approved by the Director of 

the Environmental Toxicology Program. Over 

the course of a 4-month period, the panel criti-

cally reviewed documents and identified key 

studies and issues for plenary discussions. At 

a public meeting held December 5–7, 2001, 

the expert panel discussed these studies, the 

adequacy of available data, and identified data 

needed to improve future assessments. The 

expert panel reached conclusions on whether 

estimated exposures may result in adverse effects on human reproduction or development. 

Panel assessments were based on the scientific 

evidence available at the time of the final meet-

ing. The expert panel report was made avail-

able for public comment on March 8, 2002, 

and the deadline for public comments was 

May 7, 2002 (Federal Register 67:46 [8 March 

2002] p10734). The 1-BP Expert Panel Report 

is provided in Appendix II and the public com-

ments received on the report are in Appendix 

III. Input from the public and interested groups 

throughout the panel’s deliberations was in-

valuable in helping to assure completeness and 

accuracy of the reports. The 1-BP Expert Panel 

Report is also available on the CERHR website <http://cerhr.niehs.nih.gov>.
I-2

Appendix I

Kim Boekelheide, M.D., Ph.D., Chairman

Brown University 

Providence, RI

Cynthia F. Bearer, M.D., Ph.D.* 

Case Western Reserve Univ.

Cleveland, OH

Sally Perreault Darney, Ph.D. 

U.S. EPA 

Research Triangle Park, NC

George P. Daston, Ph.D. 

Proctor & Gamble 

Cincinnati, OH

Raymond M. David, Ph.D. 

Eastman Kodak Company 

Rochester, NY

Ulrike Luderer, M.D., Ph.D. 

University of California-Irvine

Irvine, CA

Andrew F. Olshan, Ph.D. 

Univ. of North Carolina 

Chapel Hill, NC

Wayne T. Sanderson, Ph.D., C.I.H. 

NIOSH 

Cincinnati, OH

Calvin C. Willhite, Ph.D. 

DTSC, State of California 

Berkeley, CA

Susan Woskie, Ph.D., C.I.H. 

University of Massachusetts 

Lowell, MA

Appendix I. NTP-CERHR Bromopropanes Expert Panel 

(Name and Affiliation)

* Dr. Bearer was unable to attend the Expert Panel meeting or contribute to the development of summaries 

and conclusions in Section 5 of the 1-BP Expert Panel Report.
NTP-CERHR EXPERT PANEL REPORT 

ON THE REPRODUCTIVE AND 

DEVELOPMENTAL TOXICITY 

OF 1-BROMOPROPANE

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March 2002 NTP-CERHR-1-BP-02
Appendix II

II-iii

TABLE OF CONTENTS

Abbreviations.....................................................................................................................................v

List of Tables.................................................................................................................................. viii

List of Figures...................................................................................................................................ix

Preface................................................................................................................................................ x

A Report of the CERHR Bromopropanes Expert Panel.............................................................. xi

1.0 Chemistry, Use, And Exposure ................................................................................................1

1.1 Chemistry ......................................................................................................................1

 1.1.1 Nomenclature .................................................................................................1

 1.1.2 Formula and Molecular Mass.........................................................................1

 1.1.3 Chemical and Physical Properties..................................................................1

 1.1.4 Technical Products and Impurities..................................................................2

1.2 Use and Human Exposure .............................................................................................3

 1.2.1 Production.......................................................................................................3

 1.2.2 Use..................................................................................................................3

 1.2.3 Occurrence......................................................................................................3

 1.2.4 Human Exposure ............................................................................................4

1.3 Utility of Data................................................................................................................5

1.4 Summary of Human Exposure ......................................................................................5

2.0 General Toxicological And Biological Parameters.................................................................7

2.1 Toxicokinetics and Metabolism.....................................................................................7

2.2 General Toxicity ..........................................................................................................11

 2.2.1 Human Data..................................................................................................11

 2.2.2 Animal Data..................................................................................................12

2.3 Genetic Toxicity...........................................................................................................22

2.4 Carcinogenicity ...........................................................................................................24

2.5 Potentially Sensitive Sub-Populations.........................................................................24

2.6 Summary of General Toxicological and Biological Effects........................................24

3.0 Developmental Toxicity Data .................................................................................................28

3.1 Human Data.................................................................................................................28

3.2 Experimental Animal Toxicity.....................................................................................28

3.3 Utility of Data..............................................................................................................33

3.4 Summary of Developmental Toxicity..........................................................................33

4.0 Reproductive Toxicity .............................................................................................................36

4.1 Human Data.................................................................................................................36

4.2 Experimental Animal Toxicity.....................................................................................36
Appendix II

II-iv

4.3 Utility of Data..............................................................................................................43

4.4 Summary of Reproductive Toxicity.............................................................................44

5.0 Data Summary & Integration ...............................................................................................47

5.1 Summary and Conclusions of Reproductive and Developmental Hazards.................47

5.2 Summary of Human Exposure ....................................................................................47

5.3 Overall Conclusions....................................................................................................48

5.4 Critical Data Needs .....................................................................................................49

6.0 References................................................................................................................................51
II-v

Appendix II

ABBREVIATIONS

ALAT alanine amino transferase

ANOVA analysis of variance

ASAT aspartate aminotransferase

ASTM American Society for Testing and Materials

1-BP 1-Bromopropane

2-BP 2-Bromopropane

BMD benchmark dose

BMDL benchmark dose 95th percentile lower confidence limit

BSOC Brominated Solvents Consortium

BUN blood urea nitrogen

bw bodyweight

C Celsius

C2 second carbon 

C3 third carbon

CAS RN Chemical Abstract Service Registry Number

CBC complete blood count

CERHR Center for the Evaluation of Risks to Human Reproduction

CFC chlorofluorocarbon

CNS central nervous system

d days

DL distal latency

DMSO dimethyl sulfoxide

F female

F0 parental generation

F1 first filial generation

F2 second filial generation

FSH follicle stimulating hormone

g gram

GC gas chromatography

gd gestation day

GLP Good Laboratory Practices

GSH glutathione

GST glutathione S-transferase

h hour

HCFC hydrochlorofluorocarbon

2,5-HD 2,5-hexanedione

HSDB Hazardous Substances Data Bank

ip intraperitoneal

IPI interpulse intervals

IR infrared

Kg kilogram

Km Michaelis constant

Kow octanol-water partition coefficient
Appendix II

II-vi

L liter

LC50 lethal concentration, 50% mortality

LC100 lethal concentration,100% mortality

LD50 lethal dose, 50% mortality

LH luteinizing hormone

LOAEC lowest observed adverse concentration, synonymous with lowest observed adverse 

effect level (LOAEL)

LPO lipid peroxides

M male 

m3 meters cubed

MCV motor nerve conduction velocity

MFO mixed function oxidase

mg milligram

ML motor latency

mL milliliter

mm Hg millimeters mercury

mmol millimole

MQL minimal quantification limit

MRI magnetic resonance imaging

MSDS Material Safety Data Sheet

mw molecular weight

n number

ng nanogram

NIEHS National Institute of Environmental Health Sciences

NOAEC no observed adverse effect concentration, synonymous with no observed adverse

effect level (NOAEL)

NOEC no observed effect concentration, synonymous with no observed effect level (NOEL)

NIOSH National Institute of Occupational Safety and Health

NTP National Toxicology Program

OECD Organization for Economic Co-operations and Development

OSHA Occupational Safety and Health Administration

RBC red blood cell

PE/NE polychromatic/normochromatic erythrocyte

pnd postnatal day

pNPH p-nitrophenol hydroxylase

PPE personal protective equipment

ppm parts per million

PPR paired-pulse ratios

PS paired-pulse population spike

S Sulfur

sc subcutaneous

SD standard deviation

SNAP Significant New Alternatives Program

TWA time weighted average

UNEP United Nations Environment Programme
II-vii

Appendix II

US EPA United States Environmental Protection Agency

Vmax maximal velocity of metabolism

wk week

w/v weight per volume

μg microgram

μM micromolar

μmole micromole
Appendix II

II-viii

LIST OF TABLES

Table 1-1. Physicochemical properties of 1-BP........................................................................... 1

Table 1-2. Specifications for Vapor-Degreasing Grade and General Grade 1-BP ....................... 2

Table 2-1. Summary of General Toxicity Effects in Inhalation Studies..................................... 26

Table 3-1. Major Effects Observed in a Prenatal Toxicity Study............................................... 28

Table 3-2. Major Effects Observed in a Developmental Range-Finding Study......................... 32

Table 3-3. Summary of Developmental Toxicity in Inhalation Studies..................................... 35

Table 4.1. Major Effects Observed in a Two-Generation Reproductive Toxicity Study 

in Sprague Dawley Rats............................................................................................ 37

Table 4-2. Major Effects in Reproductive Toxicity Study in Wistar Rats.................................. 41

Table 4-3. Summary of Reproductive Toxicity Inhalation Studies............................................ 44
II-ix

Appendix II

LIST OF FIGURES

Figure 1-1. Chemical Structure of 1-Bromopropane.................................................................... 1

Figure 2-1. Possible Metabolic Pathway for 1-BP in the Rat ..................................................... 10

Figure 3-1. Benchmark Dose Analysis of Fetal CD Rat Bodyweight Following 

In Utero Exposure to 1-BP....................................................................................... 30
Appendix II

II-x

PREFACE

The National Toxicology Program (NTP) and the National Institute of Environmental Health Sciences 

(NIEHS) established the NTP Center for the Evaluation of Risks to Human Reproduction (CERHR) in June 

1998. The purpose of the CERHR is to provide timely, unbiased, scientifically sound evaluations of human 

and experimental evidence for adverse effects on reproduction, including development, caused by agents to 

which humans may be exposed.

1-Bromopropane (1-BP) was nominated by NIOSH and selected for evaluation by the CERHR based primarly on documented evidence of worker exposures and published evidence of reproductive and developmental toxicity in rodents. 1-BP is used in spray adhesives and as a precision cleaner and degreaser. It may 

also be used as an intermediate in the synthesis of pharmaceuticals, insecticides, quaternary ammonium 

compounds, flavors, and fragrances and as a solvent for fats, waxes, or resins.

The evaluation of 1-BP was a 4-month effort by a 10-member panel of academic, private, and government 

scientists that culminated in a public meeting in December 2001. At that meeting, the expert panel reviewed 

the scientific evidence on 1-BP and reached conclusions regarding its potential effects on human reproduction and development. The background information on 1-BP and findings of the expert panel are contained 

within this report. The Expert Panel Report on 1-Bromopropane is intended to (1) interpret the strength 

of scientific evidence that a given exposure or exposure circumstance may pose a hazard to reproduction 

and the health and welfare of children; (2) provide objective and scientifically thorough assessments of the 

scientific evidence that adverse reproductive/developmental health effects are associated with exposure to 

specific chemicals or classes of chemicals, including descriptions of any uncertainties that would diminish 

confidence in assessment of risks; and (3) identify knowledge gaps to help establish research and testing 

priorities. Staff scientists from the CERHR and members of the CERHR Core Committee (oversight committee to the CERHR whose members include NTP participating agencies) have reviewed the report and the 

CERHR will seek public review and comment through a Federal Register notice.

Subsequent to this comment period, the NTP will prepare the NTP-CERHR Report on 1-Bromopropane that 

contains its conclusions regarding the potential for 1-BP to adversely affect human reproduction or development. The NTP will base its conclusions on the Expert Panel Report on 1-Bromopropane, any public comments 

received on that report, and any relevant information available since the expert panel meeting. The NTPCERHR report will include the public comments and the expert panel report as appendices. The NTP-CERHR 

Report on 1-Bromopropane will be made publicly available and transmitted to health and regulatory agencies. 

The NTP and the CERHR wish to thank the members of the Bromopropanes Expert Panel for their contributions to the evaluation of 1-BP. We greatly appreciate their time, effort, and objectivity during this evaluation process. We also wish to thank the contract staff for their support in convening the expert panel and 

preparing the expert panel report. 

The NTP-CERHR is headquartered at NIEHS, Research Triangle Park, NC and is staffed and administered 

by scientists and support personnel at NIEHS and at Sciences International, Inc., Alexandria, Virginia.

Reports can be obtained from the website <http://cerhr.niehs.nih.gov/> or from:

Michael D. Shelby, Ph.D.

NIEHS EC-32

PO Box 12233

Research Triangle Park, NC 27709

919-541-3455

shelby@niehs.nih.gov
II-xi

Appendix II

A REPORT OF THE CERHR BROMOPROPANES EXPERT PANEL: 

Name Affiliation

Kim Boekelheide, M.D., Ph.D., Chairman Brown University, Providence, RI

Cynthia F. Bearer, M.D., Ph.D.* Case Western Reserve U., Cleveland, OH

Sally Perreault Darney, Ph.D. EPA, Research Triangle Park, NC

George P. Daston, Ph.D. Proctor & Gamble, Cincinnati, OH

Raymond M. David, Ph.D. Eastman Kodak Company, Rochester, NY

Ulrike Luderer, M.D., Ph.D. University of California-Irvine, Irvine, CA

Andrew F. Olshan, Ph.D. University of North Carolina, Chapel Hill, NC

Wayne T. Sanderson, Ph.D., C.I.H. NIOSH, Cincinnati, OH

Calvin C. Willhite, Ph.D. DTSC, State of California, Berkeley, CA

Susan Woskie, Ph.D., C.I.H. University of Massachusetts, Lowell, MA

* Dr. Bearer was unable to attend the Expert Panel meeting or contribute to the development of 

summaries and conclusions in Section 5 of this report.

With the Support of CERHR Staff:

NTP/NIEHS

Michael Shelby, Ph.D. Director, CERHR

Christopher Portier, Ph.D. Director, Environmental Toxicology Program

Lynn Goldman, M.D. Technical Advisor

Sciences International, Inc.

John Moore, D.V.M., D.A.B.T. Principal Scientist

Annette Iannucci, M.S. Toxicologist

Gloria Jahnke, D.V.M. Toxicologist

Note to Reader:

This report is prepared according to the Guidelines for CERHR Panel Members established by NTP/

NIEHS. The guidelines are available from the CERHR web site <http://cerhr.niehs.nih.gov/>. The format for Expert Panel Reports includes synopses of studies reviewed, followed by an evaluation of the 

Strengths/Weaknesses and Utility (Adequacy) of the study for a CERHR evaluation. Statements and 

conclusions made under Strengths/Weaknesses and Utility evaluations are those of the Expert Panel 

and are prepared according to the NTP/NIEHS guidelines. In addition, the Panel often makes comments or notes limitations in the synopses of the study. Bold, square brackets are used to enclose such 

statements. As discussed in the guidelines, square brackets are used to enclose key items of information 

not provided in a publication, limitations noted in the study, conclusions that differ from authors, and 

conversions or analyses of data conducted by the panel.
Appendix II

II-1

1.0 CHEMISTRY, USAGE, AND EXPOSURE

1.1 Chemistry

1.1.1 Nomenclature

1-Brompropane: CAS RN=106-94-5

Synonyms: Propyl bromide; n-Propyl Bromide 

1.1.2 Formula and Molecular Mass

Figure 1-1: Chemical Structure of 1-Bromopropane (1-BP)

Br

Chemical Formula: C3H7Br

Molecular Weight: 123.0

1.1.3 Chemical and Physical Properties

Conversion Factors: 1mg/m3 ≅ 0.198 ppm; 1ppm ≅ 5.03 mg/m3

Table 1-1: Physicochemical Properties of 1-BP

Property Value

Boiling Point 64.7 oC

Melting Point -110 oC

Flashpoint 25.6 oC a

Specific Gravity 1.353 at 20 °C

Solubility in Water 2,450 mg/L

Vapor Pressure 110.8 mm Hg at 20 °C

Stability Stable*

Reactivity Reacts with strong oxidizing agents and bases*

Flammability Flammable a

Log Kow -0.82 to -0.68

HSDB (1); *Aldrich(2)

a This flashpoint was reported in a Material Safety Data Sheet by Aldrich (2). However, no 

flashpoint was reported in closed or open cup testing of Ensolve (3), a solvent mixture containing >90.5% 1-BP (4). The results of 11 flammability studies were summarized in a letter 

submitted to the US EPA (5). It was asserted (6) that when a flashpoint was determined, it 

was at a temperature greater than the level that would classify a compound as flammable 

under the classification systems developed by the National Fire Protection Agency and four 

national or international governmental agencies.(2). 
II-2

Appendix II

1.1.4 Technical Products and Impurities

Two Material Safety Data Sheets (MSDS) from manufacturers of laboratory reagents reported the purity of 1-BP to be 99% (2, 7). The Occupational Safety and Health Administration (OSHA) analyzed 

samples of 1-BP and detected 2-bromopropane (2-BP) at concentrations ranging from 0.1−0.2% (8). 

Since that time, ASTM standard D6368 (9) for vapor degreasing and general solvent grade 1-BP was 

amended to specify that 2-BP levels remain below 0.1%. Table 1-2 lists ASTM (9) specifications for 

vapor-degreasing and general grade 1-BP.

Table 1-2. Specifications for Vapor-Degreasing Grade and General Grade 1-BP (9)

Property Specification ASTM 

Test Method

Specific gravity, 25/25°C 1.320 to 1.350 D 2111

Distillation range (760 mm Hg)

 Initial boiling point, °C, min 70.0 D 1078

 Dry point, °C, max 88.0

Acidity (as HCl), weight %, max 0.0010 D2989

Alkalinity (as NaOH), weight %, max 0.020 D 2989

Water, weight %, max 0.0150 D 3401

Appearance clear and free from 

suspended matter D 3741

Color, APHA, max 15 D 2108

Free halogen passes test D 4755

Nonvolatile residue, weight %, max 0.0010 D 2109

Acid acceptance (as NaOH), weight %, min 0.15 D 2942

Aluminum scratch passes test D 2943

Normal-propyl bromide content, weight %, min 93 GC

Iso-propyl bromide content, weight %, max 0.1 GC

Neat 1-BP is unusable as a solvent and is therefore sold as a mixture containing stabilizers or additives for solvent applications (10). Five MSDS were identified in an Internet search for 1-BP solvent 

mixtures. The compositions of the solvents included 1-BP at 70−95% with 1-BP levels exceeding 

90% in the majority of products (4, 11-14). Other ingredients listed in these MSDS included butylene 

oxide, 1,3-Dioxolane, nitromethane, dimethoxymethane, t-butanol, 1,1,1-2-tetrafluoroethane, and a 

terpene blend.

Tradenames for 1-BP solvent mixtures include Hypersolve, Abzol, Lenium, Contact Cleaner–NPB 

Heavy Duty, Leksol, Teksol, Ensolv, Solvon, Vapor Edge 1100, X-Cel, VDS-3000, Cobar-Clean 

NPB, No Flash Nu Electro Cleaner, Heavy Duty Degreaser II, and 1640 Bulk (15). Trade names of 

adhesives containing 1-BP include Whisper Spray (Imperial Adhesive), and Fire Retardant Soft Seam 

640 (Mid South Adhesive) (16). Of relevance to this Expert Panel review is that the test material used 

in a 13-week rat inhalation study was designated by the testing facility as ALBTA1 (6). This material 
Appendix II

II-3

contained no stabilizers or additives.

1.2 Use and Human Exposure

1.2.1 Production

1-BP is produced by reacting n-propyl alcohol with hydrogen bromide and then removing the water 

that forms in the process (15). 1-BP can also be produced by the dehydration of propanol with bromine 

or hydrogen bromide in the presence of sulfur catalyst (17). 

Manufacturers of 1-BP that are part of the Brominated Solvents Consortium (BSOC) include Albemarle Corporation, Dead Sea Bromine Group/AmeriBrom, and Great Lakes Chemical Corporation 

(18). ATOFINA (formerly Elf Atochem) is also a manufacturer of 1-BP (19). Additional manufacturers of 1-BP may include Diaz Chemical Corporation, Lambent Technologies, Talstar Western Chemical Inc., Cobar Americas, LPS Laboratories, CRC Industries, and Vineland Chemical Company (1). 

Other companies that have or are marketing 1-BP solvent blends include Petroferm, M.G. Chemicals, 

Albatross USA, Alpha Metals, Amity UK, Enviro Tech International, Poly Systems USA, Tech Spray, 

and Baker (15).

Between 1999 and 2000, 1.5 million pounds per year of 1-BP were produced and 2.8 million pounds 

per year imported for use in the United States (10). The BSOC estimated that global sales and emissions of 1-BP for solvent and adhesive applications as 4,839 metric tonnes [10.6 million pounds], 

3,152 metric tonnes [6.9 million pounds], and 3,736 metric tonnes [8.2 million pounds] for the 

years 2000, 2001, and 2002, respectively (6). The United Nations Environment Program (15) n-BP 

Task Force estimated current worldwide annual use and emissions of 1-BP at 5,000−10,000 metric 

tons [11−22 million pounds]. Future consumption levels of 1-BP have been estimated but are not 

being addressed in this report. However, the future growth rate for sale of 1-BP in the United States 

is not anticipated to exceed the current growth rate of 2.34% per year (10).

1.2.2 Use

1-BP is reported to be used as a solvent for fats, waxes, or resins and as an intermediate in the synthesis of pharmaceuticals, insecticides, quaternary ammonium compounds, flavors, or fragrances (1). 

1-BP is also used in spray adhesives, in precision cleaning, and as a degreaser (10, 16). 

1-BP is currently under review per the US EPA Significant New Alternatives Policy (SNAP) program 

in identification of substitutes for ozone-depleting substances (20). 1-BP is being considered as a possible replacement for CFC-113, methyl chloroform, and HCFC-141b for non-aerosol solvent cleaning 

of metals and electronics and for adhesives, coatings, aerosol propellant, and solvent applications. 

At least three manufacturers are limiting or eliminating use of 1-BP for solvent applications. Great 

Lakes Chemical no longer sells 1-BP solvent blends (15). ATOFINA (19) has decided not to market 

1-BP for solvent applications. Albemarle has stated that use of 1-BP in adhesive and other applications in which 1-BP exposure cannot be controlled should be restricted or prohibited (21).

1.2.3 Occurrence

There is very little information documenting the presence of 1-BP in ambient air, drinking or surface 
II-4

Appendix II

waters, food, or consumer products. An unspecified level of 1-BP was detected in the drinking water 

from an unreported location (1). Schwarzenbach et al. (22) reported on an investigation of leaks from 

a wastewater tank at a Swiss alkyl halide factory at which 1-BP was manufactured (>5 tons/year). 

After the plant ceased operation, the underlying aquifer was found to be heavily polluted. Following soil excavation and continuous groundwater pumping for 7 years, substantial concentrations of 

bromobenzene and chlorobenzene were found, but neither 1-BP, nor 2-BP, nor its corresponding 

alcohol metabolites could be detected in groundwater. In vitro studies by Schwarzenbach et al. (22) 

confirmed the rapid hydrolysis of 1-BP (half life of 26 days) under anaerobic conditions. 

The atmospheric lifetime of 1-BP is reported to be less than 20 days due to reactions with hydroxyl 

that result in the release of bromine atoms and formation of brominated acetone (23). Unreported 

levels of 1-BP were detected in the volatile emissions from household waxes, liquid pastes, and detergents (1). 1-BP was also detected in six species of marine microalgae at unreported levels; it was 

postulated that the 1-BP was a product of monohalo and dihalo-oxo-fatty acid hydrolysis and that it 

could be transported from the algae to the marine environment (1).

1.2.4 Human Exposure

Until occupational exposure limits are set, the US EPA is recommending an 8-hour time weighted 

average (TWA) exposure limit of 50−100 ppm (20). Doull and Rozman (24) recommended a TWAthreshold limit value of 60−90 ppm with a notation for skin absorption. Albemarle Corporation is 

recommending a TWA limit of 25 ppm (25). ATOFINA (19) is recommending an 8-hour occupational exposure limit value of 5 ppm.

NIOSH measured 1-BP levels in the breathing zones (personal samples) of workers in three plants 

where a 1-BP-containing spray adhesive was used in the manufacture of seat cushions for aircraft 

or furniture. In the first plant that used a bromopropane-containing adhesive to manufacture seat 

cushions for aircraft, 8-hour TWA exposures of 69 workers ranged from 60−381 ppm with a mean of 

169 ppm (26). The 8-hour TWA exposures of 16 workers from the second plant which manufactured 

cushions for sofas and similar types of seats ranged from 18 to 254 ppm with a mean of 96 ppm (27). 

An evaluation of 1-BP exposure was conducted in a third plant where a 1-BP-containing spray adhesive was used in the manufacture of sofa furniture cushions in the presence of a local exhaust system 

(28). Personal 8-hour TWA exposures in 12 sprayers were 41−143 ppm (mean 66 ppm) and 8.7−19.4 

ppm, respectively. Fifteen-minute, short-term exposures of 9 sprayers were measured at 34−174 ppm 

and 5-minute ceiling exposures were measured at 40−152 ppm in 11 sprayers. 

NIOSH reevaluated 1-BP levels at the first and third plants after local exhaust, ventilation, and work 

practice changes were made. After the installation of spray booths with local exhaust ventilation at 

the first plant, personal 8-hour TWA exposures in 30 workers ranged from 1.2 to 58 ppm with a mean 

of 19 ppm (16). Short-term exposures (15 minutes) were measured in 12 workers from the assembly 

or covers department. The range of short-term exposures in the assembly and covers departments 

ranged from 12 to 26 ppm and 13 to 96 ppm, respectively. After the third plant enclosed the local 

exhaust ventilation to create spray booths and increase capture efficiency, 8-hour TWA personal 

breathing zone samples measured for 12 assembly workers over 3 days (n=34) ranged from 7.7 to 35 

ppm (mean=19 ppm) (29). These evaluations demonstrate that worker exposures can be dramatically 

reduced by implementation of exhaust and ventilation controls.
Appendix II

II-5

NIOSH also measured 1-BP concentrations in a plant where 1-BP was used as a cold bath degreaser 

that was recently enclosed in a room with local exhaust ventilation to vent vapors from the workplace 

(25). Personal samples were obtained from 20 employees who worked in the area of the degreaser. 

TWA 1-BP exposures only exceeded the minimal quantification limit of 0.02 ppm in 7 workers and 

ranged from 0.04 to 0.63 ppm.

The results of selected air sampling surveys for 1-BP conducted by Albemarle Corporation for some 

of their customers were submitted for review (10). Three surveys of area and personal breathing zone 

samples indicated that worker exposures across metal cleaning and adhesive users were variable 

ranging from below the limit of detection (<0.1 ppm) to 92 ppm. The exposures of adhesive users 

were typically much higher than metal cleaning workers. These measurements fall within the range 

of adhesive worker exposures measured by NIOSH after the installation of ventilation controls, but 

are lower than measurements made before these controls were implemented.

The Expert Panel noted that it is likely that worker exposures and absorbed doses also occur through 

dermal contact. No surveys have yet evaluated dermal exposure. Due to the volatility of 1-BP, it may 

be difficult to directly measure human dermal exposure and absorption. Biological monitoring may be 

the best way to evaluate the contribution of dermal exposure to total absorbed dose in humans.

1.3 Utility of Data

The exposure data reviewed by the Expert Panel are of limited utility for assessment. Very little data 

are available on consumer or general population exposures to 1-BP. No information on the volume 

of usage or number of US workers exposed to 1-BP is available. The data available on current 1-BP 

exposures in the United States are based on exposure surveys conducted by NIOSH of three spray 

adhesive and one cold degreasing operation that used 1-BP, and some selected exposure surveys 

conducted by a manufacturer of 1-BP products. These surveys do not represent a cross-section of 

potential exposures since these investigations were prompted by request from the workers or management of the companies involved. No industry-wide exposure study has been conducted. None of the 

exposure evaluations to date have characterized the potential contribution of dermal exposures to the 

worker.

1.4 Summary of Human Exposure Data

Within the United States, 1-BP is used as a solvent in spray adhesives (16), in vapor degreasing (25), 

and in precision cleaning (10). 1-BP may also be used as a solvent for fats, waxes, or resins or as an 

intermediate in the synthesis of pharmaceuticals, insecticides, quaternary ammonium compounds, 

flavors, or fragrances (1). In the future it is possible that 1-BP may be used as a substitute for hydrochlorofluorocarbons (HCFC) (20). Current usage of 1-BP is less than 5 million pounds (10). One 

manufacturer of 1-BP is recommending that 1-BP not be used in solvent applications in which exposures cannot be controlled (21); while two other manufactures are not marketing 1-BP for solvent applications (15, 19). No information was found that documents exposure of the public to 1-BP through 

contact with air, drinking water, food, or consumer products. 

NIOSH collected 8-hour TWA personal breathing zone measurements for 1-BP in three plants where 

1-BP-containing spray adhesives were used (n=99) and in one plant where 1-BP was used as a cold 

vapor degreaser (n=20). In the plants where 1-BP was being used as a spray adhesive, exposures 
II-6

Appendix II

ranged from 18 to 381 ppm (mean=142 ppm) (26-28). After ventilation control improvements had 

been implemented in two of the adhesive-using plants, NIOSH found that exposures had decreased 

to a range of 1.2−58 ppm (n=64; mean=19 ppm) (16, 29). In the plant where 1-BP was used as a 

vapor degreaser, only 7 of 20 8-hour personal TWA exposures exceeded the minimal quantification 

limit of 0.02 ppm with a range of 0.04−0.63 ppm (25); the degreaser had recently been enclosed in 

a room with local exhaust ventilation installed to vent vapors outside the workplace. Numerous additional exposure measurements have been collected by industry, but were not assessed by the Panel. 

The NIOSH exposure measurements evaluated here were from a few selected locations and cannot be 

considered an accurate representation of the cross-section of exposure levels nationwide.

It is likely that worker exposures also occur through dermal contact with 1-BP. No measurements 

have evaluated dermal exposure. Biological monitoring may be the best way to evaluate the contribution of dermal exposure to total absorbed dose.
Appendix II

II-7

2.0 GENERAL TOXICOLOGICAL AND BIOLOGICAL PARAMETERS

2.1 Toxicokinetics and Metabolism

No human kinetic or metabolism data were identified.

Empirical evidence from rodent toxicity studies indicates that 1-BP is absorbed by the inhalation 

route. However, animal studies that characterize and quantify absorption and distribution of 1-BP 

by any route were not found. The blood:air partition coefficients for humans (7.08) and rats (11.7) 

indicate that 1-BP is readily soluble in blood; the fat:air partition coefficient for humans is 128 and 

for rats is 236 (30). The studies described below discuss metabolism and excretion of 1-BP.

Tachizawa et al. (31) studied the metabolism of 1-BP in vitro using hepatic microsomal enzyme 

preparations from phenobarbital-induced rats. Microsomes were prepared from Sprague-Dawley rats 

treated with phenobarbital according to the procedure of Neal (32), and incubated with 14C-labeled1-BP. Metabolites detected by gas chromatography (GC) included 1,2-propane-diol, propionic acid, 

and propene (a volatile metabolite) in order of relative amount produced. When glutathione was added 

to the incubation mixture, S-propyl glutathione and S-(2’-hydroxy-1’-propyl) glutathione were produced. Thin layer chromatography was used to detect glutathione metabolites.

Strengths/Weaknesses: This is a well-conducted study of potential metabolites of 1-BP. Efforts were 

made to identify substances using appropriate analytical methods. The study does not provide kinetic 

constants for metabolism, but there are no perceived limitations. 

Utility (adequacy) for CERHR Evaluation Process: This study provides information of the metabolites formed from 1-BP. The data are adequate to provide indications of potential toxic metabolites. 

Kim et al. (17) examined the inducibility of hepatic cytochrome P450 isoenzymes and other related 

enzymes in microsomes of 7-week-old male and female Sprague-Dawley rats that inhaled 50, 300, 

or 1,800 ppm 1-BP (analytical grade) for 6 hours/day, 5 days/week, for 8 weeks. [It was verified that 

units of concentration were ppm and not ppm/kg (33)]. Chamber concentrations of 1-BP were 

monitored by GC every 15 minutes. Enzyme activities were studied in 10 rats/sex/group. Methods 

of statistical analyses were paired-sample t-test using SPSS according to the original report (34). 

1-BP treatment resulted in significantly increased activities of NADH b5 reductase and p-nitrophenol 

hydroxylase (pNPH) in high-dose males and females. Western blot analyses from 1-BP treated rats 

revealed a strong signal for CYP2E. Glutathione S-transferase (GST) activity significantly increased 

in male rats of all dose groups [Expert Panel notes that no dose-related increase was observed]

and female rats in the two highest dose groups. Glutathione peroxidase activity was significantly 

increased in all treated rats. Lipid peroxides (LPO) were significantly increased in females of the 

two highest dose groups and males in the highest dose group. In most cases, enzyme activities were 

higher in male than in female rats. The authors concluded that the metabolism of 1-BP is sex-dependent; the CYP2E1 isoenzyme is possibly responsible for 1-BP metabolism; free radicals are produced 

by activated intermediates as halide radicals; and GST is involved in detoxification and protection of 

tissues against oxidative damage induced by halide radicals.

Strength/Weaknesses: This study demonstrates a concentration-related increase in overall metabolic 
II-8

Appendix II

enzyme activity that may be important in the activation or deactivation of 1-BP. Sufficient numbers 

of animals were used, and the methodology for enzyme assays was adequately described. However, 

conclusions concerning the hepatic metabolism of 1-BP by GST pathways to non-toxic substances 

appear to be unsupported.

Utility (adequacy) for CERHR Evaluation Process: The data are adequate to provide some indication 

of alterations in metabolism in response to 1-BP exposure.

Kaneko et al. (35) studied the in vitro metabolism of 1-BP in hepatic microsomes of male Wistar rats 

by measuring the rate of substrate disappearance and rate of product (n-propyl alcohol) formation. 

The authors demonstrated that there were two sets of Vmax and Km metabolic constants. According 

to authors, differences in rate between substance disappearance and n-propyl alcohol formation suggested the possibility of alternate pathways besides metabolism of 1-BP to n-propyl alcohol or that 

n-propyl alcohol is further metabolized. The procedures and results for this experiment were reported 

in the form of a short communication.

Strength/Weaknesses: This study provides information on the metabolism of 1-BP by microsomal 

enzymes (likely cytochrome P-450). In addition, there is a clear indication of two enzymatic pathways, both of which have reasonable affinity for 1-BP, but a low capacity for metabolism.

Utility (adequacy) for CERHR Evaluation Process: The data demonstrate that 1-BP is metabolized 

by hepatic microsomal enzymes, although to a minor extent. This information may be important in 

assessing risk for systemic toxicity since metabolism from mixed function oxidase (MFO) enzymes 

is not likely to play a significant part in activation of 1-BP to active metabolites.

Khan and O’Brien (36) incubated isolated rat hepatocytes in the presence of 100 μM 1-BP or 6 other 

1-bromoalkanes for up to 1 hour and measured intracellular glutathione levels. 1-BP caused a timerelated reduction in glutathione level. The magnitude of glutathione depletion was directly related to 

the chain length of the bromoalkane. Incubation with 1-BP resulted in minimal decreases (32% lower 

than untreated cells) in intracellular glutathione levels compared with long-chain bromoalkanes (88% 

lower than untreated cells). 

Strength/Weaknesses: This is a well-designed study that provides direct evidence that 1-BP can react 

with glutathione and deplete hepatocyte GSH levels.

Utility (adequacy) for CERHR Evaluation Process: This study supports the findings of Kim et al. 

(17) indicating that glutathione reacts with 1-BP. 

Barnsley et al. (37) fed 4 male rats [age and strain unspecified] a diet containing 35S-labelled yeast 

for 3 days, injected 2 of the rats subcutaneously with 1 mL of 40% w/v solution of 1-BP [purity not 

specified] in arachis oil on the fourth day, collected urine for the 24 hours after dosing, and measured 

metabolites in urine by radiochromatography. Three metabolites were detected in the urine of treated 

but not control rats: n-propylmercapturic acid, 2-hydroxypropylmercapturic acid, and n-propylmercapturic acid sulphoxide. 
Appendix II

II-9

Strength/Weaknesses: Although this study lacks the analytical sophistication that is common to current studies, it provides direct evidence of conjugation and excretion of 1-BP with glutathione, presumably via glutathione-S-transferases. 

Utility (adequacy) for CERHR Evaluation Process: This study is important in understanding the 

value of the GST pathway in the metabolism of 1-BP. GST activation is an important component of 

haloalkane metabolism and toxicity. For some haloalkanes, biotransformation to an active metabolite leads to systemic toxicities. However, there is no indication that active metabolites are produced 

from 1-BP exposures in quantities that lead to long-term adverse health effects. In fact, the data from 

Barnsley et al. (37) suggest that GST activation is minimal compared with other haloalkanes.

Jones and Walsh (38) further characterized metabolites of 1-BP in rats. Male Sprague-Dawley rats

[230−260 g; age and number treated not specified] were treated orally with 1-BP [purity not specified] in arachis oil at 200 mg/kg bw/day for 5 days and the urine was pooled and examined by thin 

layer chromatography. Three mercapturic acid compounds identified in urine were the same as those 

identified by Barnsley et al. (37): N-acetyl-S-propyl-cysteine, N-acetyl-S-(2-hydroxypropyl)cysteine, 

and N-acetyl-S-propylcysteine-S-oxide. Three additional compounds were also identified in urine: 

N-acetyl-S-(3-hydroxypropyl)cysteine, N-acetyl-S-(2-carboxyethyl)cysteine, and 3-bromopropionic 

acid. In vitro metabolism studies with 1-BP demonstrated that oxidation of C3 and C2 occurs before 

conjugation of the alkyl group with glutathione. Figure 2-1 illustrates a possible metabolic pathway 

of 1-BP as determined by Jones and Walsh (38).

Jones and Walsh (38) studied the excretion of 1-BP in the expired air and urine of Sprague-Dawley rats 

following a single intraperitoneal (ip) injection with 200 mg/kg bw. Initial excretion of unchanged 1-BP 

in expired air was rapid, with 56% and 60% exhaled after 2 and 4 hours, respectively. Only trace 

amounts were detected in expired air after 4 hours. Twenty-five percent of the administered bromide 

was excreted in urine over a period of 100 hours.

Strength/Weaknesses: This study further characterizes the metabolism of 1-BP, demonstrating the exhalation of a significant amount of unmetabolized 1-BP following parenteral exposure. On the other 

hand, details on the methodology are unclear with numbers of animals used not specified.

Utility (adequacy) for CERHR Evaluation Process: The value of this study is to define the metabolic 

pathway of 1-BP and identify intermediate metabolites.
II-10

Appendix II

Figure 2-1: Possible Metabolic Pathway for 1-BP in the Rat

CH3

CH2 NHR

CH2SCH2CHCOOH

III

O

CH3

CH2 NHR

CH2SCH2CHCOOH

II

CH3

CHOH NHR

CH2SCH2CHCOOH

X

CH2OH

CH2 NHR

CH2SCH2CHCOOH

V

COOH

CH2 NHR

CH2SCH2CHCOOH

XII

COOH

CH2

CH2OH

VII

COOH

CH2

CH2Br

VI

CH2OH

CH2

CH2Br

IV

CH3

CH

CH2

O

IX

CH3

CH2

CH2OH

XI

CH3

CH2

CH2Br

I

CH3

CHOH

CH2Br

VIII

CO2

A B

D

C

Compounds in parentheses were not isolated in urine. Reproduced with permission from Jones and 

Walsh (38).
Appendix II

II-11

2.2 General Toxicity

2.2.1 Human Data

Sclar (39) published a case report of a 19-year-old male who experienced weakness of the lower 

extremities and the right hand, numbness, and difficulty swallowing and urinating after a 2-month 

occupational exposure to a degreasing and cleaning solvent. The solvent consisted primarily of 1-BP 

(95.5%) and also butylene oxide (<0.5%), 1,3-dioxolane (<2.5%), and nitromethane (<0.25%). Levels 

of exposure were not measured and it is not clear by which route(s) exposure occurred. Although the 

patient wore gloves (material unspecified), the skin on his right (preferentially exposed) hand darkened, suggesting that the gloves may not have offered sufficient protection. Nerve conduction tests 

revealed prolonged distal motor and F response latencies with slower extremity sensory nerve conduction velocities but preserved amplitude response. Magnetic resonance imaging (MRI) scans revealed 

patchy areas of increased T2 signal in the periventricular white matter and root enhancement in the 

lumbar region of the spinal cord. An analysis of spinal fluid did not detect antibodies for infectious 

agents. According to the author, the evidence suggested that the patient was suffering from a symmetric demyelinating polyneuropathy with central nervous system (CNS) involvement. Because similar 

symptoms were observed in rats exposed to 1-BP, the author hypothesized that the patient’s symptoms 

may have resulted from 1-BP exposure.

Strength/Weaknesses: This study reports information from a single patient without exposure information. There was no demonstration that appropriate personal protective equipment (PPE) was used.

Utility (adequacy) for CERHR Evaluation Process: Very limited utility. Because this is only a casereport involving a single individual, less weight is given to it as true evidence of 1-BP adverse health 

effects in humans.

In 1998, NIOSH conducted a health hazard evaluation at a plant where a 1-BP-containing spray 

adhesive was used in the manufacture of seat cushions (40). Forty-three employees (34 females and 

9 males) provided a blood sample for a complete blood count (CBC) and answered a medical questionnaire. Individuals were 18−64 years of age (mean=31 years). Based on industrial hygiene data, 

1-BP exposures in those employees were categorized as ‘low’ (117 ppm [585 mg/m3]), ‘medium’ 

(170 ppm [850 mg/m3]), or ‘high’ (197 ppm [985 mg/m3]). NIOSH concluded that there were no 

CBC abnormalities related to individual or categorical exposure. Employees in the high exposure 

group reported headaches at least once each week. NIOSH stated that the headaches could have been 

related to 1-BP exposure but noted the lack of an exposure-response trend since the lower exposure 

groups reported a similar frequency of headache. [The Expert Panel found the information incomplete and could not reach a conclusion as to the effect of 1-BP exposure.] The questionnaire also 

included questions about reproductive function that are discussed under Section 4. 

Strength/Weaknesses: This study evaluates hematology parameters in humans from a cohort of workers whose exposure to 1-BP is known. It is possible to compare, directly, these results with animal 

data. A weakness of the study is that only 61% of individuals (43 of 70) completed the survey, and that 

raw data were not presented for hematology. The investigators should have compared the exposure 

data between those who completed the survey and those who failed to complete the survey in order to 

gauge potential selection bias. In addition, pre-exposure hematology values for these individuals were 
II-12

Appendix II

not available to ascertain if occupational 1-BP exposure resulted in changes.

Utility (adequacy) for CERHR Evaluation Process: The value of this study is that effects on hematology were assessed and can be compared with animal data. Unfortunately, no raw data were presented. The authors indicated that there was no correlation of reduced erythrocyte count and exposure. 

Although there was a suggestion of an exposure-response gradient with respect to low red blood cell 

count, the small numbers of subjects and lack of an unexposed comparison group reduce the utility 

of the preliminary study.

2.2.2 Animal Data

An acute oral toxicity study of 1-BP (41) was located, but is not reported here because those data were 

not considered to have direct utility for the evaluation of potential adverse reproductive or developmental effects.

An acute Good Laboratory Practices (GLP) dermal toxicity study of 1-BP was conducted (42) using Sprague-Dawley rats obtained from Iffa Credo, France. Animals were 283 g (males) and 233 g 

(females) and at least 8 weeks of age at the initiation of exposure. Neat 1-BP (99.3% purity; 2,000 

mg/kg bw) was applied to the shaved skin on the dorsal area of 5 rats/sex and wrapped with a gauze 

pad (semi-occlusive wrap) for 24 hours. The animals were observed for signs of toxicity, and bodyweight was measured weekly. No concurrent control animals were used but bodyweight gain was 

compared to historical control data. At termination of the 14-day observation period, animals were 

sacrificed, necropsied, and examined macroscopically for evidence of organ toxicity. There were no 

clinical signs of toxicity. One female lost weight during the first week, but all other animals gained 

weight. There was no evidence of dermal irritation, and there were no gross lesions at necropsy. The 

authors concluded that the dermal LD50 is higher than 2,000 mg/kg bw. [The Expert Panel noted 

that the lack of an occlusive wrap may have resulted in evaporation of the test substance and a 

less-than-optimal exposure period.]

Strength/Weaknesses: This is a well-conducted study according to current guidelines. A weakness is 

that the test substance was covered with a semi-occlusive wrap rather than an occlusive wrap. This 

may have allowed the test substance, which is known to be volatile, to evaporate from the application 

site resulting in a less-than optimal exposure period.

Utility (adequacy) for CERHR Evaluation Process: The data have limited utility in assessing the 

potential for dermal penetration of 1-BP. Because no effects were observed, it is unclear if this represents a lack of systemic toxicity from dermal exposure or the lack of dermal penetration.

An acute inhalation toxicity study of 1-BP (43) was conducted using 7−9 week old male and female 

Wistar rats obtained from Charles River France (SPF, WISTAR Crl rats: (WI) BR). The study was 

conducted according to GLP. In a limit test, 5 rats/sex/group were exposed to 0 or 34.6 g/m3 [34, 600 

mg/m3, equivalent to 6,879 ppm]. In the main part of the study, 5 males and 5 females/group were 

exposed to 0, 30.2, 35.1, 37.0, or 42.5 g/m3 [30,200, 35,100, 37,000, or 42,500 mg/m3, equivalent to 

6,003, 6,997, 7,355 and 8,448 ppm, respectively] 1-BP (99.5%). Five satellite males/group were exposed to 0 or 36.4 g/m3 [36,400 mg/m3, equivalent to 7,237 ppm] and blood was collected 24 hours 

and 13 days after exposure for hematology. All exposures were conducted for 4 hours in a nose-only 
Appendix II

II-13

chamber (flow-past system). Concentrations were verified by GC. Animals were observed for 14 days 

following treatment. Bodyweights were measured daily. Lungs and testes from control animals and 

those exposed to 34.6 (males only) and 42.5 g/m3 were weighed and examined microscopically (tissue fixed in 10% formalin). All animals exposed to 37.0 and 42.5 g/m3 died on test. Most animals 

exposed to 35.1 g/m3 died (7/10) and some animals exposed to 34.6 g/m3 died (3/10). The LC50 was 

estimated at 35.0 g/m3 [6,958 ppm]. Clinical signs included respiratory distress and “general weakness.” Surviving animals gained weight over the 14 days. There was an increase in leukocyte count, 

hemoglobin, and packed cell volume on day 2 for the 36.4 g/m3 group [no statistical evaluation], but 

these differences resolved by day 14. There was no apparent change in relative testis weight and no 

microscopic testicular lesions in animals exposed to 1-BP. Pulmonary lesions consisting of edema and 

“emphysema” were observed in the 1-BP-exposed animals. [The Expert Panel selected a NOEC of 

30.2 g/m3.]

Strength/Weaknesses: This study reports acute lethality after inhalation of very high concentrations 

of 1-BP. Adequate numbers of animals were used and procedures conform to current standards and 

practices. A weakness of the study is the use of 10% formalin for fixation of the testes. This fixative 

is recognized as inadequate to properly evaluate subtle effects on the testes. No ovarian or female reproductive tract data were reported.

Utility (adequacy) for CERHR Evaluation Process: This study demonstrates the acute toxicity of 

1-BP under conditions of exposure that permit direct comparison to toxic effects seen with other 

substances. The measurements of testicular weight and histopathology are helpful in ascertaining 

adverse effects that occur following acute 1-BP exposure.

Kim et al. (44) studied the acute and repeated inhalation toxicity of 1-BP in 11-week-old male and 

female Sprague-Dawley rats (SPF grade, from Dae Han Laboratory Animal Research Center). In 

both parts of the experiment, rats inhaled reagent grade 1-BP and concentrations within chambers 

were monitored and confirmed by GC every 15 minutes. For the acute study, 5 rats/sex/group inhaled 0, 11,000, 13,000 15,000, or 17,000 ppm [55,337, 65,398, 75,460, or 85,521 mg/m3] 1-BP for 4 

hours. Rats were observed for 2 weeks following exposure. Clinical signs of toxicity in treated groups 

during exposure included piloerection, reduced activity, ataxia, lacrimation, and reduced response to 

noise. Death was observed within 24 hours of exposure in groups exposed to 13,000 ppm and higher; 

incidence of death was dose-related and reached 100% in the highest dose. All surviving rats clinically recovered 24 hours after the exposure period. An LC50 of 14,374 ppm (95% confidence limit: 

13,624−15,596 ppm) was calculated. The lowest lethal concentration was <11,833 ppm and the LC100

was >18,186 ppm. At the end of the observation period, all surviving rats were sacrificed by carbon 

dioxide and necropsied; abnormal tissues were examined histologically. Cytoplasmic vacuolation of 

hepatocytes surrounding the central vein was observed in an unspecified number of treated rats but the 

effect was not dose-dependent. [The Expert Panel selected a NOEC of 11,000 ppm.]

In the repeated inhalation portion of the Kim et al. (44) study, 10 rats/sex/group inhaled 0, 50, 300, 

or 1,800 ppm 1-BP [252, 1,509, or 9,055 mg/m3] for 6 hours/day, 5 days/week, for 8 weeks. [The 

rationale for dose selection was not discussed.] Bodyweight and feed consumption were measured 

twice per week. Urine samples were collected over a 24-hour period prior to termination. Analytical 

chamber data indicate there were 40 exposure days; food was removed during the last day of expo-
II-14

Appendix II

sure, and necropsy was performed the next day (34). At termination, rats were sacrificed, blood was 

collected under anesthesia, and hematology, clinical biochemistry, and urinalyses were conducted. 

Data were analyzed by two-way analysis of variance (ANOVA) and Duncan’s multiple t-test. Thymus, adrenal, testis, heart, lung, kidney, spleen, liver, and brain were weighed and fixed in 10% neutral 

buffered formalin, stained with hematoxylin-eosin or PAS-hematoxylin, and examined histologically. 

Clinical signs of toxicity included reduced activity and mild ataxia in the 1,800 ppm rats during exposure. Bodyweight gain was reduced in males and females of the high dose group (1,800 ppm), but food 

intake was not affected. Some statistically significant changes in hematological, blood chemistry, and 

urinalysis parameters were noted in treated rats. The authors stated that most values were within normal ranges but did not specify which values were outside normal limits. Minimal effects on hemoglobin, hematocrit, and red blood cell values were observed for the high-dose group. [The Expert Panel 

considered the toxicological significance of these effects to be unclear]. Significant decreases in 

some serum biochemistry values were observed. [These are considered by the Expert Panel to be 

of no toxicological significance]. Significant increases in male relative organ weights were noted for 

the left adrenal (≥50 ppm), liver and brain (≥300 ppm), and the right kidney and both testes (1,800 

ppm). In the 1,800 ppm females, significant increases in relative organ weights were noted for ovaries, kidneys, and liver; thymus weight was significantly reduced at 50 and 1,800 ppm. [The Expert 

Panel noted that bodyweight was reduced for the 1,800 ppm group; this may have contributed 

to the increase in relative testicular, ovarian, renal, hepatic, and brain weights.] Histopathological evaluations revealed cytoplasmic vacuolation of hepatocytes surrounding the central vein in all 

treated animals, but the effect was not dose-dependent and liver enzymes (ALAT, ASAT) were not 

increased. [Therefore the increased liver weight at doses of 300 ppm and higher were not considered adverse by the authors or the Expert Panel.] Renal tubular casts were seen in females of the 

1,800 ppm group. However, there was no increase in either BUN or creatinine. There were no lesions 

observed in the other organs, including testes. [The Expert Panel agreed with the authors’ conclusion about lack of biological significance for hematology, blood chemistry, and urinalysis findings. 

Given the lack of histopathologic effects in brain, thymus, and adrenal, the Expert Panel did not 

conclude that increased weights of these organs were adverse effects. A NOAEC of 300 ppm was 

selected by the Expert Panel.]

Strength/Weaknesses: These studies used an adequate number of animals in a well-designed experiment. The details of exposure are adequate to assess how the exposures were conducted, and the inhalation procedures conform to standard practices. A weakness was that the fixative used to preserve 

testes is known to be inadequate to properly evaluate subtle histopathological effects.

Utility (adequacy) for CERHR Evaluation Process: This study demonstrates the acute and subchronic 

toxicity of 1-BP under conditions of exposure that are directly comparable to other substances. There is 

a clear dose-response for effects. The study is judged to be adequate for use in the evaluation process.

Two additional repeated-exposure inhalation studies were conducted: a 28-day repeated exposure 

study (45) and a 13-week repeated exposure study (46). The 28-day study was a range-finding study 

from which to select doses for the subsequent 13-week study. Both studies were conducted according 

to GLP. In the 28-day study, male and female 6-week old Sprague-Dawley CD rats (Crl:CD(SD)BR; 

Charles River Canada Inc., St. Constant, Quebec) were divided into 4 groups of 10 animals/sex/

group and exposed to 0, 2.0, 5.0, or 8.0 mg/L [2,000, 5,000, or 8,000 mg/m3, equivalent to 398, 
Appendix II

II-15

993 and 1,590 ppm] 1-BP for 6 hours/day, 5 days/week for 4 consecutive weeks (concentrations 

confirmed by IR spectrometry). Purity of the 1-BP was >99% (47). Exposure concentrations were 

selected on the basis of a 10-day range-finding study. Animals were observed daily, and functional 

tests for neurotoxicity were performed prior to initiation of the study and at termination. Bodyweight 

and feed consumption was measured weekly. Ophthalmologic examination was performed prior to 

study start and termination. Urine samples were collected overnight prior to sacrifice. At termination 

on day 29 (day 1 was the first day of exposure), blood was collected for hematology and clinical biochemistry. Animals were necropsied 3 days after the last exposure. Brains and respiratory systems 

from all dose groups and all tissues from the control and 8.0 mg/L groups were examined microscopically. Data were analyzed for homogeneity using a Bartlett’s test. Homogeneous data were analyzed 

using an ANOVA followed by a Dunnett’s test. Heterogeneous data were analyzed using a KruskalWallis tests followed by a Dunn’s test. Nearly all males (8/10) and a few females (3/10) exposed to 

8.0 mg/L died or were sacrificed in a moribund condition. Animals in the 5.0 mg/L group showed 

clinical signs of toxicity. An abbreviated functional observational battery performed on surviving 

2 male and 7 female rats revealed impaired gait (ataxia and hypotonic gait) in the 8.0 mg/L group. 

These animals may have been in an emaciated condition (6). No sign of neurotoxicity was seen in the 

other groups. Bodyweight and feed consumption were significantly lower for the 8.0 mg/L group. No 

ophthalmologic findings were reported. Hematology for the 8.0 mg/L male group could not be evaluated because only 2 animals survived, but decreased erythrocyte count, hemoglobin, and hematocrit 

values were seen for the 7 surviving females in the 8.0 mg/L group. Erythrocyte count and hemoglobin levels were significantly decreased for the male and female 5.0 mg/L groups. Females in the 

5.0 mg/L group also had lower hematocrit values. [The Expert Panel concluded that no toxicologically significant changes were seen in serum biochemistry or urinalysis.] Relative weights (to 

bodyweight) of the liver, lungs, and kidneys were higher for the 5.0 mg/L male group compared with 

the controls. [The organ weights for the 8.0 mg/L male group could not be evaluated by the Expert Panel because of the high mortality.] Relative weights of the liver, spleen, thyroid/parathyroid 

glands, and kidneys were significantly higher for the 5.0 and 8.0 mg/L female groups compared with 

the controls. Females in the 8.0 mg/L group also had increased relative lung and brain weights, and 

lower thymic weight. Microscopic vacuolation of the brain white matter considered to be chemically related was observed in about 50% of rats in all treated groups (9/20, 11/20, and 11/20 in low 

to high dose groups, respectively). Dose-related, mild-to-moderate, vacuolation of gray matter was 

observed in all rats from the 5.0 and 8.0 mg/L groups, and in 1 animal from the 2.0 mg/L group (48). 

Vacuolation of the spinal cord and lesions of the kidneys and urinary tract and nasal cavity were seen 

in the high-dose animals. Lesions in the bone marrow thymus, spleen, and lymph nodes of high dose 

animals may have been related to treatment. The two surviving males in the high-dose group had 

atrophic changes recorded as hypo/aspermatogenesis (testes fixed in Zenker’s fluid). No ovarian lesions were observed at the high dose.

Strength/Weaknesses: These studies used an adequate number of animals in a well-designed experiment. The details of exposure are adequate to assess how the exposures were conducted, and the 

inhalation procedures conform to standard practices. Testes were fixed in a fixative that permitted 

detailed microscopic evaluation. A weakness is that the majority of tissues from the low- and middose groups were not evaluated for histopathology. 

Utility (adequacy) for CERHR Evaluation Process: This study demonstrates the subchronic toxicity 
II-16

Appendix II

of 1-BP in rats under conditions of controlled inhalation that are directly comparable to other substances. There is a clear dose-response for histopathologic effects in the nervous system. The study is 

judged to be adequate for use in the evaluation process.

A 13-week repeated exposure study (46) was conducted in which male and female 7−7.5-week-old 

Sprague-Dawley CD rats (Crl:CD(SD)BR; Charles River Canada Inc., St. Constant, Quebec) were 

divided into 5 groups of 15 animals/sex/group and exposed to 0, 0.5, 1.0, 2.0, or 3.0 mg/L [500, 

1,000, 2,000, or 3,000 mg/m3, equivalent to 99, 199, 397 and 596 ppm] 1-BP for 6 hours/day, 5 

days/week for 13 consecutive weeks (concentrations monitored by IR spectrometry and confirmed 

by GC). Purity of 1-BP was >99% (47). Exposure concentrations were selected based on the results 

of the 28-day study. Animals were observed daily, and functional tests for neurotoxicity were performed prior to study start and during weeks 4, 8, and 13. Bodyweight and feed consumption were 

measured weekly. Ophthalmologic examination was performed prior to study start and at termination. Urine samples were collected overnight prior to sacrifice. At termination, 3 days after the 

last exposure, blood was collected for hematology and clinical biochemistry. All tissues from the 

control and high-dose groups were examined microscopically; respiratory tissues and tissues with 

lesions were examined at all doses. Data were analyzed for homogeneity using a Bartlett’s test. Homogeneous data were analyzed using an ANOVA followed by a Dunnett’s test. Heterogeneous data were 

analyzed using a Kruskal-Wallis test followed by a Dunn’s test. No clinical signs were observed that 

could be ascribed to 1-BP. No evidence of neurotoxicity was apparent. No differences in bodyweight 

were noted; feed consumption was significantly lower for the high-dose female group only during 

weeks 3 and 4. No ophthalmologic findings were reported. No toxicologically significant effects were 

seen in hematology, clinical biochemistry, or urinalysis. A concentration-related increase in relative 

liver weight was seen for males with the liver weight of the 3.0 mg/L group significantly greater than 

controls. No liver weight effect was seen for female rats. Treatment-related vacuolation of the liver 

was observed in 3/15 and 6/15 male rats at the 2.0 and 3.0 mg/L dose, respectively, and 1/15 female 

rats at the 2.0 mg/L dose. This lesion was characterized as a diffuse slight to mild vacuolation in the 

centrolobular region of the liver. The vacuolation in brain tissue, observed at higher doses in the 28-

day study was not observed in this study. No testicular or ovarian effects were noted (testes fixed in 

Zenker’s fluid). The study authors identified a no observed effect concentration (NOEC) of 1.0 mg/L 

(1,000 mg/m3) based on liver histopathology.

Strengths/Weaknesses: This is a well-conducted study according to current guidelines and practices. 

Sufficient numbers of animals were used to evaluate the potential effects of subchronic exposure. 

There are no perceived weaknesses. However, the lack of perfusion with a fixative appropriate for 

neurohistopathologic evaluation reduces the utility of this study to detect subtle microscopic effects 

in the nervous system.

Utility (adequacy) for CERHR Evaluation Process: This study is adequate to assess the potential 

subchronic systemic toxicity and functional neurotoxicity of inhaled 1-BP. 

Several studies have evaluated the potential neurotoxicity of 1-BP. 

In a short communication, Yu et al. (49) reported the results of a study in which 10-week old male 

Wistar rats (9 per group from Shizuoka Laboratory Animal Center) were exposed to a concentration 

 
Appendix II

II-17

of 1,000 ppm [5,031 mg/m3] 1-BP (99.4% purity) or filtered air in a chamber for 8 hours/day for 

up to 7 weeks as a companion group for a study of 2-BP. Exposures were conducted 7 days/week 

(50). This study by Yu et al. (49) was reported in greater detail by Yu et al. (51). The exposure 

concentrations were monitored and confirmed by GC. Parameters examined included motor nerve 

conduction velocity (MCV), distal latency (DL), and histopathology. Hematology was examined in 

5 rats/group. Organs examined histologically included testis, epididymis, prostate, seminal vesicle, 

femur, liver, kidney, heart, lung, thymus, brain, and sciatic or tibial nerves. Data were analyzed by 

ANOVA followed by the Tukey-Kramer multiple comparison method. By the fifth week of exposure, 

6 of 9 treated animals demonstrated altered locomotor activity with paddle-like gait and hindlimb 

paralysis. All treated animals exhibited hind-limb paralysis by the sixth week of exposure. Because 

the treated rats began showing signs of paralysis and emaciation, 4 exposed animals were sacrificed 

following 5 weeks of exposure, and the remaining 5 plus 5 unexposed controls were sacrificed after 7 

weeks. MCV was significantly reduced in exposed animals, and there was degeneration of peripheral 

nerves particularly of the myelin sheath. Sections of peripheral nerve were dissected from the tibial 

nerve and preserved in osmium tetroxide following fixation with 10% formalin. Histopathological 

evaluation of the nervous system revealed degeneration of the peripheral nerve and axonal swelling in the gracilis of the spinal cord. No histopathological effects were noted in the testis (fixed in 

Bouin’s solution and stained with periodic acid-Schiff’s reagent), liver, kidney, or bone marrow, and 

there were no changes in hematology parameters. Serum creatine kinase was significantly reduced in 

exposed animals. The authors concluded that 1-BP was a more potent nervous system toxicant, but 

less potent reproductive and hematopoietic system toxicant than 2-BP.

Strength/Weaknesses: A strength of this study is that appropriate methods were used for histopathologic evaluation of the nervous system and testes. A weakness is that the numbers of animals evaluated 

was minimal although it was adequate to draw reliable conclusions.

Utility (adequacy) for CERHR Evaluation Process: This study provides good histopathologic evidence for 1-BP-induced neurotoxicity and the lack of testicular effects.

Ichihara et al. (52) conducted a study to examine the dose- and duration- neurotoxicity response to 

1-BP exposure. Eleven 10-week-old male Wistar rats/group (from Shizuoka Laboratory Animal 

Center) were exposed to air or 200, 400, or 800 ppm [1,006, 2,012, or 4,025 mg/m3] 1-BP vapors 

8 hours/day for 12 weeks. Exposures were conducted 7 days per week under dynamic conditions 

(50). The highest nominal concentration was based on preliminary studies that noted debilitation of 

rats exposed to 1,000 ppm. Chamber concentrations were measured by GC. Neurological function 

was tested in 9 rats/group at weeks 0, 4, 8, and 12. Data were analyzed using one-way ANOVA followed by Dunnett’s method. Mean bodyweights for the 400 and 800 ppm groups were significantly 

lower than controls after 8 weeks of exposure. Significant decreases in hindlimb grip strength were 

observed for all groups at 4 weeks, and for the 800 ppm group at 8 and 12 weeks. Hindlimb grip 

strength was also decreased for the 400 ppm group at 12 weeks. Significant decreases in forelimb 

grip strength were seen for the 400 and 800 ppm groups at 8 weeks, and for the 800 ppm group at 12 

weeks. [The Expert Panel only considered reductions in grip strength to be treatment-related if 

they were statistically significant and consistently related to duration of treatment. Therefore, 

reductions in hindlimb grip strength and forelimb grip strength were considered treatment 

related at ≥400 ppm and 800 ppm, respectively.] MCV was reduced for the 800 ppm group at weeks 
II-18

Appendix II

8 and 12, and distal latency (DL) was increased for this group at weeks 4, 8, and 12. The rats in the 800 

ppm group also displayed weak kicking and an inability to stand on a slope. At sacrifice, brain weight 

and blood chemistry were analyzed from 9 animals per group. At necropsy, two animals from each 

group were perfused for neurohistopathology with either 10% formalin or Zamboni’s solution (one for 

each fixative). Muscular nerves were dissected out and post-fixed in osmium tetroxide. The weights 

of the cerebrum and gastrocnemius muscle were significantly reduced for the 800 ppm group. No differences in weight were seen for other parts of the brain or soleus muscle. Plasma creatinine phosphokinase activities for the 400 and 800 ppm groups were significantly reduced compared with controls. 

No changes were seen in the activities of lactate dehydrogenase, aspartate transaminase, alanine 

transferase, or alkaline phosphatase. Serum cholesterol was reduced in a dose-dependent manner, and 

plasma total protein and albumin were increased in a dose-related manner. Significant differences 

in cholesterol, aspartate transaminase, and alanine transaminase were seen for the 400 and 800 ppm 

groups. Plasma globulin levels were also significantly increased for the 800 ppm group. Morphological evidence of neurotoxicity was only noted in the high dose group (800 ppm) and included ovoid or 

bubble-like debris in myelin sheaths of peripheral nerves, swelling of preterminal axons of the gracile 

nucleus, and irregular banding of soleus muscle fibers. There was no degeneration or vacuolation of 

brain tissue. Authors noted that reductions in grip strength could not be explained by adverse changes 

in the nervous system alone, in that grip strength represents total vital factors in limb function. In 

comparing the result of this study to those obtained in a preliminary study with 2-BP, the authors concluded that 1-BP is a more potent neurotoxicant than 2-BP and is potentially neurotoxic to humans. 

[The Expert Panel determined a subchronic inhalation neurotoxicity NOAEC of 200 ppm.]

Strength/Weaknesses: Concentration-related changes were observed in a thorough study of neurotoxicity. The fixation procedures were appropriate for adequate microscopic evaluation of nerves and 

muscles. A weakness is that the numbers of animals evaluated was minimal, especially for neurohistopathology. The number of animals for functional assessment was deemed to be sufficient for 

adequate conclusions to be drawn. Another weakness is that the grip strength data were not analyzed 

using a repeated-measures analysis. The lack of repeated measures analysis does not invalidate the 

conclusions concerning exposure-related effects.

Utility (adequacy) for CERHR Evaluation Process: The data adequately define neurotoxicity in animals inhaling high concentrations of 1-BP. This information is useful for hazard assessment of 1-BP.

Zhao et al. (53) compared the neurotoxicity of 1-BP, 2-BP, and 2,5-hexanedione (2,5-HD) administered 

separately to rats. Seven to nine male Wistar rats/group (age not specified; from Seiwa Experimental 

Animal Institute) were injected subcutaneously (sc) with each chemical in olive oil once/day, 5 days/

week, for 4 weeks. Doses administered were 3.7 or 11 mmol/kg bw 1-BP [455 or 1,353 mg/kg bw]; 1.1, 

3.7, or 11.0 mmol/kg bw 2-BP [135, 455 or 1,353 mg/kg bw]; and 2.6 mmol/kg bw 2,5-HD [296 mg/

kg bw]. Purity of all chemicals was >97%. A control group of nine rats was injected with the olive oil 

vehicle. According to the study authors, doses of 1.1, 3.7, and 11 mmol/kg bw are calculated to be equivalent to doses received by inhalation of 100, 300, and 1,000 ppm BP over an unspecified time period. 

Calculations were based upon respiratory data reported in a study by Mauderly et al. (54). Bodyweights 

were measured weekly. MCV and motor latency (ML) were measured every 2 weeks using an electrophysiological method. Data were analyzed by one-way ANOVA followed by Duncan’s multiple range 

test. Bodyweight gain in the 11 mmol 1-BP/kg bw group was lower than the control group. By 2 weeks 
Appendix II

II-19

of exposure, the MCV began decreasing in treated rats and reached statistical significance in the 11 

mmol 1-BP/kg bw group at week 4. Increases in ML occurred, but were not statistically significant. 

All three compounds, 2-BP, 1-BP, and 2,5-hexanedione, produced qualitatively similar responses in 

MCV and ML. The authors concluded that 1-BP and 2-BP administered parenterally were equally 

potent neurotoxicants and both compounds were less potent neurotoxicants than 2,5-hexanedione.

Strength/Weaknesses: This study utilized a reference neurotoxicant (2,5-hexanedione) for comparison of MCV and ML. Sufficient numbers of animals were used for comparison, and varying 

dose levels were used to establish a dose-response. A weakness is the calculation of the dose to be 

administered based on calculations for inhalation of vapors in laboratory animals. In the absence 

of pharmacokinetic information, these can only be estimates of absorbed dose. Based on previous 

information indicating that a significant amount of 1-BP is exhaled unmetabolized, the calculated 

amounts of absorbed dose are likely to have been overestimated. 

Utility (adequacy) for CERHR Evaluation Process: The utility of this study for the evaluation process 

is unclear. Although there are interesting data provided, the basis for dose selection cannot be verified. 

Therefore, the value of the study in human health hazard assessment is unclear.

Fueta et al. (55) reported in a short communication changes in neuronal excitability in the brain of Wistar rats inhaling 1-BP for 6 hours/day, 5 days per week, for up to 4 weeks (under dynamic conditions). 

A total of 30, 6-week-old male rats were exposed to 1,500 ppm [7,546 mg/m3] 1-BP vapors [purity 

not specified] or air (n=14−16/exposure condition) for 6 hours/day, 5 days/week for 1, 3, or 4 weeks. 

Some animals exposed for 4 weeks were allowed to recover for 1 week prior to termination. This study 

is a follow-up to that reported by Ohnishi et al. (56) [Not available in English.] Transverse hippocampal slices were prepared following exposure for 1, 3, and 4 weeks and following a 1 week recovery 

period in rats exposed for 4 weeks. Brain slices were incubated in artificial cerebrospinal fluid during 

the stimulation of neurons and measurement of paired-pulse population spike (PS) responses in the 

granule cell layer of the dentate gyrus. When two pulses separated by a 10 msec interval were applied, 

a strong depression of the second PS was observed in control rats, but a nearly complete second PS 

response was seen in the 1-BP-treated rats. Paired-pulse ratios (PPR) were calculated by dividing the 

second PS by the first PS at interpulse intervals (IPI) ranging from 5−1,000 msec. PPRs significantly 

increased in all treated rats when interpulse intervals ranged from 5 to 20 msec. At interpulse intervals 

ranging from 500 to 1,000 msec, significant increases in PPRs were only observed in rats exposed to 

1-BP for 4 weeks, with and without the 1-week recovery period, although the magnitude of the difference after recovery was lower. Ataxic gait and convulsions were observed in the rats during the fourth 

week of exposure. The authors concluded that changes in the CNS (dentate gyrus), in conjunction with 

peripheral nerve damage, may explain neurobehavioral changes. The authors imply that adverse effects were observed in the testes, although no data are presented. 

Strength/Weaknesses: This study reports on time-related changes in the CNS that can be correlated 

with behavioral changes in animals. A strength of the study is that the exposure regimen conforms to 

standard practices, although details of monitoring the chamber concentrations were lacking. Another 

weakness is that no dose-response information is available.

Utility (adequacy) for CERHR Evaluation Process: The adequacy of these data to the evaluation 
II-20

Appendix II

process is unclear. Effects were observed in the CNS before alterations in behavior were seen. Thus 

the correlation of CNS effects with behavioral changes is lacking. There is some evidence for recovery following cessation of exposure.

In a study that focused on reproductive toxicity, Ichihara et al. (57) exposed 10-week-old male Wistar 

rats to 0, 200, 400, or 800 ppm [1,006, 2,012, or 4,025 mg/m3] 1-BP vapors for 8 hours/day for 12 

weeks (8−9 animals per group). The exposure concentrations were monitored and confirmed by GC. 

Exposures were conducted 7 days per week under dynamic conditions (50). Bodyweight gain was 

reduced in the 400 and 800 ppm groups. Significant changes included increased relative liver weight 

(400 and 800 ppm) and absolute liver weight (800 ppm), and decreased absolute spleen weight (800 

ppm). Histological effects observed in the livers of rats in the 800 ppm group included scanty spots 

in the cytoplasm of cells that were possibly glycogen, and reduced number and size of fat droplets 

around the central vein. There were no histopathological effects on the other non-reproductive organs 

examined (adrenal, thymus, spleen, lungs, heart, pituitary, and kidney). The only significant hematological effects noted were increased mean corpuscular volume at 800 ppm and decreased mean 

corpuscular hemoglobin concentration at 400 and 800 ppm. Blood chemistry was not evaluated. A 

detailed description of reproductive findings and other study details is included in Section 4. [The 

Expert Panel determined 200 ppm to be a subchronic inhalation systemic NOAEC in rats.]

Strength/Weaknesses: This study provides dose-response information for general toxicity and identifies a systemic NOAEC in male rats following repeated exposure. A weakness is that the numbers of 

animals evaluated was minimal although adequate to draw conclusions. 

Utility (adequacy) for CERHR Evaluation Process: This study is the first to have identified adverse 

effects of 1-BP inhalation on the male reproductive tract. The utility of the Ichihara et al. (57) study 

is discussed below in Section 4 on Reproductive Toxicity.

In a study sponsored by the BSOC, WIL Research Laboratories (58) evaluated the potential adverse 

effects of 1-BP whole-body inhalation exposure in F0 and F1 parental rats. The reproductive toxicity endpoints are discussed later in this document (Section 4). Groups of 25 male and female Crl:

CD(SD)IGS BR rats were exposed to filtered air or 100, 250, 500, or 750 ppm [0, 503, 1,257, 2,514, 

3,771 mg/m3] 1-BP vapors (99.8% purity) for 6 hours/day, 7 days/week. Exposure concentrations 

within each chamber were measured 9−10 times during each exposure period by a validated GC 

method. Exposure of F0 rats commenced at 7 weeks of age and F1 rats began direct exposure at 

weaning. Exposures were conducted for at least 70 days prior to mating. Females were not exposed 

on postnatal days (pnd) 0-4 and only they, not their litters, were exposed during pnd 5−21. Therefore, offspring (litters) were indirectly exposed to the test chemical in utero and through nursing. In 

addition, the F1 pups selected randomly for propagation of F2 litters were directly exposed from pnd 

22 forward. Significant reductions in cumulative weight gain of about 12% were noted in F0 males 

in the 750 ppm group throughout the study, while food consumption was increased in the same 

group. Weekly bodyweight gains were significantly reduced in F1 males of the 500 ppm group. In 

contrast, bodyweights of F0 females were significantly depressed only at treatment weeks 7 and 8 

in the 750 ppm group, while the food consumption of females in both the 500 and 750 ppm groups 

also increased throughout the 10-week treatment period. In addition, bodyweights were significantly 

lower in pregnant F0 females at gestation day (gd) 20 in the 250 mg group, and at gd 14 and 20 in the 
Appendix II

II-21

500 ppm group. The latter difference persisted throughout lactation. No clinical signs of toxicity were 

observed in the F0 or F1 generations. Significant reductions in absolute but not relative brain weight 

were seen in F1 males (≥100 ppm), F0 males (≥250 ppm), and F0 and F1 females (≥500 ppm). Significant increases in relative liver weight were seen in F0 males and F1 males and females (≥500 ppm) and 

F0 females (750 ppm). Absolute thymus weights were increased in F1 males exposed to ≥250 ppm, but 

no histological lesions were reported. 

Upon termination of each generation, males and females underwent necropsy. All organs were preserved in 10% buffered formalin for microscopic evaluation. The study was conducted in compliance 

with GLP. For the F0 generation, exposure-related effects were seen in the liver, kidneys, and spleen. 

Minimal-to-mild centrilobular hepatocellular vacuolation was noted in males from the 250, 500, and 

750 ppm groups (7/25, 22/25, 24/25), and females from the 500 and 750 ppm groups (6/24, 16/25). 

Female rats were also observed to have increased glycogen in the liver. The liver lesions were considered to be not adverse by the authors. Minimal pelvic mineralization of the kidneys was seen in 

250, 500, and 750 ppm males (1/25, 2/25, 6/25), and minimal-to-mild mineralization of the kidneys 

in 250, 500, and 750 ppm females (5/25, 12/24, 14/25). Brown pigment was observed with increasing severity in the spleen of 250, 500, and 750 ppm male and female rats. Histopathologic evaluation 

of the brain did not indicate any treatment-related lesions. [Therefore reductions in absolute brain 

weight were not considered to be adverse effects by the Expert Panel.]

For the F1 generation, exposure-related effects were also seen in the liver, kidneys, and spleen. Minimal-to-mild centrilobular hepatocellular vacuolation was noted in males from the 250 and 500 ppm 

groups (15/25 and 23/25), and females from the 250 and 500 ppm groups (2/25 and 6/25). Female 

rats were also observed to have increased glycogen in the liver. The liver lesions were considered to be 

“not adverse” by the authors. Minimal-to-mild pelvic mineralization of the kidneys was seen in 500 

ppm males (3/25), and minimal to mild mineralization of the kidneys in 250 and 500 ppm females (7/

25 and 8/25). Brown pigment was observed with increasing severity in the spleen of 500 ppm female 

rats. Lesions of the reproductive tract are discussed in Section 4 (Reproductive Toxicity).

[The Expert Panel identified a lowest observed adverse effect concentration (LOAEC) for systemic toxicity of 250 ppm based on effects in kidneys of the F0 and F1 generations. The NOAEC 

was 100 ppm.]

Strength/Weaknesses: This study provides additional information on the histopathologic effects following exposure during the prenatal, perinatal, and adult periods. The methods used were appropriate 

and the study was well-conducted. A weakness is that the method of tissue fixation was not optimal 

to detect subtle lesions in nervous tissue. 

Utility (adequacy) for CERHR Evaluation Process: This study is adequate and useful to evaluate the 

effects of prolonged exposure to 1-BP.
II-22

Appendix II

2.3 Genetic Toxicity

Barber et al. (59) examined the mutagenicity of 1-BP in Salmonella strains TA1535, TA1537, TA1538, 

TA98, and TA100 with and without S9 (from Arochlor-induced rat livers) metabolic activation. The 

protocol employed a closed, inert incubation system designed to test volatile compounds. Five concentrations ranging from 1.1 to 20.3 μmole/plate [135−2497 μg/plate] were tested in a total of 5 

replicates. Reference mutagens included methyl-N-nitro-N’-nitrosguanidine, 2-aminoanthracene, 

9-aminoacridine, and picrolonic acid. Control cultures were incubated without the addition of any 

chemicals. 1-BP treatment increased the mutation frequency in strains TA1535 and TA100 with and 

without metabolic activation. It does not appear that cytotoxicity occurred at the highest concentration. Negative results were obtained in all other strains. Authors noted that for 1-BP, the closed 

method of testing is a superior technique for assessing mutagenicity in volatile compounds because 

previous testing according to the standard plate method gave negative results. 

Strength/Weaknesses: This study provides information of genetic toxicity in relevant strains of 

bacteria. The study was well conducted and used techniques for exposure to vapors. There are no 

perceived weaknesses.

Utility (adequacy) for CERHR Evaluation Process: The study provides evidence that 1-BP can induce mutations in prokaryotes with or without metabolic activation. It is of interest that mutagenic 

events were observed only in strains TA1535 and TA100, not in other strains. Strains TA100 and 

TA1535 are known to possess nascent glutathione transferase (GST) activity (60, 61), which may be 

linked to the mutations observed.

Elf Atochem (62) examined the mutagenicity of 1-BP (>99% purity) in Salmonella strains TA1535, 

TA1537, TA1538, TA98, and TA100 with and without S9 (from male Sprague-Dawley rats induced 

with Aroclor 1254) metabolic activation. Culture plates were incubated in closed stainless-steel 

vessels. The test substance was introduced into the culture using dimethyl sulfoxide (DMSO) as 

the vehicle. Concentrations ranging from 100 to 10,000 μg/plate were used. A concentration of 

10,000 μg/plate was cytotoxic as noted by partial sparcity of background lawn. DMSO was used as 

a negative control. Reference mutagens included sodium azide, 2-aminoanthracene, 2-nitrofluorene, 

and 9-aminoacridine. Control cultures were incubated without the addition of any chemicals. There 

was no evidence of mutagenicity in any strain either with or without S9. The study was conducted 

according to GLP standards. 

Strength/Weaknesses: This study provides information of genetic toxicity in relevant strains of 

bacteria. The study was well conducted and used techniques for exposure to vapors. There are no 

perceived weaknesses.

Utility (adequacy) for CERHR Evaluation Process: The study provides additional evidence that 1-BP 

does not induce mutations with or without metabolic activation. It is of interest that mutagenic events 

were not observed in strains TA1535 and TA100 in contrast with the results of Barber et al (59). 

Kim et al. (34) examined the mutagenicity of 1-BP in Salmonella strains TA98, TA100, TA1535, and 

TA1537 and E coli strain Wp2uvrA with and without S9 (from male Sprague-Dawley rats induced 

with Aroclor 1254) metabolic activation. [It was not specified if the protocol employed a closed 
Appendix II

II-23

incubation system designed to test volatile compounds.] Five concentrations ranging from 313 to 

5,000 μg/plate were tested. Reference mutagens included sodium azide, 2-aminoanthracene, 9-aminoacridine, and 2-(2-furyl)-3-(5-nitro-2-furyl) acrylamide. [A negative control was also examined but 

the solvent used was not specified.] 1-BP treatment did not increase the frequency of mutations at 

any dose studied. [Cytotoxicity was not reported by the study authors.]

Strengths/Weaknesses: The tests used appropriate strains of bacteria and employed positive and 

negative control chemicals. The failure to describe if a closed incubation system was used interjects 

some uncertainty in the interpretation of the negative results.

Utility (adequacy) for CERHR Evaluation Process: This study provides a third source of data where 

1-BP was tested in an in vitro microbial system.

Elf Atochem (63) examined the mutagenicity of 1-BP in L5178Y mouse lymphoma cells. The cells 

were treated for 3 hours with 125−1,500 mg/L 1-BP (99.3% purity) in the absence of metabolic 

activation or 125−2,500 mg/L 1-BP with S9 (from rats treated with Aroclor 1254) activation. The 

vehicle, DMSO, was used as a negative control. Methylmethane sulfonate and cyclophosphamide 

were used as reference mutagens. The highest concentration (2,500 mg/L) produced 100% cytolethality while the 2,000 mg/L concentration produced ∼40–90% cytolethality, as assessed by 

relative cloning efficiency. A reproducible two-fold increase in mutation frequency compared to 

the concurrent control and/or evidence of a dose relationship were considered indicative of a positive response. Two separate experiments were conducted. In the absence of metabolic activation, a 

reproducible increase in mutation frequency was observed in cells treated with 1,000–1,500 mg/L 

1-BP in both experiments. No increase in mutation frequency was observed in the first experiment 

with S9 activated cells. However, in the second experiment with S9 activated cells, an increase in 

mutation frequency was noted at 1,500–2,000 mg/L 1-BP. Study authors concluded that this study 

demonstrated mutagenic activity, especially in the absence of S9 activation.

Strengths/Weaknesses: This is a well conducted study to evaluate the potential of 1-BP to cause mutations in mammalian cells. The study was conducted according to current guidelines and accepted 

practices. There are no perceived weaknesses.

Utility (adequacy) for CERHR Evaluation Process: These data provide evidence of mutagenic activity in a mammalian cell line. In order to draw conclusions concerning the genotoxicity of 1-BP, these 

data must be viewed with other genetic toxicity data and metabolism data.

Elf Atochem (64) conducted a micronucleus study of 1-BP in bone marrow of mice. In the initial 

study, male and female Swiss OF1/ICO:OF1 (IOPS Caw) mice from Iffa Credo were treated twice 

with 0, 100, 400, or 800 mg/kg 1-BP (99.3%) in corn oil by ip injection. Cyclophosphamide was used 

as a reference clastogen. At least 5 animals/sex/group were used. Animals were killed 24 hours after 

the last treatment. The initial toxicity study indicated that 800 mg/kg would be a suitable high dose, 

and a second study was conducted with 0 and 800 mg/kg 1-BP. Mortality in males during the second 

study prompted a third study using an additional dose level of 600 mg/kg for males. Only the 600 mg/

kg males and 800 mg/kg females were evaluated because the polychromatic/normochromatic erythrocyte (PE/NE) ratio for the controls from the initial attempt (100, 400, 800 mg/kg) were outside of 
II-24

Appendix II

the historic range and the test was considered invalid. No increase in micronucleated erythrocytes 

in bone marrow was observed in males treated with 600 mg/kg or in females treated with 800 mg/

kg. The group treated with cyclophosphamide demonstrated a significant increase in micronucleated 

erythrocytes.

Strength/Weaknesses: This study provides information of the lack of 1-BP genetic toxicity in vivo. 

The study was well conducted and there are no perceived weaknesses.

Utility (adequacy) for CERHR Evaluation Process: The study indicates that parenteral injection of 

1-BP in mice failed to induce clastogenicity.

Kim et al. (34) conducted a micronucleus assay by exposing 10 Sprague-Dawley rats/sex/group to 

0, 50, 300, or 1,800 ppm [0, 252, 1,509, or 9,055 mg/m3] 1-BP vapors for 6 hours/day, 5 days/week, 

for 8 weeks. After treatment was complete, the rats were sacrificed and bone marrow was examined 

to determine the frequency of micronucleated polychromatic erythrocytes. 1-BP treatment did not increase the frequency of micronucleated polychromatic erythrocytes. The rats used in this experiment 

were apparently from the study described in Kim et al. (44). In that study, toxicity was observed at 

the highest dose (1,800 ppm) and consisted of decreased bodyweight and ataxia. 

Strengths/Weaknesses: This is a study of appropriate design and was adequately reported.

Utility (adequacy) for CERHR Evaluation Process: The study is of significant utility given that the 

route of exposure is directly relevant to human health risk assessment. The Kim et al. (34) results enhance confidence in the negative finding in the Elf Atochem (64) study where 1-BP was administered 

parenterally.

2.4 Carcinogenicity

No bioassays for carcinogenicity of 1-BP were identified. 

2.5 Potentially Sensitive Sub-populations 

There are no data available to evaluate the sensitivity of populations based on gender, age, or genotype.

2.6 Summary of General Toxicological and Biological Parameters

Toxicokinetics 

No information concerning the toxicokinetics of 1-BP in humans was found. Evidence from animal 

data indicates that 1-BP can be absorbed into the systemic circulation following inhalation exposure. 

The blood:air partition coefficient indicates that 1-BP is readily soluble in blood (30). However, a 

major portion of absorbed 1-BP is exhaled (excreted in the expired air) unchanged (38). Metabolism 

of 1-BP can occur through the mixed function oxidase (MFO) system (17) and via conjugation with 

glutathione (31, 37, 38). The available data suggest that metabolism via MFO enzymes is slow and 

may be easily saturable. Conjugation with glutathione can occur either enzymatically or non-enzymatically producing several cysteine conjugates that are excreted in the urine. Whether glutathione 

S-transferases are involved in the activation of 1-BP to a reactive species is unclear, although the 
Appendix II

II-25

data from mutagenicity tests suggests that such activation can occur (59-61). This suggests that 

conjugation with glutathione and glutathione S-transferases may play a role in the toxicity of 1-BP. 

General Toxicity

Limited human data were found. One case report indicated peripheral neuropathy in a worker exposed 

to a degreasing and cleaning solvent containing 95.5% 1-BP (39). This study was considered unusable. 

NIOSH conducted a survey of workers exposed to 1-BP dividing them into groups of ‘low’ (117 ppm, 

[585 mg/m3]), ‘medium’ (170 ppm, [850 mg/m3]), or ‘high’ (197 ppm, [985 mg/m3]) exposure (40). 

The authors suggested that no adverse health effects were associated with repeated occupational exposures at these concentrations. [The Expert Panel considered the data to be inconclusive.]

Data in Wistar rats indicate that the acutely lethal concentration is >30,200 mg/m3 [6,003 ppm] (43). 

There may be a difference in the LC50 for Wistar rats compared with Sprague-Dawley rats (44) suggesting intraspecies variability. Hepatocyte vacuolation around the central vein was observed in animals exposed for one 4-hour period (44). Pulmonary edema was observed following acute exposure 

to lethal concentrations (>30,200 mg/m3 [6,003 ppm]) (43). Repeated exposure to concentrations of 

≥400 ppm [2,012 mg/m3] result in adverse effects to the peripheral nervous system, possibly striated 

muscle, and liver (52, 57). Peripheral nervous system and muscular effects are associated with ataxia, 

altered gait, and decreased grip strength. One study also identified lesions in the brain (gray and white 

matter vacuolation) following 28 days of exposure to relatively high concentrations (45). These lesions 

were not observed in other studies of longer duration and lower concentration (46, 58). The Expert 

Panel concluded that the method of fixation used in the 13-week study (46) was not optimal for evaluation of neurohistopathology. Liver effects are defined by minimal to mild centrilobular hepatocyte 

vacuolation in male rats, but with little other evidence of adverse effect. This lesion is considered to be 

reversible, and in the absence of other signs of hepatotoxicity was considered to be adaptive. No effect 

levels for systemic toxicity of ∼100–400 ppm (∼500–2,000 mg/m3) have been reported in repeat-dose 

studies of rats. Table 2-1 summarizes NOEC values and effects observed in animal general toxicity 

studies. Testicular and ovarian toxicity has been reported and are discussed in Section 4 on Reproductive Toxicity.

Genetic Toxicity

The genetic toxicity of 1-BP has been tested in S. typhimirium strains TA98, TA100, TA1535, TA1537, 

and TA1538 (34, 59, 62). Positive results were reported only for TA100 and TA1535 in one study (59), but 

no increase in revertants was observed in two other studies (34, 62). The TA100 and TA1535 strains 

are known to possess GST activity that may result in the metabolism of 1-BP to a reactive metabolite (60, 61). Because direct evidence of such a reactive metabolite is not available, this hypothesis 

is speculative. A mouse micronucleus test (64) and rat micronucleus test (34) of 1-BP were negative. 

Positive results were obtained in a mutagenicity assay in cultured L5178Y mouse lymphoma cells 

(63); however, the increase in mutation frequency was noted at cytotoxic concentrations.

Carcinogenicity

There are no data available on the potential carcinogenicity of 1-BP in humans or animals.

Sensitive Subpopulations

There are no data available to evaluate the sensitivity of populations based on gender, age, or genotype.
II-26

Appendix II

Table 2-1. Summary of General Toxicity Effects in Inhalation Studies

Concentration 

in ppm (mg/m3)

Exposure

Regimen 

Species

Strain

Sex

Concentration: Effect Reference

6,003 (30,200)

6,879 (34, 600)

6,997 (35,100)

7,355 (37,000)

8,448 (42,500)

4h/1d

Nose-only

Wistar rat, 

M & F

NOEC = 6,003 ppm (30,200 mg/m3)

6,879 ppm (34,600 mg/m3): 

Mortality in 3/10

6,997 ppm (35,100 mg/m3): 

Mortality in 7/10

7,355 ppm (37,000 mg/m3): 

Mortality in 10/10 

Elf Atochem 

(43)

11,000 (55,337)

13,000 (65,398)

15,000 (75,460)

17,000 (85,521)

4h/1d

Whole-body

SpragueDawley rat, 

M & F

NOEC = 11,000 ppm (55, 337 mg/m3)

17,000 ppm (85,521 mg/m3): 

Mortality in 10/10; number of deaths dose-related 

at lower concentrations 

Kim et al. 

(44)

398 (2,000)

993 (5,000)

1,590 (8,000)

6h/5d/4wk

Whole-body

SpragueDawley rat, 

M & F

398 ppm (2,000 mg/m3): 

Vacuolation of the brain 

(1/20 gray matter; 9/20 white matter)

993 ppm (5,000 mg/m3): 

↓RBC, hemoglobin, hematocrit 

↑Relative liver, spleen, thyroid/parathyroid, and 

kidney weights 

Vacuolation of the brain z

(11/20 white and 20/20 gray matter)

1590 ppm (8,000 mg/m3): 

Mortality (8/10 M; 3/10 F)

Ataxia and hypotonic gait 

Vacuolation of brain (11/20 white and 20/20 gray 

matter) and spinal cord

Kidney lesions

Atrophic changes in testis

ClinTrials 

(45)

50 (252)

300 (1,509)

1,800 (9,055)

6h/5d/8wk

Whole-body

SpragueDawley rat, 

M & F

NOAEC = 300 ppm (1,509 mg/m3) 

1,800 ppm (9,055 mg/m3): 

Ataxia, ↓ activity, ↓ bodyweight gain; 

Renal tubular casts

Kim et al. 

(44)

99 (500)

199 (1,000)

397 (2,000)

596 (3,000)

6h/5d/13wk

Whole-body

SpragueDawley rat, 

M & F

NOEC = 199 ppm (1,000 mg/m3)

397 ppm (2,000 mg/m3): 

Slight centrilobular vacuolation of the liver

596 ppm (3,000 mg/m3): 

↑Relative liver weight (M) and slight to mild centrilobular vacuolation of the liver 

ClinTrials 

(46)

1,000 (5,031) 8h/7d/7wk

Whole-body

Wistar rat, 

M

Hind-limb paralysis, paddle-like gait 

↓Creatine kinase activity, ↓MCV 

Degeneration of myelin sheath and peripheral nerve, 

axonal swelling of gracilis of the spinal cord

Yu et al. 

(49, 51)

200 (1,006)

400 (2,012)

8h/7d/12wk

Whole-body

Wistar rat,

M

NOAEC = 200 ppm (1,006 mg/m3)*

400 (2,012 mg/m3): 

↓Bodyweight; hind-limb grip strength 

↓Creatinine phosphokinase activity

↑Relative liver weight

Ichihara et al.

(52, 57
Appendix II

II-27

800 (4,025) 8h/7d/12wk

Whole-body

Wistar rat,

M

800 ppm (4,025 mg/m3): 

↓Bodyweight 

↓Fore-limb and hind-limb grip strength 

↓Motor nerve conduction velocity 

↑Distal latency 

↑Relative and absolute liver weight, 

↓Spleen weight 

↓creatinine phosphokinase activity 

Ovoid or bubble-like debris in myelin sheaths of 

peripheral nerves, swelling of preterminal axons 

of the gracile nucleus, and irregular banding of 

soleus muscle fibers 

Cytoplasmic spots in liver.

Ichihara et al.

(continued)

100 (503)

250 (1,257)

500 (2,514)

750 (3,771) 

[F0 only]

6h/7d/10wk

prior to mating and during gestation 

and lactation.

Whole body.

SpragueDawley Rat, 

M & F

NOEC = 100 ppm (503 mg/m3) *

250 ppm (1,257 mg/m3): 

No clinical signs of toxicity (F0 or F1 generations) 

↓in absolute but not relative brain weight (F1 M) 

↑absolute thymus weights F1 males (no lesions 

reported) 

centrilobular hepatocellular vacuolation (M) 

↑liver glycogen (F) 

↑renal pelvic mineralization (M&F F0, F F1) 

↑hemosiderin in spleen (M&F).

500 ppm (2,514 mg/m3): 

No clinical signs of toxicity (F0 or F1 generations)

↓Weight gain 

(F1 M; F0 and F1 F during gestation and lactation) 

↓Absolute but not relative brain weight (M) 

↑Relative liver weight (M&F) 

↑Absolute thymus weights F1 M 

(no lesions reported) 

Centrilobular hepatocellular vacuolation (M&F) 

↑Liver glycogen (F) 

↑Renal pelvic mineralization (M&F) 

↑Hemosiderin in spleen (M&F F0, F F1).

750 ppm (3,771 mg/m3): 

No clinical signs of toxicity 

↓Weight gain (M&F) 

↓Absolute but not relative brain weight (M&F) 

↑Relative liver weight (M&F) 

↑Absolute thymus weights F1 males 

(no lesions reported) 

Centrilobular hepatocellular vacuolation (M&F) 

↑Liver glycogen (F) 

↑Renal pelvic mineralization (M&F) 

↑Hemosiderin in spleen (M&F).

WIL 

Research 

Laboratories 

(58)

M=Males 

F=Females 

h=hours

d=days

wk=week

↑=Increased Effect

↓=Decreased Effect

RBC=Red blood cell

MCV=Maximum motor nerve conduction velocity

*See Table 4-3 for effect levels based on reproductive effects.
II-28

Appendix II

3.0 DEVELOPMENTAL TOXICITY DATA

3.1 Human Data

No case report or epidemiological data were available for any aspect of potential developmental 

toxicity induced by exposure to 1-BP.

3.2 Experimental Animal Data

The BSOC sponsored a standard developmental toxicity study using Crl: CD (SD) IGS BR SpragueDawley rats (18). Pregnant animals (25/group) were exposed to actual vapor concentrations of 0, 520, 

2,530, or 5,060 mg/m3 [0, 103, 503, or 1,005 ppm] 1-BP (99.9% purity) for 6 hours/day from gd 6–19 

(day of conception=day 0). Exposures were conducted in whole-body chambers under dynamic conditions. Concentrations were monitored by infrared (IR) spectrometry. Nominal chamber concentrations 

were selected to produce a gradation of effects from the lowest to the highest dose. Pregnancy was 

terminated on gd 20 and the fetuses removed by cesarean section. The uterine contents were weighed 

and one-half the fetuses preserved in Bouin’s fluid for soft-tissue evaluation, while the other half were 

eviscerated and processed for skeletal evaluation using Alizarin Red-S and Alcian Blue. Continuous 

data were analyzed by ANOVA, Dunnett’s test, and/or the Kruskal-Wallis test and incidence data 

were analyzed by a Fisher Exact Test with Bonferonni correction. The study was conducted according to GLP. Results of this study are summarized in Table 3-1. 

Table 3-1. 

Major Effects Observed in a Prenatal Toxicity Study by Huntingdon Life Sciences (18)

Number a Dose in ppm 

(mg/m3) Maternal Effects Fetal Effects

25/23 0

25/23 103 (520) NOEC ↓Fetal weight (48%) b

25/25 503 (2,530) ↓Weight gain and food intake ↓Fetal weight (48%) b

↑Litters with reduced skull ossification 

(17 vs 4%)

25/24 1,005 (5,060) ↓Weight gain and food intake

Clinical signs

↓Fetal weight (73%) b

↑Litters with reduced skull ossification

 (18 vs 4%)

↑Litters with bent ribs (13 vs 0%)

No increases in prenatal mortality, 

sex distribution, or external, skeletal, 

or visceral malformations

Protocol: CD rats were exposed to 1-BP on gd 6–19. 

Dams were sacrificed on gd 20 for evaluation of prenatal toxicity. 

Note: ↑,↓=Statistically significant increase, decrease.

a Number of pregnant dams/litters evaluated.

b [BMDs for 5% reduction in fetal weight were 561 ppm (central estimate) and 305 ppm 

(95th percentile lower confidence interval)]

There was no effect on pregnancy rate. One animal from the 1,005 ppm (5,060 mg/m3) group was 
Appendix II

II-29

sacrificed moribund. Examination of this animal indicated extramedullary hematopoiesis, hepatocellular necrosis, hepatocellular inflammation, and lymphoid cell hyperplasia of the spleen. These 

findings were not considered to be treatment related. Lacrimation and salivation were observed in 

animals exposed to 1,005 ppm (5,060 mg/m3). Mean maternal bodyweight and bodyweight corrected for gravid uterus weight in the 503 ppm (2,530 mg/m3) and 1,005 ppm (5,060 mg/m3) groups 

were significantly reduced compared to the concurrent controls; maternal bodyweight gain and food 

consumption were also significantly reduced in these two groups. No signs of embryotoxicity were 

observed, and no treatment-related visceral or skeletal anomalies were noted. Fetal bodyweight was 

significantly reduced in all treated groups. A significant treatment-related increase in the litter incidence of bent ribs was seen in the 1,005 ppm (5,060 mg/m3) group, but the authors considered this 

condition reversible and frequently observed in untreated rats. [The Panel noted that bent ribs (also 

referred to as undulating, angulated, bowed or wavy rib (65, 66)) is a term applied to congenital 

undulations of several ribs and these changes are considered a fetal aberration (deviation) as 

contrast to a frank malformation.] A slight (but not significant) increase in the incidence of wavy 

ribs was observed in litters exposed to 503 ppm (2,530 mg/m3) 1-BP. No fetuses with wavy ribs were 

found in either control litters or in those recovered from dams inhaling 103 ppm (520 mg/m3). [The 

incidence of ‘wavy’ ribs in control rat fetuses is generally low (0 to 2.7%), is bilateral and the 

condition resolves without sequelae (65, 67). Bent or wavy ribs are associated with reduced local 

alkaline phosphatase activity and reduced calcium deposition and are thought to be the result of 

opposing cervical and abdominal muscular forces acting upon incompletely ossified ribs (65).]

Reduced skull ossification was observed at 503 and 1,005 ppm (2,530 and 5,060 mg/m3), and was associated with maternal toxicity and reduced fetal bodyweight by authors. Thus, reduced ossification of 

the fetal rat skull occurred after 1-BP exposures less than those required to retard ossification of the 

ribs (18). The authors identify 103 ppm (520 mg/m3) as a NOEC for maternal and fetal toxicity, and 

1,005 ppm (5,060 mg/m3) for teratogenicity. 

The Expert Panel noted that Huntingdon Life Sciences (18) did not consider reduced fetal weight at 

the lowest dose to be treatment-related. Huntingdon Life Sciences (18) suggested that the practice of 

holding “1 or 2” control dams “until the end of the daily cesarean section period” resulted in “many 

control group fetuses weighing ~0.2 g heavier in bodyweight versus the laboratories’ usual 3.9 gram 

fetuses” (68). Huntingdon Life Sciences (18) speculated that this practice resulted in apparent bodyweight reductions among treated as compared to concurrent control groups when considered for individual male and female fetuses. There is no question that normal fetal rodent bodyweights increase 

rapidly near term. However, 23−25 dams/group and their litters were examined (18). Therefore, the 

Panel questioned whether holding one dam/group (from 23-25 total litters) until the end of the workday could result in a statistical distortion of the data that was not related to exposure history. 

The Expert Panel addressed the question of whether reduced fetal bodyweights at the 103 ppm (520 

mg/m3) concentration were due to 1-BP treatment by calculating a benchmark dose (BMD). The 

EPA BMD Software program (BMDS Version 1.3) was used. Initial attempts to model the data indicated that none of the models fit the data adequately. Examination of the raw data suggested that a 

single litter in the 103 ppm (520 mg/m3) group was aberrantly low (i.e., an outlier): the mean for this 

litter was 3.2 grams, approximately three SD lower than the mean of 3.9 grams. Therefore, this litter 

was excluded from subsequent analyses. Doing this changed the mean and SD for this group from 3.9 

± 0.23 to 4.0 ± 0.17 grams. More importantly, it made the data amenable to dose-response modeling 
II-30

Appendix II

using the BMDS software.

The polynomial model provided the best data fit (Figure 3-1). The BMD was calculated as the concentration at which fetal weight was reduced 5% from the concurrent control mean. This provided 

a central estimate for the BMD of 561 ppm, and a 95th percentile lower confidence limit (BMDL) 

of 305 ppm. The Expert Panel noted that the BMD is consistent with the LOAEC for skeletal variations.

Figure 3-1. 

Benchmark Dose Analysis of Fetal CD Rat Bodyweight Following In Utero Exposure to 1-BP (18)

Polynomial Model with 0.95 Confidence Level

Dose

Mean Respons

e

BMDL BMD

Polynomial

0 200 400 600 800 1000

3.7

3.8

3.9

4.0

4.1

4.2

Strength/Weaknesses: The Huntingdon Life Sciences (18) bioassay is a well-conducted, GLP study 

performed in accord with current regulatory guidelines and standard practices using appropriate 

numbers of animals. Chamber concentrations were determined by weighing the 1-BP vapor generation apparatus prior to and following cessation of exposure, then dividing by the duration and airflow. 

The purity of the test material was determined “using a modified method provided by the sponsor” 

and was stated as 99.87%. The chamber air concentrations were measured using a Miran air analyzer, 

but specific details of that infrared method were not provided. Fetuses were evaluated for signs of developmental toxicity using appropriate methods.

Utility (adequacy) for CERHR Evaluation Process: The Huntingdon Life Sciences (18) rat data are 

directly applicable to the evaluation process in that the protocol conformed to that expected from 

a standard inhalation bioassay carried out under GLP. It is noteworthy that only rats were included 

in the protocols available to date. No data for other common laboratory species (e.g., mice, rabbits) 

as required for standard developmental toxicity risk assessments were found. No pharmacokinetic, 

disposition, or transplacental transfer data were collected that could be applied in quantitative interspecies extrapolation of dose. 
Appendix II

II-31

Limited information about developmental toxicity associated with exposure to 1-BP is also available 

from a two-generation reproductive toxicity study in which Crl:CD(SD) IGS BR rats were exposed to 

0, 100, 250, 500, or 750 ppm [0, 503, 1,257, 2,514, 3,771 mg/m3] 1-BP vapors during premating, mating, gestation, and lactation (pnd 5−21) (58). Complete details of the WIL Research Laboratories (58) 

study are included in Section 4. Statistically significant reductions in live litter size were observed in 

F0 and F1 females exposed to 500 ppm and no offspring were observed in F0 females exposed to 750 

ppm. Given that there were proportionate decreases in implantation sites in the F0 dams, the Panel 

noted the plausible explanation of an effect on fertility rather than adverse effects on development. 

Significant reductions in neonatal weight gain during nursing occurred in F1 males and F2 males and 

females of the 500 ppm group. There were no treatment-related effects on postnatal survival in either 

F1 or F2 litters. The authors stated that skeletal examinations would be conducted according to the 

Dawson method if external abnormalities were observed. There were no reports of external malformations in offspring. [The Expert Panel identified a developmental NOEC of 250 ppm.]

Strength/Weaknesses: This is a well-conducted GLP study performed according to standard practices 

and guidelines. Adequate numbers of animals were used in the evaluation and all the appropriate endpoints for reproductive toxicity were examined. One limitation is that developmental effects may have 

been missed because animals were allowed to give birth, which may prevent detection of malformed 

or otherwise abnormal fetuses.

Utility (adequacy) for CERHR Evaluation Process: This two generation study provides convincing 

evidence that adverse effects on rat reproductive performance associated with inhaled 1-BP were due 

to reduced fertility; no evidence of developmental toxicity was found in pregnant females (through 

500 ppm groups). This study provides useful indirect evidence that inhaled 1-BP is not a developmental toxicant in rats at up to 500 ppm.

Limited information about potential developmental effects is available from a range-finding onegeneration GLP study conducted by Huntingdon Life Sciences (69). Ten individually housed groups 

of Crl: CD (SD) IGS BR rats were randomly assigned and exposed (whole body) to HEPA-filtered air 

or 1-BP vapors (99.9% purity) in nitrogen at concentrations of 100, 199, 598, or 996 ppm [503, 1,001, 

3,008, 5,010 mg/m3] on gd 6–19 for 6 hours/day. Dams delivered and were exposed to 1-BP together 

with their litters on pnd 4–20. Concentrations in dynamic inhalation chambers were verified using an 

unstated infrared method. At birth, pups from 7–9 litters/group were sexed, weighed, and examined 

for viability and external abnormalities. Pup growth and survival were monitored from birth 

through weaning. At weaning, 1 pup/sex/litter was randomly selected for a post-weaning growth 

study and exposed to 1-BP on pnd 22–28. Hematology and clinical chemistry analyses and organ 

weight measurements were conducted in dams at the end of the lactation period and offspring from 

the pnd 22–28 day post-weaning study on pnd 29. Data were analyzed by ANOVA, Dunnett’s test, 

and/or the Kruskal-Wallis test. Results in this study are summarized in Table 3-2. Dams in the 996 

ppm group experienced lacrimation and increased salivation. Maternal bodyweight gain was reduced 

during treatment in the 199, 598, and 996 ppm groups but did not reach statistical significance. Food 

intake was not affected by treatment. Significant organ weight changes in dams included increases 

in relative weights (to bodyweight) of the liver and kidneys in the 598 and 996 groups. The authors 

did not consider any of the changes in maternal hematology or clinical chemistry parameters to be 

toxicologically significant. No external abnormalities or reduced birth weight were reported. During 
II-32

Appendix II

the period from birth to weaning, no increased pup mortality was observed; pup bodyweights were 

slightly, but not significantly, reduced in the 996 ppm group. Bodyweight gain during the post-weaning 

period (pnd 22–29) was significantly lower for males in the 598 and 996 groups and females in the 996 

group. Significant organ weight changes in male offspring included increased absolute adrenal (100 

and 199 ppm) and reduced brain weight (996 ppm) and increased relative adrenal weight (100, 199, and 

996 ppm). In female offspring, absolute brain weight was significantly reduced in the 996 ppm group. 

The only hematological and biochemical effects in offspring that were considered treatment-related 

by authors included statistically significant reductions in platelet count in 598 and 996 ppm females 

and 996 ppm males, elevations in gamma-glutamyl transferase levels in 996 ppm males and females, 

and reduced circulating glucose levels in the 996 ppm females and in all treated males (significant 

only at high dose for males). Authors identified a maternal NOEC of 100 ppm but did not identify a 

developmental NOEC. [The Expert Panel noted that exposure to 1-BP during the post-weaning 

period reduced bodyweight gain and may have targeted adrenals, platelets and the liver.]

Table 3-2. 

Major Effects Observed in a Developmental Range-Finding Study by Huntingdon Life Sciences (69)

Numbera Dose in ppm 

(mg/m3) Maternal Effects Offspring Effects

10/8 0

10/9 100 (503) NOEC ↑Relative adrenal weight (M)

10/8 199 (1,001) ↓Bodyweight gainb ↑Relative adrenal weight (M)

10/7 598 (3,008) ↓Bodyweight gainb

↑Relative liver and kidney weight

↓Bodyweight gain on pnd 22–25(M)

↓Platelets (F)

10/10 996 (5,010) ↓Bodyweight gainb

↑Relative liver and kidney weight

Clinical signs

No toxicologically significant 

effects on hematology or blood 

chemistry

↓Bodyweight gain on pnd 22–29 

(M) and 22–25 (F)

↑Relative adrenal weight (M)

↓Absolute brain weight

↓Platelets

↓Glucose levels

↑Gamma-glutamyl transferase

No reduced birth weight, external 

abnormalities or increased mortality

Protocol: CD rats were exposed to 1-BP on gd 6–19. Dams delivered and were then exposed to 1-BP with 

litters on pnd 4–20. One offspring/sex/litter was exposed on pnd 22–28.

Notes: ↑, ↓=significant increase, decrease. 

M, F=Males, Females only.

a Number of pregnant dams/litters evaluated.

b Although not statistically significant, bodyweight effects were considered by authors in selection 

of NOEC.

Strength/Weaknesses: One deficiency noted concerned 1-BP purity and stability in that a [unstated]

“modified method provided by the study sponsor” was utilized in those analyses. Chamber nominal 

concentrations were determined by weighing the 1-BP vapor generation apparatus prior to and follow-
Appendix II

II-33

ing cessation of exposure, then dividing by the duration and airflow. Huntingdon Life Sciences (69) 

indicated that chamber air was collected at four time points over the 6-hour exposures and evaluated 

using a ‘Miran air analyzer.’ The report neither presented the details of chamber air sampling and 

infrared quantification, provided references to published or standardized methods for 1-BP measurement nor was it clear whether the calculated nominal concentrations were confirmed using conventional GC techniques.

Utility (adequacy) for CERHR Evaluation Process: While the protocol is of little utility in hazard 

identification for teratogens, the investigation is valuable inasmuch as exposures were conducted 

throughout organogenesis, through neonatal life, and infancy. A rat LOAEC for developmental toxicity of 100 ppm can be identified based on the significant increase in absolute and relative adrenal 

weights for the F1 males. After exposure to 598 or 996 ppm, adrenal to bodyweight ratios were also 

increased for the males, but not for the female offspring. Huntingdon Life Sciences (69) identified a 

maternal NOEC of 100 ppm based on reduced maternal bodyweight gain after exposure to 199, 598, 

and 996 ppm.

3.3 Utility of Data

No data are available to evaluate potential developmental toxicity of 1-BP exposures in humans.

In rats, appropriate methods were used to evaluate teratogenicity following exposure on gd 6-19 (18). 

Postnatal growth and survival were evaluated in a two-generation reproductive toxicity assay (58) 

and in a range-finding reproductive toxicity assay (69). Dams in the two-generation study were exposed throughout the entire gestation period and from pnd 5 to 21, while dams in the screening study 

were exposed on gd 6–19 and pnd 4–20. All studies were conducted according to GLP. The data were 

adequate to evaluate developmental toxicity in rats. No data were available for other common laboratory species such as mice and rabbits. In addition, there are no pharmacokinetic, disposition, or transplacental data that could be applied to quantitative interspecies extrapolation.

3.4 Summary of Developmental Toxicity

There were no studies located that address potential developmental toxicity in humans exposed to 

1-BP.

The data are sufficient to indicate that inhalation exposure to 1-BP in rats can induce signs of developmental toxicity. A prenatal inhalation developmental toxicity study in rats observed reduced ossification of the skull at ≥503 ppm (≥2,530 mg/m3) and increased bent ribs at 1,005 ppm (5,060 mg/m3); 

decreased maternal bodyweight gain and food consumption also occurred at these concentrations 

(18). Significant reductions in fetal bodyweight were observed at ≥103 ppm (520 mg/m3). No evidence of embryotoxicity (lethality/terata) was seen at concentrations up to 1,005 ppm (5,060 mg/m3) 

1-BP on gd 6–19.

There was no NOAEC for fetal weight decrease in the 1-BP developmental toxicity study. The authors of the study speculated on non-treatment-related reasons for the statistically significant effect at the lowest exposure concentration (103 ppm) and suggested that the true LOAEC was the 

next higher concentration level, 503 ppm. The Expert Panel addressed the question by calculating a 

BMD. The EPA BMD Software program (BMDS Version 1.3) was used as described in Section 3.2. 
II-34

Appendix II

The BMD was calculated as the concentration at which fetal weight was decreased by 5% from the 

control mean. This provided a central estimate for the BMD of 561 ppm, and a 95th percentile lower 

confidence limit (BMDL) of 305 ppm. The Expert Panel noted that the BMD is consistent with the 

LOAEC for skeletal variations.

Two studies examined postnatal growth in rat pups whose dams were exposed to 1-BP during gd 6–19 

and pnd 4−20 (69) or throughout the entire gestation and majority of the lactation period (pnd 5−21) 

(58). Whereas reduced fetal bodyweights were seen at day 20 after dams inhaled 103 ppm 1-BP from 

days 6–19 (18), no such changes were observed at birth (day 21) in male and female CD neonatal 

rats born to dams inhaling 100 ppm 1-BP from days 6–19 (69). Postnatal pup bodyweight gain was 

reduced in litters from dams exposed to ≥598 ppm (3,008 mg/m3) (69). F1 and F2 pup weight gain 

was reduced during the nursing period at 500 ppm (2,514 mg/m3) in a two-generation study in (58). 

Additional relevant effects are listed in Table 3-3.

The Panel concluded there is sufficient evidence in rats that inhalation exposure to 1-BP causes developmental toxicity in the form of skeletal variations, consistent with developmental delay, following inhalation at ≥503 ppm, 6 hours/day, gd 6–19. There was also a concentration-related reduction 

in fetal bodyweight consistent with developmental delay. The data are assumed relevant to consideration of potential risk to human health.

There is insufficient evidence in humans that 1-BP causes developmental toxicity, due to an absence 

of data.
Appendix II

II-35

Table 3-3. Summary of Developmental Toxicity in Inhalation Studies

Analytical 

Concentration 

in ppm (mg/m3)

Exposure 

Regimen

Species/ 

Strain Concentration: Effect Reference

103 (520)

503 (2,530)

1,005 (5,060)

6h/d 

gd 6–19

CD (SD) 

IGS BR 

Rat

Dams:

Maternal NOEC=103 ppm (520 mg/m3)

503 ppm (2,530 mg/m3): 

↓Weight gain and food intake

1,005 ppm (5,060 mg/m3): 

↓Weight gain and food intake

Lacrimation, Excessive salivation

Fetuses a:

103 ppm (520 mg/m3): 

↓Bodyweight

503 ppm (2,530 mg/m3): 

↓Bodyweight; ↓Skull ossification

1,005 ppm (5,060 mg/m3): 

↓Bodyweight; ↓Skull ossification;↑Bent ribs

Huntingdon 

Life Sciences 

(18)

100 (503)

199 (1,001)

598 (3,008)

996 (5,010)

6h/d 

gd 6–19 and 

pnd 4−20

CD Rat Dams:

Maternal NOEC=100 ppm (503 mg/m3)

199 ppm (1,001 mg/m3): 

↓Bodyweight gain

598 ppm (3,008 mg/m3): 

↓Bodyweight gain 

↑Relative liver and kidney weight

996 ppm (5,010 mg/m3): 

↓Bodyweight gain 

↑Relative liver and kidney weight 

Clinical signs

Pups:

100 ppm (503 mg/m3): 

↑Relative adrenal weight (M)

199 ppm (1,001 mg/m3): 

↑Relative adrenal weight (M)

598 ppm (3,008 mg/m3): 

↓Bodyweight gain (M; pnd 22–25)

↓Platelets (F)

996 ppm (5,010 mg/m3): 

↓Bodyweight gain (M: pnd 22–29, F: pnd 22–25) 

↓Absolute brain weight (M,F) 

↑Relative adrenal weight (M)

↓Platelets (M,F); ↓Glucose (M,F)

↑Gamma-glutamyl transferase (M,F)

Huntingdon 

Life Sciences 

(69)

100 (503)

250 (1,257)

500 (2,514)

6h/7d/wk for 

gestation and 

most of lactation.

Whole body.

CD Rat Dams: See Table 4-3 in Section 4

Pups:

Developmental NOEC=250 ppm (1,257 mg/m3)

500 ppm (2,514 mg/m3): 

↓Weight gain during lactation period

WIL 

Research 

Laboratories 

(58) b

h = hours; d = days; wk = week; M=Male, F=Female; ↑=Increased Effect; ↓=Decreased Effect a [BMDs for fetal bodyweight: 561 ppm (central estimate); 305 ppm (95th percentile lower confidence limit).]

b Reproductive effects for this study are summarized in Section 4.
II-36

Appendix II

4.0 REPRODUCTIVE TOXICITY

4.1 Human Data

In 1998, NIOSH conducted a health hazard evaluation at a plant where a 1-BP-containing spray adhesive was used in the manufacture of seat cushions (40). Forty-three employees (34 females and 9 

males), whose exposure levels were classified as ‘low’ (117 ppm [585 mg/m3]), ‘medium’ (170 ppm 

[850 mg/m3]), or ‘high’ (197 ppm [985 mg/m3]), were asked about reproductive problems. One employee (sex not specified) in the low exposure group reported seeing a doctor for reproductive/fertility 

problems and two males and one female in the low or mid exposure groups said they could not have a 

child after attempting to conceive for 1 year. NIOSH noted that their ability to detect reproductive or 

fertility problems was limited by the small sample size and personal nature of the questions asked. An 

analysis of blood samples for complete blood count was also conducted and is discussed in Section 2.

Strength/Weaknesses: The NIOSH (40) case report is very limited in content. The survey analysis 

was based on only 43 of 70 workers. According to the National Center for Health Statistics (70), 

about 10% of couples in the US seek medical attention for infertility. Therefore, 3 of 42 workers reporting possible fertility problems is not unexpected. 

Utility (adequacy) for CERHR Evaluation Process: The study is not useful except to point out the need 

for a well-designed human study with adequate exposure information and adequate power to detect an 

effect, i.e., one that monitors menstrual cycles and examines semen quality and serum hormones. A 

well-designed study would also include identification and analysis of potentially confounding factors.

4.2 Experimental Animal Toxicity

In a study sponsored by the BSOC, WIL Research Laboratories (58) evaluated the potential adverse 

effects of 1-BP whole-body inhalation exposure in F0 and F1 parental rats; reproductive capabilities 

were examined in the F0 and F1 generations and neonatal survival, growth and development were 

evaluated in F1 and F2 offspring. In this two-generation reproductive toxicity study, groups of 25 

male and female Crl:CD(SD)IGS BR rats were exposed to filtered air or 100, 250, 500, or 750 ppm 

[0, 503, 1,257, 2,514, 3,771 mg/m3] 1-BP vapors (99.8% purity) for 6 hours/day, 7 days/week. Exposure concentrations within each chamber were measured 9–10 times during each exposure period by 

a validated GC method. Exposure of F0 rats commenced at 7 weeks of age and F1 rats began direct 

exposure at weaning. Exposures were conducted for at least 70 days prior to mating. Females were 

not exposed on pnd 0–4 and only they, not their litters, were exposed during pnd 5–21. Therefore, 

offspring (litters) were indirectly exposed to the test chemical in utero and through nursing. In addition, the F1 pups selected randomly for propagation of F2 litters were directly exposed from pnd 22 

forward. Results in treated animals were compared to both air control and historical control data from 

WIL Research Laboratories. Statistical analyses were stated to generally be conducted using twotailed tests for a minimum significance of p=0.05. Most data were analyzed by one-way ANOVA with 

Dunnett’s test. Exceptions were Chi-square test with Yates correction factor for parental mating and 

fertility indices; Kruskall-Wallis test with Mann-Whitney U-test for sperm motility, % normal sperm, 

pup sex at birth, and proportional postnatal survival; and Fisher’s Exact test for histopathological 

findings. The study was stated to have been conducted in compliance with GLP.

Evidence of general toxicity was observed in the higher dosage groups and is discussed under Section 2. 
Appendix II

II-37

Reproductive effects are outlined in Table 4-1. 

Table 4.1. Major Effects Observed in a Two-Generation Reproductive Toxicity Study 

in Sprague Dawley Rats by WIL Research Laboratories (58)

Number a

Dose in 

ppm 

(mg/m3)

Effects in F0 Parents b Effects in F1 Offspring 

[F2 Offspring] b

25 0

25 100 (503) NOAEC NOAEC

25 250 (1,257) ↓Prostate weight ↓F1 weight gain on pnd 21–28 (M)

↑Estrous cycle length (49 vs 45 days) d

25 500 (2,514) ↑Precoital interval (43 vs 34 days) c

↑Estrous cycle length (55 vs 42 days ) d

↓Fertility (52 vs 92%)

↓Implantation sites (90 vs 153)

↓Litter size (n=83 vs 144)

↓Normal sperm (982 vs 997%)

↓Sperm motility (72 vs 87%)

↓Cauda epididymis and prostate weights 

No effects on gestation length or parturition, testicular weight or sperm counts, 

ovarian weight

↓F1 weight gain through pnd 28 (M)

 and pnd 21–28 (F)

↑Estrous cycle length (51 vs 45 days)c

↓Implantation sites (98 vs 155)

↓Litter size (86 vs 145)

↓Normal sperm (953 vs 995%)

↓Sperm motility (74 vs 89%)

↓F1 cauda epididymis and pituitary weight

[↓F2 postnatal weight gain on pnd 4–21]

No effect on F1 or F2 postnatal survival, F1 age 

at vaginal patency, F1 age at balanopreputial 

separation, mating indices, gestation length, 

parturition, or testicular lesions

25 750 (3,771) ↓Weight gain (M)

↑Estrous cycle length (56 vs 42 days) d

↓Mating (68 vs 96%)

↑Pre-coital interval (48 vs 34 days) c

No conceptions

↓Ovary weight

↓Corpora lutea 

↑Ovarian cysts 

↓Normal sperm (906 vs 997%)

↓Sperm motility (53 vs 87%) 

↓Epididymal sperm count 

(370 vs 472x106/gram tissue)

↓Epididymis, prostate, seminal vesicle, 

and pituitary weight 

No F1 rats available due to complete infertility 

in F0 rats

Protocol: Inhalation exposure to 1-BP from 70 days prior to mating, during gestation and most of lactation in F0 and F1. 

Reproductive function evaluated in F0 and F1; postnatal mortality and growth evaluated in F1 and F2 litters.

Notes: M=Male; F=Female; ↑,↓=Statistically significant increase, decrease. a Number of F0 and F1 male and female pairs, except that no F1 offspring were available at 750 ppm.

b See synopses for details about systemic effects.

c Not statistically significant but above historical control value. 

d No statistical analyses conducted, but considered test article related (see text). 

Prior to mating, the F0 female rats exhibited increased estrous cycle length. While this effect appeared 

to be dose-related, statistical analysis of the data was not conducted, in part because several animals 

in each of the high dose groups did not cycle at all. However, the study authors considered values 
II-38

Appendix II

for the 500 and 750 ppm groups to be test agent related since they exceed the range of their historic 

control data for this end point (4.1–5.1 days). Reproductive performance was impaired in the higher 

dosage F0 groups as evidenced by significant decreases in male/female mating index in the 750 ppm 

group, and in the male/female fertility index in the 500 and 750 ppm groups. An increased time to 

coitus in the F0 500 and 750 ppm groups was not statistically significant but was considered test agent 

related since it exceeded historical control values. None of the females in the F0 750 ppm group 

became pregnant. In contrast, 1-BP treatment had no effect on gestation length or complications during delivery. However, numbers of implantation sites and pups born to F0 females were significantly 

reduced in the 500 ppm group.

At necropsy, significant reductions in F0 absolute reproductive organ weights were observed for ovary 

(750 ppm), cauda epididymis (500 and 750 ppm), prostate (≥250 ppm, but did not decrease with 

increasing dose), seminal vesicles (750 ppm), and pituitary (750 ppm). Significant decreases in relative weights of these organs were only observed in the 750 ppm group for caudae epididymides and 

ovaries. Ovarian histologic analysis in F0 rats in the 750 ppm group revealed a significant increase in 

the incidence of ovaries with reduced numbers of corpora lutea and with follicular luteinized cysts. 

In males, a slightly increased incidence of seminiferous tubule degeneration was not considered treatment related by the study authors since lesions in 4 of 6 affected rats were of minimal severity. Also, 

testicular sperm counts (absolute or per gram testis) were not significantly altered by treatment. An 

analysis of cauda epididymal spermatozoa from F0 rats revealed significant reductions in morphologically normal sperm at ≥ 250 ppm. However the decrease from 99.7% normal sperm in controls 

to 99.3% at 250 ppm was not considered by the authors to be treatment related because this value is 

above historical control value of 99.0%. Cauda epididymal sperm numbers were significantly reduced 

at 750 ppm and the percentage of motile sperm was significantly reduced at 500 and 750 ppm. [The 

Panel concurred with the authors’ conclusions discussed in this paragraph.]

A statistically significant decrease in implantation sites and in the number of offspring at birth was 

seen at the 500 ppm dose in both generations. The F1 rats were evaluated for postnatal growth, development, and survival. A slight, but significant, reduction in pup viability on pnd 14–21 in the F1 500 

ppm group (97.7% vs. 100% in controls) was not considered of sufficient magnitude to be treatment 

related, especially because postnatal survival calculated from pnd 4 to pnd 21 was not different by 

treatment. Therefore, the authors concluded that there were no effects on pup survival. [The Expert 

Panel agrees with this interpretation of the data.] Mean offspring weights (litter as experimental 

unit) were lower at the 500 ppm dose in both generations. Significant reductions in F1 litter weight 

gain were found in males of the 250 ppm group (pnd 21–28) and 500 ppm group (pnd 4–7, 7–14, and 

21–28). A significant reduction in F1 female weight gain was only noted in the 500 ppm group on pnd 

21–28. The age of balanopreputial separation was significantly increased in the F1 500 ppm group 

but authors attributed that effect as secondary to reduced weight gain in that group. The age at which 

female offspring attained of vaginal patency was not significantly different in treated F1 offspring. 

1-BP exposure in the F1 animals was initiated on pnd 22. Twenty-five rats/sex/group in control and 

100–500 ppm treatment groups were selected for mating. The mating experiment was conducted as 

described for the F0 rats. Increased estrous cycle lengths in the 250 and 500 ppm F1 groups (4.9 and 

5.1 days) were within ranges of historical controls (4.1–5.1) but were nevertheless attributed by the 

authors to be related to 1-BP treatment. This judgement was based on the fact that 3 and 4 animals, 
Appendix II

II-39

in the 250 and 500 ppm groups, respectively, had no complete estrous cycles (versus only 1 each in 

the control and 100 ppm groups). Again, no statistical analysis was performed for this endpoint. No 

significant effects were noted for F1 fertility or mating indices, days to mating, gestation length, or 

birthing complications. However, authors noted that non-significant and non-dose-related reductions 

in fertility indices in the F1 100, 250, and 500 ppm groups (68, 64, 72%, respectively) were below 

fertility indices of historical controls (∼90%). Mean numbers of implantation sites were reduced in 

the F1 dams in the 250 and 500 ppm groups with statistical significance achieved at the higher dose 

level. Live litter size was significantly decreased at 500 ppm. Apparent increases in the incidence of 

ovarian follicular cysts and interstitial cell hyperplasia (mild) in F1 females in the 500 ppm group 

were not statistically significant. Absolute (but not relative) epididymis and pituitary weights were 

significantly reduced in the F1 500 ppm males. Lesions observed in testes were considered minimal 

and their incidence was not altered significantly by treatment, although there appeared to be a trend. 

Other male reproductive organs were histologically normal. The percentage of motile sperm was 

slightly, but significantly, reduced in the F1 males (from 89% in controls to 85%) at 250 ppm. The 

study authors did not consider this treatment-related since this value exceeds that of historic controls. 

However, the percentage of motile sperm was further (and significantly) reduced to 74% in the 500 

ppm group. The percentages of morphologically normal sperm were significantly reduced at 500 

ppm. A slight but statistically significant reduction from 99.5% normal sperm in controls to 98.9% 

in the 100 ppm group was not considered by the study authors to be test article related because the 

difference was very small, and no significant changes were seen in the 250 ppm group. [The Expert 

Panel agreed with this interpretation.] F2 rats were only evaluated for postnatal growth and survival to pnd 21. Postnatal weight gain in males and females was significantly reduced in the F2 500 

ppm group. Survival was unaffected.

[The Expert Panel identified 100 ppm as a NOAEC in this study, and 250 ppm as a LOAEC, based 

on decreased prostate weight in the F0 males and increased estrous cycle length in the F1 female 

offspring. From the perspective of the LOAECs observed, both sexes are equally sensitive to 1-BP. 

Alterations in male and female reproductive outcomes at 500 ppm may contribute to the altered 

fertility and reduced litter size seen at this concentration, and the infertility seen at 750 ppm.]

Strength/Weaknesses: This is a comprehensive study conducted under GLP and it meets specifications of EPA’s harmonized reproductive test guidelines. It includes indices of puberty as measures for 

reproductive development, and sperm measures as indices of testicular and epididymal function. This 

allows effects on reproductive organ function to be detected in the absence of an effect on reproductive 

performance at lower doses. Results provide convincing evidence that 1-BP is a reproductive toxicant 

in both male and female rats, with neither sex being obviously more sensitive than the other.

Adverse effects on litter size and sperm measures at 500 and 750 ppm were consistent across generations, suggesting a lack of a transgeneration effect, or increased susceptibility during perinatal 

or pubertal stages. Apparent increase in age at balanopreputial separation appears to be related to 

reduced bodyweights in offspring in the highest dosage group rather than to direct effects of the test 

agent on puberty. Despite significant (though not dramatic) reductions in epididymal weight, sperm 

morphology, sperm motility, and epididymal sperm counts, there were no effects on testicular histology or testicular sperm counts. Likewise, in the F0 females, alterations in estrous cyclicity and litter 

size were found in the absence of significant decreases in ovarian weight or significantly abnormal 
II-40

Appendix II

ovarian histology at 500 ppm. 

Criteria for scoring histology were not provided (p. 55 of study). Some animals at 500 and 750 ppm 

were apparently more than “minimally” affected, especially as the testes contained at least some 

tubules with “Sertoli cell only.” One might expect to see histologic evidence of abnormal spermatogenesis based on significant reduction of epididymal sperm counts in the 750 ppm group. The Panel 

suggested that study authors may want to reconsider the statistical analyses for testicular pathology.

The report has a section titled “Discussion and Conclusions” but it is a summary, with no rigorous 

discussion of the data or significance of the findings. For example, decreased weights of epididymis, 

prostate, and seminal vesicle could be indicative of lower weight gain in offspring, or could be indicative of an endocrine effect

Utility (adequacy) for CERHR Evaluation Process: This is an excellent study for hazard identification and is adequate for the CERHR evaluation process. The wide array of endpoints provides a 

comprehensive picture of alterations in both the male and female reproductive system that together 

appear to account for the subfertility at 500 ppm and infertility at 750 ppm. Effects on many endpoints at 500 ppm, in the absence of significantly decreased bodyweight or other pathology, provide 

strong evidence for specificity of the reproductive toxicity.

A study by Ichihara et al. (57) examined the dose response of 1-BP-induced testicular toxicity including sperm measures (motility/morphology) and detailed testicular histology (testes fixed in Bouin’s 

and stained with period acid Schiff’s reagent). In the examination of testicular histology, subtle 

changes in seminiferous tubule cell associations, similar to those recommended by Creasy (71), were 

evaluated. These included enumeration of spermatogenic cells in stage VII tubules and elongated 

spermatids retained in stage IX−XI tubules (normally released at stage VIII). The rationale for this 

study included the increased use of 1-BP in industry and the previously reported reproductive toxicity 

induced by its isomer, 2-BP. Eight-to-nine, 10-week-old male Wistar rats (from the Shizuoka Laboratory Animal Center) were exposed to air or 200, 400, or 800 ppm [1,006, 2,012, or 4,025 mg/m3]

1-BP vapors (99.81% purity) for 8 hours/day for 12 weeks. The maximum dose in this study was selected based on observations in previous studies that exposure to 1,000 ppm resulted in debilitation. 

Chamber concentrations of 1-BP were measured by GC and reported. At the end of the exposure period the rats were sacrificed and necropsied. Data were evaluated by one-way ANOVA followed by 

Dunnett’s method. Reproductive effects are discussed here while other systemic effects are discussed 

in Section 2. Table 4-2 lists findings of this study. Significant reductions in absolute organ weights 

were observed for seminal vesicles (≥200 ppm), epididymides and pituitary (≥400 ppm), and prostate (800 ppm). Significant reductions in relative organ weights were noted in seminal vesicles (≥200 

ppm) and epididymides (800 ppm). Bodyweight gain was reduced in the 400 and 800 ppm groups. 

Histopathological changes were observed in the epididymides, prostate, and seminal vesicles of the 

800 ppm group. Epididymides had reduced duct cavity diameter, wider interstitial space, increased 

epithelial cell height and contained neutrophils or degenerated epithelial cells. Prostate and seminal 

vesicles had reduced alveoli size and degenerated cells were observed in the seminal vesicle cavity. 

Histological evaluation of testes revealed vacuolated seminiferous epithelium in 2 of 9 rats of the 800 

ppm group. The numbers of retained elongated spermatids in stages IX, X, and XI were significantly 

increased in 400 and 800 ppm groups and a significant increase in degenerating spermatocytes in 
Appendix II

II-41

stage VII was seen in the 800 ppm group. Sperm quality was also affected as observed by significant 

reductions in sperm count and motility and increases in tailless sperm at ≥400 ppm. At 800 ppm a 

significant increase in sperm with abnormal heads (banana-like or straight) was observed. Table 4-2 

includes values for sperm parameters. Plasma testosterone level was significantly reduced in the 800 

ppm group, but there were no changes in follicle stimulating hormone (FSH) or luteinizing hormone 

(LH) levels. The presence of retained elongated spermatid during the postspermiation periods (stages 

IX−XI) led authors to conclude that the likely mode of 1-BP toxicity results in failure of spermiation. Authors stated that this pattern of toxicity differs from that of 2-BP which has been reported to 

target spermatogonia. 

Table 4-2. Major Effects in Reproductive Toxicity Study in Wistar Rats by Ichihara et al. (57)

Number/

Dose

Dose in ppm 

(mg/m3) Effects

8 0

9 200 (1,006) ↓Absolute seminal vesicle weight

↓Relative seminal vesicle weight

9 400 (2,012) ↓Absolute seminal vesicle, epididymides, and pituitary weight

↓Relative seminal vesicle weight

↑Retained elongated spermatids (13 vs 049/tubule)

↓Sperm count (588 vs 792x106/g cauda)

↓Motile sperm (67 vs 83%)

↑Tailless sperm (18 vs 4%)

↓Bodyweight gain

↑Relative liver weight

↓Mean corpuscular hemoglobin concentration

9 800 (4,025) ↓Absolute seminal vesicle, epididymides, pituitary, and prostate weight

↓Relative seminal vesicle and epididymides weight

↑Histological changes in epididymides, prostate, and seminal vesicles

↑Retained elongated spermatids (48 vs 049/tubule)

↑Degenerating spermatocytes (06 vs 004/tubule)

↓Sperm count (240 vs 792x106/g cauda)

↓Motile sperm (25 vs 83%)

↑Tailless sperm (36 vs 4%)

↑Abnormal sperm (100 vs 1%)

Vacuolated seminiferous epithelium in 2/9 rats

↓Plasma testosterone (29 vs 45 ng/mL) with no change in LH or FSH 

↓Bodyweight gain

↑Relative and absolute liver weight; ↓absolute spleen weight

↑Histological changes in liver

↑Mean corpuscular volume

↓Mean corpuscular hemoglobin concentration

Protocol: 10-week-old male rats exposed to 1-BP vapors for 8 hours/day for 12 weeks.

Notes: ↑,↓: Statistically significant increase, decrease.

Strength/Weaknesses: A strength of this study is the thorough evaluation of testicular effects of 1-BP 

including detailed histology, sperm measures, and serum hormones. The exposure period is suffi-
II-42

Appendix II

ciently long to see effects on all spermatogenic stages, and the range of doses is sufficiently wide to 

determine a no effect level and begin to see systemic effects on bodyweight. Enumeration of spermatogenic cell types in seminiferous tubule cross sections allowed conclusions about sensitive cell types 

and/or stages. The conclusion that the main effect in testis is spermatid retention beyond Stage VIII is 

consistent with a possible effect on Sertoli cell function and/or possible effect on the endocrine support of spermatogenesis. Decreased testosterone levels in the high-dose group coupled with decreased 

weights of testosterone-dependent organs (most consistently the seminal vesicles) are consistent with 

the latter hypothesis, as is observed decrease in sperm quality (motility/morphology). Retained spermatids may account for the decreased numbers of sperm in the epididymides.

A weakness of the study is that relatively low numbers of animals per group (9–10) limits the power 

of the study to detect an effect. For example, lower and more variable serum testosterone level might 

obtain statistical significance if more animals were assessed. Also, the significance of the adverse effects on testicular and sperm measures is hard to interpret without fertility data. 

Utility (adequacy) for CERHR Evaluation Process: This study is particularly useful for characterizing effects of 1-BP in males since it includes detailed histology with quantification of germ cells and 

serum hormones. It has limited usefulness for hazard identification since it does not include a fertility 

assessment, but is a valuable adjunct to 1-BP weight of evidence considerations.

Kim et al. (44) and Yu et al. (51) examined testes microscopically and no adverse effects were reported. In the Kim et al. (44) study, Sprague-Dawley rats inhaled 1,800 ppm 1-BP for 6 hours/day, 5 

days/week, for 8 weeks. Testes were fixed in 10% neutral buffered formalin, embedded in paraffin, 

sectioned and stained with hematoxylin-Eosin and/or PAS hematoxylin. In the Yu et al. (51) study, 

male Wistar rats were exposed to 1,000 ppm 1-BP vapors (99.4% purity) for 8/hours/day for 5 or 7 

weeks. Kim et al. (44) reported an increase in relative weight of ovaries, but no ovarian lesions were 

observed. Additional details of these two studies are included in Section 2.

Strength/Weaknesses: The experimental designs of the Kim et al. (44) and Yu et al. (51) studies could 

allow comparison of relative effects on gonads and blood. However, since there is no indication that 

testes (or ovaries) were examined for subtle effects such as retained spermatids or vacuolated Sertoli 

cells, it is doubtful that testes were evaluated in sufficient detail to detect changes seen in the other 

studies. Lack of effect could also be due to the shorter duration of exposure, but 7–8 weeks should be 

sufficient to detect changes in spermiation and sperm counts. Increased relative weights of testes and 

ovaries could simply be due to bodyweight depression without change in absolute gonad weights.

Utility (adequacy) for CERHR Evaluation Process: These studies by Kim et al. (44) and Yu et al. (51) 

are not useful for evaluating reproductive effects. They may be useful for comparing blood measures 

with other studies.

Two unpublished general toxicity studies also included evaluation of the testes. In a 28-day inhalation study, testicular hypo/aspermatogenesis was seen in two surviving Sprague-Dawley rats after 

exposure to 8,000 mg/m3 or about 1,600 ppm (45), but this effect could not be specifically related to 

the exposure due to systemic toxicity at this concentration. On the other hand, no testicular or ovarian lesions were observed in Sprague-Dawley rats exposed to up to 3,000 mg/m3 (~700 ppm) 1-BP 
Appendix II

II-43

vapors for 13 weeks (46). This finding is consistent with the results of the multigeneration study described above. Complete details of these studies and a review of strengths, weaknesses, and utility is 

included in Section 2.

Saito-Suzuki et al. (72) conducted dominant lethal studies in rats to determine the structure-activity 

relationships of 5 halogenated propanes. In addition to 1-BP (>98% purity) the following compounds 

were examined: 1,2,3-tribromopropane, 1,2-dibromopropane, 1,2,3-trichloropropane, and 1-chloropropane. Eleven-week-old male Crl: Sprague Dawley rats (n=15/group) were gavaged with 10% of 

the acute lethal dose of each compound in olive oil for 5 days. 1-BP was administered at a dose of 400 

mg/kg bw. Olive oil was the negative control and 1,2-dibromo-3-chloropropane was the positive control (n=15/group). At 1–8 weeks after treatment, the males were mated weekly with untreated females. 

Data were analyzed using Fisher’s Exact Method and the Mann-Whitney U test. 1-BP treatment had 

no effect on male fertility. Females (n=15/time period) were sacrificed 13–14 days after mating and examined for corpora lutea, implants, live embryos, and early and late embryonic deaths. 1-BP treatment 

increased the number of mean dead implants at the 8-week mating but had no effect on the dominant 

lethal mutation index (live embryos per test female/live embryos per control females). The authors 

concluded that dominant lethal mutations were induced by propanes containing a bromine or chlorine 

atom on each carbon with bromine comprising two of the atoms.

Strength/Weaknesses: This is a classic dominant lethal protocol showing that a relatively high oral 

dose of 1-BP (~maximum tolerated dose) does not induce dominant lethality. Other halogenated propanes serve as controls in that they are effective at lower dosages.

Utility (adequacy) for CERHR Evaluation Process: This paper is important since it eliminates 1-BP 

as a germ cell mutagen, and thereby rules out a mechanism of action exhibited by related halogenated 

propanes. The study also shows that short-term (5 day) exposure at high levels failed to produce adverse effects sufficient to affect fertility. The protocol neglected specific changes in testis/epididymis 

function.

An abstract is available that describes a reproductive study conducted in rats according to OECD 

Guideline 422 (73). While the abstract reported results similar to those observed by WIL Research 

Laboratories (58), the full study report was not available to the Expert Panel during the present review 

of 1-BP.

4.3 Utility of Data

The only pertinent information on humans comes from a Health Hazard Evaluation performed by 

NIOSH in 1998 (40). This study, which was based on questionnaire fertility data, was not of adequate 

sample size. Several studies provide convincing evidence that 1-BP is a reproductive toxicant in the 

rat. A two-generation study (58) demonstrated adverse reproductive effects associated with a range 

of concentrations of 1-BP. The consistency of effects across the two generations and lack of significant effects on pubertal indices suggests that 1-BP is an adult, but not a perinatal or juvenile toxicant 

with respect to adverse effects on reproduction. The Expert Panel considered this study relevant since 

it was conducted under GLP conditions, and protocols were consistent with U.S. EPA’s harmonized 

Reproductive Test Guidelines. A second inhalation toxicity study by Ichihara et al. (57) provides 

complementary information about the male reproductive toxicity of 1-BP in rats that is consistent 
II-44

Appendix II

with the results of the WIL Research Laboratories study. These data are assumed relevant to judging 

hazard potential of 1-BP exposures in humans.

4.4 Summary of Reproductive Toxicity

There are insufficient data upon which to evaluate the reproductive toxicity of 1-BP in humans.

Reproductive studies, including a two-generation study, were conducted in rats. Major findings of 

these studies are included in Table 4-3.

Table 4-3. Summary of Reproductive Toxicity Inhalation Studies

Concentration 

in ppm (mg/m3)

Exposure 

Regimen

Species/

Strain Concentration: Effect Reference

100 (503)

250 (1,257)

500 (2,514)

750 (3,771) 

[F0 only]

6h/7d/10 wk 

prior to mating 

and during gestation and most 

of lactation.

Whole body.

Male and 

female 

CD Rat

NOAEC= 100 ppm (503 mg/m3

250 ppm (1,257 mg/m3):

↑Estrous cycle length in F1

↓Prostate weight (F0)

500 ppm (2,514 mg/m3):

↑Estrous cycle length 

↓Normal sperm and sperm motility 

↓Epididymis and prostate (F0) weights 

↓Fertility, implantation sites, and litter size

↑Precoital interval

750 ppm (3,771 mg/m3):

↑Estrous cycle length 

↑Ovarian follicular cysts and ↓ corpora lutea 

↓Sperm count, normal sperm and sperm motility

↓Ovary weight and numbers of corpora lutea

↓Epididymis, prostate, seminal vesicle and pituitary 

weights

↓Mating 

↑Precoital interval, and complete infertility

WIL Research 

Laboratories 

(58)

200 (1,006)

400 (2,012)

800 (4,025)

8h/12 wk

Whole body.

Male 

Wistar 

Rats

200 ppm (1,006 mg/m3):

↓Absolute and relative seminal vesicle weight

400 ppm (2,012 mg/m3):

↑Retained elongated spermatids 

↓Sperm count and motility and ↑tailless sperm 

↓Absolute seminal vesicle, epididymides, and pituitary weight and relative seminal vesicle weight

800 ppm (4,025 mg/m3):

↑Retained elongated spermatids and degenerating 

spermatocytes 

↓Sperm count and motility

↑Tailless sperm and abnormal sperm

Vacuolated seminiferous epithelium in 2/9 rats

Epididymis, prostate, and seminal vesicle lesions

↓Testosterone

↓Absolute seminal vesicle, epididymides, prostate, 

and pituitary weight and relative seminal vesicle 

and epididymides weight

Ichihara et al. 

(57)

h = hours; d = days; wk = week

↑=Increased Effect; ↓=Decreased Effect

F0=Effects observed only in F0

F1=Effects observed only in F1.
Appendix II

II-45

The two-generation study provides sufficient data to indicate that repeated chronic inhalation exposure 

of female Sprague-Dawley rats to 1-BP at doses of 250 ppm (1,257 mg/m3) and higher results in reproductive toxicity (58). Effects included a dose-related increase in estrous cycle length in F1 females 

exposed to ≥ 250 ppm (1,257 mg/m3) and F0 females exposed to ≥ 500 ppm. Follicular cysts were seen 

in ovaries of F0 females exposed to 750 ppm (3,771 mg/m3) and were accompanied by decreased ovarian size and decreased numbers of corpora lutea (58). Reduced fertility and litter size were observed 

in the F0 and F1 generations at ≥500 ppm (2,514 mg/m3), but the experimental design did not permit 

differentiation as to whether these effects were due to reduced female or male fertility, or both.

There are sufficient data to indicate that repeated inhalation exposure of male rats to 1-BP results in 

reproductive toxicity at doses of 200 ppm (1,006 mg/m3) and higher. Effects in a two-generation study 

included decreased prostate weight in F0 males at 250 ppm (1,257 mg/m3), and dose-related decreases 

in percentages of normal sperm and motile sperm in F0 and F1 generations at ≥500 ppm (2,514 mg/

m3) (58). Decreased epididymal sperm count, epididymal weight, and seminal vesicle weight were observed at the 750 ppm (3,771 mg/m3) dose. Reduced fertility and litter size were observed in the F0 and 

F1 generations but the experimental design did not permit differentiation as to whether these effects 

were due to reduced female or male fertility, or both. Testicular toxicity consistent with the above study 

was also characterized in a subchronic inhalation study (57). Decreased absolute and relative seminal 

vesicle weights were observed at 200 ppm (1,006 mg/m3). Histopathological changes were observed 

in epididymides, prostate, and seminal vesicles at a dose of 800 ppm (4,025 mg/m3). The presence of 

retained elongated spermatids was increased at doses of 400 and 800 ppm (2,012 and 4,025 mg/m3), 

and reductions in sperm count and motility were observed. Plasma testosterone levels were reduced at 

800 ppm (4,025 mg/m3) (57). The Expert Panel noted a conclusion by Ichihara et al. (57) that the main 

effect in testis is spermatid retention beyond Stage VIII. The Panel concludes that such effects are consistent with altered Sertoli cell function or impaired endocrine support of spermatogenesis.

The Expert Panel selected a NOAEC of 100 ppm (503 mg/m3) for the two-generation reproductive 

toxicity study (58), and opined that reduced fertility in the two-generation study was due to reproductive toxicity in both males and females. This was based on the observation that exposure to 2,514

mg/m3 (500 ppm) increased estrous cycle length and compromised sperm quality (as discussed above 

in separate summaries for male and female rats). Further, the Panel noted that the male and female 

reproductive systems may be equally sensitive since decreased prostate weight at 250 ppm (58) and 

decreased seminal vesicle weight at 200 ppm (57), as well as extended estrous cycles in F1 females 

at 250 ppm occurred at similar concentrations. However, difficulties in analyzing the length of the 

estrous cycle when some of the animals were not cycling precluded a definitive statistical analysis on 

this last point. Lastly, the Expert Panel noted consistency of effects across the two generations and 

stated there was no evidence of increased sensitivity in developing rats exposed in utero and indirectly through mother’s milk, or during pubertal development.

Summary Statements

There is insufficient evidence in humans that 1-BP causes reproductive toxicity due to an absence of 

data.

There is sufficient evidence in female rats that exposure to 1-BP causes reproductive toxicity manifested as ovarian dysfunction following inhalation at ≥250–500 ppm daily for 6 h/d for 10 weeks. 
II-46

Appendix II

Subfertility is observed following inhalation at ≥ 500 ppm under the same conditions. These data are 

assumed relevant to consideration of human risk.

There is sufficient evidence in male rats that exposure to 1-BP causes reproductive toxicity manifested 

as decreased secondary sex organ weights following inhalation at ≥200–500 ppm daily for 6–8 h/day 

for 10–12 weeks. The data are assumed relevant to consideration of human risk.
Appendix II

II-47

5.0 SUMMARIES, CONCLUSIONS AND CRITICAL DATA NEEDS

5.1 Summary and Conclusions of Reproductive and Developmental Hazards

Developmental Toxicity

Prenatal developmental toxicity was assessed in Crl:CD rats (18). The data are sufficient to conclude 

that 1-BP caused developmental toxicity, in the form of decreased fetal weight and increased incidence 

of skeletal variations, in rats exposed to the compound by inhalation on a daily basis during the period 

of in utero development. The skeletal effects are typical of those associated with developmental delay 

and are believed to be reversible. The skeletal effects occurred in pups whose dams were exposed 6 

hours/day to concentrations of 503 ppm (2,530 mg/m3) and higher; a benchmark analysis of the fetal 

weight data indicated a BMD that detected a 5% change was 561 ppm (central estimate) with a lower 

95th percent confidence limit of 305 ppm. These data are assumed relevant for assessing human hazard. No information was available on developmental outcome after 1-BP exposure in humans.

Reproductive Toxicity

Reproductive effects of 1-BP were observed in a two-generation inhalation study in Crl:CD rats (58). 

Decreased fertility, decreased numbers of implantation sites and litter size and increased precoital interval were observed after exposure at concentrations of 500 ppm (2,514 mg/m3) and higher. These effects could be attributable to effects on either the male or female parent. Evaluation of other endpoints 

indicated adverse effects in both sexes. In males, prostate weight was decreased at concentrations of 

250 ppm (1,257 mg/m3) and higher, and there were effects on seminal vesicle weight and sperm quality 

at higher concentrations. Effects in females included an increase in ovarian follicular cysts at 750 ppm 

(3,771 mg/m3). There was also an increase in estrous cycle length that was judged to be 1-BP-related 

at 250 ppm (1,257 mg/m3) and higher. The NOAEC for this study was 100 ppm (503 mg/m3).

A subchronic inhalation study in male Wistar rats confirms the effect on reproductive organ weights 

(57). These effects were observed at the lowest concentration tested, 200 ppm (1,006 mg/m3). Histopathologic evidence of inhibited spermiation was also observed in this study at concentrations of 400 

ppm (2,012 mg/m3) and higher.

There is sufficient evidence to conclude that inhaled 1-BP causes reproductive toxicity in male and 

female rats. The NOAEC for these effects was 100 ppm (503 mg/m3). These results are assumed relevant for human hazard assessment. 

The human data on potential effects of 1-BP are too limited in content to conclude that 1-BP is a human 

reproductive or developmental toxicant.

5.2 Summary of Human Exposure

Within the United States, 1-BP is used as a solvent in spray adhesives (16), cold bath degreasing 

(25), and precision cleaning (10). 1-BP may also be used as a solvent for fats, waxes, or resins or as 

an intermediate in the synthesis of pharmaceuticals, insecticides, quaternary ammonium compounds, 

flavors or fragrances (1). In the future it is possible that 1-BP may be used as a substitute for hydrochlorofluorocarbons (HCFCs) (20), but current usage of 1-BP is less than 5 million pounds/year (10). 

No information was found that documents exposure of the public to 1-BP through contact with air, 
II-48

Appendix II

drinking water, food, or consumer products. 

NIOSH collected 8-hour TWA personal breathing zone measurements for 1-BP in 3 plants where 

1-BP-containing spray adhesives were used (n=99) and in 1 plant where 1-BP was used as a cold 

bath degreaser (n=20). In the plants where 1-BP was used as a solvent in spray adhesives, exposures 

ranged from 18 to 381 ppm (mean=142 ppm) (26-28). After ventilation control improvements had 

been implemented in two of the adhesives-using plants, NIOSH found that exposures had decreased 

to a range of 1.2–58 ppm (n=64; mean=19 ppm) (16, 29). These surveys demonstrated that exposures 

may be significantly reduced by ventilation control. In the plant where 1-BP was used in a cold bath 

degreaser that had been isolated in an enclosed room with local exhaust, only 7 of 20 workers who 

used the degreaser at least once a day had 8-hour personal TWA exposures that exceeded the minimal 

quantification limit of 0.02 ppm. Their exposures ranged from 0.04 to 0.63 ppm (25). Numerous additional exposure measurements have been collected by industry, but those data were not assessed by 

the Panel. The exposure measurements evaluated were from a few selected locations and cannot be 

considered to represent the full cross-section of exposure levels nationwide.

It is likely that worker exposures also occur through dermal contact with 1-BP. No studies have yet 

evaluated dermal exposure. Biological monitoring may be the best way to evaluate the contribution 

of dermal exposure to total absorbed dose.

5.3 Overall Conclusions 

Available human data are insufficient to draw conclusions on the potential for reproductive or developmental toxicity. Available data are sufficient to conclude that 1-BP exposure can induce developmental 

and reproductive toxicity in rats. In evaluating the potential effects on human reproduction, the rat data 

are assumed to be relevant for humans. Accordingly, dose levels were identified from animal studies 

to use in this evaluation. 

• A benchmark concentration 95th percentile lower confidence limit of 305 ppm (1,534 mg/m3) 

was identified from a rat inhalation developmental toxicity. 

• A LOAEC of 250 ppm (1,257 mg/m3) for female reproduction (NOAEC=100 ppm [503 mg/m3]

was identified from an inhalation, two-generation reproductive toxicity study.

• A LOAEC of 200 ppm (1,006 mg/m3) for male reproduction (NOAEC=100 ppm [503 mg/m3]

was identified from the Ichihara et al. (57) study and WIL Research Laboratories (58) study. 

Available data in rats suggest that adverse effects on reproduction and development can occur independent of systemic toxicity; the mechanisms that lead to reproductive or developmental toxicity are 

unknown. In addition, there are no relevant kinetic or metabolism data for 1-BP to develop dosimetric 

comparisons. As a result, exposure concentrations from animal studies were used to compare directly 

to human exposure concentrations to ascertain levels of concern.

Limited occupational exposure data are available. NIOSH collected 8-hour TWA personal breathing 

zone measurements for 1-BP in 3 plants where 1-BP-containing spray adhesives were used (n=99) 

and in 1 plant where 1-BP was used as a cold-bath degreaser (n=20). In the plants where 1-BP was 

being used as a spray adhesive, exposures ranged from 18 to 381 ppm (mean=142). After ventilation 

control improvements had been implemented in two of the adhesives-using plants, NIOSH found that 
Appendix II

II-49

exposures had decreased to a range of 1.2–58 ppm (n=64; mean=19). In the plant where 1-BP was 

used as a cold-bath degreaser, 7 of 20 8-hour personal TWA exposures exceeded the minimal quantification limit (MQL) of 0.02 ppm. Of the 7 measurements with concentrations higher than the MQL, 

the values ranged from 0.04 to 0.63 ppm; the degreaser had recently been enclosed in a room with 

local exhaust ventilation installed to vent vapors outside the workplace. The exposure measurements 

evaluated were from a few selected locations and cannot be considered an accurate representation 

of occupational exposure levels nationwide. In addition, no data are available to quantify the contribution of occupational dermal exposure to total daily dose. Workplace air concentrations fall into 

a broad range of inhalation exposures. Furthermore, no data are available to estimate consumer or 

environmental exposure. Thus, the Expert Panel can only compare the reported range of workplace 

air concentrations to the critical concentrations identified in the animal studies. 

Considering the workplace air concentrations summarized in the previous paragraph, and provided 

there is no additional exposure from other sources and routes:

• The Expert Panel expressed minimal concern for adverse effects on human reproduction and 

development in situations where exposures were intermittent and well-controlled, as in the example of the cold-bath degreaser.

• The Expert Panel expressed serious concern at the upper end of the exposure range, as in the 

example of the poorly controlled spray adhesive applications.

• The Expert Panel concluded that considerable uncertainty remains as to the safety of the intermediate range of exposure concentrations. The Panel was unable to assign a level of concern 

associated with such exposures.

5.4 Critical Data Needs

Critical data needs are defined as tests or experiments that could provide information to substantially 

improve an assessment of human reproductive risks. The items listed below under Exposure and 

Effects are considered by the Panel as critical data needs. 

Exposure:

• Because of the limited data currently available, usage information in occupational settings and 

consumer products is needed. This would include data on the specific industries, operations, 

volumes and numbers of workers potentially exposed. For consumers, information on products 

containing 1-BP is needed. 

• No data are currently available on dermal absorption of 1-BP. As this may be a significant route 

of human exposure, percutaneous absorption of 1-BP should be evaluated.

• Given concerns about multiple routes of exposure, the development of a validated method for 

determining total absorbed dose would significantly contribute to human risk evaluation.

Effect:

• A well conducted study of men and women occupationally exposed to 1-BP is urgently needed. 

At a minimum, such a study should include a thorough exposure assessment and comprehensive evaluation of neurological, hematopoietic, and reproductive endpoints. The study should 

have adequate statistical power and collect data on potential confounding factors.

Although not considered critical data needs, the following studies would provide information that 
II-50

Appendix II

would contribute to our understanding of the toxicity of 1-BP.

• Basis of Toxicity. Because 1-BP is structurally related to a group of haloalkanes with known 

reproductive toxicity, mechanistic studies evaluating these compounds would be useful to identify pathways of activation and targets. 

• Metabolism. Because only very limited information is currently available, additional studies of 

the metabolism of 1-BP would be useful. In particular, the role of glutathione in 1-BP metabolism and the role of metabolic activation of 1-BP should be explored.
Appendix II

II-51

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Appendix II

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Appendix III

PUBLIC COMMENTS

ON THE 1-BROMOPROPANE

EXPERT PANEL REPORT

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Appendix III
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Appendix III