TOXICOLOGICAL PROFILE FOR

CHLOROMETHANE

U.S. DEPARTMENT OF HEALTH AND HUMAN SERVICES

Public Health Service

Agency for Toxic Substances and Disease Registry

December 1998
CHLOROMETHANE ii

DISCLAIMER

The use of company or product name(s) is for identification only and does not imply endorsement by the

Agency for Toxic Substances and Disease Registry.
CHLOROMETHANE iii

UPDATE STATEMENT

A Toxicological Profile for Chloromethane was released in September 1997. This edition supersedes any

previously released draft or final profile.

Toxicological profiles are revised and republished as necessary, but no less than once every three years.

For information regarding the update status of previously released profiles, contact ATSDR at:

Agency for Toxic Substances and Disease Registry

Division of Toxicology/Toxicology Information Branch

1600 Clifton Road NE, E-29

Atlanta, Georgia 30333



CHLOROMETHANE vii

QUICK REFERENCE FOR HEALTH CARE PROVIDERS

Toxicological Profiles are a unique compilation of toxicological information on a given hazardous substance.

Each profile reflects a comprehensive and extensive evaluation, summary, and interpretation of available

toxicologic and epidemiologic information on a substance. Health care providers treating patients potentially

exposed to hazardous substances will find the following information helpful for fast answers to often-asked

questions.

Primary Chapters/Sections of Interest

Chapter 1: Public Health Statement: The Public Health Statement can be a useful tool for educating

patients about possible exposure to a hazardous substance. It explains a substance’s relevant

toxicologic properties in a nontechnical, question-and-answer format, and it includes a review of the

general health effects observed following exposure.

Chapter 2: Health Effects: Specific health effects of a given hazardous compound are reported by route

of exposure, by type of health effect (death, systemic, immunologic, reproductive), and by length of

exposure (acute, intermediate, and chronic). In addition, both human and animal studies are reported

in this section.

NOTE: Not all health effects reported in this section are necessarily observed in

the clinical setting. Please refer to the Public Health Statement to identify general

health effects observed following exposure.

Pediatrics: Four new sections have been added to each Toxicological Profile to address child health issues:

Section 1.6 How Can (Chemical X) Affect Children?

Section 1.7 How Can Families Reduce the Risk of Exposure to (Chemical X)?

Section 2.6 Children’s Susceptibility

Section 5.6 Exposures of Children

Other Sections of Interest:

Section 2.7 Biomarkers of Exposure and Effect

Section 2.10 Methods for Reducing Toxic Effects

ATSDR Information Center

Phone: l-800-447-1544 (to be replaced by l-888-42-ATSDR in 1999)

or 404-639-6357 Fax:404-639-6359

E-mail: atsdric@,cdc.gov Internet: http://atsdr1.atsdr.cdc.gov:8080

The following additional material can be ordered through the ATSDR Information Center:

Case Studies in Environmental Medicine: Taking an Exposure History--The importance of taking an

exposure history and how to conduct one are described, and an example of a thorough exposure

history is provided. Other case studies of interest include Reproductive and Developmental

Hazards; Skin Lesions and Environmental Exposures; Cholinesterase-Inhibiting Pesticide

Toxicity; and numerous chemical-specific case studies.
CHLOROMETHANE viii

Managing Hazardous Materials Incidents is a three-volume set of recommendations for on-scene

(prehospital) and hospital medical management of patients exposed during a hazardous materials incident.

Volumes I and II are planning guides to assist first responders and hospital emergency department personnel

in planning for incidents that involve hazardous materials. Volume III-Medical Management Guidelines

for Acute Chemical Exposures-is a guide for health care professionals treating patients exposed to

hazardous materials.

Fact Sheets (ToxFAQs) provide answers to frequently asked questions about toxic substances.

Other Agencies and Organizations

The National Center for Environmental Health (NCEH) focuses on preventing or controlling disease, injury,

and disability related to the interactions between people and their environment outside the workplace.

Contact: NCEH, Mailstop F-29,4770 Buford Highway, NE, Atlanta, GA 30341-3724 • Phone:

770-488-7000 • FAX:770-488-7015.

The National Institute for Occupational Safety and Health (NIOSH) conducts research on occupational

diseases and injuries, responds to requests for assistance by investigating problems of health and

safety in the workplace, recommends standards to the Occupational Safety and Health

Administration (OSHA) and the Mine Safety and Health Administration (MSHA), and trains

professionals in occupational safety and health. Contact: NIOSH, 200 Independence Avenue, SW,

Washington, DC 20201 • Phone:800-356-4674 or NIOSH Technical Information Branch, Robert

A. Taft Laboratory, Mailstop C-19,4676 Columbia Parkway, Cincinnati, OH 45226-1998 • Phone:

800-35-NIOSH.

The National Institute of Environmental Health Sciences (NIEHS) is the principal federal agency for

biomedical research on the effects of chemical, physical, and biologic environmental agents on

human health and well-being. Contact: NIEHS, PO Box 12233,104 T.W. Alexander Drive,

Research Triangle Park, NC 27709 • Phone:919-541-3212.

Referrals

The Association of Occupational and Environmental Clinics (AOEC) has developed a network of clinics in

the United States to provide expertise in occupational and environmental issues. Contact: AOEC,

1010 Vermont Avenue, NW, #513, Washington, DC 20005 • Phone:202-347-4976 • FAX:202-

347-4950 • e-mail: aoec@,dgs.dnsvs.com • AOEC Clinic Director: http://occ-envmed.mc.duke.edu/oem/aoec.htm.

The American College of Occupational and Environmental Medicine (ACOEM) is an association of

physicians and other health care providers specializing in the field of occupational and environmental

medicine. Contact: ACOEM, 55 West Seegers Road, Arlington Heights, IL 60005 • Phone:847-

228-6850 • FAX:847-228-1856.
CHLOROMETHANE ix

CONTRIBUTORS

CHEMICAL MANAGER(S)/AUTHORS(S):

Alfred Dorsey, Ph.D.

ATSDR, Division of Toxicology, Atlanta, GA

Robert DeWoskin, Ph.D.

Research Triangle Institute, Research Triangle Park, NC

THE PROFILE HAS UNDERGONE THE FOLLOWING ATSDR INTERNAL REVIEWS:

1. Health Effects Review. The Health Effects Review Committee examines the health effects chapter of

each profile for consistency and accuracy in interpreting health effects and classifying end points.

2. Minimal Risk Level Review. The Minimal Risk Level Workgroup considers issues relevant to

substance-specific minimal risk levels (MRLs), reviews the health effects database of each profile,

and makes recommendations for derivation of MRLs.\

3. Data Needs Review. The Research Implementation Branch reviews data needs sections to assure

consistency across profiles and adherence to instructions in the Guidance.

CHLOROMETHANE xi

PEER REVIEW

A peer review panel was assembled for chloromethane. The panel consisted of the following members:

1. Dr. Herbert Comish, Private Consultant, 830 W. Clark Road, Ypsilanti, MI;

2. Dr. Anthony DeCaprio, Associate Professor, State University of New York at Albany, Albany, NY;

3. Dr. Theodore Mill, Senior Scientist, SRI International, Menlo Park, CA; and

4. Dr. Nancy Tooney, Associate Professor, Brooklyn, NY.

These experts collectively have knowledge of chloromethane’s physical and chemical properties, toxicokinetics, key health end points, mechanisms of action, human and animal exposure, and quantification of risk

to humans. All reviewers were selected in conformity with the conditions for peer review specified in Section

104(1)(13) of the Comprehensive Environmental Response, Compensation, and Liability Act, as amended.

Scientists from the Agency for Toxic Substances and Disease Registry (ATSDR) have reviewed the peer

reviewers’ comments and determined which comments will be included in the profile. A listing of the peer

reviewers’ comments not incorporated in the profile, with a brief explanation of the rationale for their

exclusion, exists as part of the administrative record for this compound. A list of databases reviewed and a

list of unpublished documents cited are also included in the administrative record.

The citation of the peer review panel should not be understood to imply its approval of the profile’s final

content. The responsibility for the content of this profile lies with the ATSDR









CHLOROMETHANE 1

1. PUBLIC HEALTH STATEMENT

This public health statement tells you about chloromethane and the effects of exposure.

The Environmental Protection Agency (EPA) identifies the most serious hazardous waste sites in

the nation. These sites make up the National Priorities List (NPL) and are the sites targeted for

long-term federal cleanup. Chloromethane has been found in at least 172 of the 1,467 current or

former NPL sites. However, it’s unknown how many NPL sites have been evaluated for this

substance. As more sites are evaluated, the sites with chloromethane may increase. This is

important because exposure to this substance may harm you and because these sites may be

sources of exposure.

When a substance is released from a large area, such as an industrial plant, or from a container,

such as a drum or bottle, it enters the environment. This release does not always lead to

exposure. You are exposed to a substance only when you come in contact with it. You may be

exposed by breathing, eating, or drinking the substance or by skin contact.

If you are exposed to chloromethane, many factors determine whether you’ll be harmed. These

factors include the dose (how much), the duration (how long), and how you come in contact with

it. You must also consider the other chemicals you’re exposed to and your age, sex, diet, family

traits, lifestyle, and state of health.

1.1 WHAT IS CHLOROMETHANE?

Chloromethane (also known as methyl chloride) is a clear, colorless gas. It has a faint, sweet odor

that is noticeable only at levels which may be toxic. It is heavier than air and is extremely

flammable.

Chloromethane is produced in industry, but the it also occurs naturally, and most of the

chloromethane that is released to the environment (estimated at up to 99%) comes from natural
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1. PUBLIC HEALTH STATEMENT

sources. Chloromethane is always present in the air at very low levels. Most of the naturally

occurring chloromethane comes from chemical reactions that occur in the oceans or from

chemical reactions that occur when materials like grass, wood, charcoal, and coal are burned. It

is also released to the air as a product of some plants or from rotting wood.

Chloromethane is produced industrially. In the past, chloromethane was widely used as a

refrigerant, but refrigerators no longer use chloromethane because of its toxic effects. It was also

used as a foam-blowing agent and as a pesticide or fumigant. A working refrigerator that is more

than 30 years old may still contain chloromethane, and may be a source of high-level exposure.

Today, nearly all commercially produced chloromethane is used to make other substances, mainly

silicones (72% of the total chloromethane used). Other products that are made from reactions

involving chloromethane include agricultural chemicals (8%), methyl cellulose (6%), quaternary

amines (5%), and butyl rubber (3%). Chloromethane is completely used up so that by the end of

the process there is no or little chloromethane left to be released, disposed of, or reused. It is,

however, found as a pollutant in municipal waste streams from treatment plants and industrial

waste streams as a result of formation or incomplete removal. There are also some manufacturing

processes for vinyl chloride that result in chloromethane as an impurity in the vinyl chloride end

product.

See Chapters 3 and 4 for more information on the nature and uses of chloromethane.

1.2 WHAT HAPPENS TO CHLOROMETHANE WHEN IT ENTERS THE

ENVIRONMENT?

Chloromethane has been identified in air, surface water, groundwater, soil, and sediment. Most

releases of chloromethane will be to the air. Chloromethane rapidly moves through the air and is

present at very low concentrations throughout the atmosphere. Naturally occurring

chloromethane is continuously released into the atmosphere from oceans, rotting wood, forest

fires, and volcanoes. When grass, coal, or wood are burned, chloromethane is released to the air.

The burning of grasslands and forests accounts for about 20% (ranging from 10 to 40%) of the

total chloromethane in the air. Releases from the oceans account for another 80 to 90%.
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1. PUBLIC HEALTH STATEMENT

Chemical companies release some chloromethane gas to the air during the production of

chloromethane or when it is used to make other substances, but the amount is relatively very small

(0.2 to 0.6%) compared to natural sources of the total chloromethane in the atmosphere.

Chloromethane breaks down very slowly (months to years) in the air. Chloromethane can

dissolve in water, and small amounts of chloromethane in air may go into surface waters or

groundwater when it rains. Chloromethane can also enter water from industrial or municipal

waste streams or from water that comes in contact with municipal or hazardous waste sites.

Chemical companies generally treat waste water to remove chloromethane.

Chloromethane is a gas at room temperature, and when present in water, most will evaporate

rapidly to the air. Small amounts of dissolved chloromethane may move below the surface of the

water or be carried to the groundwater. It breaks down very slowly (months to years) in plain

water, but certain kinds of small organisms in water may break it down more quickly (days).

When chloromethane comes in contact with soil it does not stick to the soil. Most of the

chloromethane in soil will move to the air. Some may dissolve in water and move down through

the soil layers to the groundwater or into well water. Chloromethane does not concentrate in

sediments, or in animals and fish in the food chain.

See Chapters 4 and 5 for more information on how chloromethane moves through the

environment.

1.3 HOW MIGHT I BE EXPOSED TO CHLOROMETHANE?

Most (99%) of the chloromethane in the environment comes from natural sources. Because

chloromethane is made in the oceans by natural processes, it is present in air all over the world.

In most areas, the outside air contains less than 1 part of chloromethane in a billion parts of air

(ppb). In cities, human activities, mostly combustion and manufacturing, add to the

chloromethane in the air, resulting in somewhat higher levels, up to 1 ppb. Chloromethane

exposures in the less than 5 ppb range are much lower (1,000 to 10,000 times lower) than the
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1. PUBLIC HEALTH STATEMENT

exposure levels that have been shown to have toxic effects. Chloromethane is also present in

some lakes and streams and has been found in drinking water (including well water) at very low

levels in the parts per billion to part per trillion (ppt) range. Chloromethane may be formed to a

small extent in tap water that has been chlorinated. You could be exposed to levels in air higher

than the background levels if you live near a hazardous waste site or an industry that uses

chloromethane. If chloromethane is present at waste sites, it can move through the soil into

underground water. We have very little information on the levels of chloromethane in

groundwater. Chloromethane is not generally found in food.

The people most likely to be exposed to increased levels of chloromethane in the air are those

who work in chemical plants where it is made or used. Chloromethane is also an impurity in vinyl

chloride when the vinyl chloride is produced by heating another chemical, 1,2-dichloroethane.

Exposure to chloromethane can occur from this kind of vinyl chloride or the disposal of vinyl

chloride waste from this process. The proper enforcement of workplace regulations and the

recycling of chloromethane during the manufacturing process help prevent worker exposures to

levels that would be considered harmful. In the past (more than 30 years ago), chloromethane

was also widely used as the refrigerant in refrigerators. Some of these old refrigerators may still

be in use or may be located in storage areas. Chloromethane may be released from leaks in these

refrigerators, leading to potentially very high exposures, especially in areas with poor ventilation.

Liquid contact could also occur following a leak in an older refrigerator containing

chloromethane. Other general population sources of chloromethane exposure include cigarette

smoke; polystyrene insulation; aerosol propellants; home burning of wood, grass, coal, or certain

plastics; and chlorinated swimming pools. The chloromethane in the outdoor environment,

however, is almost totally from natural sources.

In Chapter 5, you can find more information on how you might be exposed to chloromethane.
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1. PUBLIC HEALTH STATEMENT

1.4 HOW CAN CHLOROMETHANE ENTER AND LEAVE MY BODY?

Chloromethane can enter your body through your lungs, if you breathe it in, or through your

digestive tract if you drink water containing it. The chloromethane that you breathe in or drink

rapidly enters the bloodstream from the lungs or the digestive tract and moves throughout the

body to organs such as the liver, kidneys, and brain. Very little of the chloromethane that enters

the body remains unchanged. The portion of the chloromethane that does not get changed in your

body leaves in the air you breathe out. The rest is changed in your body to other breakdown

products that mostly leave in the urine. The breakdown process takes anywhere from a few hours

to a couple of days.

Breathing air that contains chloromethane vapor is the most likely way you would be exposed if

you live near a hazardous waste site. Contact with liquid chloromethane is rare, but could occur

in an industrial accident from a broken metal container. Prolonged skin contact with liquid

chloromethane is unlikely, because it turns into a gas very quickly at room temperature. It is not

known how much chloromethane liquid or gas will enter the body through contact with the skin,

but the amount is probably very low.

See Chapter 2 for more information on how chloromethane can enter and leave the body.

1.5 HOW CAN CHLOROMETHANE AFFECT MY HEALTH?

If the levels are high enough (over a million times the natural levels in outside air), even brief

exposures to chloromethane can have serious effects on your nervous system, including

convulsions, coma, and death. Some people have died from breathing chloromethane that leaked

from refrigerators in rooms that had little or no ventilation. Most of these cases occurred more

than 30 years ago, but this kind of exposure could still happen if you have an old refrigerator that

contains chloromethane as the refrigerant. Some people who were exposed to high levels of

chloromethane while they were repairing refrigerators did not die, but they did have toxic effects

like staggering, blurred or double vision, dizziness, fatigue, personality changes, confusion,
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1. PUBLIC HEALTH STATEMENT

tremors, uncoordinated movements, nausea, or vomiting. These symptoms can last for several

months or years. Complete recovery has occurred in some cases, but not in others. Exposure to

chloromethane can also harm your liver and kidney, or have an effect on your heart rate and blood

pressure. If you work in an industry that uses chloromethane to make other products, you might

be exposed to levels that could cause symptoms resembling drunkenness and impaired ability to

perform simple tasks.

To protect the public from the harmful effects of toxic chemicals and to find ways to treat people

who have been harmed, scientists use many tests.

One way to see if a chemical will hurt people is to learn how the chemical is absorbed, used, and

released by the body; for some chemicals, animal testing may be necessary. Animal testing may

also be used to identify health effects such as cancer or birth defects. Without laboratory animals,

scientists would lose a basic method to get information needed to make wise decisions to protect

public health. Scientists have the responsibility to treat research animals with care and

compassion. Laws today protect the welfare of research animals, and scientists must comply with

strict animal care guidelines.

Harmful liver, kidney, and nervous system effects have developed after animals breathed air

containing high levels of chloromethane (one million times higher than natural levels). Some of

these animals died from exposure to high levels of chloromethane. Similar effects were seen in

animals that breathed low levels continuously and animals that breathed high levels for shorter

periods with some breaks from exposure.

Animals that breathed relatively low test levels of chloromethane (but still one hundred thousand

to one million times higher than background levels people are exposed to) over a long period

(weeks to months) had slower growth and developed brain damage. Some male animals were less

fertile or even sterile or produced sperm that were damaged. Females that became pregnant by

the exposed males lost their developing young.
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1. PUBLIC HEALTH STATEMENT

Male mice that breathed air containing chloromethane (one million ppb) for 2 years developed

tumors in their kidneys, but female mice and male and female rats did not develop tumors. It is

not known whether chloromethane can cause sterility, miscarriages, birth defects, or cancer in

humans. The Department of Health and Human Services (DHHS) has not classified

chloromethane for carcinogenic effects. The International Agency for Research on Cancer

(IARC) calls chloromethane a Group 3 compound, which means it cannot be determined whether

or not it is a carcinogen because there is not enough human or animal data. The Environmental

Protection Agency (EPA) considers chloromethane possibly carcinogenic to humans (i.e.,

Group C) based on limited evidence of carcinogenicity in animals.

See Chapter 2 for more information on how chloromethane can affect your health.

1.6 HOW CAN CHLOROMETHANE AFFECT CHILDREN?

This section discusses potential health effects from exposures during the period from conception

to maturity at 18 years of age in humans.

Children may be exposed to chloromethane from the same sources as adults. These sources

include outside air, indoor air, and drinking water. Exposures are generally well below safe

levels. The people most heavily exposed to chloromethane are workers in chemical plants where

it is made or used. With proper safeguards to prevent children from entering these work areas,

children would not be expected to have high exposures. Old refrigerators that used

chloromethane as a refrigerant and that are leaking chloromethane, however, are a potential

source that could result in high exposures to children.

There have been no studies on whether children are more or less susceptible than adults to

harmful health effects from a given amount or chloromethane. We do not know if chloromethane

affects the developing fetus or the development of young children. There is no information on

exposure to high levels of chloromethane in children (for example, accidental poisoning), but we
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1. PUBLIC HEALTH STATEMENT

expect similar effects to those seen in adults (including harmful effects on the nervous system and

kidneys). We do not know if the effects for children would be similar to those in adults for lower

levels or for longer exposures. There have been no studies where young animals were exposed to

chloromethane. Animal studies have shown that female adult rats that were exposed to

chloromethane during pregnancy had young that were smaller than normal, with underdeveloped

bones, and possibly abnormal hearts (although this effect remains uncertain).

We do not know if chloromethane or its breakdown products in the body can cross the placenta

and enter into the developing young. We also do not know if chloromethane or its breakdown

products can enter into a nursing woman’s milk. We do know that chloromethane is broken

down and eliminated from the body very quickly in adults. Although we expect the breakdown

and elimination of chloromethane to be the same in children as in adults, more studies are needed

to answer this question and the other questions concerning the movement of chloromethane into

the fetus or into nursing young through breast milk, and what amounts might result in harmful

effects.

More information on the effects of chloromethane can be found in Chapters 2 and 5.

1.7 HOW CAN FAMILIES REDUCE THE RISK OF EXPOSURE TO

CHLOROMETHANE?

If your doctor finds that you have been exposed to significant amounts of chloromethane, ask

your doctor if children may also be exposed. When necessary your doctor may need to ask your

state Department of Public Health to investigate.

Families can reduce the risk of exposure to chloromethane by properly disposing of the older

types of refrigerators that used chloromethane as a refrigerant. If you live near a chemical plant

that makes or uses chloromethane, or near a hazardous waste site that stores it, you should teach

your children not to play in or around these sites. If family members work in a chemical facility

that manufactures or uses chloromethane, they should become familiar with the safety practices

that are used to prevent exposure to harmful levels. They should also become familiar with their
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1. PUBLIC HEALTH STATEMENT

rights to obtain information from their employer concerning the use of chloromethane and any

potential exposure they might be subject to at work.

You should teach your children about the dangers of breathing smoke from burning vinyl plastic

or silicone rubber products, and should properly dispose of all such products. Chloromethane (as

well as other toxic compounds) is released from burning polyvinyl chloride. If you are concerned

that chloromethane may be in your drinking water, you can have your water tested and learn

about the proper water filter to use to remove chloromethane (as well as other possible

contaminants) from your drinking water. If you are concerned that products you are using might

contain chloromethane, you can check the labels for ingredients or contact the manufacturer for

additional information.

Chapter 5 contains additional information on the how you or your family might be exposed to

chloromethane.

1.8 IS THERE A MEDICAL TEST TO DETERMINE WHETHER I HAVE BEEN

EXPOSED TO CHLOROMETHANE?

There are no known reliable medical tests to determine whether you have been exposed to

chloromethane. Symptoms resembling drunkenness and food poisoning, along with a sweet odor

of the breath, may alert doctors that a person has been exposed to chloromethane.

See Chapters 2 and 6 for more information on tests to determine exposure to chloromethane.

1.9 WHAT RECOMMENDATIONS HAS THE FEDERAL GOVERNMENT MADE TO

PROTECT HUMAN HEALTH?

The federal government develops regulations and recommendations (sometimes called advisories

or guidelines) to protect public health. Regulations can be enforced by law. Federal agencies that

develop regulations for toxic substances include the Environmental Protection Agency (EPA), the

Occupational Safety and Health Administration (OSHA), and the Food and Drug Administration
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1. PUBLIC HEALTH STATEMENT

(FDA). Recommendations provide valuable guidelines to protect public health but cannot be

enforced by law. Federal organizations that develop recommendations for toxic substances

include the Agency for Toxic Substances and Disease Registry (ATSDR) and the National

Institute for Occupational Safety and Health (NIOSH).

Regulations and recommendations can be expressed in not-to-exceed levels in air, water, soil, or

food that are usually based on levels that affect animals; then they are adjusted to help protect

people. Sometimes these not-to-exceed levels differ among federal organizations because of

different exposure times (an 8-hour workday or a 24-hour day), the use of different animal

studies, or other factors.

Recommendations and regulations are also periodically updated as more information becomes

available. For the most current information, check with the federal agency or organization that

provides it. Some regulations and recommendations for chloromethane include the following:

To protect workers, OSHA has set a regulation of an average permissible exposure limit of 50

parts of chloromethane per million parts of workroom air (50 ppm) during each 8-hour work shift

in a 40-hour workweek.

See Chapter 7 for more information on government recommendations to protect human health

from the toxic effects of chloromethane.

1.10 WHERE CAN I GET MORE INFORMATION?

If you have any more questions or concerns, please contact your community or state health or

environmental quality department or

Agency for Toxic Substances and Disease Registry

Division of Toxicology

1600 Clifton Road NE, Mailstop E-29

Atlanta, GA 30333
CHLOROMETHANE 11

1. PUBLIC HEALTH STATEMENT

* Information line and technical assistance

Phone: l-800-447-1544

Fax: (404) 639-6359

ATSDR can also tell you the location of occupational and environmental health clinics. These

clinics specialize in recognizing, evaluating, and treating illnesses resulting from exposure to

hazardous substances.

* To order toxicological profiles, contact

National Technical Information Service

5285 Port Royal Road

Springfield, VA 22161

Phone: (800) 553-6847 or (703) 487-4650

CHLOROMETHANE 13

2. HEALTH EFFECTS

2.1 INTRODUCTION

The primary purpose of this chapter is to provide public health officials, physicians, toxicologists, and

other interested individuals and groups with an overall perspective of the toxicology of chloromethane. It

contains descriptions and evaluations of toxicological studies and epidemiological investigations and

provides conclusions, where possible, on the relevance of toxicity and toxicokinetic data to public health.

A glossary and list of acronyms, abbreviations, and symbols can be found at the end of this profile.

This chapter contains descriptions and evaluations of studies and interpretation of data on the health effects

associated with exposure to chloromethane. Its purpose is to present levels of significant exposure for

chloromethane based on toxicological studies, epidemiological investigations, and environmental exposure

data. This information is presented to provide public health officials, physicians, toxicologists, and other

interested individuals and groups with (1) an overall perspective of the toxicology of chloromethane and

(2) a depiction of significant exposure levels associated with various adverse health effects.

2.2 DISCUSSION OF HEALTH EFFECTS BY ROUTE OF EXPOSURE

To help public health professionals and others address the needs of persons living or working near

hazardous waste sites, the information in this section is organized first by route of exposure- inhalation,

oral, and dermal; and then by health effect-death, systemic, immunological, neurological, reproductive,

developmental, genotoxic, and carcinogenic effects. These data are discussed in terms of three exposure

periods-acute (14 days or less), intermediate (l-364 days), and chronic (365 days or more).

Levels of significant exposure for each route and duration are presented in Table 2-l and illustrated in

Figure 2-1. The points in the figures showing no-observed-adverse-effect levels (NOAELs) or lowestobserved-adverse-effect levels (LOAELs) reflect the actual doses (levels of exposure) used in the studies.

LOAELS have been classified into “less serious” or “serious” effects. “Serious” effects are those that evoke

failure in a biological system and can lead to morbidity or mortality (e.g., acute respiratory distress or

death). “Less serious” effects are those that are not expected to cause significant dysfunction or death, or
CHLOROMETHANE 14

2. HEALTH EFFECTS

those whose significance to the organism is not entirely clear. ATSDR acknowledges that a considerable

amount of judgment may be required in establishing whether an end point should be classified as a

NOAEL, “less serious” LOAEL, or “serious” LOAEL, and that in some cases, there will be insufficient

data to decide whether the effect is indicative of significant dysfunction. However, the Agency has

established guidelines and policies that are used to classify these end points. ATSDR believes that there is

sufficient merit in this approach to warrant an attempt at distinguishing between “less serious” and

“serious” effects. The distinction between “less serious” effects and “serious” effects is considered to be

important because it helps the users of the profiles to identify levels of exposure at which major health

effects start to appear. LOAELs or NOAELs should also help in determining whether or not the effects

vary with dose and/or duration, and place into perspective the possible significance of these effects to

human health.

The significance of the exposure levels shown in the Levels of Significant Exposure (LSE) tables and

figures may differ depending on the user’s perspective. Public health officials and others concerned with

appropriate actions to take at hazardous waste sites may want information on levels of exposure associated

with more subtle effects in humans or animals (LOAEL) or exposure levels below which no adverse effects

(NOAELs) have been observed. Estimates of levels posing minimal risk to humans (Minimal Risk Levels

or MRLs) may be of interest to health professionals and citizens alike.

Levels of exposure associated with carcinogenic effects (Cancer Effect Levels, CELs) of chloromethane are

indicated in Table 2-1 and Figure 2-1. Cancer effects could occur at lower exposure levels, but a range for

the upper bound of estimated excess risks, ranging from a risk of 1 in 10,000 to 1 in 10,000,000 (10-4 to

10-7), has not been developed by EPA.

Estimates of exposure levels posing minimal risk to humans (Minimal Risk Levels or MRLs) have been

made for chloromethane. An MRL is defined as an estimate of daily human exposure to a substance that is

likely to be without an appreciable risk of adverse effects (noncarcinogenic) over a specified duration of

exposure. MRLs are derived when reliable and sufficient data exist to identify the target organ(s) of effect

or the most sensitive health effect(s) for a specific duration within a given route of exposure. MRLs are

based on noncancerous health effects only and do not consider carcinogenic effects. MRLs can be derived

for acute, intermediate, and chronic duration exposures for inhalation and oral routes. Appropriate

methodology does not exist to develop MRLs for dermal exposure.
CHLOROMETHANE 15

2. HEALTH EFFECTS

Although methods have been established to derive these levels (Barnes and Dourson 1988; EPA 1990),

uncertainties are associated with these techniques. Furthermore, ATSDR acknowledges additional

uncertainties inherent in the application of the procedures to derive less than lifetime MRLs. As an

example, acute inhalation MRLs may not be protective for health effects that are delayed in development or

are acquired following repeated acute insults, such as hypersensitivity reactions, asthma, or chronic

bronchitis. As these kinds of health effects data become available and methods to assess levels of

significant human exposure improve, these MRLs will be revised.

A User’s Guide has been provided at the end of this profile (see Appendix B). This guide should aid in the

interpretation of the tables and figures for Levels of Significant Exposure and the MRLs.

2.2.1 Inhalation Exposure

2.2.1.1 Death

Thirty or more years ago, chloromethane was used as a refrigerant, and many human deaths resulted from

exposure to chloromethane vapors from leaks in home refrigerators and industrial cooling and refrigeration

systems (Baird 1954; Borovska et al. 1976; Kegel et al. 1929; McNally 1946; Thordarson et al. 1965). In

some cases, the individuals were found comatose or dead in their homes. In other cases, patients were

admitted to hospitals with typical neurological signs and symptoms of chloromethane poisoning (confusion,

staggering, slurred speech). These patients eventually became comatose, developed convulsions, and died.

The concentrations and durations of these exposures were not known.

Exposure to high concentrations of chloromethane can result in moderate to severe neurological effects (see

Section 2.2.1.4) but death does not always result if exposure ceases and medical attention is received in

time. For example, refrigerator repairmen developed neurological symptoms after exposures to

chloromethane from leaks at concentrations as high as 600,000 ppm, but no deaths resulted (Jones 1942).

In other cases death did occur. Seventeen crew members (male) were exposed for 2 days in 1963 to

chloromethane that leaked from a refrigerator on board an Icelandic fishing trawler (no estimates of

exposure levels were reported). The refrigerator was located under the sleeping quarters of the crew. In

the acute phase of the illness, nine patients exhibited abnormal neurological signs. Four died, one within

24 hours of the exposure. Two patients developed severe depression and committed suicide 11 and

18 months later. The fourth patient was” assessed as 75% disabled due to severe neurological and
CHLOROMETHANE 16

2. HEALTH EFFECTS

psychiatric disturbances, and died 10 years postexposure at the age of 34. Autopsy revealed recent

coronary occlusion which was not necessarily connected with the primary illness (Gudmundsson 1977). In

a follow-up study, Rafnsson and Gudmundsson (1997) reported an excess mortality from cardiovascular

diseases in this exposed population compared to a reference group. The excess mortality was more

prominent for the deckhands who received the higher exposures to chloromethane. The results and

conclusions from this study, however, are based upon the assumption that the reference group had similar

lifestyle factors including smoking habits and diet (which may not have been the case). There was also a

relatively low number of individuals with significant exposure.

Animals exposed to sufficiently high levels of chloromethane die after developing severe signs of

neurotoxicity. In an extensive investigation, a variety of species including rats, mice, guinea pigs, rabbits,

dogs, cats, and monkeys were exposed to lethal concentrations of chloromethane (Dunn and Smith 1947;

Smith 1947; Smith and von Oettingen 1947a, 1947b). Severe neurological effects, such as paralysis,

convulsions, and opisthotonos, developed before death. Precise determination of concentration-durationresponse relationships was not possible from these studies because of limitations including unknown purity

of chloromethane, unconventional reporting of lethality data, and generally poor reporting of details.

Nonetheless, these earlier studies demonstrated the universal response of animals to the neurotoxic and

lethal effects of chloromethane.

More recent studies provide better dose-response information. Sprague-Dawley rats were exposed to

99.5% chloromethane at 0, 200, 500, 1,000, or 2,000 ppm for 48 or 72 hours. One-half of the animals

were sacrificed immediately after exposure, and the remaining half were observed for 12 days postexposure

prior to sacrifice. At 2,000 ppm for 48 hours, rats were either lethargic, moribund or dead. At 52 hours,

rats exposed to 1,000 ppm remained lethargic; rats exposed to 2,000 ppm were all dead or moribund. At

72 hours of exposure, all rats receiving 2,000 ppm were dead. No male and 1 of 10 female rats died by

12 days postexposure to 1,000 ppm for 48 hours. Six of 10 male and 8 of 10 female rats died by 12 days

postexposure to 1,000 ppm for 72 hours. No deaths occurred at 200 or 500 ppm for up to 72 hours of

exposure. Cause of death was thought to be kidney failure (Burek et al. 1981).

Chellman et al. (1986a) studied the effects of 3-amino-l-[m-(trifluoromethyl)phenyl]-Zpyrazoline

(BW755C), a potent anti-inflammatory agent, on chloromethane-induced lethality and reproductive toxicity

in male Fischer 344 rats. Rats were exposed to 5,000 ppm chloromethane for 5 days or 7,500 ppm

chloromethane for 2 days, 6 hours/day, with or without treatment with BW755C (10 mg/kg,
CHLOROMETHANE 17

2. HEALTH EFFECTS

intraperitoneally 1 hour pre- and postexposure). Exposure to 7,500 ppm chloromethane for 2 days,

6 hours/day was fatal to 8 of 12 rats. No deaths occurred in 6 rats treated with both chloromethane and

BW755C. One of 5 rats exposed to 5,000 ppm chloromethane died. No deaths occurred in 5 rats treated

with both chloromethane and BW755C. The authors concluded that protection from

chloromethane-induced injury by BW755C was not simply the result of altered metabolism because

BW755C had no effect on tissue distribution or excretion of 14C-chloromethane and administration of

BW755C did not decrease hepatic glutathione content. The protection of BW755C may have been related

to an inhibition of leukotriene and prostaglandin synthesis.

Morgan et al. (1982) investigated the lesions induced by inhalation exposure to chloromethane in C3H,

C57BL/6, and B6C3F1 mice and in Fischer 344 rats. Ten rats/sex were exposed to chloromethane for

5 days, 6 hours/day with a break in exposure for 2 days, and then a further 4 days of exposure. Rats were

exposed to 0, 2,000, 3,500, or 5,000 ppm. Animals were sacrificed 18 hours after the last exposure or

immediately after exposure if found to be moribund. After 5 days, 6 males and 5 females exposed to

5,000 ppm, and 2 females exposed to 3,500 ppm, were killed in extremis. Five mice/sex were exposed to

chloromethane for 12 days, 6 hours/day. Mice were exposed to 0, 500, 1,000, or 2,000 ppm. In mice

exposed to 2,000 ppm, all male B6C3F1 mice were moribund or died by day 2, one C57BL/6 male died on

day 2, and others were moribund by day 5. All other mice survived except one male C3H mouse exposed

to 1,000 ppm, which died by day 11. This study confirmed the existence of species, sex, and strain

differences in susceptibility to chloromethane-induced toxicity. The authors further speculated that,

although the mechanism of death is unknown, it may be associated with liver and kidney pathology.

Chellman et al. (1986b) investigated the role of glutathione in the mediation of chloromethane-induced

toxicity in the liver, kidney, and brain of male B6C3F1 mice. In one experiment, groups of 5 mice were

exposed to chloromethane at concentrations from 500 ppm to 2,500 ppm in increments of 500 ppm with or

without pretreatment with buthionine-S,R,-sulfoximine (BSO), a depleter of glutathione (GSH), and were

observed for death up to 18 hours after exposure. The resulting mortality data was used to estimate an

approximate LC50 value. The LC50 in the non-pretreated rats was 2,200 ppm, while the LC50 for the

pretreated rats was 3,200 ppm. The authors concluded that pretreatment with BSO, and hence GSH

depletion, protected mice from the lethal effects of chloromethane. The GSH metabolic pathway appeared

to be activating toxicity rather than detoxifying.
CHLOROMETHANE 18

2. HEALTH EFFECTS

In two further experiments by Chellman et al. (1986b), 36 and 45 mice were exposed by inhalation to

1,500 ppm chloromethane for 2 weeks, 5 days/week, 6 hours/day, with or without daily pretreatment with

BSO. In the two experiments using this protocol, 10 of 36 (28%) and 5 of 45 (11%) of the mice died by the

end of the first day (6 hours) of exposure to 1,500 ppm chloromethane. In contrast, none of the

BSO-pretreated mice died after the first exposure. The authors concluded that pretreatment with BSO, and

hence GSH depletion, protected mice from the lethal effects of chloromethane. This provided further

evidence that the GSH metabolic pathway activated toxicity rather than detoxified.

Jiang et al. (1985) characterized cerebellar lesions resulting from an acute inhalation exposure to

chloromethane in female C57BL/6 mice. Ten mice each were exposed to room air or 1,500 ppm

chloromethane for 2 weeks, 5 days/week, 6 hours/day. Two mice died, and several had motor

incoordination. Only one exposure concentration was used, but the study was designed to study the

neurological and kidney effects specifically, and therefore, used an exposure regimen known to produce

these effects. The authors concluded that the brain lesions seen after exposure to chloromethane were

probably not a direct consequence of renal lesions.

Landry et al. (1985) evaluated the neurologic effects of continuous versus intermittent chloromethane

exposure in female C57BL/6 mice Groups of 12 mice each were exposed to chloromethane in whole body

inhalation chambers for 11 days either continuously (C) 22 hours/day at 0, 15, 50, 100, 150, 200, or

400 ppm or intermittently (I) 5.5 hours/day at 0, 150, 400, 800, 1,600, or 2,400 ppm. At 2,400-I ppm, the

condition of the mice gradually deteriorated until they were killed in a moribund condition after 8 or 9 days

of exposure. No deaths occurred in the 1,600-I ppm mice or in mice receiving lower intermittent exposures.

The 400-C ppm exposed mice died or were sacrificed by day 4, and the 200-C ppm group by day 5, due to

severe toxicity. Mice exposed to 150-C ppm were sacrificed in moribund condition by day 10.5. No deaths

occurred in the mice exposed to ≤ 100-C ppm. The authors concluded that exposure duration affected

susceptibility to chloromethane-induced neurotoxicity, with those continuously exposed exhibiting a

non-proportionate greater susceptibility. The authors speculated that the greater susceptibility was due to a

combination of glutathione depletion, the formation of a toxic metabolic intermediate, and the effects of

nocturnal exposure.

Wolkowski-Tyl et al. (1983a) assessed the teratogenicity of an inhalation exposure to chloromethane in

female Fischer 344 rats and B6C3F1 mice. Groups of 33 mice per exposure level were exposed to 0, 100,

500 or 1,500 ppm chloromethane in whole-body exposure chambers, 6 hours daily on gestation days (Gd)
CHLOROMETHANE 19

2. HEALTH EFFECTS

6-17. Actual chloromethane concentrations in the chambers were 0.05 (the ambient level; for the 0 dose),

102 (100 ppm), 479 (500 ppm), 1,492 (1500 ppm). At 1,492 ppm, there was severe maternal toxicity

resulting in tremors, hunched appearance, difficulty righting, disheveled fur, bloody urine, and granular cell

degradation in cerebellum with selective necrosis of neurons in the internal granular layer. All females in

this group were sacrificed on gestation days 11-14 prior to the completion of exposure to Gd 17; two

females died prior to necropsy (as early as Gd 9 after only 4 days of exposure). The authors concluded

that in B6C3F1 mice, an inhalation exposure to 1,492 ppm chloromethane resulted in severe maternal

toxicity; exposure to 102 and 479 ppm chloromethane did not produce maternal toxicity. No

chloromethane-related deaths were observed in female rats.

Wolkowski-Tyl et al. (1983b) assessed the reproductive and developmental effects of an inhalation

exposure to chloromethane in C57BL/6 females mated to C3H males to produce B6C3F1 offspring. After

mating, 74-77 females were exposed to chloromethane at concentrations of 0, 250, 500, or 750 ppm on Gd

6-17. At 750 ppm, six dams were found dead and one was found moribund on Gd 15-18. The authors

concluded that an inhalation exposure to chloromethane during Gd 6-17 resulted in maternal toxicity at

750 ppm, but not at 500 or 250 ppm. Exposure of pregnant mice to 250 ppm chloromethane produced

neither maternal nor fetal toxicity nor teratogenicity.

Chellman et al. (1987) investigated the role of chloromethane-induced testicular and epididymal

inflammation in the induction of sperm cytotoxicity and preimplantation loss in male Fischer 344 rats.

The rats were exposed to 3,056 ppm chloromethane 6 hours/day for 5 consecutive days, with or without

concurrent treatment with 3-amino-l-[m-(tri-fluoromethyl)phenyl]-2-pyrazoline (BW755C), an

anti-inflammatory agent. None of the animals died during the course of exposure.

Working et al. (1985a) studied the effects of an inhalation exposure to chloromethane on germ cell viability

in male Fischer 344 rats. Forty males each were exposed to 0, 1,000, or 3,000 ppm chloromethane for

5 days, 6 hours/day. No males died during the 5-day treatment period or 8-week breeding period.

In an evaluation of the toxicologic and oncogenic effects of inhaled chloromethane in male and female

Fischer 344 rats and B6C3F1 mice, 120 animals per sex per exposure level were exposed to chloromethane

in whole body inhalation exposure chambers at target concentrations of 0 (control), 50, 225, or 1,000 ppm,

6 hours/day, 5 days/week. Necropsies were completed at 6, 12, 18, or 24 months after the initial exposure

(n=10, 10, 20, 80 for rats; and n=10, 10, 10, 90 for mice; respectively). Actual measured concentrations
CHLOROMETHANE 20

2. HEALTH EFFECTS

averaged over the 24-month exposure period were 0.3±4, 51±9, 224±16, and 997±65 ppm. During the

acute exposure time frame (≤ 14 days), chloromethane exposure had no effect on the survival curves of

male or female rats or mice at the exposure levels received. During the intermediate exposure time frame

(15-364 days) there was some increased mortality beginning at 10 months in female mice exposed to

1,000 ppm chloromethane, but no effect on the survival of male mice or male or female rats. During the

second half of the study (i.e., the chronic exposure of ≥365 days), there was increased mortality in

1,000 ppm exposed male mice beginning at 17 months with a large increase in mortality by 19 months. For

1,000 ppm female mice, increased mortality began at 10 months and continued to rise by 20 months. The

1,000 ppm mice groups were terminated at 21 months (2 males) and 22 months (18 females) due to high

mortality. Chloromethane had no effect on the survival of male or female rats (CIIT 1981).

No deaths occurred in male dogs (4 per group) exposed to ≥400 ppm chloromethane for 90 days (McKenna

et al. 1981b). Female dogs were not tested.

The LC50 values and all reliable LOAEL values for death in each species and duration category are

recorded in Table 2-1 and plotted in Figure 2-1.

2.2.1.2 Systemic Effects

The highest NOAEL values and all reliable LOAEL values for systemic effects in each species and

duration category are recorded in Table 2-1 and plotted in Figure 2-1.

Respiratory Effects. Case reports generally have not described respiratory effects in humans exposed

to chloromethane. No effects on pulmonary function were observed in volunteers who participated in a

study of neurological and neurobehavioral effects of acute inhalation exposure of up to 150 ppm

chloromethane (Stewart et al. 1980). This study, however, had several limitations such as small sample

size, multiple dosing schemes, and a confusing protocol. Specifically, groups of two to four men and two

to four women were exposed to 10, 100, or 150 ppm or to concentrations that were increased from

50-150 ppm in the same group for 1, 3, or 7.5 hours per day over 2-5 days per week for 1 or 2 weeks.

Several subjects, both male and female, dropped out of the study before some of the experiments were

completed, and other subjects were added. Furthermore, the same subjects were used for different

protocols during different weeks of the study. Despite the limitations, chloromethane exposure did not

appear to have any effect on pulmonary function.



























CHLOROMETHANE 48

2. HEALTH EFFECTS

Acute exposure of dogs to 15,000 ppm caused an initial rise in heart rate and blood pressure, followed by

markedly reduced respiration, decreased heart rate, and a progressive fall in blood pressure until the dogs

died within 4-6 hours (von Oettingen et al. 1949, 1950). These effects may have resulted from

vasodilation due to depression of the central nervous system. Pulmonary congestion was a common finding

among the various species exposed to chloromethane until death (Dunn and Smith 1947; Smith and von

Oettingen 1947a). As discussed above in Section 2.2.1.1, however, limitations of these reports preclude

precise determination of concentration-duration-response relationships. More recent studies using very

pure chloromethane (99.5-99.9%) failed to find any exposure-related histopathological lesions in the lungs

of dogs and cats exposed acutely to 500 ppm chloromethane (McKenna et al. 1981a), rats exposed acutely

to 2,000 ppm (Burek et al. 1981), male dogs exposed to 400 ppm, and rats and mice exposed to up to

1,500 ppm chloromethane for intermediate durations (McKenna et al. 1981b; Mitchell et al. 1979).

Dodd et al. (1982) examined the effects of an inhalation exposure to chloromethane on tissue nonprotein

sulfhydryl (NPSH) content in male Fischer 344 rats. Groups of four animals each were exposed to

chloromethane at concentrations of 0, 100, 500, or 1,500 ppm for 6 hours. Additional groups of four were

exposed to 500 ppm chloromethane for periods of 1, 2, or 4 hours. Other groups of four were pretreated

with Aroclor-1254 (metabolic inducer) or SKF-525A (metabolic inhibitor) prior to exposure to 500 ppm

chloromethane [duration not noted]. The animals were sacrificed at various time points (0-18 hours) after

exposure, at which time blood, liver, lung, and one kidney were collected for subsequent NPSH

determinations. NPSH content of liver, kidney, and lung were decreased in a concentration-related manner.

At 1,500 ppm, NPSH levels were 30% of control values in lungs immediately following exposure. At

500 ppm, levels were 55% of control values. No differences in NPSH content of the organs were observed

after exposure to 100 ppm chloromethane compared with control. Lung NPSH levels returned to control

values within 18 hours of exposure. A duration-related decrease was observed when rats were exposed to

500 ppm chloromethane for 1, 2, 4, or 6 hours. Pretreatment with Aroclor 1254 (inducer of microsomal

enzymes) did not alter the decreases in tissue NPSH seen after exposure to chloromethane alone.

Pretreatment with SKF-525A (inhibitor of microsomal enzymes) may have interfered with the ability of

chloromethane to decrease NPSH in some tissues. Treatment with chloromethane significantly increased

the activity of glutathione-S-alkyltransferase, and pretreatment with Aroclor 1254 did not alter the increase.

The toxicological significance of this effect is not clear.

Male and female Fischer 344 rats and B6C3F1 mice were exposed to chloromethane in whole body

inhalation exposure chambers at target concentrations of 0 (control), 50, 225, or 1,000 ppm, 6 hours/day,
CHLOROMETHANE 49

2. HEALTH EFFECTS

5 days/week. Necropsies were completed at 6, 12, 18, or 24 months after the initial exposure. At

6 months, relative lung weight was significantly increased at 50, 225, and 1,000 ppm in male rats and at

1,000 ppm in female rats. One male and 4 female rats at 1,000 ppm, 1 female at 225 ppm, and 2 males

and 1 female at 50 ppm had minimal to moderate interstitial pneumonia with lymphocytic peribronchiolitis

and perivasculitis. The interstitial lesions consisted of macrophage and lymphocytic infiltration. Also

present were alveolar cell hyperplasia and mild alveolar luminal infiltrates consisting of large macrophages,

lymphocytes, and in some areas, a few neutrophils. Five females at 1,000 ppm had areas of minimal

subacute tracheitis (this lesion also occurred in 1 control male rat). At 12, 18, or 24 months, no

chloromethane-related lung effects were observed. No effects on lungs were observed at any time point in

mice. These respiratory effects were transitory, and the authors did not consider the effects to be

associated with exposure to chloromethane (CIIT 1981).

Cardiovascular Effects. Cardiovascular effects of chloromethane have been described in case reports

of humans exposed occupationally or accidentally due to refrigerator leaks (Gummert 1961; Hansen et al.

1953; Kegel et al. 1929; McNally 1946; Spevak et al. 1976; Verriere and Vachez 1949). These effects

include electrocardiogram abnormalities, tachycardia and increased pulse rate, and decreased blood

pressure. The precise concentrations and durations of exposure are not known. A retrospective

epidemiological study of workers exposed to chloromethane in a butyl rubber manufacturing plant found no

statistical evidence that the rate of death due to diseases of the circulatory system was increased in the

exposed population when compared with U.S. mortality rates (Holmes et al. 1986). In a study of

neurological and neurobehavioral effects of acute inhalation exposure in volunteers, no abnormalities of

cardiac function or electrocardiograms were found at concentrations up to 150 ppm (Stewart et al. 1980).

The long-term cardiotoxic effects from an acute exposure to chloromethane were also studied by Rafnsson

and Gudmundsson (1997) who found an excess mortality rate from cardiovascular disease. Seventeen crew

members (males) were exposed for 2 days in 1963 to chloromethane that leaked from a refrigerator on

board an Icelandic fishing trawler (exposure levels were not reported). The refrigerator was located under

the sleeping quarters of the crew. This study followed a cohort of 24 men on board the vessel (6 officers

and 18 deckhands) at 32 years postexposure. The reference group was selected from three registries of

seamen. The Icelandic registries for seamen are some of the most comprehensive and complete available.

The reference group contained five times as many individuals as the study group, and was controlled for

age, occupation, and social class. The authors assumed simultaneous control for lifestyle factors including

smoking habits and diet. The authors report excess mortality from all causes of death associated with acute
CHLOROMETHANE 50

2. HEALTH EFFECTS

exposure to chloromethane (Mantel-Haenszel point estimate=2.2, 95%; CI=1.3-3.1), and a clear excess

mortality from cardiovascular disease (M-H=2.1, 95%; CI= 1.2-3.8). This excess was more prominent

among the deckhands who had received the highest exposure to chloromethane from the leaking

refrigerator. The Risk ratios were elevated for all causes of death (RR=2.5, 95%; CI=l.0-5.7) as well as

for cardiovascular disease (RR=3.9, 95%; CI=1.0-14.4). The study is weakened by the assumption of a

simultaneous control for lifestyle factors including smoking habits and diet, and by the relatively small

numbers of individuals with significant exposure. The authors also do not discuss the potential influence of

the documented neurological deficits in this cohort on cardiovascular function (Gudmundsson 1977), and

no definite mechanism of action was found in the literature. The authors suggest, however, that additional

study on chloromethane’s potential cardiovascular toxicity is warranted (Rafnsson and Gudmundsson

1997).

Scharnweber et al. (1974) presented 6 case studies of workers who were exposed to relatively low levels

(200-400 ppm) of chloromethane for at least 2-3 weeks before onset of symptoms. Two cases occurred

after “prolonged” (not otherwise specified) exposure to 8 hour time-weighted average (TWA) levels up to

300 ppm. Four cases occurred after work exposure on the order of 265 ppm (g-hour TWA) after

2-3 weeks of 12-16 hour days. One of the workers having prolonged exposure to 8-hour TWA levels up to

300 ppm experienced moderate hypertension (160/120 mm Hg).

Dogs exposed acutely to 15,000 ppm had an initial rise in heart rate and blood pressure, followed by

markedly reduced respiration, decreased heart rate, and a progressive fall in blood pressure until death,

which occurred within 4-6 hours (von Oettingen et al. 1949, 1950). These effects may have resulted from

vasodilation due to depression of the central nervous system. Chloromethane exposure does not appear to

result in histopathological lesions in the heart, as demonstrated by acute studies in male dogs and cats

exposed to 500 ppm chloromethane (McKenna et al. 1981a), by intermediate duration studies in male dogs

exposed to 400 ppm, and in rats and mice exposed to up to 1,500 ppm chloromethane (McKenna et al.

1981b; Mitchell et al. 1979).

Male and female Fischer 344 rats and B6C3F1 mice were exposed to chloromethane in whole body

inhalation exposure chambers at target concentrations of 0 (control), 50, 225, or 1,000 ppm, 6 hours/day,

5 days/week. Necropsies were completed at 6, 12, 18, or 24 months after the initial exposure. No

cardiovascular effects were observed in male or female rats at any time point. No cardiovascular effects

were observed in male mice. At 12 and 18 months, 1000 ppm female mice had increased relative heart
CHLOROMETHANE 51

2. HEALTH EFFECTS

weight, and at 24 months, 225 ppm female mice had increased relative heart weight. These effects were

considered to be chloromethane-related, but no associated histopathological lesions were observed (CIIT

1981).

Gastrointestinal Effects. Numerous case reports of humans exposed to chloromethane have

described symptoms of nausea and vomiting (Baird 1954; Baker 1927; Battigelli and Perini 1955;

Borovska et al. 1976; Hansen et al. 1953; Kegel et al. 1929; Mackie 1961; Jones 1942; Raalte and van

Velzen 1945; Spevak et al. 1976; Verriere and Vachez 1949). In all cases, these symptoms were

accompanied by central nervous system toxicity, which was usually severe. It is not clear, therefore, if the

nausea and vomiting were secondary to the neurotoxic effects of chloromethane. Two of the reports

(Battigelli and Perini 1955; Jones 1942) provided exposure concentration data.

Morgan et al. (1982) investigated the lesions induced by an inhalation exposure to chloromethane in C3H,

C57BL/6, and B6C3F1 mice and in Fischer 344 rats. Ten rats per sex were exposed to chloromethane for

5 days, 6 hours/day with a break in exposure for 2 days, and then a further 4 days of exposure. Rats were

exposed to 0, 2,000, 3,500, or 5,000 ppm. Five mice per sex were exposed to chloromethane for 12 days,

6 hours/day. Mice were exposed to 0, 500, 1,000, or 2,000 ppm. Animals were sacrificed 18 hours after

the last exposure or immediately after exposure if found to be moribund. Within 2 days of treatment, male

and female rats in the 5,000 ppm group developed foul-smelling diarrhea. Gastrointestinal effects were not

observed in mice.

Histopathological examination of animals exposed to various concentrations of chloromethane for acute,

intermediate, or chronic durations did not show evidence of gastrointestinal damage (CIIT 1981; McKenna

et al. 1981a, 1981b).

Hematological Effects. No hematological effects were found in volunteers who participated in a

study of neurological and neurobehavioral effects of acute inhalation exposure of up to 150 ppm

chloromethane (Stewart et al. 1980). Case reports of human overexposure have also generally been

negative for hematological effects.

No long-term effect on the hematological system from an acute exposure was reported by Gudmundsson

(1977). Seventeen crew members (males) were exposed for 2 days in 1963 to chloromethane that leaked

from a refrigerator on board an Icelandic fishing trawler (no estimates of exposure levels were reported).
CHLOROMETHANE 52

2. HEALTH EFFECTS

The refrigerator was located under the sleeping quarters of the crew. Thirteen years later (i.e., in 1976) 10

of the 11 survivors were examined (one lived in a foreign country and could not be located). All 10 were

employed; 8 were employed at sea. The mean age of the 10 patients examined was 38.3 years (range

30-50 years). All 10 patients had normal hemoglobin, white cell count, differential leukocyte count,

erythrocyte sedimentation rate, and serum creatinine.

Spleen enlargement, suggestive of extramedullary hematopoiesis, and hemoglobinuria, suggestive of

intravascular hemolysis, were found in mice exposed intermittently to a high concentration (2,400 ppm) of

chloromethane for 11 days (Landry et al. 1985). These effects were not seen when mice were exposed

continuously to a lower concentration (150 ppm) (Landry et al. 1985). Male mice were not used in this

study. No exposure-related effects on hematological parameters were found in male dogs or cats exposed

continuously for 3 days to 500 ppm (McKenna et al. 1981a), or in rats exposed continuously for 3 days to

2,000 ppm (Burek et al. 1981). In addition, male dogs exposed to 400 ppm, rats and mice exposed to

1,500 ppm for 90 days (McKenna et al. 198 lb; Mitchell et al. 1979), and rats and mice exposed for 6, 12,

18, or 24 months to up to 1,000 ppm (CIIT 1981) did not have hematological effects.

Musculoskeletal Effects. Case reports generally have not described muscular or skeletal effects in

humans exposed to chloromethane.

No adverse muscular or skeletal effects related to chloromethane exposure were observed in dogs and cats

exposed acutely to 500 ppm chloromethane (McKenna et al. 1981 a), male dogs exposed to 400 ppm, and

rats and mice exposed to 21,500 ppm chloromethane for intermediate durations (McKenna et al. 1981 b;

Mitchell et al. 1979) or rats and mice exposed to up to 1,00 ppm chloromethane for chronic durations

(CIIT 1981).

Hepatic Effects. Case reports of humans exposed to chloromethane have described clinical jaundice

(Kegel et al. 1929; Mackie 1961; Weinstein 1937). A case of jaundice and cirrhosis of the liver was

attributed to chloromethane exposure in a man who had been a refrigeration engineer for 10 years and had

frequently been exposed to chloromethane vapors (Wood 1951). There was no reason to believe that these

liver effects were due to other causes such as infective hepatitis or alcohol consumption.

Hepatic effects have also been observed in animals exposed to chloromethane, and mice appear to be more

susceptible than rats. Rats exposed to l,000-1,500 ppm for acute, intermediate, or chronic durations had
CHLOROMETHANE 53

2. HEALTH EFFECTS

either no liver effects or relatively mild to moderate changes, such as loss of normal areas of basophilia,

cloudy swelling, increased liver weight, fatty infiltration, and increased serum levels of alanine

aminotransferase (ALT), aspartate aminotransferase (AST), and serum bilirubin (Burek et al. 1981; CIIT

1981; Mitchell et al. 1979; Morgan et al. 1982). No necrosis was seen. Acute, intermediate, or chronic

exposure of mice to 1,000-l ,500 ppm generally resulted in necrosis and degeneration (CIIT 1981; Landry

et al. 1985; Mitchell et al. 1979; Morgan et al. 1982). Although no significant liver effects were observed

in male dogs and cats (McKenna et al. 1981 a, 1981 b), the exposure concentrations (400 or 500 ppm) may

not have been high enough to produce liver toxicity in these species.

Chapin et al. (1984) investigated the cellular targets and the mechanism of reproductive tract lesions

induced by inhaled chloromethane in male Fischer 344 rats. The animals were exposed to 3500 ppm

chloromethane or air (controls) for 5 days, 6 hours/day, were subsequently not exposed for 3 days, and then

exposed again for 4 days. Rats were killed on days 5, 7, 9, 11, 13, 15, 19, and 70 after starting exposure.

To test for the effects of lower feed consumption in exposed rats, four weight-matched naive animals for

each time interval were pair-fed identical amounts of feed to that consumed by the exposed animals and

killed in the same manner. Tissue non-protein sulfhydryl (NPSH) content was measured in testes, caput

and caudal epididymides, liver and heart blood. Liver NPSH content was significantly depleted within

1 hour of exposure (1.33 versus 5.44 μmol/g tissue; p<0.05).

Chellman et al. (1986a) studied the effects of 3-amino-l-[m-(trifluoromethyl)phenyl]-2-pyrazoline

(BW755C), a potent anti-inflammatory agent, on chloromethane-induced lethality and reproductive toxicity

in male Fischer 344 rats. Rats were exposed to 5,000 ppm chloromethane for 5 days, 6 hours/day, with or

without treatment with BW755C (10 mg/kg, intraperitoneally 1 hour pre- and postexposure). Rats exposed

to 5,000 ppm chloromethane, 6 hours/day for 5 days exhibited cloudy swelling of hepatocytes in the liver

with subsequent obliteration of the sinusoids. Rats exposed to both chloromethane and BW755C had only

very subtle, if any, lesions. The results are surprising because the liver lesions were not inflammatory in

nature. The authors concluded that protection from chloromethane-induced injury by BW755C was not

simply the result of altered metabolism because BW755C had no effect on tissue distribution or excretion

of 14C-chloromethane and administration of BW755C did not decrease hepatic glutathione content. The

protection afforded by BW755C may have been related to an inhibition of leukotriene and prostaglandin

synthesis.
CHLOROMETHANE 54

2. HEALTH EFFECTS

Dodd et al. (1982) examined the effects of an inhalation exposure to chloromethane on tissue nonprotein

sulfhydryl (NPSH) content in male Fischer 344 rats. Groups of four animals each were exposed to

chloromethane at concentrations of 0, 100, 500, or 1,500 ppm for 6 hours. Additional groups of four were

exposed to 500 ppm chloromethane for periods of 1, 2, or 4 hours. Other groups of four were pretreated

with Aroclor-1254 (metabolic inducer) or SKF-525A (metabolic inhibitor) prior to exposure to 500 ppm

chloromethane (duration not noted). The animals were sacrificed at various time points (0 to 18 hours)

after exposure, at which time blood, liver, lung, and one kidney were collected for subsequent NPSH

determinations. NPSH content of liver was decreased in a concentration-related manner. At 1,500 ppm,

NPSH levels were 17% of control values immediately following exposure. At 500 ppm, NPSH levels were

41% of control values. No differences in NPSH content were observed after exposure to 100 ppm

chloromethane compared with control. Liver NPSH levels returned to control values within 8 hours of

treatment. Pretreatment with Aroclor 1254 (inducer of microsomal enzymes) did not alter the decreases in

liver NPSH seen after exposure to chloromethane alone. Pretreatment with SKF-525A (inhibitor of

microsomal enzymes) may have interfered with the ability of chloromethane to decrease NPSH in some

tissues. Treatment with chloromethane significantly increased the activity of glutathione-S-alkyltransferase,

and pretreatment with Aroclor 1254 did not alter the increase. The toxicological significance

of this effect is not clear.

Chellman et al. (1986b) investigated the role of glutathione in the mediation of chloromethane-induced

toxicity in the liver, kidney and brain of male B6C3F1 mice. Animals were exposed for 6 hours to

1,500 ppm chloromethane, with and without pretreatment with buthionine-S,R-sulfoximine (BSO), diethyl

maleate (DEM), or fasting to deplete glutathione (GSH). The mice were sacrificed 18 hours after

completion of exposures, blood samples were collected, and the serum was analyzed for alanine

aminotransferase (ALT) to measure liver toxicity. There was a 50-fold increase in ALT activity in exposed

mice without pretreatment. Fasting or pretreatment with BSO or DEM resulted in ALT values which were

similar to those of controls. Therefore, depletion of GSH protected mice from hepatic toxicity of

chloromethane.

Jager et al. (1988) investigated the effects of an inhalation chloromethane exposure on tissue levels of

glutathione-S-transferase (GST) and formaldehyde dehydrogenase (FDH) in male and female Fischer 344

rats and B6C3F1 mice. Activities of GST were 2-3 times higher in livers of male B6C3F1 mice, compared

with those of female mice, and with rats of both sexes. In kidneys, GST activities of male mice were about

7 times lower than those found in the liver. The activity of FDH was higher in mouse liver (both sexes)
CHLOROMETHANE 55

2. HEALTH EFFECTS

than in rat liver. More formaldehyde was produced in the liver of male, as compared to those of female

mice. After a single, g-hour exposure to 1,000 ppm chloromethane in males or female mice, formaldehyde

levels were not observed to increase in livers or kidneys (ex vivo). Lipid peroxidation was significantly and

markedly increased in the liver of male and female mice, and to a lesser extent in the kidney, from the single

exposure to chloromethane.

Landry et al. (1985) observed mild hepatic effects in mice intermittently exposed to 400 to 2,400 ppm

(glycogen depletion, no hepatic degeneration or necrosis). Only the 1,600 ppm mice had significantly

increased liver absolute (22%) and relative (23%) weight. Mice continuously exposed to 400 ppm died or

were sacrificed by day 4, and by day 5 for a 200 ppm group, due to severe toxicity. Mice continuously

exposed to 150 ppm were sacrificed in moribund condition by day 10.5. Decreased food consumption was

indicated by diminished amount of feces and scratched food under the cages of the 150 or 200 ppm groups.

The 150 ppm exposure resulted in a significant decrease in absolute liver weight (13%), but not relative

weight. Mice had a decreased hepatocyte size (due to glycogen depletion) at 100 ppm with focal necrosis

at 150 ppm and greater.

Morgan et al. (1982) investigated the lesions induced by an inhalation exposure to chloromethane in C3H,

C57BL/6, and B6C3F1 mice and in Fischer 344 rats. Ten rats per sex were exposed to chloromethane for

5 days, 6 hours/day with a break in exposure for 2 days, and then a further 4 days of exposure. Rats were

exposed to 0, 2,000, 3,500, or 5,000 ppm. Animals were sacrificed 18 hours after the last exposure or

immediately after exposure if found to be moribund. All exposed groups except 2,000 ppm males had high

incidences (8/10 to 10/10) of minimal hepatocellular lesions, consisting of loss of normal area of

cytoplasmic basophilia. Five mice per sex were exposed to chloromethane for 12 days, 6 hours/day at

levels of 0, 500, 1,000, or 2,000 ppm. Animals were sacrificed 18 hours after the last exposure or

immediately after exposure if found to be moribund. Hepatocellular degeneration consisting of necrosis,

hyaline accumulation in bile ducts, vacuolization, and glycogen depletion was observed. The lesions

resembled those usually described for carbon tetrachloride and chloroform. Necrosis was confined to male

C57BL/6 and B6C3F1 mice exposed to 2,000 ppm. The other lesions occurred to varying degrees in other

groups and were of minimal severity. No liver lesions were observed in controls.

Wolkowski-Tyl et al. (1983b) assessed the reproductive and developmental effects of an inhalation

exposure to chloromethane in C57BL/6 females mated to C3H males to produce B6C3F1 offspring. After

mating, 74-77 females were exposed to chloromethane at concentrations of 0, 250, 500, or 750 ppm on
CHLOROMETHANE 56

2. HEALTH EFFECTS

Gd 6-17. Surviving dams were weighed and sacrificed on gestation day 18. A significant increase in

maternal absolute liver weight (9%) and relative liver weight (6%) was observed in the 500 ppm mice. A

nonsignificant decrease was observed in the 750 ppm dams.

Male and female Fischer 344 rats and B6C3F1 mice were exposed to chloromethane in whole body

inhalation exposure chambers at target concentrations of 0 (control), 50, 225, or 1,000 ppm, 6 hours/day,

5 days/week (CIIT 1981). Necropsies were completed at 6, 12, 18, or 24 months after the initial exposure.

Increased ALT associated with exposure-related liver lesions was seen in male mice exposed to 1,000 ppm

chloromethane at all time points. The lesions were centrilobular and characterized by mild to moderate

hepatocellular degeneration often associated with vacuolization of most of the cytoplasm, individual

hepatocellular necrosis, cytomegaly and karyomegaly, and numerous hepatocytes containing eosinophilic,

intranuclear inclusion material. Increased ALT was also seen in 50 and 225 ppm males but no

histopatholgical changes to the liver were observed at these exposure levels. Increased ALT in female mice

exposed to 50, 225, and 1,000 ppm at 6 and 12 months was observed, but no histopathological changes

were observed in females at any of the dose levels. ALT levels returned to normal at 18 and 24 months in

female mice. Females that became moribund or that were exposed to 1,000 ppm for the longer 18- and

24-month exposure periods had liver lesions similar to those found in the males, but with less frequency

and severity. Statistically significant increases in relative liver weight were observed in both male and

female mice at 1,000 ppm. Male and female rats did not have the histopathological liver lesions seen in

mice. Male rats did generally have increased relative liver weights at 1,000 ppm. No effect on ALT levels

was observed in rats.

McKenna et al. (1981b) exposed CD-l mice to 99.9% pure chloromethane. Complete histological

examination performed on the control and 400 ppm groups. In the liver, there was a significant increase in

relative liver weight in 400 ppm females and a trend in 400 ppm males and 150 ppm males and females.

The increase was accompanied by equivocal lesions (change in tinctorial properties of liver cells, possibly

due to decrease vacuolization). The lesions were subtle and reversible and not considered adverse.

McKenna et al. (1981b) also exposed Beagle dogs to 99.9% pure chloromethane. There were no effects on

ALT or AST, but hepatocytes were swollen in 2 of 4 dogs at 400 ppm, 1 of 4 dogs at 150 ppm, 2 of 4 dogs

at 50 ppm, and 0 of 4 controls. No other liver effects were observed, and the toxicological significance of

these effects are unclear.
CHLOROMETHANE 57

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The lowest concentration for dose-related hepatic effects is the LOAEL of 51 ppm for increased ALT in

male mice (CIIT 1981). This LOAEL is used as the basis for an intermediate inhalation MRL of 0.2 ppm,

calculated as described in the footnote to Table 2-1 and in Appendix A. This MRL is presented in

Figure 2-1.

Renal Effects. Case reports of humans exposed to chloromethane have described such indicators of

renal toxicity as albuminuria, increased serum creatinine and blood urea nitrogen, proteinuria, and anuria

(Kegel et al. 1929; Mackie 1961; Spevak et al. 1976; Verriere and Vachez 1949). Exposure concentrations

at which these effects occurred are not known.

Sprague-Dawley rats exposed to chloromethane at 1,000 ppm for 72 hours had slightly increased blood

urea nitrogen (BUN), but this effect only occurred significantly in females. Abnormal urinalysis

parameters indicative of renal failure occurred in both sexes of rats exposed to 1,000 or 2,000 ppm for 48

or 72 hours. Histological examination revealed renal tubular cell necrosis, increased lipid accumulation in

tubule cells at 1,000 ppm for both exposure periods, and evidence of regeneration after the recovery period.

Greatly increased (statistically significant) BUN in 2,000 ppm male and female rats sacrificed at 48 hours

indicated kidney failure (Burek et al. 1981).

Chellman et al. (1986a) exposed male Fischer 344 rats to 5,000 ppm chloromethane for 5 days,

6 hours/day resulting in necrosis of the proximal convoluted tubules. Dodd et al. (1982) exposed male

Fischer 344 rats to chloromethane at 0, 100, 500, or 1,500 ppm for 6 hours. Nonprotein sulfhydryl

(NPSH) content of kidney was decreased in a concentration-related manner. Kidney NPSH levels returned

to control values within 8 hours of treatment. The toxicological significance of this effect is not clear.

Morgan et al. (1982) investigated the lesions induced by an inhalation exposure to chloromethane in C3H,

C57BL/6, and B6C3F1 mice and in Fischer 344 rats. Rats were exposed to 0, 2,000, 3,500, or 5,000 ppm

for 5 days, 6 hours/day with a break in exposure for 2 days, and then a further 4 days of exposure. Mice

were exposed to 0, 500, 1,000, or 2,000 ppm for 12 days, 6 hours/day. Two types of kidney lesions were

seen, basophilia of renal tubules and degeneration and necrosis of renal proximal convoluted tubules. The

degeneration was found mainly in the 2,000 ppm groups in both males and females of all strains. The

basophilia, presumed to be regeneration, was found mainly in the 1,000 ppm group. Hematuria occurred in

mice exposed to 1,000 and 2,000 ppm, but it was not clear whether it was due to renal damage or lesions

elsewhere in the urogenital tract. In the rat kidneys, there was a dose-related increased incidence and
CHLOROMETHANE 58

2. HEALTH EFFECTS

severity of degeneration of proximal tubules. No basophilia in renal tubules occurred in rats as was seen in

mice. The authors speculated that the basophilia in mice is a proliferative response related to the induction

of kidney tumors seen in mice and not rats.

Chellman et al. (1986b) investigated the role of glutathione in the mediation of chloromethane-induced

toxicity in the liver, kidney and brain of male B6C3F1 mice. Mice exposed to 1,500 ppm chloromethane

6 hours/day, 5 days/week for 2 weeks had no significant changes in kidney weight, glomerular filtration

rate, urinary excretion of glucose and protein, or urinary concentrating ability. Histologically, the only

effect of chloromethane exposure was a slight increase in the number of basophilic cortical tubules.

Incorporation of tritiated thymidine into deoxyribonucleic acid (DNA) was 3-fold greater in kidneys of

chloromethane exposed male mice than controls. Incorporation of tritiated thymidine was not significantly

elevated in mice exposed and pretreated with BSO. BSO alone had no effect on DNA synthesis. In female

mice, incorporation of tritiated thymidine into DNA was S-fold greater in kidneys of chloromethaneexposed

versus controls. Therefore, depletion of GSH protected mice from increased DNA synthesis

induced by chloromethane. The increased DNA synthesis may result from a compensatory proliferation in

response to cell death. Although cell death was not observed in kidneys histologically, basophilic foci are

consistent with regenerative cellular response following cell death.

Jager et al. (1988) investigated the effects of a chloromethane inhalation exposure on tissue levels of

glutathione-S-transferase (GST) and formaldehyde dehydrogenase (FDH) in male and female Fischer 344

rats and B6C3F1 mice. Activities of GST in kidneys of male mice were about 7 times lower than those

found in the liver. About 50% more formaldehyde was produced in the male mouse kidney, compared to

the female kidney (indicative of higher levels of P-450 in the male kidney). No DNA-protein crosslinks in

the kidney and only some evidence of single-strand breaks was observed in male B6C3F1 mice exposed to

1,000 ppm chloromethane for 4 days, 6 hours/day. After a single, 8 hour exposure to 1,000 ppm

chloromethane in male or female mice, formaldehyde levels were not observed to increase in livers or

kidneys (ex vivo). Lipid peroxidation was significantly and markedly increased in the liver of male and

female mice, and to a lesser extent in the kidney, from the single exposure to chloromethane.

Female C57BL/6 mice exposed to 1,500 ppm chloromethane for 2 weeks, 5 days/week, 6 hours/day

showed a slight degeneration of proximal convoluted tubules and proteinaceous material in tubular lumen.

The renal and brain lesions in the study were unrelated in terms of severity; therefore, the authors
CHLOROMETHANE 59

2. HEALTH EFFECTS

concluded that the brain lesions seen after exposure to chloromethane were probably not a direct

consequence of renal lesions (Jiang et al. 1985).

Landry et al. (1985) evaluated the neurologic effects of continuous versus intermittent chloromethane

exposure in female C57BL/6 mice. Mice were exposed to chloromethane in whole body inhalation

chambers for 11 days either continuously for 22 hours/day at 0, 15, 50, 100, 150, 200, or 400 ppm or

intermittently for 5.5 hours/day at 0, 150, 400, 800, 1,600, or 2,400 ppm. Kidney effects were only

observed in the intermittently exposed mice at 2,400 ppm. The effects consisted of a slight multifocal

degeneration and regeneration of tubules, and an eosinophilic staining cast within the tubules. The

2,400 ppm mice had a nonsignificant increase in relative kidney weight. No histopathological lesions were

observed in the kidney, thus the increased weight does not appear to represent an adverse effect.

Beagle dogs and cats exposed to 200 or 500 ppm chloromethane for 23.5 hours/days for 3 days had no

significant differences in clinical chemistry or urinalysis parameters. A comprehensive histological

examination revealed no exposure-related lesions in any system other than neurological. This was a good

comprehensive study, but is limited by the number of animals (3) per group (McKenna et al. 1981a).

Beagle dogs were also exposed to 0, 50, 150, and 400 ppm for 6 hours/day, 5 days/week for 90 days.

There were no exposure-related gross or histopathological lesions in the kidneys and no effect on BUN

(McKenna et al. 1981b). This was a comprehensive study, but is limited by the number of animals (4) per

group.

Sprague-Dawley rats were exposed to 0, 50, 150, or 400 ppm chloromethane 6 hours/day, 5 days/week, for

90 days. There was no effect on BUN, but urinary specific gravity was decreased in males at 400 ppm and

females at 150 ppm. This decrease was not associated with gross histologic pathology, and therefore, the

toxicological significance of this effect is unclear. CD-l mice were exposed to the same regimen with no

apparent effects on the kidneys (McKenna et al. 1981b).

Fischer 344 rats exposed to 0, 375, 750, and 1,500 ppm for 6 hours/day, 5 days/week, for 13 weeks

developed a significant increase in relative left kidney weight for the 1,500 ppm males. There were no

clinically significant hematological, clinical chemistry, or urinalysis abnormalities so the significance of

this effect is unclear (Mitchell et al. 1979).
CHLOROMETHANE 60

2. HEALTH EFFECTS

B6C3F1 mice were exposed to 0, 375, 7.50, and 1,500 ppm for 6 hours/day, 5 days/week, for 13 weeks.

No exposure-related histopathological lesions of the kidneys, and no clinically significant effects on

hematological and urinalysis indices were observed. Relative kidney weight was increased in 1,500 ppm

males, but no histopathological lesions were associated with the increase (Mitchell et al. 1979).

Male and female Fischer 344 rats and B6C3F1 mice were exposed to chloromethane in whole body

inhalation exposure chambers at target concentrations of 0 (control), 50, 225, or 1,000 ppm, 6 hours/day,

5 days/week. Necropsies were completed at 6, 12, 18, or 24 months after the initial exposure. Increased

relative kidney weights were noted in female mice at 1,000 ppm, while decreased absolute kidney weights

were seen in males at 1,000 ppm; there was no apparent reason for the sex difference. The authors

interpreted the decrease in absolute kidney weight in male mice as biologically significant. Males exposed

to 1,000 ppm developed renal tubuloepithelial hyperplasia and karyomegaly that became progressively

worse, followed by the development of renal adenomas and adenocarcinomas. Females did not develop

these lesions until after 18 months and to a much lesser extent. Male and female rats had varying levels of

increased relative kidney weights throughout the study, but these were not associated with clinical, gross, or

histopathological findings; thus, the toxicological significance of these effects is unclear (CIIT 1981).

Endocrine Effects. No studies were located regarding endocrine effects in humans after inhalation

exposure to chloromethane.

Some effects have been observed in high-level, acute exposure animal studies. Male Fischer 344 rats

exposed to 5,000 ppm chloromethane for 5 days, 6 hours/day developed vacuolar degeneration in the cell

cytoplasm of the adrenal cortex in the outer region of the zona fasciculata (Chellman et al. 1986a). Fatty

droplets were seen in the epithelial cells of the zona fasciculata in the adrenals of Fischer 344 rats exposed

to 3,500 and 5,000 ppm chloromethane for 5 days, 6 hours/day with a break in exposure for 2 days, and

then a further 4 days of exposure; the severity of this lesion increased with dose (Morgan et al. 1982).

Results are generally negative with lower level or longer duration exposures. No chloromethane-related

effects on the endocrine organs were observed from acute exposures up to 500 ppm in Beagle dogs or cats

(McKenna et al. 198 la), or from intermediate and chronic exposures up to 1,000 ppm in mice or rats (CIIT

1981).
CHLOROMETHANE 61

2. HEALTH EFFECTS

Dermal Effects. No studies were located regarding dermal effects in humans after inhalation exposure

to chloromethane.

No dermal effects were observed from acute chloromethane exposures up to 500 ppm in Beagle dogs or

cats (McKenna et al. 1981a), or from intermediate exposures up to 400 ppm in Sprague-Dawley rats or

CD-l mice (McKenna et al. 1981b), up to 1,500 ppm in Fischer 344 rats.(Mitchell et al. 1979), or up to

400 ppm in Beagle dogs (McKenna et al. 1981b).

Ocular Effects. Case reports of humans exposed to chloromethane have described such symptoms as

blurred and double vision (Baker 1927; Borovska et al. 1976; Gummert 1961; Kegel et al. 1929; Mackie

1961). These symptoms probably reflect effects on the nervous system rather than effects on the eye itself.

Ophthalmological examination of male cats and Beagle dogs exposed to 500 ppm continuously for 3 days

(McKenna et al. 1981a), dogs exposed to 400 ppm for 90 days (McKenna et al. 1981b), or of rats and

mice exposed to 1,000 ppm for up to 24 months (CIIT 1981) failed to reveal eye lesions. However,

mucopurulent conjunctivitis with total destruction of the eye in some cases was found in mice exposed to

≥375 ppm for 6 hours/day, 5 days/week, for 90 days (Mitchell et al. 1979). These lesions were attributed

to exposure because no lesions were found in controls; however, the failure of longer-term studies to detect

eye lesions at higher concentrations makes the findings of Mitchell et al. (1979) questionable. If the eye

lesions were due to chloromethane exposure, the effect was probably due to direct contact of the vapor with

the eye, rather than a consequence of inhalation.

Body Weight Effects. No studies were located regarding body weight effects in humans after

inhalation exposure to chloromethane.

A consistent systemic effect of chloromethane exposure in animals is reduced body weight gain, which was

observed in rats and mice exposed to chloromethane for acute, intermediate, and chronic durations (Burek

et al. 1981; CIIT 1981; Landry et al. 1985; Mitchell et al. 1979). Landry et al. (1985) evaluated the

neurologic effects of continuous versus intermittent chloromethane exposure in female C57BL/6 mice.

Groups of 12 mice each were exposed to chloromethane in whole body inhalation chambers for 11 days

either continuously for 22 hours/day at 0, 15, 50, 100, 150, 200, or 400 ppm or intermittently for

5.5 hours/day at 0, 150, 400, 800, 1,600, or 2,400 ppm. Mice were weighed prior to exposure, on

exposure days 4 and 8, and at necropsy. The 400 ppm exposed mice died or were sacrificed by day 4, and
CHLOROMETHANE 62

2. HEALTH EFFECTS

the 200 ppm group by day 5, due to severe toxicity. Mice exposed to 150 ppm were sacrificed in moribund

condition by day 10.5. Continuous exposure to chloromethane resulted in significantly decreased body

weight in the 200 ppm group (33%) by day 4 compared to the controls, and in the 150 ppm group by day 4

(16%) persisting to the sacrifice at day 10.5 (12%). A nonsignificant decrease was seen in the 100 ppm

group and no effects on body weight were seen at 50 ppm.

Other Systemic Effects. No studies were located regarding other systemic effects in humans after

inhalation exposure to chloromethane.

The only other systemic effect reported in animal studies was a decrease in food consumption in the Landry

et al. (1985) study. This study evaluated the neurologic effects of continuous versus intermittent

chloromethane exposure in female C57BL/6 mice exposed to chloromethane in whole body inhalation

chambers for 11 days either continuously (C) for 22 hours/day at 0, 15, 50, 100, 150, 200, or 400 ppm or

intermittently (I) for 5.5 hours/day at 0, 150, 400, 800, 1,600, or 2,400 ppm. There was a significant

degree of inanition in the 200-C and 400-C ppm mice prior to necropsy with decreased carcass size,

amount of abdominal fat, amount of ingesta in the gastrointestinal tract, and small, pale livers.

2.2.1.3 Immunological and Lymphoreticular Effects

No studies were located regarding immunological or lymphoreticular effects in humans after inhalation

exposure to chloromethane.

In animals, lymphoid depletion of the spleen and splenic atrophy were observed in mice exposed to

1,000 ppm chloromethane for up to 2 years (CIIT 1981). The lymphoid depletion was first observed in

mice killed after 6 months of exposure, while the splenic atrophy was observed in mice killed after

18 months. This LOAEL value for immunological effects in mice is recorded in Table 2-l and plotted in

Figure 2-l for both intermediate and chronic duration categories. The lower exposure level in this study

(225 ppm) cannot be considered the most reliable NOAEL for immunological effects, however, because

more sensitive tests for immune function were not conducted. In addition, cats exposed continuously to

chloromethane for 3 days had higher incidences of immunologically-related brain lesions than did control

cats (McKenna et al. 1981a). The lesions, however, were consistent with infection or post-vaccinal

reaction (the cats were vaccinated for panleukopenia by the supplier). Exacerbation of viral-induced
CHLOROMETHANE 63

2. HEALTH EFFECTS

central nervous system disease could not be ruled out. It is not known whether the exacerbation would

represent an immunological effect.

Landry et al. (1985) exposed female C57BL/6 mice to chloromethane for 11 days either continuously for

22 hours/day at 0, 15, 50, 100, 150, 200, or 400 ppm or intermittently for 5.5 hours/day at 0, 150, 400,

800, 1,600, or 2400 ppm. The absolute and relative weight of the thymus was significantly decreased at

the 1,600 ppm (40% and 39%, respectively) and 2,400 ppm intermittent exposures (89% and 87%,

respectively). There was no exposure-related histopathology in the thymus, but the decreased relative

thymus weight is generally considered to be evidence of possible immunotoxicity. There was decreased

absolute and relative thymus weight at 15 (23% and 22%, respectively), 50 (21% and 21%), 150 ppm

(71% and 69%) continuous exposures, but not at 100 ppm. The decrease at 150 ppm was considered to be

exposure-related, but the decreases at 15 and 50 ppm were not because they were within normal historical

range.

In contrast to the results of the Landry et al. (1985) study, exposure to chloromethane at levels up to

400 ppm for 6 hours/day, 5 days/week for 90 days resulted in no observed exposure-related adverse effects

to the organs and tissues of the immune system of Sprague-Dawley rats, CD-1 mice, or male Beagle dogs

(McKenna et al. 1981b). Thus, the potential for chloromethane-induced immunotoxicity remains

unresolved.

2.2.1.4 Neurological Effects

Numerous case reports of humans exposed to chloromethane vapors as a result of industrial leaks and

defective refrigerators have described neurological effects (Baird 1954; Baker 1927; Battigelli and Perini

1955; Borovska et al. 1976; Gummert 1961; Hansen et al. 1953; Hartman et al. 1955; Jones 1942; Kegel

et al. 1929; MacDonald 1964; McNally 1946; Raalte and van Velzen 1945; Spevak et al. 1976; Wood

1951). In general, symptoms develop within a few hours after exposure and include fatigue, drowsiness,

staggering, headache, blurred and double vision, mental confusion, tremor, vertigo, muscular cramping and

rigidity, sleep disturbances, and ataxia. These symptoms may persist for several months, and depression

and personality changes may develop. In some cases, complete recovery eventually occurs. In other cases

of more severe poisoning, convulsion, coma, and death may ensue; or neurological effects may persist.

Microscopic examination of the brain of an individual who died following chloromethane exposure revealed
CHLOROMETHANE 64

2. HEALTH EFFECTS

accumulation of lipoid-filled histiocytes in the leptomeninges of the hemispheres, hyperemia of the cerebral

cortex, and lipoid droplets in the adventitia cells of the capillaries throughout the brain (Kegel et al. 1929).

Battigelli and Perini (1955) report two cases of workers in a cooling plant who were exposed to a leak of

chloromethane while repairing refrigeration system with an estimated exposure of >29,000 ppm. Both

workers developed symptoms of vertigo, tremors, dulled senses, nausea, vomiting, and abdominal pain.

The symptoms appeared 3-4 hours after the inhalation exposure. Disturbances began to recede about

6 hours postexposure and disappeared completely by 1 day postexposure.

A case was reported by Lanham (1982) of a man and wife who developed symptoms of blurred vision,

fatigue, vertigo, tremor, and abnormal gait several days after storing insulating boards made of Styrofoam

in the basement of their house. Air levels of chloromethane measured by 3 different devices were above

200 ppm.

Seven men had acute exposures to chloromethane while repairing refrigeration systems. Four of the cases

provided sufficient information to estimate an exposure level of 39,000, 50,000,440,000, and

600,000 ppm, respectively. Common symptoms were ataxia, staggering, headache, drowsiness, anorexia,

blurred and double vision, convulsions, nausea, and vomiting (Jones 1942).

Putz-Anderson et al. (1981b) assessed the behavioral effects of inhaled chloromethane when administered

alone at 0 or 200 ppm, or in combination with alcohol or caffeine. Chloromethane exposures in volunteers

lasted 3.5 hours. Patients were subjected to three performance tests (visualvigilance, dual task, and time

discrimination (designed to test human attention or alertness) prior to and during the treatment period.

Venous blood and alveolar air concentrations of chloromethane were obtained prior to and 90 minutes after

beginning chloromethane exposures. Chloromethane alone had no effect. Alcohol caused a significant

impairment in performance, but there was no difference in alcohol-induced impairment when chloromethane

was given with alcohol. Caffeine alone improved performance, but there was no effect on improvement

when chloromethane was given with caffeine. There was much variation in alveolar air and blood levels of

chloromethane.

Putz-Anderson et al. (198 la) assessed the behavioral effects of inhaled chloromethane, alone or in

combination with oral diazepam (a central nervous system depressant), in 56 men and women.

Chloromethane was administered alone at concentrations of 0, 100, or 200 ppm, or in combination with
CHLOROMETHANE 65

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10 mg orally administered diazepam. Chloromethane exposures lasted 3 hours. Patients were subjected to

three performance tests (visual vigilance, dual task, and time discrimination; designed to test human

attention or alertness) prior to and during the treatment period. Venous blood and alveolar air

concentrations of chloromethane were obtained prior to and 90 minutes after beginning chloromethane

exposures. Due to a limited number of patients, data from the 100 ppm chloromethane group was excluded

from the analysis. For all tests, the control group (no chloromethane or diazepam) had a 2.73% decline in

performance between the precontrol and control test (i.e., a control for the fatigue effect). The net

impairment resulting from exposure to 200 ppm chloromethane was a marginally significant 4% (total

impairment 6.7% minus the 2.73% negative control). The net impairment of diazepam alone was 10.1%.

The net impairment of the combined chloromethane and diazepam was 13.5%. The authors concluded that

the effects of chloromethane exposure were minimal and were not potentiated by concomitant diazepam

exposure.

Spevak et al. (1976) describe a case of chloromethane poisoning among four family members (one brother

[age 64] and three sisters [ages 50, 52, and 60]). All were exposed to fluid and vapors leaking from a

refrigerator for approximately 1 hour while cleaning the spill. Approximately 4 hours after their exposure,

all four subjects felt weak and had abdominal pains, vomiting, hiccups, and severe headaches; which they

thought was due to food poisoning. All subjects lost consciousness until the next day. Neighbors told the

subjects that a doctor visited them and administered some medication, but the identity of the medication

was unknown. By 2 days after the exposure, the symptoms had not disappeared, and all four were

admitted to the hospital with clinical signs of drunkenness, confusion, somnolence, ataxia, and dysarthria.

Nervous system damage progressed with cerebellar symptoms of nystagmus in all four patients, and

adiadochokinesis developing in one of the women. All subjects had disturbances of the cranial nerves

(optic, oculomotor, and facial), as well as speech disturbances, tremors, and elevated reflexes.

Tachycardia, faint heart sounds and slightly elevated blood pressure were also noted. The most severely

affected subject (one of the sisters who also had the longest exposure) suffered from jaundice, conjunctival

hemorrhages, and epigastric tenderness; however, her liver and spleen were not enlarged. The brother had

the shortest exposure and had a normal skin color. Biochemical analysis of blood and urine revealed

increases in indirect bilirubin in all three sisters and serum creatinine for all four patients. Blood urea was

increased only for the most severely affected sister. All other hematology and blood chemistry data were

normal including number of red and white blood cells, platelets, and reticulocytes; red cell osmotic fragility

test; coagulation factors; serum electrophoresis, cholesterol, alkaline phosphatase, ALT, AST, and

fibrinogen; and blood glucose, blood ammonia, bone marrow smears, blood pH, and blood gases.
CHLOROMETHANE 66

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Electroencephalograms were also normal. The three sisters received symptomatic treatment with isotonic

glucose, B complex vitamin, and oxygen. The treatment resulted in a disappearance of all symptoms of

intoxication except ataxia. The brother refused treatment. Symptoms of kidney damage disappeared after

two weeks, and the outcome of the intoxication was, in the words of the physicians, good in all cases

(Spevak et al. 1976).

Stewart et al. (1980) found no exposure-related neurological abnormalities, abnormal EEG, effect on

cognitive test, or significant subjective response from acute exposures up to 150 ppm in volunteers. This

study, however, had several limitations such as small sample size, multiple dosing schemes, and a

confusing protocol. Specifically, groups of two to four men and two to four women were exposed to 10,

100, or 150 ppm or to concentrations that were increased from 50-1.50 ppm in the same group for 1, 3, or

7.5 hours per day over 2-5 days per week for 1 or 2 weeks. Several subjects, both male and female,

dropped out of the study before some of the experiments were completed, and other subjects were added.

The same subjects were also included in different protocols during different weeks of the study.

Gudmundsson (1977) reports on a 20-month and 13-year follow-up after an acute high level exposure to

chloromethane. Seventeen crew members (males) were exposed for 2 days in 1963 to chloromethane that

leaked from a refrigerator on board an Icelandic fishing trawler (no estimates of exposure levels were

reported). The refrigerator was located under the sleeping quarters of the crew. This case history describes

both the acute phase of the illness and a follow-up of the survivors at 20 months and 13 years postexposure.

Fifteen of the seventeen crew members exposed to chloromethane showed signs of intoxication.

In the acute phase of the illness, nine patients exhibited abnormal neurological signs. Four died, one within

24 hours of the exposure. Two patients developed severe depression and committed suicide 11 and

18 months later, respectively. The fourth patient was assessed as 75% disabled due to severe neurological

and psychiatric disturbances, and died 10 years postexposure at the age of 34. Autopsy revealed recent

coronary occlusion (not necessarily connected with the primary illness). At 20 months postexposure, 7

patients had neurological symptoms (not specified), and 8 had psychiatric complaints primarily

psychoneurosis and depression. Five survivors stated they had a reduced tolerance to alcohol. Thirteen

years later (i.e., in 1976) 10 of the 11 survivors were examined (one lived in a foreign country and could

not be located). The mean age of the 10 survivors examined was 38.3 years (range 30-50 years). All 10

were employed; 8 were employed at sea. Neurological deficits included fine tremor of the hands in three

survivors, paralysis of accommodation in two, and signs of peripheral neuropathy in two. Five survivors

had no abnormal neurological signs. Six survivors had marked neurotic and depressive symptoms. Two
CHLOROMETHANE 67

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complained of decreased libido and two complained of severe headache. Alcohol may be a confounding

factor. Nine survivors complained of a markedly reduced tolerance for alcohol, and the same number

complained of early fatigue and decreased stamina. Excessive alcohol consumption was admitted by four

survivors. Alcohol may contribute to the peripheral neuropathy. Regarding the progress or reversibility of

the symptoms, one patient who had considerable muscle atrophy and fasiculations 20 months after the

accident had improved by 13 years postexposure, but still exhibited signs of anterior horn damage. In two

survivors, the paralysis of accommodation remained unchanged, but in one there was a complete

regression. In conclusion, all survivors of the acute chloromethane exposure suffered from mild to

permanent neurological and/or psychiatric sequelae directly attributable to chloromethane neurotoxicity.

Some information on longer term exposures is available. MacDonald (1964) presented eight case reports

of chloromethane poisoning in a polymer plant. Symptoms of blurring vision, mental confusion, headache,

loss of coordination, and dizziness were common. More severely intoxicated individuals experienced

nausea and vomiting. Personality changes, depression and irritability were reported by many of the cases.

The symptoms persisted for months. It was not possible to determine the LOAEL.

Schamweber et al. (1974) presented 6 case studies of workers who were exposed to relatively low levels

(200-400 ppm) of chloromethane for at least 2-3 weeks before onset of symptoms. Two cases occurred

after “prolonged” (not otherwise specified) exposure to S-hour TWA levels up to 300 ppm. Four cases

occurred after work exposure on the order of 265 ppm (S-hour TWA) after 2-3 weeks of 12-16 hour days.

A 54-year-old worker initially suffered from confusion, blurry vision, erratic driving, difficulty in eating

and swallowing, headache, and disturbance of balance. Three weeks after hospitalization, the patient still

complained about headache and had a staggered gait. Memory difficulties persisted for 2 months. Patient

improved at three months, but still had tremors and nervousness. A second B-year-old worker had

delirium, confusion, disorientation, and combativeness. Two months after hospitalization, the patient still

had poor memory and nervousness. Three months later, the patient was well enough to return to work. A

33-year-old foam worker had blurred vision, increased tiredness, nervousness, and stuttering that resolved

after a 6-week recovery period. Other foam workers developed similar symptoms with impairment in

memory, gait, and speech (tongue swelling, slurring) and vision (diplopia, blurred), slight to moderate

increase in blood pressure, and an EEG with a predominance of slow waves in the beta range that resolved

from 1 to 3 months after removal from exposure. The authors concluded that an 8-hour TWA of 200 ppm

or greater is necessary for development of chronic chloromethane intoxication based on these and other

industrial experiences.
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Repko et al. (1977) performed a study on the effects of chloromethane from exposures to workers.

Seventy-three behavioral measures of task performance, four indices of exposure, eight indicators of

neurological function, and a clinical EEG were obtained. The exposed population was derived from several

fabricating plants. Ambient air concentrations of chloromethane ranged from 7.4 to 70 ppm, with means

from each plant ranging from 8.46 to 58.72 ppm. The overall mean was 33.57 ppm. Mean concentration

of chloromethane in breath ranged from 2.67 to 24.19 ppm, with a mean of 13.32 ppm. Correlations were

found between the duration of exposure and breath concentration, duration and ambient concentration,

concentration in air and concentration in breath, chloromethane in air and hematocrit, urine pH and

hematocrit, and duration and hematocrit. There were no significant differences in neurological tests or

EEGs. In the behavioral battery, effects on cognitive time-sharing and finger tremor were found, but

correlation coefficients indicated that chloromethane in breath is not a sensitive indicator of performance

deficit. Workers showed a general tendency toward poorer performance as chloromethane levels in air

increased. The authors concluded that occupational exposure to chloromethane below 100 ppm produces

subtle, quantifiable behavioral effects, but that data on the threshold at which chloromethane begins to

produce these changes in functional capacity are not currently available. A limitation of this study was the

inability to achieve perfect matching as to sex, race, age, and level of education.

Chloromethane exposure also results in neurological effects in animals. Rats, mice, rabbits, guinea pigs,

dogs, cats, and monkeys exposed to chloromethane until death all displayed signs of severe neurotoxicity,

including paralysis and convulsions (Smith and von Oettingen 1947a, 1947b). As discussed in Section

2.2.1.1, these studies have several limitations that preclude determination of concentration-duration-response

relationships, but the results do demonstrate the universal response of animals to the neurotoxic

effects of chloromethane.

More recent animal studies support the neurotoxic potential of chloromethane, with sufficiently high levels

of acute inhalation exposure leading to ataxia, tremors, limb paralysis and incoordination, and cerebellar

lesions consisting of degeneration of the granular layer. Mice appear to be more sensitive than rats, with

similar but more severe responses at lower exposure concentrations.

After 48 continuous hours of chloromethane exposure at 1,000 ppm, Sprague-Dawley rats were lethargic

compared to the controls, and their condition worsened to sick or moribund by the end of a 72-hour

exposure. The 2,000 ppm exposure eventually led to death. There were no effects on brain weight, and no
CHLOROMETHANE 69

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exposure-related gross or histopathological lesions in the brain. No effects were seen at 500 ppm for up to

72 hours of exposure (Burek et al. 1981).

Male Fischer 344 rats exposed to 5,000 ppm chloromethane alone for 5 days, 6 hours/day had more

pronounced signs of central nervous system toxicity (tremors, ataxia, forelimb/hindlimb paralysis) than

those receiving chloromethane plus pre-and post-treatment with the potent anti-inflammatory agent,

BW755C (10 mg/kg, intraperitoneally 1 hour pre- and postexposure). Chloromethane alone caused a

degeneration of cerebellar granule cells, while rats exposed to chloromethane and BW755C did not exhibit

this effect. The result was surprising because this brain lesion is not usually associated with inflammation.

The authors concluded that protection from chloromethane-induced injury by BW755C was not simply the

result of altered metabolism because BW755C had no effect on tissue distribution or excretion of

14C-chloromethane, and administration of BW755C did not decrease hepatic glutathione content. The

protection of BW755C may have been related to an inhibition of leukotriene and prostaglandin synthesis

(Chellman et al. 1986a).

Fischer 344 rats were exposed to 0, 2,000, 3,500, or 5,000 ppm chloromethane for 6 hours/day,

5 days/week, for 2 weeks. On day 5, hind limb paralysis was observed in two males and one female in the

5,000 ppm group. After the fifth day, 13 animals were killed in extremis (5,000 ppm:6 males, 5 females;

3,500 ppm:2 females). By the second week, the rats appeared to tolerate the exposures much better, but

one 5,000 ppm female had convulsive seizures during the last exposure. Histological examination of the

brain and thoracic spinal cord revealed minimal to moderate degeneration of cerebellar internal granular

layer in two females and three males exposed to 5,000 ppm. The lesions were identical to those seen in

mice. There were no lesions in the spinal cord. The authors concluded that this study confirmed the

existence of species, sex, and strain differences in susceptibility to chloromethane-induced toxicity. No

neurological or histopathological lesions were reported for the 3,500 ppm group. The 3,500 ppm dose is

not designated a NOAEL due to the absence in the report of an explicit statement that no neurotoxicity

occurred at 3,500 ppm and the severity of this effect reported for the 5,000 ppm mice. C3H, C57BL/6, or

B6C3F1 mice were exposed to chloromethane for 12 days, 6 hours/day. Mice were exposed to 0,500,

1,000, or 2,000 ppm. Some of the mice that died had moderate to severe ataxia. Histologically, there were

no brain lesions at 500 ppm in any strain. Cerebellar degeneration was seen as follows: C3H mice (none);

C57BL/6 mice, 3 of 5 males and 5 of 5 females exposed to 1,000 ppm and 0 of 5 males and 4 of 4 females

exposed to 2,000 ppm; B6C3F1 mice, 2 of 5 females exposed to 2,000 ppm. The lesions were most severe

in 2,000 ppm C57BL/6 females, followed by 1,000 ppm C57BL/6 males. The cerebellar lesions consisted
CHLOROMETHANE 70

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of focal degeneration of the granular layer, which affect posture and coordination. The authors concluded

that this study confirmed the existence of species, sex, and strain differences in susceptibility to

chloromethane-induced neurotoxicity (Morgan et al. 1982).

Chellman et al. (1988a) investigated the role of glutathione in the mediation of chloromethane-induced

toxicity in the brain of male B6C3F1 mice. Mice exposed to 1,500 ppm chloromethane for 6 hours/day,

5 days/week, for 2 weeks developed multiple degenerative, necrotic foci in the internal granule cell layer of

the cerebellum; in some areas the foci involved the whole thickness of the granular cell layer. Cerebellar

degeneration consisted of granule cells with pyknotic nuclei and clear, swollen perikarya. Tremors, ataxia,

and forelimb/hindlimb paralysis were seen in chloromethane-exposed mice prior to death, and were

associated with cerebellar damage. Cerebellar damage was not observed in chloromethane-exposed mice

pretreated with a glutathione depleter. The authors concluded that the depletion of GSH protected mice

from cerebellar damage due to exposure to chloromethane. Based on this result, the mechanism of

neurotoxicity may involve conjugation of chloromethane with glutathione in the liver, followed by biliary

excretion and enterohepatic circulation of the glutathione conjugate, or possibly a cysteine conjugate, and

further metabolism by kidney and/or gut flora beta-lyase to methanethiol. Methanethiol produces similar

central nervous system symptoms (tremors, convulsion, coma) as seen in animals or humans acutely

intoxicated with chloromethane (Chellman et al. 1986b).

Jiang et al. (1985) characterized the cerebellar lesions resulting from an acute inhalation exposure of

1,500 ppm chloromethane to female C57BL/6 mice for 2 weeks, 5 days/week, 6 hours/day. Two mice

died, and several had motor incoordination. All exposed mice had varying degrees of cerebellar

degeneration located mainly in the ventral paraflocculus, but also occurring in dorsal paraflocculus.

Granule cells were mainly affected, with two distinct types of lesions: (1) nuclear and cytoplasmic

condensation of scattered granule cells with slight hydropic swelling of astrocytes (also seen to a lesser

extent in controls); and (2) focal malacia with varying degrees of watery swelling of groups or extensive

areas of granule cells, nuclear condensation, karyorrhexis, and necrosis. The second type of lesion was

more prevalent. Purkinje cells were largely unaffected by the malacic process, and the inflammatory

response was minimal. Electron microscopy showed that the damage in the areas of malacia (the type 2

lesion above) ranged in severity from edema of granule cell perikarya to severe edema and almost complete

destruction of all tissue components. Involvement of cell types other than granule cells occurred only in the

most severely affected areas (i.e., Purkinje cells were well preserved while astrocytes adjacent to Purkinje

cells [the Bergmann’s glia] showed moderate to severe cytoplasmic distention by translucent edema fluid).
CHLOROMETHANE 71

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The biochemical mechanism for the induced defects in granule cell fluid/electrolyte balance is unknown.

Only one exposure concentration was used, but the study was designed to examine the neurological and

kidney effects specifically, and therefore, used an exposure regimen known to produce these effects. Based

on the severity of the kidney effects, the authors concluded that the observed brain lesions were probably

not a direct consequence of renal lesions; rather, the mechanism may be associated with metabolic changes

in granule cells.

Landry et al. (1985) observed decreased performance on the rotating rod at an 800 ppm and greater

intermittent exposure (5.5 hours/day for 11 days) when tested at 4 days, but persisting to day 8 only in the

2,400 ppm mice (with considerably greater deficit in this group). Histological lesions consisted of slight

cerebellar granule cell degeneration in some of the mice exposed to 400, 800, or 1,600 ppm. In the

2,400 ppm group, all of the mice were affected to a slight degree. Mice exposed continuously for

22 hours/day for 11 days had similar effects at exposure levels of 100 ppm. The apparent greater

sensitivity to continuous exposure may be related to the conversion of chloromethane to an active

metabolite, decreased respiration at concentrations that are intolerable when exposure is continuous, and/or

diurnal susceptibility. Diurnal susceptibility (i.e., in this case lower sensitivity during the daytime

intermittent exposure) could result from the lower activity of mice during the daytime and the lower

respiratory minute volume.

Pregnant B6C3F1 mice exposed to 1,500 ppm chloromethane in whole-body exposure chambers,

6 hours/day on Gd 6-17 developed tremors, hunched appearance, difficulty righting, disheveled fur, bloody

urine, and granular cell degradation in cerebellum with selective necrosis of neurons in the internal granular

layer. All females in this group were sacrificed on Gd 11-14 prior to the completion of exposure to Gd 17;

two females died prior to necropsy (as early as Gd 9, after only 4 days of exposure). These effects were

not seen in the 479 ppm or lower exposure (Wolkowski-Tyl et al. 1983a).

C57BL/6 females were mated to C3H males to produce B6C3F1 offspring. After mating, 74-77 females

were exposed to chloromethane at concentrations of 0, 250, 500, or 750 ppm on Gd 6-17. Exposure to

500 ppm chloromethane resulted in ataxia in 6 of 74 females by Gd 18; exposure to 750 ppm resulted in

hyperactivity, ataxia, piloerection, tremors and convulsions. The authors concluded that inhalation

exposure to chloromethane during Gd 6-17 resulted in maternal toxicity at 750 ppm; teratogenic effects

were seen at 500 and 750 ppm. Exposure of pregnant mice to 250 ppm chloromethane produced neither

maternal nor fetal toxicity nor teratogenicity (Wolkowski-Tyl et al. 1983b).
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Beagle dogs (n=3) exposed to 500 ppm chloromethane for 23.5 hours/days for 3 days had moderate to

severe limb stiffness, tremors, salivation, and incoordination. These effects became less severe but

persisted during a 4-week recovery. All 500 ppm dogs had neurological deficiencies based on clinical

testing at 4 days after exposure, but nearly complete recovery on day 26 after exposure. Histological

examination revealed brain and spinal cord lesions in all 3 dogs consisting of vacuolization, swollen

eosinophilic axons, loss of axons, demyelinization and gitter cells. These changes were very slight and

multifocal in the brain stem (medulla, pons, or both) and slight and multifocal in the lateral and ventral

funiculi of the spinal cord. No lesions were observed in the cerebrum or cerebellum nor in the dorsal

funiculi or grey matter of the spinal cord (McKenna et al. 1981a).

Cats (n=3) exposed to 500 ppm chloromethane for 23.5 hours/days for 3 days were less active than

controls after 24 hours of exposure, but had no clinical signs after exposure. Cats did not undergo

neurological tests. Histological lesions in cats were seen in l/3 control, l/3 at 200 ppm, and 3/3 at

500 ppm; and consisted of lesions in the brain occurring in a multifocal or random pattern in the white

matter of the cerebrum, cerebellum and midbrain. In the spinal cord they primarily occurred in the lateral

and ventral funiculi. The authors did not believe that these were treatment related but were instead

consistent with infection or post-vaccinal reaction (cats were vaccinated for panleukopenia by supplier).

The authors stated that exposure to 500 ppm may have resulted in an exacerbation of a viral-induced,

spontaneously occurring disease process in the central nervous system of the cats. (McKenna et al. 1981a).

Intermittent exposures for longer durations also resulted in less severe neurotoxicity. B6C3F1 mice or

Fischer 344 rats exposed to 0, 375, 750, and 1,500 ppm for 6 hours/day, 5 days/week, for 13 weeks

showed no exposure-related histopathological lesions of brain and spinal cord and no effect on brain weight

(Mitchell et al. 1979). Beagle dogs, CD-l mice, or Sprague-Dawley rats exposed to as high as 400 ppm

chloromethane for 6 hours/day, 5 days/week for 90 days showed no apparent neurological effects

(McKenna et al. 1981b).

Longer-term higher-level exposures have, however, resulted in neurotoxicity in mice even if only for

6 hours/day. Male and female Fischer 344 rats and B6C3F1 mice were exposed to chloromethane in whole

body inhalation exposure chambers at target concentrations of 0 (control), 50, 225, or 1,000 ppm,

6 hours/day, 5 days/week for up to 24 months. Necropsies were completed at 6, 12, 18, or 24 months after

the initial exposure. As early as 6 months, the absolute brain weight was reduced in male and female mice

exposed to 1,000 ppm chloromethane; however, relative brain weights were not affected by chloromethane
CHLOROMETHANE 73

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exposure. Clinical signs of neurotoxicity (tremor, paralysis) were observed in both sexes (exposure level

not specified, but most likely 1,000 ppm). By 18 months, decreased absolute brain weights were noted in

females exposed to 1,000 ppm chloromethane. Clinical signs of neurotoxicity (tremor, paralysis) were seen

in both sexes, along with abnormal functional test neurological results (restricted use of rear legs, abnormal

gait, poor extensor thrust, leg rigidity), and cerebellar lesions (minimal to mild reduction in the number of

neurons in the granular cell layer, most prominently in the sulci). Axonal swelling and degenerative

changes of minimal severity were observed in the spinal nerves and cauda equina in the lumbar spinal cord

of 3 of 7 male mice (1,000 ppm), 5 of 5 male and 10 of 10 female mice (225 ppm), 4 of 5 male and 10 of

10 female mice (50 ppm), and 1 of 5 male and 2 of 10 female mice (control). The neurotoxic lesions

progressed in frequency and severity in mice to the end of the exposure period. In contrast to its effects in

mice, chloromethane did not produce neurotoxicity in rats (i.e., negative clinical, pathological, and

functional tests) at levels up to 1,000 ppm for 6 to 24 months in duration (CIIT 1981). The mechanisms

underlying this dramatic difference in species susceptibility are not understood.

The highest NOAEL values and all reliable LOAEL values in each species and duration category are

recorded in Table 2-l and plotted in Figure 2-l. The 50 ppm concentration in mice exposed acutely

(Landry et al. 1985) is the highest NOAEL below which no LOAEL exists. At 100 ppm, the mice had

cerebellar lesions. Based on the NOAEL of 50 ppm, an acute inhalation MRL of 0.5 ppm was calculated

as described in the footnote to Table 2-l and in Appendix A. The 51 ppm concentration in mice exposed

chronically to chloromethane (CIIT 1981) is the lowest LOAEL (axonal swelling and slight degeneration of

axons in the spinal cord). Based on this LOAEL, a chronic inhalation MRL of 0.05 ppm was calculated as

described in the footnote to Table 2-1 and in Appendix A. These MRLs are presented in Figure 2-1.

2.2.1.5 Reproductive Effects

No studies were located regarding reproductive effects in humans after inhalation exposure to

chloromethane.

Chloromethane has been shown to be a reproductive toxicant in a variety of animal studies.

Sprague-Dawley rats exposed to 500 ppm for 48 hours had increased proteinaceous and cellular aggregates

in the epididymis with interstitial edema (2/5 rats) and focal suppurative inflammation (l/5) immediately

after the exposure. By 12 days postexposure, the lesions had increased in severity with the formation of

sperm granulomas, decreased sperm in the tubule lumen, interstitial edema, coagulated proteinaceous
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debris or inflammation leading to obstructive changes causing at least partial occlusion of the affected

lumen, and unilateral testicular atrophy. The lesions were more severe in rats exposed to higher

concentrations and/or for the longer duration. Mean absolute and relative testicular weight was decreased

to 50% in rats exposed to 1,000 ppm for 72 hours; this effect was thought to be secondary to a severely

obstructed epididymis. The decreased testes weight was not observed in 1,000 ppm rats exposed for

48 hours or in males exposed to 200 or 500 ppm for either duration (Burek et al. 1981).

Male Fisher 344 rats were exposed to 3,500 ppm chloromethane for 6 hours/day for 5 days, then a stop in

exposure for 3 days, and then a restarting of the exposure for another 4 days. This regimen resulted in

several testicular and epididymal lesions and interference with neuroendocrine control of spermatogenesis.

The initial testicular effects were directed at either the late stage spermatids or the Sertoli cells with a

resultant delay in spermiation. No testicular abnormalities were found at 5 days, but at 7 days one rat had

scattered foci of disruption of seminiferous epithelium, and exfoliation of germinal cells. By day 9 all

exposed rats had disruption of spermatogenesis, and by day 13 all had disruption and disorganization of

seminiferous epithelium and epithelial vacuolation. At 70 days, 70-90% of seminiferous tubules were

shrunken, contained whorls of Schiff’s reagent-positive material, and had Sertoli cell nuclei near the

basement membrane. The remainder showed varying degrees of recovery. All animals killed after 19 days

displayed bilateral epididymal granulomas in regions 5 or 6 of the cauda epididymis. The nature and

distribution of the inflammatory cells indicated that the primary neutrophilic response may have been

against the tubular epithelium and not extravasated sperm. Serum testosterone showed a time dependent

decrease during the 5 consecutive days of exposure (not seen in the pair-fed controls). Leydig cell and

gonadotropin function was normal when challenged with hCG and LHRH; thus, the authors propose that

chloromethane lowers circulating testosterone by acting in the brain to decrease circulating levels of

gonadotrophic hormones. NPSH content was depleted in testis, caput and caudal epididymides samples,

but not in heart blood. This effect is thus probably the result of enzyme-mediated conjugation of

glutathione with chloromethane, and not a consequence of direct alkylation. The authors speculate that

chloromethane conjugation with testicular and epididymal glutathione may result in depletion of

glutathione, which serves in a variety of protective cellular functions (Chapin et al. 1984).

Rats exposed to 7,500 ppm chloromethane 6 hours/day for 2 days developed epididymal granulomas within

3 weeks after exposure (Chellman et al. 1986a). Effects of 7,500 ppm chloromethane on testes were not

reported. Rats exposed to 5,000 ppm, 6 hours/day for 5 days developed sperm granulomas in the

epididymides, and testicular lesions (exfoliation of pachytene spermatocytes and early stage spermatids).
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No granulomas were found in rats treated concurrently with chloromethane and the anti-inflammatory

agent, amino-l-[m-(trifluoromethyl)-phenyl]-2-pyrazoline (BW755C). There was also no evidence of

epididymal or testicular lesions in rats treated with both 5,000 ppm chloromethane and BW755C.

BW755C, therefore, protected rats against chloromethane toxicity. The authors concluded that protection

from chloromethane-induced injury by BW755C was not simply the result of altered metabolism because

BW755C had no effect on tissue distribution or excretion of 14C-chloromethane, and administration of

BW755C did not decrease hepatic glutathione content. The protection of BW755C may have been related

to an inhibition of leukotriene and prostaglandin synthesis.

Chellman et al. (1986c) investigated the relationship between chloromethane-induced epididymal

inflammation and the occurrence of dominant lethal mutations in male Fischer 344 rats. Chloromethane

exposure at 3,009 ppm for 6 hours/day for 5 days resulted in a significant increase in pre-implantation loss

in females mated with exposed males at weeks 2 and 3 postexposure, and BW755C did not protect against

this effect. The authors concluded that pre-implantation losses were due to the cytotoxic effect of

chloromethane on the testes. A subsequent study by the authors (see Chellman et al. 1987) showed reduced

numbers and abnormal sperm from chloromethane induced testicular toxicity in male rats, leading to a

failure to fertilize.

Chellman et al. (1987) also investigated the role of chloromethane-induced testicular and epididymal

inflammation in the induction of sperm cytotoxicity and preimplantation loss in male Fischer 344 rats.

Rats exposed to 3,056 ppm chloromethane 6 hours/day for 5 consecutive days had significantly decreased

relative weight of seminal vesicles at week 1, epididymis at weeks 2 and 3, and testes at week 3; disruption

of spermatogenesis (delayed spermiation, disorganization of seminiferous epithelium, and decreased

number of mid- and late spermatids); and decreased sperm production per day at weeks 1, 2, and 3

postexposure. Epididymal examination revealed visible sperm granulomas and inflammation; a large

amount of PAS-positive material in epididymis associated with greatly decreased number of sperm,

increased number of abnormal sperm and cellular debris of testicular origin; reduced number of sperm,

decreased percent motile sperm and percent intact sperm, and increased abnormal sperm in the vas deferens

by week 3. Concurrent treatment with BW755C did not protect the rats from these testicular effects, but

did protect the rats from the formation of sperm granulomas and inflammation in the epididymides. The

authors concluded that chloromethane-induced sperm toxicity was due to toxicity to the testes, rather than

the result of inflammation and granuloma formation in the epididymis. This testicular toxicity and
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2. HEALTH EFFECTS

movement of damaged sperm out of the testes into the epididymis and vas deferens was probably

responsible for fertilization failures and preimplantation losses seen by Working and Bus (1986).

Male Fischer 344 rats were exposed to chloromethane at 0, 2,000, 3,500, or 5,000 ppm for 5 days,

6 hours/day with a break in exposure for 2 days, and then a further 4 days of exposure. Histological

examination of the testes and epididymides revealed testicular degeneration in all males of all exposed

groups with a clear dose-related increase in severity. The testicular lesions consisted of a reduction in or

lack of late stage spermatids, separation of spermatocytes, and early stage spermatids. The lumen of

epididymal tubules contained greatly reduced numbers of sperm. There was a dose-related increase in

eosinophilic, hyaline droplets and degenerating cells of unknown type (Morgan et al. 1982).

Pregnant Fischer 344 rats exposed to 1,492 ppm chloromethane 6 hours/day on Gd 7-19 had significantly

depressed maternal food consumption and weight gain during exposure, but there were no statistically

significant differences among the treatment groups for number of litters, percent litters with live fetuses, the

number of corpora lutea, number of implantations, number or percent resorptions, number of live fetuses

per litter, or fetal sex ratio. B6C3F1 mice exposed to 1,492 ppm chloromethane for 6 hours/day on

Gd 6-17 developed severe maternal toxicity resulting in tremors, hunched appearance, difficulty righting,

disheveled fur, bloody urine, and granular cell degradation in cerebellum with selective necrosis of neurons

in the internal granular layer. All females in this group were sacrificed on Gd 11-14 prior to the completion

of exposure to Gd 17; two females died prior to necropsy (as early as Gd 9, after only 4 days of exposure).

These effects were not seen in the 479 ppm group. There were no significant differences for exposures of

479 ppm or less for the number of litters, percent litters with live fetuses, the number of corpora lutea,

number of implantations, number or percent resorptions, number of live fetuses per litter, or fetal sex ratio

(Wolkowski-Tyl et al. 1983a).

Working and Bus (1986) assessed the effects of inhalation exposure to chloromethane on preimplantation

loss to distinguish between cytotoxicity (i.e., fertilization rate) and genotoxicity in rats. Male Fischer 344

rats exposed to chloromethane at 3,000 ppm for 5 days, 6 hours/day were bred to no more than 2 females

weekly during weeks l-4 and week 8 post-exposure. Males in the 1,000 ppm group were bred to no more

than 2 females during week 3 post-exposure. Females were sacrificed lo-12 hours postmating, and

embryos and ova were scored as fertilized or unfertilized. In an in vitro experiment, fertilized ova were

examined in culture for cleavage. The combined fertilization rate in all females bred to control males was

88%. In females bred to the 1,000 ppm males, 80% of ova were fertilized. In females bred to the
CHLOROMETHANE 77

2. HEALTH EFFECTS

3,000 ppm males, fertilization of ova was 39% at week 1 of mating, 3.4% at week 2, 22.1% at week 3,

41% at week 4, and 72% at week 8. There were no significant differences in the cleavage rates of ova from

females bred to controls (96.5%) or to males exposed to 1,000 or 3,000 ppm chloromethane (92.4-93.8%).

The authors concluded that all preimplantation losses observed in previous studies (Working et al. 1985a)

could be explained by a cytotoxic effect resulting in failure of fertilization and not a genotoxic effect

resulting in early embryonic death (Working and Bus 1986).

Working et al. (1985a) studied the effects of inhalation exposure to chloromethane on germ cell viability in

male Fischer 344 rats. At 17 weeks after exposure to 3,000 ppm chloromethane for 6 hours/day for

5 days, 30% of the males had sperm granulomas in one or both epididymides; none were noted in the

1,000 ppm or control groups. Exposure to 3,000 ppm chloromethane also resulted in a slight increase

(9.5%) in postimplantation loss only at week 1 postexposure (sperm exposed in epididymis or vas

deferens), but increased preimplantation losses at week 1 (31.4%), peaking at week 2 (93.6%) then

declining to 14.1% by week 8 postexposure. Fertility in males exposed to 3,000 ppm chloromethane was

significantly decreased by postexposure week 2 and remained depressed throughout the study period. The

authors concluded that a cytotoxic rather than genotoxic mechanism may play a role in the observed

preimplantation losses. They further speculated that inflammation-derived reactive metabolites (e.g.,

superoxide anion) could damage DNA or sperm in epididymis (Working et al. 1985a).

Fischer 344 rats exposed to 3,000 ppm chloromethane at 6 hours/day for 5 days had decreased testicular

weight from the third post-exposure week with a steady decline to 50% by week 8, and a recovery by week

16. Histologically, sperm granulomas in epididymides were observed in 50% of the exposed rats.

Disruption of spermatogenesis in testes, decreased number of sperm, increased number of abnormal sperm,

and decreased sperm motility were also observed. Recovery was nearly complete by week 16. The authors

concluded that inhalation of high concentrations of chloromethane produce a prolonged cytotoxicity in

testes leading to oligospermia due initially to depletion of postmitotic stages of spermatogenic cells, and

ultimately to the killing of spermatogonial stem cells. The resultant decreased fertility was not permanent.

The inflammation of the epididymis may account for depressed motility and increased numbers of abnormal

sperm, but a genotoxic effect could not be ruled out on the basis of this study (Working et al. 1985b).

Exposure to chloromethane up to 750 ppm had no effect on reproductive parameters in C57BL/6 females

mated to C3H males to produce B6C3F1 offspring, such as the percentage of pregnant females, the number

of implantations/litter, number of resorptions/litter, or the number of dead/litter. The authors concluded
CHLOROMETHANE 78

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that inhalation exposure to chloromethane during Gd 6-17 resulted in maternal toxicity only at 750 ppm

and teratogenic effects at 500 and 750 ppm. Exposure of pregnant mice to 250 ppm chloromethane

produced neither maternal nor fetal toxicity nor teratogenicity (Wolkowski-Tyl et al. 1983b).

Beagle dogs or cats exposed to 500 ppm chloromethane for 23.5 hours/days for 3 days and observed for

4 weeks (dogs) or two weeks (cats) postexposure showed no changes in weights of testes or development of

histopathological lesions in the testes (McKenna et al. 1981a). No exposure-related gross or

histopathological lesions in reproductive organs and no changes in testes weight occurred from exposures

up to 400 ppm for 6 hours/day 5 days/week for 90 days in CD-l mice, Beagle dog, or Sprague-Dawley rat

(McKenna et al. 1981b) or up to 1,473 ppm in Fisher 344 rats (Mitchell et al. 1979).

Han-n-n et al. (1985) examined whether an inhalation exposure to chloromethane affected the reproductive

status of Fischer 344 rats exposed to 1,500 ppm chloromethane 6 hours/day, 5 days/week for 10 weeks

premating, and then for 7 days/week during a 2-week mating period. Male rats exhibited seminiferous

tubule atrophy (lo/lo) and granulomas in the epididymis (3/10) following exposure. No treatment effects

were noted for litter size, sex ratio, pup viability, pup survival, or pup growth, and there was no significant

difference in fertility between exposed and nonexposed females. In the F0 recovery study, males exposed to

1,500 ppm chloromethane experienced a partial recovery of fertility, while males exposed to 475 ppm

chloromethane experienced a full recovery. There were no F1 litters from the 1,500 ppm group. Chloromethane

had no statistically significant effect on fertility in the second generation (F1 for 151 and 472 ppm

exposures), but there was a dose related trend towards fewer litters and fewer males proven fertile in the

475 ppm group. Litters in the 475 ppm group had a significantly decreased percentage of males and

significantly less male and female F2 pup growth only during postnatal days 14 to 21. The significance of

these affects are unknown (Han-m et al. 1985). The study did not mate unexposed males with exposed

females. Such a mating with females exposed to 1,500 ppm would be necessary to rule out an effect on

female fertility. Reduced fertility may be due to a cytotoxic effect on the testes (Working et al. 1985a,

1985b).

Male and female Fischer 344 rats and B6C3F1 mice were exposed to chloromethane in whole body

inhalation exposure chambers at target concentrations of 0 (control), 50, 225, or 1,000 ppm, 6 hours/day,

5 days/week for 6, 12, 18, or 24. At 12 months, there were no exposure-related lesions in reproductive

organs of mice exposed to chloromethane at concentrations up to 1,000 ppm., but lesions developed in the

later months. Seven of 43 males exposed to 1,000 ppm, and that died or were sacrificed between 18 and
CHLOROMETHANE 79

2. HEALTH EFFECTS

21 months, had testicular germinal cell degeneration, giant cell formation, and tubular atrophy, compared

with l/20 controls sacrificed at 24 months. Lesions developed earlier in the rat. By 6 months of exposure

in rats, one male rat from the 1,000 ppm group had bilateral, diffuse degeneration and atrophy of the

seminiferous tubules. This lesion significantly increased in this group at later sacrifices. At 12 months,

gross and histological examination of testes and epididymides of males revealed germinal epithelial

degeneration and atrophy of seminiferous tubules (4/10 males exposed to 1,000 ppm chloromethane).

Chloromethane exposure had no effect on testis or ovary weights. At 18 months, gross and histological

examination of testes and epididymides of male rats exposed to 1,000 ppm revealed germinal epithelial

degeneration and atrophy of seminiferous tubules. Exposure to chloromethane had no effect on testes or

ovary weights. Sperm granulomas were seen in two 1,000 ppm male rats at the 6-month sacrifice, in one

male each at 50 and 225 ppm at 18 month, and in one male at 1,000 ppm at 24 months. None were seen at

12 months. The authors stated that it is possible that the sperm granulomas were induced early but

resolved at later times, or that the lesion was spontaneous, but it is not possible to definitively attribute the

lesions to chloromethane exposure on the basis of the results of this study. By 24 months, all male rats,

including controls, had interstitial cell hyperplasia or adenomas associated with aging, which precluded

detection of further exposure-related seminiferous tubule degeneration and atrophy. Absolute and relative

testes weights were decreased in the 1,000 ppm group. There was a concentration-related decrease in

bilateral compressive degeneration and atrophy and increase in unilateral compressive degeneration and

atrophy (caused by testicular tumors), which correlated with decreased interstitial cell tumor size. This

observation was supported by the testicular weight decreases observed in 1,000 ppm exposed male rats

(CIIT 1981).

The highest NOAEL values and all reliable LOAEL values for reproductive effects in each species and

duration category are recorded in Table 2-1 and plotted in Figure 2-1.

2.2.1.6 Developmental Effects

No studies were located regarding developmental effects in humans after inhalation exposure to

chloromethane.

Maternal toxicity, evidenced by decreased body weight gain and retarded development of fetuses, was

observed in rats exposed to 1,500 ppm chloromethane for 6 hours per day during gestational days

(Gd) 7-19 (Wolkowski-Tyl et al. 1983a). The fetal effects consisted of reduced fetal body weight and
CHLOROMETHANE 80

2. HEALTH EFFECTS

crown-rump length and reduced ossification of metatarsals and phalanges of the anterior limbs, thoracic

centra in the pubis of the pelvic girdle, and metatarsals of the hindlimbs.

Wolkowski-Tyl et al. (1983a) also found increased incidences of heart malformations in the fetuses of

mouse dams exposed by inhalation to 480 ppm chloromethane during Gd 6-17. The heart malformations

consisted of absence or reduction of atrioventricular valves, chordae tendineae, and papillary muscles.

Heart malformations, however, were not found in fetuses of mouse dams exposed to higher concentrations

of chloromethane during Gd 11.5-125, which they considered to be the critical period for development of

the embryonal heart (John-Greene et al. 1985). John-Greene et al. (1985) suggested that the heart anomaly

reported by Wolkowski-Tyl et al. (1983) may have been an artifact of the sectioning technique, due to the

examination of the fixed as opposed to unfixed fetal tissue, or a misdiagnosis. They also found much interanimal variability in the appearance of the papillary muscles in control mice. However, Wolkowski-Tyl

(1985) countered that the inability of John-Greene et al. (1985) to detect the abnormality was due to the

different exposure protocol, and that the critical period is more appropriately gestational day 14. The

developmental toxicity of chloromethane in mice is, therefore, controversial; it is not known whether

chloromethane could produce developmental effects in humans.

The highest NOAEL and all reliable LOAEL values for developmental effects in mice and rats are recorded

in Table 2-1 and plotted in Figure 2-1.

2.2.1.7 Genotoxic Effects

No studies were located regarding genotoxic effects in humans after inhalation exposure to chloromethane.

In animals, chloromethane exposure has resulted in dominant lethal mutations in the sperm of male rats

(Chellman et al. 1986c; Rushbrook 1984; Working et al. 1985a). Experiments on the mechanism of the

postimplantation loss observed in the females mated to the exposed males indicated that the dominant lethal

effect may be secondary to epididymal inflammation, rather than a direct genotoxic effect of chloromethane

(Chellman et al. 1986c). Chloromethane did not result in unscheduled DNA synthesis in hepatocytes,

spermatocytes, or tracheal epithelial cells when male rats were exposed to 3,500 ppm, 6 hours per day for

5 days, but did produce a marginal increase in unscheduled DNA synthesis in hepatocytes when rats were

exposed to 15,000 ppm for 3 hours (Working et al. 1986).
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Jager et al. (1988) have shown that the formation of formaldehyde (via P-450 activity) was 10 times higher

in male mouse liver than in male kidney. Male mouse liver also produced formaldehyde at about twice the

amount produced by female liver, and male kidney about 50% more than female kidney. This led to the

hypothesis that male mice renal tumors resulted from increased production of formaldehyde and increased

numbers of formaldehyde-induced DNA lesions. Glutathione depletion also removes the cofactor for

formaldehyde dehydrogenase (FDH), the enzyme that inactivates formaldehyde. Jager et al. (1988),

however, did not observe increased formaldehyde levels in mouse liver or kidney after a single 8-hour

exposure to 1,000 ppm chloromethane, or an increase in DNA protein cross links (DPC), a typical

formaldehyde-induced lesion, after exposure to 1,000 ppm for 6 hours per day for 4 days. Ristau et al.

(1989), however, did observe an increase in DPC in the renal tissue of male but not female B6C3F1 mice

exposed to chloromethane at 1,000 ppm for 8 hours. DNA-protein crosslinks were not observed in liver.

In a follow-up study, Ristau et al. (1990) showed a rapid removal of DPC whereas single strand breaks

appeared to accumulate. Both types of lesions were ascribed to the action of formaldehyde. Ristau et al.

(1989) assayed for DPC immediately after a single 8-hour exposure, whereas Jager et al. (1988) dosed

over a 4-day period. Delays from exposure to assays that allow rapid repair of formaldehyde-induced

DPCs could possibly explain why Jager et al. (1988) did not observe an increase. Both the DPCs and the

incomplete and delayed repair of chloromethane-induced DNA lesions may contribute to the formation of

renal tumors. Other genotoxicity studies are discussed in Section 2.5.

2.2.1.8 Cancer

A retrospective epidemiology study of male workers exposed to chloromethane in a butyl rubber

manufacturing plant produced no statistical evidence that the rates of death due to cancer at any site were

increased in the exposed population when compared with U.S. mortality rates (Holmes et al. 1986). No

specific exposure levels were given in this study.

Rafnsson and Gudmundsson (1997) report on excess mortality from cancer in a long-term follow-up after

an acute high-level exposure. Seventeen crew members (males) were exposed for 2 days in 1963 to

chloromethane that leaked from a refrigerator on board an Icelandic fishing trawler (no estimates of

exposure levels were reported). The refrigerator was located under the sleeping quarters of the crew.

Gudmundsson (1977) reported mild to permanent neurological and/or psychiatric sequelae at 20 months

and 13 years postexposure. This study evaluated a cohort of 24 men on board the vessel at 32 years

postexposure (6 officers and 18 deckhands including the surviving crew members who had the highest
CHLOROMETHANE 82

2. HEALTH EFFECTS

exposure). The reference group was selected from three registries of seamen. The Icelandic registries for

seamen are some of the most comprehensive and complete available. The reference group contained five

times as many individuals as the study group, and was controlled for age, occupation, and social class.

The authors report an excess mortality from all causes associated with chloromethane exposure (MantelHaenszel point estimate=2.2, 95%; CI=1.3-3.1). An elevated mortality from all cancers was also reported

(M-H=15, 95%; CI=0.3-5.6) and for lung cancer (M-H=2.7, 95%; CI=0.l-52.6). Because the reference

group matched for age, occupation, and social class, the authors assumed simultaneous control for lifestyle

factors including smoking habits and diet. Conclusions from this study are limited because of this

assumption. Indirect effects of the neurological deficits in this cohort on cancer susceptibility or lifestyle

factors were also not discussed.

A high incidence of renal tumors was found in male mice that were exposed to 1,000 ppm chloromethane

and died or were killed at 12 months or later in a 2-year oncogenicity study (CIIT 1981). Tumors consisted

of renal cortex adenomas and adenocarcinomas, papillary cystadenomas, tubular cystadenomas, and

papillary cystadenocarcinomas. No evidence of carcinogenicity was found in female mice or in male or

female rats exposed to concentration of 1,000 ppm or less in this study. The cancer effect levels from this

study are recorded in Table 2-l and plotted in Figure 2-1.

2.2.2 Oral Exposure

2.2.2.1 Death

No studies were located regarding death in humans or animals after oral exposure to chloromethane.

2.2.2.2 Systemic Effects

No studies were located regarding respiratory, cardiovascular, gastrointestinal, hematological,

musculoskeletal, renal, endocrine, dermal, ocular, or body weight effects in humans or animals after oral

exposure to chloromethane.

Hepatic Effects. No studies were located regarding hepatic effects in humans after oral exposure to

chloromethane.
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Only one animal study was located in which chloromethane was administered orally. In this study, the

hepatotoxic effects of chloroform, carbon tetrachloride, dichloroethane, and chloromethane were compared

(Reynolds and Yee 1967). Rats were given chloromethane in mineral oil by gavage at a single dose of

420 mgkg. Only the livers were examined for effects, but no liver necrosis was found in the rats given

chloromethane. Higher doses of chloromethane were not administered because of the known anesthetic and

lethal effects of the compound. The NOAEL from this study is recorded in Table 2-2 and plotted in

Figure 2-2.

No studies were located regarding the following health effects in humans or animals after oral exposure to

chloromethane:

2.2.2.3 Immunological and Lymphoreticular Effects

2.2.2.4 Neurological Effects

2.2.2.5 Reproductive Effects

2.2.2.6 Developmental Effects

2.2.2.7 Genotoxic Effects

Genotoxicity studies are discussed in Section 2.5.

2.2.2.8 Cancer

No studies were located regarding cancer in humans or animals following oral exposure to chloromethane.

2.2.3 Dermal Exposure

2.2.3.1 Death

No studies were located regarding death in humans or animals after dermal exposure to chloromethane.


CHLOROMETHANE 86

2. HEALTH EFFECTS

2.2.3.2 Systemic Effects

No studies were located regarding respiratory, cardiovascular, gastrointestinal, hematological,

musculoskeletal, hepatic, renal, endocrine, dermal, or body weight effects in humans or animals after

dermal exposure to chloromethane.

Ocular Effects. No studies were located regarding ocular effects in humans after dermal exposure to

chloromethane.

A limited number of animal studies report ocular effects, but the results are mixed. Beagle dogs and cats

were exposed by inhalation to 0, 200, or 500 ppm chloromethane 23.5 hours/day for 3 days, and were

observed for 4 weeks (dogs) or 2 weeks (cats) postexposure before sacrifice. No ocular effects were

observed in dogs from direct contact with chloromethane gas. On postexposure day 13, examination of the

cat eye revealed focal opacity of the cornea consistent with a temporally persistent papillary membrane in

the left eye of a control cat and a 200 ppm cat. These lesions were not considered to be treatment related

(McKenna et al. 1981a).

Mitchell et al. (1979) reported mucopurulent conjunctivitis with total destruction of the eye in B6C3F1 mice

exposed to 375, 750, or 1,500 ppm for 6 hours/day, 5 days/week, for 13 weeks. No eye lesions were

observed in controls. These lesions were attributed to exposure because no lesions were found in controls;

however, the failure of longer-term studies to detect comparable eye lesions at higher concentrations makes

the findings of Mitchell et al. (1979) questionable.

Beagle dogs exposed to 400 ppm chloromethane for 6 hours/day, 5 days/week for 90 days had no

exposure-related gross or histopathological lesions in the eyes from direct contact with chloromethane gas

(McKenna et al. 1981b).

Male and female Fischer 344 rats and B6C3F1 mice were exposed to chloromethane at target

concentrations of 0, 50, 225, or 1,000 ppm, 6 hours/day, 5 days/week. Ophthalmic exams were performed

at baseline and at sacrifice. At 6 months, cornea1 cloudiness or opacity without conjunctivitis was noted in

control rats (2 of 10 male rats and 1 of 10 females), at 50 ppm (1 of 10 males at 12 months), and at

225 ppm (1 of 10 females at 18 months). The significance of this lesion is not clear because there was no

dose-related incidence pattern at later sacrifices. At 12 months, a cornea1 lesion described as a haze
CHLOROMETHANE 87

2. HEALTH EFFECTS

elliptically patterned over a central portion of the eye was seen in control rats (1 of 10 males and l/ of 10

females), at 50 ppm (8 of 10 males and 6 of 10 females), at 225 ppm (9 of 10 males and 7 of 10 females),

and at 1,000 ppm group (9 of 10 males and 9 of 10 females). This lesion was only seen at 12 months and

was distinctly different from the cornea1 cloudiness or opacity seen at 6 or 18 months. This cornea1 haze

may have been the result of chemical effects upon the eyes in which the lacrimal function was compromised

by intercurrent disease (an outbreak of sialodacryo-adenitis [SDA] was histopathologically diagnosed at

12 months). At 18 months in rats, the incidence of cornea1 cloudiness in exposed male rats was similar to

that of control males. In females, the incidence of cornea1 cloudiness increased with dose: controls (2/20),

at 50 ppm (4/20), at 225 ppm (12/20), and at 1,000 ppm (12/20). No significant difference in ocular

lesions were observed in rats at 24 months. In mice, at 6 months, an acute, focal scleritis was observed in

3 of 10 males and 1 of 10 females in the 1,000 ppm group. This lesion was always associated with a

neutrophilic inflammatory infiltrate which was present at the corneoscleral junction. At 12, 18, and

24 months, there were no statistically significant ocular lesions observed in mice (CIIT 1981).

The highest NOAEL and all reliable LOAEL values for ocular effects in mice and rats are recorded in

Table 2-3.

No studies were located regarding the following effects in humans or animals after dermal exposure to

chloromethane.

2.2.3.3 Immunological and Lymphoreticular Effects

2.2.3.4 Neurological Effects

2.2.3.5 Reproductive Effects

2.2.3.6 Developmental Effects

2.2.3.7 Genotoxic Effects

Genotoxicity studies are discussed in Section 2.5


CHLOROMETHANE 90

2. HEALTH EFFECTS

2.2.3.8 Cancer

No studies were located regarding cancer in humans or animals after dermal exposure to chloromethane.

2 . 3 TOXICOKINETICS

Chloromethane is readily absorbed from the lungs and rapidly reaches equilibrium with levels in blood and

expired air approximately proportional to the exposure concentrations. At high concentrations, kinetic

processes like metabolism or excretion may become saturated, limiting the rate of uptake. Differences in

these processes may account for some of the observed differences in species uptake and distribution. It is

not known what levels, if any, of chloromethane or its metabolites cross the placenta or enter the milk.

There is also no information on differences between adults and children for the toxicokinetics of

chloromethane.

Animal studies demonstrate that chloromethane absorbed from the lungs is extensively distributed

throughout the body with relatively little variation in the pattern of distribution with respect to dose.

Chloromethane is metabolized by conjugation with glutathione to yield S-methylglutathione, S-methylcysteine, and other sulfur-containing compounds. These compounds are excreted in the urine or can be

further metabolized to methanethiol. Cytochrome P-450 dependent metabolism of methanethiol may yield

formaldehyde and formic acid, whose carbon atoms are then available to the one-carbon pool for

incorporation into macromolecules or for formation of CO2. Alternatively, formaldehyde may be directly

produced from chloromethane via a P-450 oxidative dechlorination.

The conjugation of chloromethane with glutathione is primarily enzyme catalyzed. In contrast to all other

animal species investigated (rats, mice, bovine, pigs, sheep, and rhesus monkeys), human erythrocytes

contain a glutathione transferase isoenzyme that catalyzes the conjugation of glutathione with

chloromethane. There are two distinct human subpopulations based on the amount or forms of this

transferase. They are, for practical purposes, known as fast metabolizers (i.e., lower body burdens and

higher excretion rates) and slow metabolizers (i.e., higher body burdens and lower excretion rates). These

two subpopulations are also called conjugators and nonconjugators. Determination of the relative

proportion of these subpopulations to the whole has just begun, but early results indicate considerable

variation among different ethnic groups. There is considerable interest in further evaluating the

relationship between endogenous levels of glutathione transferase and susceptibility of subpopulations to
CHLOROMETHANE 91

2. HEALTH EFFECTS

chloromethane-induced toxicity. There is no information available on differences in isoforms or levels of

glutathione transferase or P-450 in children (i.e., a different metabolic profile) that would result in a

significantly increased or decreased susceptibility to chloromethane toxicity compared to that observed in

adults. Research that addresses this issue is needed.

Little is known about the toxicokinetics of chloromethane from the oral or dermal routes of exposure.

2.3.1 Absorption

2.3.1.1 inhalation Exposure

Chloromethane is absorbed readily from the lungs of humans following inhalation exposure. Alveolar

breath levels of chloromethane reached equilibrium within 1 hour during a 3- or 3.5hour exposure of men

and women (Putz-Anderson et al. 1981a, 1981b). Mean f SD alveolar breath levels were 63±23.6 ppm in

24 men and women exposed to 200 ppm and 36±12 ppm in 8 men and women exposed to 100 ppm for

3 hours. Mean ± SD blood levels were 11.5±12.3 ppm for the 200 ppm exposed group and 7.7±6.3 ppm

for the 100 ppm exposed group. The results indicate that uptake was roughly proportional to exposure

concentration, but individual levels were quite variable. A high correlation between alveolar air and blood

levels (r=0.85, p<0.01) was found.

Blood and alveolar air levels of chloromethane also reached equilibrium during the first hour of exposure in

6 men exposed to 10 or 50 ppm for 6 hours (Nolan et al. 1985). The levels in blood and expired air were

proportional to the exposure concentrations. Based on elimination data, the subjects were divided into two

groups, fast and slow metabolizers. The difference between inspired and expired chloromethane

concentrations indicated that the fast metabolizers absorbed 3.7 μg/min/kg and the slow metabolizers

absorbed 1.4 μg/min/kg.

In experiments in rats, uptake of chloromethane reached equilibrium within 1 hour and was proportional or

nearly proportional to exposure concentrations of 50-1,000 ppm for 3-6 hours (Landry et al. 1983a,

1983b). Absorbed doses were calculated as 67 mg/kg for rats exposed to 1,000 ppm and 3.8 mg/kg for

rats exposed to 50 ppm (i.e., a ratio of 17.6 compared to a predicted ratio of 20 based on absorption being

directly proportional to exposure concentration). The rate of uptake was 0.167 mg/min/kg for 1,000 ppm

and 0.01 mg/min/kg for 50 ppm (ratio of 16.7). Where the uptake was not completely proportional to
CHLOROMETHANE 92

2. HEALTH EFFECTS

exposure, the difference in the ratio of absorbed doses from the predicted ratios may be due to a lower

respiratory minute volume in the rats exposed to 1,000 ppm or to different amounts remaining in the body

at the end of exposure and how much is metabolized. Blood chloromethane concentrations reached

equilibrium within 1 hour and were proportional to exposure concentration for dogs exposed to 50 or

1,000 ppm (Landry et al. 1983a) or 15,000 or 40,000 ppm (von Oettingen et al. 1949, 1950) for 6 hours.

At relatively low exposure concentrations, absorption of chloromethane from the lungs appears to be

proportional to exposure concentration in rats and humans, but at higher concentrations, kinetic processes

like metabolism or excretion may become saturated, limiting the rate of uptake. In dogs, however, it

appears that absorption is proportional to exposure concentration through a wide range of exposure levels.

2.3.1.2 Oral Exposure

No studies were located regarding absorption in humans or animals after oral exposure to chloromethane.

2.3.1.3 Dermal Exposure

No studies were located regarding absorption in humans or animals after dermal exposure to

chloromethane.

2.3.2 Distribution

2.3.2.1 Inhalation Exposure

No studies were located regarding distribution in humans after inhalation exposure to chloromethane.

After absorption of chloromethane, distribution of chloromethane and/or its metabolites is extensive in

animals. Total uptake of radioactivity (as μmol 14C-chloromethane equivalents/g wet weight) in whole

tissue homogenates following exposure of rats to 500 ppm for 6 hours was 1.21 for lung, 4.13 for liver,

3.43 for kidney, 2.29 for testes, 0.71 for muscle, 0.57 for brain, and 2.42 for intestine (Kornbrust et al.

1982). Little difference in the pattern of distribution was found at an exposure concentration of 1,500 ppm

as compared with 500 ppm. Upon acid precipitation of protein, 80% of the radioactivity present In liver
CHLOROMETHANE 93

2. HEALTH EFFECTS

and testes was found in the acid soluble (unbound) fraction. The remainder was found to have been

metabolically incorporated into lipid, ribonucleic acid (RNA), DNA, and protein, rather than bound to the

macromolecules as a result of direct alkylation. Tissue levels of chloromethane (in mg%) in dogs exposed

to chloromethane for 6 hours were 4.5 in liver, 4.1 in heart, and 3.7 in brain at 15,000 ppm and 9.3 in liver,

8.1 in heart, and 9.9 in brain at 40,000 ppm (von Oettingen et al. 1949, 1950).

2.3.2.2 Oral Exposure

No studies were located regarding distribution in humans or animals after oral exposure to chloromethane.

2.3.2.3 Dermal Exposure

No studies were located regarding distribution in humans or animals after dermal exposure to

chloromethane.

2.3.3 Metabolism

Information regarding metabolism of chloromethane in humans is limited. In a group of 6 workers exposed

to TWA 8-hour workroom concentrations of 30-90 ppm, the urinary excretion of S-methylcysteine showed

wide variations, with little correlation to exposure levels (van Doorn et al. 1980). S-methylcysteine is

formed from conjugation of chloromethane with glutathione (Kornbrust and Bus 1983). In four of the

workers, all values were higher than in controls, and appeared to build up during the course of the week.

Two of the workers had only minor amounts of S-methylcysteine in the urine, but these workers

experienced the highest exposure concentrations. There are two distinct subpopulations of individuals: fast

metabolizers with lower body burdens and higher excretion, and slow metabolizers with higher body

burdens and lower excretion (van Doorn et al. 1980). The difference may be due to a deficiency of the

enzyme glutathione-S-transferase that catalyzes the conjugation of chloromethane with glutathione. Other

possible reasons for the differences in chloromethane elimination among subjects include differences in

tissue glutathione levels and differences in biliary excretion and fecal elimination of thiolated conjugates.

As a working hypothesis, however, the two distinct subpopulations are referred to as fast and slow

eliminators. Two distinct subpopulations were also found based on venous blood and expired

concentrations of chloromethane in volunteers (Nolan et al. 1985). The urinary excretion of S-methylcysteine

in the volunteers exposed to chloromethane was variable, and was not significantly different in pre-
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and postexposure levels. No change was detected in the S-methylcysteine concentration or in the total

sulfhydryl concentration in the urine of 4 workers before and after a 7-hour shift in a styrene production

plant by DeKok and Antheunius (1981) who concluded that S-methylcysteine is not a human metabolite of

chloromethane. It is possible, however, that the workers examined by DeKok and Antheunius (1981) were

slow eliminators.

Peter et al. (1989a, 1989b) assayed erythrocyte cytoplasm of humans with chloromethane and monitored

the decline of chloromethane and the production of S-methylglutathione. About 60% of the human blood

samples showed a significant metabolic elimination of the substance (conjugators), whereas 40% did not

(nonconjugators). The results suggested that a minor form of human erythrocyte glutathione S-transferase

is responsible for the unique metabolism of methyl chloride in human erythrocytes. Hallier et al. (1990)

demonstrated that other monohalogenated methanes (methyl iodide and methyl bromide) could undergo

enzymatic conjugation with glutathione, but that in contrast to chloromethane, methyl iodide and methyl

bromide also showed significant non-enzymatic conjugation with glutathione.

Warholm et al. (1994) studied the polymorphic distribution of the erythrocyte glutathione transferases in a

Swedish population and found three distinct sub-groups:11.1% lacked activity, 46.2% had intermediate

activity, and 42.8% had high activity. The authors calculated two allelic frequencies, one for a functional

allele with a gene frequency of 0.659 and one for a defect allele with a frequency of 0.341. This two allele

hypothesis is compatible with the observed distribution of the three phenotypes. A follow-up study on

genotype indicated that approximately 10% of the Swedish population lacked the glutathione transferase

isoenzyme (Warholm et al. 1995). This 10% number is considerably smaller than a previously proposed

proportion of nonconjugators of 30-40% reported for a German population (Peter et al. 1989a). A

different study by Kempkes et al. (1996) found a frequency of 15% for nonconjugators in a German cohort

of 40 people. Whether this lack of activity poses an increased risk of developing disease such as cancer is

not known. Warholm et al. (1995) suggest that additional ethnic groups be evaluated for percentage of

non-conjugators.

The metabolism of chloromethane has been studied in rats, mice, and dogs in vivo after inhalation exposure

and in vitro. Based on these studies, the metabolic pathway shown in Figure 2-3 was proposed (Kornbrust

and Bus 1983). According to the proposed pathways, chloromethane metabolism involves conjugation with

glutathione to yield S-methylglutathione, S-methylcysteine, and other sulfur-containing compounds (Dodd

et al. 1982; Kornbrust and Bus 1984; Landry et al. 1983a, 1983b; Redford-Ellis and Gowenlock 1971a,

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1971b). These compounds can be excreted in the urine (Landry et al. 1983a), or S-methylglutathione may

be further metabolized to methanethiol. Cytochrome P-450 dependent metabolism of methanethiol may

yield formaldehyde and formic acid, whose carbon atoms are then available to the one-carbon pool for

incorporation into macromolecules or for formation of CO2 (Heck et al. 1982; Jager et al. 1988; Kornbrust

and Bus 1983; Kornbrust et al. 1982). Formaldehyde may also be a direct product of chloromethane via

oxidative dechlorination. Production of methanethiol and formaldehyde, and lipid peroxidation due to

glutathione depletion have been suggested as possible mechanisms for the toxicity of chloromethane, but

the precise mechanisms are not known (Kornbrust and Bus 1983, 1984; Jager et al. 1988). Dekant et al.

(1995) demonstrated oxidation of chloromethane to formaldehyde by cytochrome P-450 (2El) in male

mouse kidney microsomes, and that the amount of formaldehyde formed was dependent upon the hormonal

status of the animal. Female mouse kidney microsomes produced considerably less formaldehyde than

male kidney microsomes. Liver microsomal activity from both sexes was 2-fold higher than in kidney

microsomes from the male. In contrast, rat kidney microsomes did not catalyze formaldehyde formation

from chloromethane.

Peter et al. (1989a) assayed erythrocyte cytoplasm of a variety of test animals with chloromethane and

monitored the decline of chloromethane and the production of S-methylglutathione. Rats, mice, bovine,

pigs, sheep, and rhesus monkeys showed no conversion of chloromethane in erythrocyte cytoplasm.

2.3.4 Elimination and Excretion

2.3.4.1 Inhalation Exposure

Very little unchanged chloromethane is excreted in the urine. In volunteers exposed to chloromethane,

Stewart et al. (1980) found no chloromethane in the urine, and urinary excretion was <0.01 %/min in

another study (Morgan et al. 1970). The excretion patterns of chloromethane following prolonged

exposure will differ from those observed in these experiments, which followed single breath exposure;

therefore, these data are not useful for monitoring occupational exposure. Volunteers exposed to 10 or

50 ppm eliminated chloromethane from blood and the expired air in a biphasic manner when exposure

ceased (Nolan et al. 1985). Based upon data presented in the report, the half-life for the β-phase was

estimated at 50-90 minutes, with differences possibly due to different metabolic rates. These results

suggest that chloromethane is unlikely to accumulate in tissues during repeated intermittent exposures.
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In rats exposed to chloromethane for 6 hours and dogs exposed for 3 hours at concentrations of 50 or

1,000 ppm, blood levels rose rapidly and reached equilibrium proportionate or nearly proportionate to

exposure levels (Landry et al. 1983a). Blood concentrations declined rapidly in a biphasic,

nonconcentration-dependent manner when exposure was stopped. The disappearance from blood was

consistent with a linear 2-compartment open model. Half-lives for the a-phase were 4 minutes in rats, and

8 minutes ‘in dogs; half-lives for the β-phase were 15 minutes in rats and 40 minutes in dogs. The

disappearance of chloromethane from blood probably represents metabolism rather than excretion of parent

compound. As discussed above in Section 2.3.3 on metabolism, chloromethane is conjugated with

glutathione and cysteine, leading to urinary excretion of sulfur-containing compounds. Further metabolism

of the cysteine conjugate by one-carbon metabolic pathways leads to incorporation of the carbon atom into

macromolecules, and the production of carbon dioxide.

2.3.4.2 Oral Exposure

No studies were located regarding excretion in humans or animals following oral exposure to chloromethane.

2.3.4.3 Dermal Exposure

No studies were located regarding excretion in humans or animals following dermal exposure to

chloromethane.

2.3.5 Physiologically Based Pharmacokinetic (PBPK)/Pharmacodynamic (PD) Models

Physiologically based pharmacokinetic (PBPK) models use mathematical descriptions of the uptake and

disposition of chemical substances to quantitatively describe the relationships among critical biological

processes (Krishnan et al. 1994). PBPK models are also called biologically based tissue dosimetry models.

PBPK models are increasingly used in risk assessments, primarily to predict the concentration of

potentially toxic moieties of a chemical that will be delivered to any given target tissue following various

combinations of route, dose level, and test species (Clewell and Andersen 1985). Physiologically based

pharmacodynamic (PBPD) models use mathematical descriptions of the dose-response function to

quantitatively describe the relationship between target tissue dose and toxic end points.
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PBPK/PD models refine our understanding of complex quantitative dose behaviors by helping to delineate

and characterize the relationships between: (1) the external/exposure concentration and target tissue dose of

the toxic moiety, and (2) the target tissue dose and observed responses (Andersen and Krishnan 1994;

Andersen et al. 1987). These models are biologically and mechanistically based and can be used to

extrapolate the pharmacokinetic behavior of chemical substances from high to low dose, from route to

route, between species, and between subpopulations within a species. The biological basis of PBPK

models results in more meaningful extrapolations than those generated with the more conventional use of

uncertainty factors.

The PBPK model for a chemical substance is developed in four interconnected steps: (1) model

representation, (2) model parametrization, (3) model simulation, and (4) model validation (Krishnan and

Andersen 1994). In the early 1990s validated PBPK models were developed for a number of

toxicologically important chemical substances, both volatile and nonvolatile (Krishnan and Andersen 1994;

Leung 1993). PBPK models for a particular substance require estimates of the chemical substancespecific

physicochemical parameters, and species-specific physiological and biological parameters. The

numerical estimates of these model parameters are incorporated within a set of differential and algebraic

equations that describe the pharmacokinetic processes. Solving these differential and algebraic equations

provides the predictions of tissue dose. Computers then provide process simulations based on these

solutions.

The structure and mathematical expressions used in PBPK models significantly simplify the true

complexities of biological systems. If the uptake and disposition of the chemical substance(s) is adequately

described, however, this simplification is desirable because data are often unavailable for many biological

processes. A simplified scheme reduces the magnitude of cumulative uncertainty. The adequacy of the

model is, therefore, of great importance, and model validation is essential to the use of PBPK models in risk

assessment.

PBPK models improve the pharmacokinetic extrapolations used in risk assessments that identify the

maximal (i.e., the safe) levels for human exposure to chemical substances (Andersen and Krishnan 1994).

PBPK models provide a scientifically-sound means to predict the target tissue dose of chemicals in humans

who are exposed to environmental levels (for example, levels that might occur at hazardous waste sites)

based on the results of studies where doses were higher or were administered in different species.

Figure 2-4 shows a conceptualized representation of a PBPK model.

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If PBPK models for chloromethane exist, the overall results and individual models are discussed in this

section in terms of their use in risk assessment, tissue dosimetry, and dose, route, and species

extrapolations.

No PBPK models for adults, children, or test animal models were located for chloromethane.

2.4 MECHANISMS OF ACTION

2.4.1 Pharmacokinetic Mechanisms

As presented in Section 2.3.3, metabolism of chloromethane involves conjugation with glutathione to yield

S-methylglutathione, S-methylcysteine, and other sulfur-containing compounds (Dodd et al. 1982;

Kornbrust and Bus 1984; Landry et al. 1983a, 1983b; Redford-Ellis and Gowenlock 1971a, 1971b).

These compounds can be excreted in the urine (Landry et al. 1983a), and S-methylglutathione may be

further metabolized to methanethiol. Cytochrome P-450 dependent metabolism of methanethiol may yield

formaldehyde and formic acid whose carbon atoms can then enter the one-carbon pool for incorporation

into macromolecules or formation of CO2 (Heck et al. 1982; Jager et al. 1988; Kornbrust and Bus 1983).

Guengerich and Shimada (1991) suggest that the human cytochrome P-450 enzyme 2El is a major catalyst

in the oxidation of chloromethane. Formaldehyde may also be a direct product of chloromethane via

oxidative dechlorination. Methanethiol and formaldehyde, and lipid peroxidation due to glutathione

depletion have been suggested as the toxic intermediates and mechanism responsible for the toxicity of

chloromethane (Dekant et al. 1995; Jager et al. 1988; Kornbrust and Bus 1983, 1984; Ristau et al. 1989,

1990). There is no information available on differences in isoforms or levels of glutathione transferase or

P-450 in children that would result in significantly different metabolic rates (i.e., increased or decreased

susceptibility to chloromethane toxicity) than those observed in adults.

2.4.2 Mechanisms of Toxicity

Hepatic effects: While the exact mechanism for the hepatotoxic effects of chloromethane is unclear,

chloromethane can elicit lipid peroxidation as a secondary consequence of glutathione depletion (Kornbrust

and Bus 1984). Comparison of lipid peroxidation in the S-9 fraction from mouse and rat livers revealed

much greater lipid peroxidation in mouse liver than in rat liver. Further evidence that the mechanism of
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hepatotoxicity may involve lipid peroxidation comes from the finding that mice exposed to 2,500 ppm

chloromethane expired ethane to an extent comparable to that produced by 2 mL/kg carbon tetrachloride,

and developed moderate to severe hepatocellular hydropic degeneration.

Dodd et al. (1982) examined the effects of an inhalation exposure to chloromethane on tissue nonprotein

sulfhydryl (NPSH) content in male Fischer 344 rats. NPSH content of liver, kidney, and lung were

decreased in a chloromethane concentration-related manner. Pretreatment with Aroclor 1254 (an inducer of

microsomal enzymes) did not alter the decreases in tissue NPSH seen after exposure to chloromethane

alone. Pretreatment with SKF-525A (an inhibitor of microsomal enzymes) may have interfered with the

ability of chloromethane to decrease NPSH in some tissues. Treatment with chloromethane significantly

increased the activity of glutathione-S-alkyltransferase, and pretreatment with Aroclor 1254 did not alter

the increase. The toxicological significance of this effect is not clear. These results support the hypothesis

that chloromethane reacts enzymatically with glutathione (GSH), which is the most abundant NPSH, and

the hypothesis that the reaction is not dependent upon the formation of a reactive intermediate by

microsomal enzymes. Possible mechanisms for the toxicity of chloromethane related to glutathione

depletion include: enhancement of the toxicity of chemicals that are detoxified via conjugation with GSH;

prevention of GSH from acting as a cellular reducing agent, thereby interfering with a variety of

physiological functions; or an increase in chloromethane-glutathione conjugates that are then further

metabolized to putative toxic metabolite (e.g., formaldehyde or methanethiol).

Neurological effects: Chellman et al. (1986b) investigated the role of glutathione in the mediation of

chloromethane-induced toxicity in the brain of male B6C3F1 mice. Mice exposed to 1,500 ppm

chloromethane for 6 hours/day, 5 days/week for 2 weeks, developed multiple degenerative, necrotic foci in

the internal granule cell layer of the cerebellum; in some areas the foci involved the whole thickness of the

granular cell layer. Cerebellar degeneration consisted of granule cells with pyknotic nuclei and clear,

swollen perikarya. Tremors, ataxia, and forelimb/hindlimb paralysis were seen in chloromethane-induced

lethality and were associated with chloromethane-induced cerebellar damage. Cerebellar damage was not

observed in chloromethane-exposed mice pretreated with BSO, a glutathione depleter. The authors

concluded that the depletion of GSH protected mice from cerebellar damage due to exposure to

chloromethane. The mechanism may involve conjugation of chloromethane with glutathione in the liver,

followed by biliary excretion and enterohepatic circulation of the glutathione conjugate or possibly a

cysteine conjugate and further metabolism by kidney and/or gut flora beta-lyase to methanethiol.
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Methanethiol produces similar central nervous system symptoms (tremors, convulsion, coma) as seen in

animals or humans acutely intoxicated with chloromethane (Chellman et al. 1986b).

In the metabolic scheme proposed by Kornbrust and Bus (1983), chloromethane reacts with glutathione to

form S-methylglutathione. Subsequent metabolism of S-methylglutathione produces methanethiol as an

intermediate. Jiang et al. (1985) discuss the possibility of a relationship between degenerative effects in the

kidney and granular layer lesions in the brain, which were also observed in mice. Granular cell necrosis is

often seen in people who die of renal insufficiency (i.e., not due to chloromethane exposure). In the Jiang et

al. (1985) mouse study, however, the severity of the brain and kidney lesions were unrelated, and the

authors conclude that the brain lesions were probably not a direct consequence of the chloromethaneinduced

kidney lesions.

Reproductive effects: Studies on the mechanism of chloromethane-induced testicular effects suggest that

preimplantation loss is due to chloromethane cytotoxicity to the sperm in the testes at the time of exposure

rather than genotoxic effects on the sperm (Chellman et al. 1986a, 1986c, 1987; Working and Bus 1986;

Working and Chellman 1989; Working et al. 1985a, 1985b). Working et al. (1985a) previously had

. provided results indicating that chloromethane-induced postimplantation loss results from an inflammatory

response in the epididymis that indirectly produces genetic damage to the sperm rather than from a direct

genotoxic effect of chloromethane. Inhibition of the chloromethane-induced epididymal inflammatory

response with anti-inflammatory agent BW755C (Chellman et al. 1986c) was subsequently shown to

reduce the amount of postimplantation loss (Chellman et al. 1986c).

Genotoxicitv: Chloromethane exposure consistently produced dominant lethal mutations in the sperm of

rats, as measured by postimplantation loss in females mated to exposed males (Chellman et al. 1986c;

Rushbrook 1984; Working et al. 1985a). Because of the known transit times for sperm in the epididymis

and the resulting observed times of the postimplantation losses, Working et al. (1985a) observed that the

timing of the genetic damage to the sperm coincided with their location in the chloromethane induced

inflammation of the epididymis. Since concurrent exposure of male rats to chloromethane and BW755C, an

anti-inflammatory agent, greatly reduced the amount of postimplantation loss, the dominant lethal

mutations probably resulted secondary to the epididymal inflammatory response (Chellman et al. 1986c;

Working and Chellman 1989). The activation of phagocytic cells during the inflammatory process may

result in the production of potentially genotoxic chemical species including the superoxide anion radical,
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hydrogen peroxide, and lipid peroxide decomposition products (Fridovich 1978; Goldstein et al. 1979,

1981; Working et al. 1985a).

Renal tumors: Some proposed mechanisms for the carcinogenic effect (renal tumors) detected in male mice

include glutathione depletion in the target tissue, increased lipid peroxidation, and formation of

formaldehyde-induced DNA lesions (Bolt and Ganswendt 1993). Chloromethane can be metabolized to

formaldehyde (Kornbrust and Bus 1982). Exposure to 1,000 ppm chloromethane depletes glutathione in

the kidney to ≈5% of the pre-exposure levels (Bolt et al. 1986; Hallier et al. 1990), effectively removing the

cofactor for the glutathione-dependent primary metabolic pathway for chloromethane. The alternate

oxidative pathway leads directly to the formation of formaldehyde via cytochrome P-450. Jager et al.

(1988) have shown that the formation of formaldehyde (via P-450 activity) was 10 times higher in male

mouse liver than in male kidney. Male mouse liver also produced formaldehyde at about two times the

amount of female liver, and male kidney about 50% more than female kidney. This led to the hypothesis

that male mice tumors resulted from increased production of formaldehyde and increased numbers of

formaldehyde-induced DNA lesions. Glutathione depletion also removes the cofactor for formaldehyde

dehydrogenase (FDH), the enzyme that inactivates formaldehyde. Jager et al. (1988), however, did not

observe increased formaldehyde levels in mouse liver or kidney after a single, 8-hour exposure to

1,000 ppm chloromethane, or an increase in DNA protein cross links (DPC), a typical formaldehydeinduced

lesion, after exposure to 1,000 ppm for 6 hours per day for 4 days. Ristau et al. (1989), however,

did observe an increase in DPC in the renal tissue of male but not female mice. In a follow-up study,

Ristau et al. (1990) showed a rapid removal of DPC whereas single strand breaks appeared to accumulate.

Both types of lesions were ascribed to the action of formaldehyde. Ristau et al. (1989) assayed for DPC

immediately after a single 8-hour exposure, whereas Jager et al. (1988) dosed over a 4-day period. Delays

from exposure to assay that allow rapid repair of formaldehyde-induced DPCs could possibly explain why

Jager et al. (1988) did not observe an increase. Both the DPCs and the incomplete and delayed repair of

chloromethane-induced DNA lesions may contribute to the formation of renal tumors. Morgan et al.

(1982) also noted a proliferative response in male and female mouse proximal tubules following exposure

to 1,000 ppm of chloromethane. This proliferative response could also contribute to the tumorigenicity of

chloromethane in the males.
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2.4.3 Animal-to-Human Extrapolations

Acute and chronic inhalation studies indicate that mice are more sensitive than rats to the lethal effects of

chloromethane (Chellman et al. 1986a, 1986b; CIIT 1981). The greater susceptibility of mice may be due

to different metabolic rates involving glutathione or different oxidative rates for the production of

formaldehyde. Chloromethane conjugates with glutathione to much greater extent in mouse liver, kidney,

and brain compared with rats (Kornbrust and Bus 1984). Pretreatment of mice with buthionine-S,Rsulfoxime (BSO), a glutathione depleter, protected mice from the chloromethane-induced lethal effects

(Chellman et al. 1986b). Thus, the reaction of chloromethane with glutathione to produce S-methylglutathione

appears to be a toxifying rather than a detoxifying reaction (Chellman et al. 1986b).

Alternatively, chloromethane can elicit lipid peroxidation as a consequence of depletion of glutathione

(Kornbrust and Bus 1984).

In humans, S-methylcysteine appears as a metabolite of chloromethane (see Section 2.3.3), so conjugation

with glutathione probably also occurs in humans.

Different P-450 activities between species, sexes, and tissues within the body (i.e., liver versus kidney)

affect the dehalogenation of chloromethane to formaldehyde, and can thus influence the level of

formaldehyde-induced DNA or tissue damage (Dekant et al. 1995; Jager et al. 1988; Ristau et al. 1989,

1990).

2.5 RELEVANCE TO PUBLIC HEALTH

Overview.

Information regarding health effects of chloromethane in humans and animals is available primarily for the

inhalation route of exposure. Oral and dermal routes of exposure are of concern because chloromethane is

ubiquitous in the environment. Because it is highly volatile, however, chloromethane rapidly moves from

water or soil to the air (see Chapter 5). Issues relevant to children are explicitly discussed in Sections 2.6,

Children’s Susceptibility, and 5.6, Exposures of Children.

The central nervous system is the major target of chloromethane toxicity in both humans and animals, as

demonstrated by such signs and symptoms as dizziness, staggering, blurred vision, ataxia, muscle
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incoordination, convulsions, and coma after acute exposure to high levels. High acute exposures can also

result in death of humans and animals. The liver and kidney are also target organs for chloromethane

toxicity in humans and animals from acute or longer-term exposure. Toxic manifestations seen in humans,

but generally not in animals, include cardiovascular and gastrointestinal effects. These may be secondary to

the neurotoxicity. Effects that have been observed in animals, but not reported in humans, include

epididymal occlusion, testicular atrophy, infertility, sterility in males, carcinogenicity (e.g., kidney tumors in

male mice), and possibly developmental effects (e.g., heart defects) in mice.

Species differences in susceptibility to chloromethane toxicity have been observed. Different P-450

activities between species, sexes, and tissues within the body affect the dehalogenation of chloromethane to

formaldehyde, and can thus influence the level of formaldehyde-induced DNA or tissue damage. Rates of

conjugation with glutathione differ and lead to differing levels of toxic metabolites. In animal studies, mice

have been shown to be more sensitive than rats to the lethal effects of chloromethane, probably due to the

higher rate of formation of the toxic metabolite, S-methylglutathione. S-methylcysteine appears as a

metabolite of chloromethane in humans, so conjugation with glutathione probably also occurs in humans.

There is no information available on differences in isoforms or levels of glutathione transferase or P-450 in

children that would result in significantly different metabolic rates (i.e., increased or decreased susceptibility

to chloromethane toxicity) than those observed in adults.

Minimal Risk Levels for Chloromethane.

Inhalation MRLs.

• An MRL of 0.5 ppm has been derived for acute-duration inhalation exposure (14 days or less) to

chloromethane.

An acute MRL of 0.5 ppm was derived from a NOAEL of 50 ppm for no effect on motor coordination or

damage to the cerebellar granule cells in a study by Landry et al. (1985). This study evaluated the

neurologic effects of continuous versus intermittent chloromethane exposure in female C57BL/6 mice. The

results support a good dose-response effect for cerebellar damage and motor incoordination. The NOAEL

of 50 ppm was converted to a human equivalent dose by multiplying with the ratio of the blood:gas (air)

partition coefficient for the mouse to the human value. The default value of 1.0 was used because the
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coefficients are not known (see formula 4-48a, EPA 1994b). The resulting NOAEL[HEC] of 50 ppm was then

divided by an uncertainty factor of 100 (10 for interspecies variability and 10 for human variability). The

obtained MRL value is 0.5 ppm (see Appendix A).

Neurological effects have been described in numerous case reports of humans exposed to chloromethane

vapors as a result of industrial leaks and leaks from defective home refrigerators (Baird 1954;

Gudmundsson 1977; Hansen et al. 1953; Hartman et al. 1955; Jones 1942; Kegel et al. 1929; MacDonald

1964; McNally 1946; Raalte and van Velzen 1945; Rafnsson and Gudmundsson 1997; Spevak et al. 1976;

Wood 1951). Depending on the extent of exposure and the availability of medical treatment, the signs and

symptoms can range from staggering and blurred vision to coma, convulsions, and death. In some cases,

mild to permanent neurological and/or psychiatric deficits have been reported 13 years after an acute high

level exposure (Gudmundsson 1977).

Severe neurological signs (ataxia, tremors, limb paralysis, incoordination, convulsions) have also been

observed in rats, mice, rabbits, guinea pigs, dogs, cats, and monkeys exposed acutely by inhalation to high

concentrations of chloromethane (Burek et al. 1981; Chellman et al. 1986a, 1986b; Landry et al. 1985;

McKenna et al. 1981a; Morgan et al. 1982; Smith and von Oettingen 1947b). Cerebellar lesions have been

observed microscopically in guinea pigs and rats (Kolkmann and Volk 1975; Morgan et al. 1982). Mice are

more susceptible than rats (CIIT 1981; Morgan et al. 1982), and more sensitive to neurological effects after

continuous exposure to low concentrations than after intermittent exposure to higher concentrations of

chloromethane (Landry et al. 1985). The greater sensitivity of mice to continuous exposure makes the

mouse a good model for the neurotoxicological effects seen in humans.

• An MRL of 0.2 ppm has been derived for intermediate-duration inhalation exposure (15 to

364 days) to chloromethane.

An intermediate MRL of 0.2 ppm was derived from a LOAEL of 51 ppm for significantly increased serum

alanine amino transferase levels (indicative of hepatotoxicity) in male mice at the 6 month time point in a

2-year study (377 I.U./L ± 124 versus 170 ±49 in controls). This LOAEL is a minimal LOAEL because no

histopathological lesions were observed in the low- or mid-dose levels, but were observed at the high dose

level. The objective of the study was to evaluate the toxicologic and oncogenic effects of inhaled

chloromethane in male and female Fischer 344 rats and B6C3F1 mice. The dose-response effect for liver

toxicity was observed in male mice. Females also had increased ALT, but the increase was not associated
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with treatment-related histopathological changes in the liver. Liver necrosis and other pathological changes

in the liver of high dose male mice was also observed at 12, 18, and 24 months. No further adjustments in

the LOAEL were made for a continuous exposure, and the comparable LOAEL[ADJ] of 51 ppm was then

converted to a human equivalent dose by multiplying with the ratio of the blood:gas (air) partition coefficient

for the mouse to the human value. The default value of 1.0 was used because the coefficients are not known

(see formula 4-48a, EPA 1994b). The resulting LOAEL[HEC] of 51 ppm was then divided by an uncertainty

factor of 300 (3 for the use of a minimal LOAEL, 10 for interspecies variability, and 10 for human

variability) and rounded to one significant figure. The obtained MRL value is 0.2 ppm (see Appendix A).

Case reports of humans exposed to chloromethane vapors have described clinical jaundice and cirrhosis of

the liver (Kegel et al. 1929; Ma&e 1961; Weinstein 1937; Wood 1951), but exposure concentrations were

not known.

Hepatic effects have been observed in animals exposed by inhalation to chloromethane at concentrations

> 1,000 ppm in acute, intermediate, and chronic duration experiments (Burek et al. 1981; Chellman et al.

1986a; CIIT 1981; Landry et al. 1985; Mitchell et al. 1979; Morgan et al. 1982). Milder liver effects

occurred in mice exposed acutely to an intermittent but relatively high concentration than to a low but

continuous concentration (Landry et al. 1985). The greater susceptibility to continuous exposure may result

from relatively greater metabolism to a toxic intermediate or from diurnal susceptibility. Hepatic effects

were more severe in mice (necrosis and degeneration) than in rats (cloudy swelling, fatty infiltration,

increased ALT and AST with no necrosis). Furthermore, no hepatic lesions were observed in rats over the

course of 2 years of inhalation exposure to 1,000 ppm, while mice similarly exposed had necrotic lesions

after 6 months (CIIT 1981). The greater susceptibility of mice to the hepatotoxic effects of chloromethane

may be related to the greater ability of chloromethane to conjugate with hepatic glutathione in mice than in

rats (Dodd et al. 1982; Kornbrust and Bus 1984). The reaction of chloromethane with glutathione appears

to be toxifying rather than detoxifying (Chellman et al. 1986b). While the exact mechanism for the

hepatotoxic effects of chloromethane is unclear, chloromethane can elicit lipid peroxidation as a secondary

consequence of depletion of glutathione (Kombrust and Bus 1984). Comparison of lipid peroxidation in the

S-9 fraction from mouse and rat livers revealed much greater lipid peroxidation in mouse liver than in rat

liver. The finding that mice exposed to 2,500 ppm chloromethane expired ethane to an extent comparable to

that produced by 2 mL/kg carbon tetrachloride, and developed moderate to severe hepatocellular hydropic

degeneration provide further evidence that the mechanism of hepatotoxicity may involve lipid peroxidation.
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• An MRL of 0.05 ppm has been derived for chronic-duration inhalation exposure (365 days or

more) to chloromethane.

A chronic MRL of 0.05 ppm was derived from a LOAEL of 51 ppm for axonal swelling and degeneration .

of axons of the spinal cord in mice after 18 months of exposure (CIIT 1981). This two year study evaluated

the toxicologic and oncogenic effects of inhaled chloromethane in male and female Fischer 344 rats and

B6C3F1 mice. There was a consistent dose-response for neurological effects in male and female mice. At

the high dose, there was a mild reduction in the number of neurons in the granular cell layer of the

cerebellum with decreased width of the granular cell layer. In the high, mid, and low dose groups, axonal

swelling and degeneration of minimal severity was observed in the spinal nerves and the cauda equina

associated with the lumbar spinal cord. The LOAEL was converted to a human equivalent dose by

multiplying the LOAEL with the ratio of the blood:gas (air) partition coefficient for the mouse to the human

value. The default value of 1.0 was used because the coefficients are not known (see formula 4-48a, EPA

1994b). The resulting LOAEL[HEC] of 5.1 ppm was then divided by an uncertainty factor of 1,000 (10 for

the use of a LOAEL, 10 for interspecies variability, and 10 for human variability) and rounded to one

significant figure. The obtained MRL value is 0.05 ppm (see Appendix A).

As with support for the acute MRL, neurological effects have been described in numerous case reports of

humans exposed to chloromethane vapors (Baird 1954; Gudmundsson 1977; Hansen et al. 1953; Hartman

et al. 1955; Jones 1942; Kegel et al. 1929; MacDonald 1964; McNally 1946; Raalte and van Velzen 1945;

Rafnsson and Gudmundsson 1997; Spevak et al. 1976; Wood 1951). Signs and symptoms can range from

staggering and blurred vision to coma, convulsions, and death. Severe neurological signs (ataxia, tremors,

limb paralysis, incoordination, convulsions) have also been observed in rats, mice, rabbits, guinea pigs,

dogs, cats, and monkeys exposed acutely by inhalation to high concentrations of chloromethane (Burek et al.

1981; Chellman et al. 1986a, 1986b; Landry et al. 1985; McKenna et al. 1981a; Morgan et al. 1982; Smith

and von Oettingen 1947b). Cerebellar lesions have been observed microscopically in guinea pigs and rats

(Kolkmann and Volk 1975; Morgan et al. 1982).

Oral MRLs.

No acute, intermediate, or chronic-duration oral MRLs were derived for chloromethane because of lack of

appropriate data on effects of oral exposure to chloromethane.
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Death. Case reports of humans who have died from exposure to chloromethane involved the inhalation of

fumes that leaked from home refrigerators or industrial cooling and refrigeration systems (Baird 19.54;

Borovska et al. 1976; Gudmundsson 1977; Kegel et al. 1929; McNally 1946; Thordarson et al. 1965).

Exposure concentrations were probably very high, perhaps >30,000 ppm, because the leaks occurred in

rooms with little or no ventilation. Exposure to high concentrations, even as high as 600,000 ppm, result in

neurological effects (Jones 1942), but need not result in death if exposure is discontinued and/or medical

attention is received in time. Since the use of chloromethane as a refrigerant in refrigeration devices has

declined, exposure from leaks is of less concern than in the past, although some old refrigerators containing

chloromethane are probably still in use. Concentrations of chloromethane in the environment, even at

hazardous waste sites, are not likely to be high enough to cause death.

Acute inhalation lethality data in animals indicate that high intermittent concentrations can be tolerated

better than lower continuous concentrations (Burek et al. 1981; Jiang et al. 1985; Landry et al. 1985;

Morgan et al. 1982). This phenomenon may be related to the conversion of chloromethane to a toxic

metabolite or to diurnal susceptibility (Landry et al. 1985). Acute and chronic inhalation studies also

indicated that mice are more sensitive than rats to the lethal effects of chloromethane (Chellman et al. 1986a,

1986b; CIIT 1981). The greater susceptibility of mice may be due to differences in the ability of

chloromethane to react with glutathione in the two species. Chloromethane is conjugated with glutathione in

liver, kidney, and brain to a much greater extent in mice than in rats (Kornbrust and Bus 1984).

Pretreatment of mice with buthionine-S,R-sulfoximine (BSO), which depletes glutathione, thereby

preventing its reaction with chloromethane, protected mice from the lethal effects of chloromethane

(Chellman et al. 1986b). Thus, the reaction of chloromethane with glutathione to produce S-methylglutathione appears to be a toxifying rather than a detoxication mechanism (Chellman et al. 1986b). While

the exact mechanism for the lethal effects of chloromethane is unclear, subsequent metabolism of S-methylglutathione may result in the formation of methanethiol and formaldehyde (Kornbrust and Bus 1983), which

have been postulated to be toxic intermediates (Chellman et al. 1986b; Kornbrust and Bus 1982).

Alternatively, chloromethane can elicit lipid peroxidation as a consequence of depletion of glutathione

(Kombrust and Bus 1984). Conjugation of chloromethane with glutathione probably occurs in humans

because S-methylcysteine appears to be a human metabolite (see Section 2.3.3). No information was

located regarding the extent to which chloromethane reacts with glutathione in humans or the ability of

chloromethane to elicit lipid peroxidation in humans. The clinical signs and histopathological lesions noted

with death in humans are similar to those in animals, suggesting a commonality of mechanism, but it is

difficult to determine which animal species best serves as a model for extrapolating results in humans.
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Systemic Effects.

Respiratory Effects. Case reports generally have not described respiratory effects in humans exposed to

chloromethane.

In dogs acutely exposed to lethal concentrations there was a marked reduced in respiration prior to death,

but this effect was probably secondary to central nervous system depression (von Oettingen et al. 1949,

1950). Pulmonary congestion prior to death was a common finding among a variety of species (rats, mice,

guinea pigs, rabbits, dogs, cats, and monkeys), but the study limitations precluded the determination of a

good dose-response relationship (Dunn and Smith 1947; Smith and von Oettingen 1947a). More recent

studies failed to find exposure-related histopathological lesions in the lungs of dogs and cats exposed acutely

to 500 ppm chloromethane (McKenna et al. 198 la), rats exposed acutely to 2,000 ppm (Burek et al. 198 l),

male dogs exposed to 400 ppm, and rats and mice exposed to up to 1,500 ppm chloromethane for

intermediate durations (CIIT 1981; McKenna et al. 198 lb; Mitchell et al. 1979), or rats and mice exposed

chronically to up to 1,000 ppm (CIIT 1981).

Cardiovascular Effects. Cardiovascular effects, such as electrocardiogram abnormalities, tachycardia and

increased pulse rate, and decreased blood pressure; and gastrointestinal effects such as nausea and vomiting,

have been described in case reports of humans exposed to chloromethane vapors occupationally or

accidentally due to refrigerator leaks (Baird 1954; Baker 1927; Battigelli and Perini 1955; Borovska et al.

1976; Gummert 1961; Hansen et al. 1953; Kegel et al. 1929; Mackie 1961; McNally 1946; Jones 1942;

Raalte and van Velzen 1945; Spevak et al. 1976; Verriere and Vachez 1949). These case reports also

describe neurological effects; therefore, the cardiovascular and gastrointestinal effects may be secondary to

the neurotoxic effects of chloromethane. Exposure concentrations were probably very high, perhaps

>30,000 ppm, because the leaks occurred in rooms with little or no ventilation.

Rafnsson and Gudmundsson (1997) report a clear excess mortality from cardiovascular disease

(Mantel-Haenszel point estimate=2.1, 95%; CI=1.2-3.8) in crew members (males) exposed for 2 days to

chloromethane that leaked from a refrigerator on board an Icelandic fishing trawler (no estimates of

exposure levels were reported). This excess was more prominent among deckhands who had received the

highest exposure to chloromethane. The Risk ratios were elevated for all causes of death (RR=2.5, 95%;

CI=l.0-5.7) as well as for cardiovascular disease (RR=3.9, 95%; CI=l.0-14.4). The study is weakened by

an assumption of comparable lifestyle factors (including smoking habits and diet) between the cohort and the
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reference group and by the relatively small size of the exposed cohort. The authors also do not discuss the

potential influence of the documented neurological deficits in this cohort (Gudmundsson 1977) on

cardiovascular function. The authors suggest, however, that additional study on chloromethane’s potential

cardiovascular toxicity is warranted.

Increased heart rate and blood pressure followed by decreased heart rate and blood pressure, possibly due to

vasodilation resulting from depression of the central nervous system, occurred in dogs exposed by inhalation

to high concentrations of chloromethane (15,000 and 40,000 ppm) ( von Oettingen et al. 1949, 1950). The

dogs died within 4-6 hours. Cardiovascular effects have not been described in other species after acute,

intermediate, or chronic exposure by inhalation.

Gastrointestinal Effects. Numerous case reports of humans exposed to chloromethane have described

symptoms of nausea and vomiting (Baird 1954; Baker 1927; Battigelli and Perini 1955; Borovska et al.

1976; Hansen et al. 1953; Kegel et al. 1929; Mackie 1961; Jones 1942; Raalte and van Velzen 1945;

Spevak et al. 1976; Verriere and Vachez 1949). In all cases, these symptoms were accompanied by central

nervous system toxicity, which was usually severe. It is not clear, therefore, if the nausea and vomiting

were secondary to the neurotoxic effects of chloromethane.

Histopathological examination of animals exposed to various concentrations of chloromethane for acute,

intermediate, or chronic durations did not show evidence of gastrointestinal damage (CIIT 1981; McKenna

et al. 1981a, 1981b).

Hematological Effects. No hematological effects were found in volunteers who participated in a study of

neurological and neurobehavioral effects of acute inhalation exposure of up to 150 ppm chloromethane

(Stewart et al. 1980). Case reports of human overexposure have also generally been negative for

hematological effects.

No long-term effect on the hematological system from an acute exposure was reported by Gudmundsson

(1977). Seventeen crew members (males) were exposed for 2 days in 1963 to chloromethane that leaked

from a refrigerator under the crew sleeping quarters on board an Icelandic fishing trawler (no estimates of

exposure levels were reported). Thirteen years later (i.e., in 1976) 10 of the 11 survivors were examined.

All 10 were employed; 8 were employed at sea. The mean age of the 10 survivors examined was 38.3 years
CHLOROMETHANE 112

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(range 30-50 years). All 10 survivors had normal hemoglobin, white cell count, differential leukocyte

count, erthrocyte sedimentation rate, and serum creatinine.

No studies were located regarding the hematological effects of chloromethane in humans following oral or

dermal exposures.

The only hematological effects described in animals were spleen enlargement, suggestive of extramedullary

hematopoiesis, and hemoglobinuria, suggestive of intravascular hemolysis, in mice exposed acutely to

chloromethane by inhalation (Landry et al. 1985). It is not clear if similar hematological effects would

occur in humans.

Musculoskeletd Effects. No studies were located regarding the musculoskeletal effects of chloromethane

in humans or animals following inhalation, oral, or dermal exposures.

Hepatic Effects. Case reports of humans exposed to chloromethane vapors have described clinical jaundice

and cirrhosis of the liver (Kegel et al. 1929; Mackie 1961; Weinstein 1937; Wood 1951), but exposure

concentrations were not known.

Hepatic effects have also been observed in animals exposed by inhalation to chloromethane at concentrations

> 1,000 ppm in acute, intermediate, and chronic duration experiments (Burek et al. 1981; Chellman et al.

1986a; CIIT 1981; Landry et al. 198.5; Mitchell et al. 1979; Morgan et al. 1982). Milder liver effects

occurred in mice exposed acutely to an intermittent but relatively high concentration than to a low but

continuous concentration (Landry et al. 1985). The greater susceptibility to continuous exposure may result

from relatively greater metabolism to a toxic intermediate or from diurnal susceptibility. Hepatic effects

were more severe in mice (necrosis and degeneration) than in rats (cloudy swelling, fatty infiltration,

increased ALT and AST with no necrosis). Furthermore, no hepatic lesions were observed in rats over the

course of 2 years of inhalation exposure to 1,000 ppm, while mice similarly exposed had necrotic lesions

after 6 months (CIIT 1981). The greater susceptibility of mice to the hepatotoxic effects of chloromethane

may be related to the greater ability of chloromethane to conjugate with hepatic glutathione in mice than in

rats (Dodd et al. 1982; Kornbrust and Bus 1984). The reaction of chloromethane with glutathione appears

to be a toxifying ratherthan a detoxication mechanism (Chellman et al. 1986b). While the exact mechanism

for the hepatotoxic effects of chloromethane is unclear, chloromethane can elicit lipid peroxidation as a

secondary consequence of depletion of glutathione (Kornbrust and Bus 1984). Comparison of lipid
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peroxidation in the S-9 fraction from mouse and rat livers revealed much greater lipid peroxidation in mouse

liver than in rat liver. The finding that mice exposed to 2,500 ppm chloromethane expired ethane to an

extent comparable to that produced by 2 mL/kg carbon tetrachloride, and developed moderate to severe

hepatocellular hydropic degeneration provide further evidence that the mechanism of hepatotoxicity may

involve lipid peroxidation.

Endocrine Effects. No studies were located regarding the endocrine effects of chloromethane in humans

following inhalation, oral, or dermal exposures.

Only one animal study reported fatty droplets in the epithelial cells of the zona fasciculata in the adrenals of

Fischer 344 rats acutely exposed to 3,500 and 5,000 ppm chloromethane; the severity of the lesion

increasing with dose (Morgan et al. 1982). Rats were exposed for 5 days, 6 hours/day with a break in

exposure for 2 days, and then a further 4 days of exposure.

Renal Effects. Indicators of renal toxicity, such as albuminuria, increased serum creatinine and blood urea

nitrogen, proteinuria, and anuria have been described in case reports of humans exposed to high levels of

chloromethane vapors due to refrigerator leaks (Kegel et al. 1929; Mackie 1961; Spevak et al. 1976;

Verriere and Vachez 1949).

Effects on the kidney have also been observed in animals exposed by inhalation for acute, intermediate, and

chronic durations. In acute studies, rats developed more severe effects (evidence of renal failure) when

1,000 ppm chloromethane was administered continuously (Burek et al. 1981) than when a 2-fold higher

concentration was administered intermittently (degeneration and necrosis of convoluted tubules) (Chellman

et al. 1986a; Morgan et al. 1982). The greater susceptibility of mice to continuous exposure than to

intermittent exposure for lethal and hepatotoxic effects (Landry et al. 1985), however, did not hold true for

renal toxicity. Only the mice exposed intermittently to the highest concentration had degenerative and

regenerative changes in the tubules. No explanation for this apparent contradiction was offered.

Degeneration and regeneration of renal tubules were also found in other acute duration studies in mice (Jiang

et al. 1985; Morgan et al. 1982), and hyperplasia and kidney tumors were found after 12 months of

exposure and later in a 2-year study (CIIT 1981). The biological significance of the proliferative kidney

lesions in mice is discussed more fully in the subsection on Cancer below.
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The possible relationship between the degenerative effects in the kidneys of mice and granular layer lesions

in the brain, which are also observed in mice, was discussed by Jiang et al. (1985). People who die of renal

insufficiency (not due to chloromethane exposure) often have granular cell necrosis. Since the brain and

kidney lesions in mice in this study were unrelated in severity, however, the brain lesions were probably not

a direct consequence of chloromethane-induced kidney lesions. Although chloromethane depleted

glutathione in the kidney, comparison of lipid peroxidation in the S-9 fractions revealed much less lipid

peroxidation in kidney than in liver, suggesting that the mechanism for renal toxicity may not involve

glutathione-related peroxidase activity (Kornbrust and Bus 1984).

Because some refrigerators more than 30 years old are still in use, leaks of chloromethane vapor at

concentrations high enough to produce hepatic effects, renal effects, and neurotoxicity with consequent

cardiovascular and gastrointestinal effects in humans are possible. It is not known whether exposure of

humans to chloromethane outside or at hazardous waste sites could result in hepatic and renal effects.

Dermal Effects. No studies were located regarding the dermal effects of chloromethane in humans or

animals following inhalation, oral, or dermal exposures.

Ocular Effects. No studies were located regarding the dermal effects of chloromethane in humans following

inhalation, oral, or dermal exposures.

Ophthalmological examination of male cats and dogs exposed to 500 ppm continuously for 3 days

(McKenna et al. 1981a), dogs exposed to 400 ppm for 90 days (McKenna et al. 1981b), or of rats and mice

exposed to 1,000 ppm for up to 24 months (CIIT 1981) failed to reveal eye lesions. Mucopurulent

conjunctivitis with total destruction of the eye in some cases was found in mice exposed to ≥375 ppm for

90 days (Mitchell et al. 1979). These lesions were attributed to exposure because no lesions were found in

controls; however, the failure of longer-term studies to detect eye lesions at higher concentrations makes the

findings of Mitchell et al. (1979) questionable. The effect was probably due to direct contact of the

chloromethane vapor with the eye, rather than a consequence of inhalation.

Body Weight Effects. No studies were located regarding the body weight effects of chloromethane in

humans or animals following inhalation, oral, or dermal exposure to chloromethane.
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Metabolic Effects. No studies were located regarding the metabolic effects of chloromethane in humans or

animals following inhalation, oral, or dermal exposures.

Immunological and Lymphoreticular Effects. No studies were located regarding immunological

and/or lymphoreticular effects in humans after inhalation exposure to chloromethane.

The only effects that could possibly be considered immunological were lymphoid depletion of the spleen and

splenic atrophy observed in mice exposed by inhalation for up to 2 years (CIIT 1981). Since more sensitive

tests for immune function were not conducted, the biological significance of the splenic effects cannot be

assessed. Furthermore, splenic alterations were not observed in rats in the same study. In another study,

cats exposed continuously to chloromethane for 3 days had higher incidences of brain lesions than the

control (McKenna et al. 1981a). The lesions were consistent with infection or post-vaccinal reaction (the

cats were vaccinated for panleukopenia by the supplier). Exacerbation of viral-induced central nervous

system disease, however, could not be ruled out. It is not known whether the exacerbation would represent

an immunological effect.

Neurological Effects. Neurological effects have been described in numerous case reports of humans

exposed to chloromethane vapors as a result of industrial leaks and leaks from defective home refrigerators

(Baird 1954; Gudmundsson 1977; Hansen et al. 1953; Hartman et al. 1955; Kegel et al. 1929; MacDonald

1964; McNally 1946; Jones 1942; Raalte and van Velzen 1945; Spevak et al. 1976; Wood 1951).

Depending on the extent of exposure and the availability of medical treatment, the signs and symptoms can

range from staggering and blurred vision to coma, convulsions, and death. Such effects as abnormal gait,

tremors, and personality changes may persist for several months or years (Gudmundsson 1977), but

complete recovery may eventually occur. In cases in which exposure was quantitated, concentrations were

generally >29,000 ppm (Battigelli and Perini 1955; Jones 1942). Symptoms of blurred vision, fatigue,

vertigo, nausea, vomiting, tremor, and unsteadiness, however, developed in a man and a woman a few days

after they stored insulated boards containing polystyrene foam in the basement of their house (Lanham

1982). The concentration of chloromethane in the house was found to be in excess of 200 ppm (exact levels

not reported). It should be noted, however, that this exposure probably represented an unusual situation

because the rate of air turnover in the couple’s home was an order of magnitude lower than the typical rate.

In addition, a small statistically nonsignificant decrement in performance in behavioral tests was found in

volunteers exposed to 200 ppm (Putz-Anderson et al. 1981a).
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Severe neurological signs (ataxia, tremors, limb paralysis, incoordination, convulsions) have been observed

in rats, mice, rabbits, guinea pigs, dogs, cats, and monkeys exposed acutely by inhalation to high

concentrations of chloromethane (Burek et al. 1981; Chellman et al. 1986a, 1986b; Landry et al. 1985;

McKenna et al. 1981a; Morgan et al. 1982; Smith and von Oettingen 1947b). Signs of neurotoxicity

developed after 6 and 12 months, and degeneration of the granular cell layer of the cerebellum was observed

after 18 months in mice exposed by inhalation for 2 years (CIIT 1981). Cerebellar lesions have also been

observed microscopically in guinea pigs and rats (Kolkmann and Volk 1975; Morgan et al. 1982). Mice

were more susceptible than rats (CIIT 1981; Morgan et al. 1982), and dogs were more susceptible than cats

to the neurological effects of chloromethane (McKenna et al. 1981a). Mice were more sensitive to

neurological effects after continuous exposure to low concentrations than after intermittent exposure to

higher concentrations of chloromethane (Landry et al. 1985). The greater sensitivity of mice to continuous

exposure may be a consequence of metabolism of chloromethane to a toxic intermediate or diurnal

susceptibility.

The mechanism by which chloromethane produces neurological effects is unclear. Pretreatment of mice

with BSO to deplete glutathione protected mice from cerebellar damage due to inhalation exposure to

chloromethane (Chellman et al. 1986b), suggesting that the reaction of chloromethane with glutathione to

form S-methylglutathione is required for the degenerative changes in the brain to occur. In the metabolic

scheme proposed by Kornbrust and Bus (1983), subsequent metabolism of S-methylglutathione produces

methanethiol as an intermediate. Methanethiol produces signs and symptoms of neurotoxicity (tremors,

convulsions, coma) similar to those seen in animals or humans acutely exposed to chloromethane (Chellman

et al. 1986b). The possibility of a relationship between degenerative effects in mice was discussed by Jiang

et al. (1985). Granular cell necrosis is often seen in people who die of renal insufficiency (not due to

chloromethane exposure). Since the brain and kidney lesions in mice in this study were unrelated in severity,

however, Jiang et al. (1985) concluded that the brain lesions were probably not a direct consequence of

chloromethane-induced kidney lesions.

Because refrigerators more than 30 years old are still in use, leaks of chloromethane vapor at concentrations

high enough to produce neurological effects in humans are possible. These exposures have generally

occurred in rooms with poor ventilation. It is not known whether exposure of humans to chloromethane in

the outside environment or at hazardous waste sites could result in neurological effects.
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Reproductive Effects. No studies were located regarding reproductive effects in humans exposed to

chloromethane by any route.

Acute-, intermediate-, and chronic-duration inhalation exposures of male rats to chloromethane have resulted

in such reproductive effects as inflammation of the epididymis and sperm granuloma formation in

epididymides, disruption of spermatogenesis, decreased fertility at about 500 ppm, and sterility at higher

concentrations of 1,000 or 3,000 ppm (Burek et al. 1981; Chapin et al. 1984; Chellman et al. 1986a, 1986b,

1987; CIIT 1981; Han-m et al. 1985; Morgan et al. 1982; Working and Bus 1986; Working et al. 1985a,

1985b). Testicular effects of chloromethane have been manifested as preimplantation loss in unexposed

female rats mated with males exposed to chloromethane (Working et al. 1985a). Testicular lesions were

also observed in mice after 18 months of exposure to chloromethane (CIIT 1981). Studies on the

mechanism of chloromethane-induced testicular effects suggested that preimplantation loss was due to

cytotoxicity of chloromethane to sperm in the testes at the time of exposure, rather than to a genotoxic effect

on the sperm (Chellman et al. 1986a, 1986c, 1987; Working and Bus 1986; Working et al. 1985a, 1985b).

Although testicular effects were observed in mice in the CIIT (1981) study, the incidence was much lower

and occurred much later in mice than it did in rats. The mechanism for testicular and epididymal effects has

been studied only in rats. It is not known whether chloromethane could produce reproductive effects in

humans.

Developmental Effects. No studies were located regarding developmental effects in humans exposed

to chloromethane by any route.

Maternal toxicity, evidenced by decreased body weight gain and retarded development of fetuses, was

observed in rats exposed to 1,500 ppm chloromethane for 6 hours per day during gestational days (Gd) 7-19

(Wolkowski-Tyl et al. 1983a). The fetal effects consisted of reduced fetal body weight and crown-rump

length and reduced ossification of metatarsals and phalanges of the anterior limbs, thoracic centra in the

pubis of the pelvic girdle, and metatarsals of the hindlimbs. These researchers also reported increased

incidences of heart malformations in the fetuses of mouse dams exposed by inhalation to 500 ppm

chloromethane during Gd 6-17. The heart malformations consisted of absence or reduction of

atrioventricular valves, chordae tendineae, and papillary muscles. Heart malformations, however, were not

found in fetuses of mouse dams exposed to higher concentrations of chloromethane during Gd 11.5-12.5,

which they considered to be the critical period for development of the embryonal heart (John-Greene et al.
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1985). John-Greene et al. (1985) suggested that the heart anomaly reported by Wolkowski-Tyl et al. (1983)

may have been an artifact of the sectioning technique, due to the examination of the fixed as opposed to

unfixed fetal tissue, or a misdiagnosis. They also found much inter-animal variability in the appearance of

the papillary muscles in control mice. However, Wolkowski-Tyl(l 985) countered that the inability of JohnGreene et al. (1985) to detect the abnormality was due to the different exposure protocol, and that the

critical period is more appropriately gestational day 14. The developmental toxicity of chloromethane in

mice is, therefore, controversial; it is not known whether chloromethane could produce developmental effects

in humans.

The investigators also found increased incidences of heart malformations in the fetuses of mouse dams

exposed by inhalation to 500 ppm chloromethane during Gd 6-17. Heart malformations, however, were not

found in fetuses of mouse dams exposed to higher concentrations of chloromethane during Gd 11.5-12.5,

which they considered to be the critical period for development of the embryonal heart (John-Greene et al.

1985). According to Wolkowski-Tyl(1985), however, the critical period of embryonal heart development is

more appropriately gestational day 14. The developmental toxicity of chloromethane in mice is, therefore,

controversial; it is not known whether chloromethane could produce developmental effects in humans.

Genotoxic Effects. Chloromethane has been tested for genotoxicity in a number of in vitro and in vivo

systems (Tables 2-4 and 2-5). Chloromethane gave positive results for gene mutation, sister chromatid

exchange, and transformation in cultured mammalian cells, including human lymphoblast cells (Fostel et al.

1985; Hatch et al. 1982, 1983; Working et al. 1986); and appears to be a direct-acting genotoxicant in

vitro. The ability of inflammatory cells (human phagocytes) to produce superoxides capable of genetic

damage has been demonstrated (Weitzman and Stossel 1981). Although chloromethane produced genotoxic

effects in human lymphocytes in culture, it is not known whether chloromethane could produce dominant

lethal mutations or other genotoxic effects in humans exposed by any route.

Although chloromethane was positive for unscheduled DNA synthesis in rat hepatocytes, spermatocytes, and

tracheal epithelial cells in vitro, a marginally positive response was found only in hepatocytes of rats

exposed to chloromethane in vivo, and only at very high concentrations (Working et al. 1986).

Chloromethane exposure consistently produced dominant lethal mutations in the sperm of rats, as measured

by postimplantation loss in females mated to the exposed males (Chellman et al. 1986c; Rushbrook 1984;

Working et al. 1985a). Since concurrent exposure of male rats to chloromethane and BW755C, an antiinflammatory agent, did not result in postimplantation loss, it was suggested that the dominant lethal


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mutation was probably due to chloromethane-induced epididymal inflammation, possibly by production by

inflammatory cells of a superoxide capable of damaging DNA, rather than by a genotoxic effect of

chloromethane itself (Chellman et al. 1986c). Since studies using 14C-chloromethane indicated that the

carbon atom from chloromethane becomes incorporated into normal macromolecules via the one-carbon

pool rather than binding to macromolecules as an alkylating agent (Kornbrust et al. 1982; Peter et al. 1985),

and since the dominant lethal effect may be secondary to inflammation, it is possible that in vivo

genotoxicity and carcinogenicity (see Section 2.2.1.8) may be secondary to other toxic effects of

chloromethane. Nevertheless, the in vitro studies demonstrate the direct genotoxicity of chloromethane.

Positive results have generally been found in the reverse mutation assay in Salmonella typhimurium with

and without metabolic activation (Andrews et al. 1976; DuPont 1977; Simmon et al. 1977). In addition, a

positive result was obtained in S. typhimurium for 8-azaguanine resistance (Fostel et al. 1985).

Cancer. The information regarding carcinogenicity in humans after exposure to chloromethane is limited.

An epidemiology study on a cohort of 24 Icelandic fishermen reported a slight increase in excess mortality

from all cancers, and more specifically, lung cancer (Rafnsson and Gudmundsson 1997). The study was

conducted 32 years after an acute (i.e., 2 days) high level exposure to chloromethane from a leaking

refrigerator. Confounding factors for lifestyle and smoking were not explicitly controlled in this study, but

assumed to be similar based on controls for age, social class, and occupation. One epidemiology study of

butyl rubber workers chronically exposed to chloromethane reported no statistically significant increase in

the rate of death due to cancer (Holmes et al. 1986).

Chloromethane has been tested for carcinogenicity in animals only by the inhalation route. No evidence of a

carcinogenic effect was found in rats or in female mice (CIIT 1981). In a 2-year inhalation study, a

statistically significant increased incidence of kidney tumors developed in 1,000 ppm-exposed B6C3F1 male

mice. Renal hyperplasia was also observed after 12 months of exposure. In an acute study, Chellman et al.

(1986b) found significant increases in cell proliferation in the kidneys of male B6C3F1 mice, as measured by

incorporation of tritiated thymidine into DNA of the kidneys. Such proliferation may be involved in the

development of kidney tumors, a hypothesis supported by the evidence that chloromethane is probably not

an alkylating agent, but acts by an epigenetic mechanism (Korubrust et al. 1982; Peter et al. 1985). Female

B6C3F1 mice exposed to 1,500 ppm chloromethane also had increased cell proliferation in the kidney

(Chellman et al. 1986b), but did not develop kidney tumors in the CIIT (1981) study; however, the exposure

concentrations in the CIIT (1981) study were lower than those in the study by Chellman et al. (1986b). In
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addition, greater evidence of regeneration of renal tubular cells, presumably in response to cell death, was

found in B6C3F1 males than in females of the same strain exposed to 500 and 1,000 ppm chloromethane for

12 days (Morgan et al. 1982). In mice exposed to 2,000 ppm, however, there was no sex difference. It is

possible, therefore, that at relatively low concentrations, female mice are less sensitive than male mice to the

renal toxicity of chloromethane.

Since data that chloromethane exposure was associated with tumors were found in only one sex of one

species in only one study, the evidence that chloromethane is a carcinogen is limited. It is not known

whether cancer could develop in humans exposed to chloromethane by any route.

2.6 CHILDREN’S SUSCEPTIBILITY

This section discusses potential health effects from exposures during the period from conception to maturity

at 18 years of age in humans, when all biological systems will have fully developed. Potential effects on

offspring resulting from exposures of parental germ cells are considered, as well as any indirect effects on

the fetus and neonate due to maternal exposure during gestation and lactation. Relevant animal and in vitro

models are also discussed.

Children are not small adults. They differ from adults in their exposures and may differ in their

susceptibility to hazardous chemicals. Children’s unique physiology and behavior can influence the extent

of their exposure. Exposures of children are discussed in Section 5.6, Exposures of Children.

Children sometimes differ from adults in their susceptibility to hazardous chemicals, but whether there is a

difference depends on the chemical (Guzelian et al. 1992; NRC 1993). Children may be more or less

susceptible than adults to health effects, and the relationship may change with developmental age (Guzelian

et al. 1992; NRC 1993). Vulnerability often depends on developmental stage. There are critical periods of

structural and functional development during both pre-natal and post-natal life and a particular structure or

function will be most sensitive to disruption during its critical period(s). Damage may not be evident until a

later stage of development. There are often differences in pharmacokinetics and metabolism between

children and adults. For example, absorption may be different in neonates because of the immaturity of

their gastrointestinal tract and their larger skin surface area in proportion to body weight (Morselli et al.

1980; NRC 1993); the gastrointestinal absorption of lead is greatest in infants and young children (Ziegler

et al. 1978). Distribution of xenobiotics may be different; for example, infants have a larger proportion of
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their bodies as extracellular water and their brains and livers are proportionately larger (Altman and Dittmer

1974; Fomon 1966; Fomon et al. 1982; Owen and Brozek 1966; Widdowson and Dickerson 1964). The

infant also has an immature blood-brain barrier (Adinolfi 1985; Johanson 1980) and probably an immature

blood-testis barrier (Setchell and Waites 1975). Many xenobiotic metabolizing enzymes have distinctive

developmental patterns and at various stages of growth and development, levels of particular enzymes may

be higher or lower than those of adults and sometimes unique enzymes may exist at particular developmental

stages (Komori 1990; Leeder and Kearns 1997; NRC 1993; Vieira et al. 1996). Whether differences in

xenobiotic metabolism make the child more or less susceptible also depends on whether the relevant enzymes

are involved in activation of the parent compound to its toxic form or in detoxification. There may also be

differences in excretion, particularly in the newborn who has a low glomerular filtration rate and has not

developed efficient tubular secretion and resorption capacities (Altman and Dittmer 1974; NRC 1993; West

et al. 1948). Children and adults may differ in their capacity to repair damage from chemical insults.

Children also have a longer lifetime in which to express damage from chemicals; this potential is particularly

relevant to cancer.

In adults, there appear to be two distinct populations with regard to metabolism and elimination of

chloromethane. One population has higher amounts of the metabolizing enzyme, glutathione-S-transferase,

and thus a higher rate of elimination of chloromethane from the body. The toxicity of chloromethane,

however, is thought to result from toxic metabolites formed following the conjugation with glutathione

(Chellman et al. 1986b; Jager et al. 1988; Kornbrust and Bus 1983, 1984; Nolan et al. 1985; Stewart et al.

1980; Warholm et al. 1995). It is anticipated that children would have a polymorphism similar to the adult

population, although no specific data have been collected to test this hypothesis. If a polymorphism is

present in children, then some children (i.e., those with higher levels of glutathione-S-transferase) would be

more susceptible to the toxic effects of chloromethane.

Certain characteristics of the developing human may increase exposure or susceptibility while others may

decrease susceptibility to the same chemical. For example, the fact that infants breathe more air per

kilogram of body weight than adults may be somewhat counterbalanced by their alveoli being less

developed, so there is a disproportionately smaller surface area for absorption (NRC 1993).

There have been no human studies to determine the health effects of exposure to chloromethane in children,

or whether children are more or less susceptible to the potential health effects of chloromethane at a given

exposure level and duration of exposure. There is no information on whether the effects in children would

be similar to those in adults for either accidental short-term exposures or longer-term lower level exposures.

It is not known whether chloromethane affects the developing fetus or the development of young children.
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There have also been no studies where young animals were exposed to chloromethane. With mid- to high

levels of chloromethane administered to female adult rats and mice during pregnancy, the offspring were

smaller than normal, with underdeveloped bones, and possibly abnormal hearts (although this latter effect

remains uncertain and occoured only in mice).

It is not known whether chloromethane or methanethiol in the body can cross the placenta and enter into the

developing young, or if either compound can enter into breast milk. We do know that chloromethane is

broken down and eliminated from the body very quickly in adults (Nolan et al. 1985) and animals (Landry et

al. 1983a; von Oettingen et al. 1949, 1950). Thus, it is unlikely that chloromethane would be stored in

maternal tissues or be mobilized (i.e., released from stores) during pregnancy or lactation.

In adults, there appear to be two distinct populations with regard to metabolism and elimination of

chloromethane. One population appears to have higher amounts of the metabolizing enzyme, glutathione-Stransferase, and thus a higher rate of elimination of chloromethane from the body. The toxicity of

chloromethane, however, is thought to result from toxic metabolites formed following the conjugation with

glutathione (Chelhnan et al. 1986b; Jager et al. 1988; Kornbrust and Bus 1983, 1984; Nolan et al. 1985;

Stewart et al. 1980; Warholm et al. 1995). It is anticipated that children would have a polymorphism

similar to the adult population, although no specific data have been collected to test this hypothesis. If a

polymorphism is present in children, then some children (i.e., those with higher levels of glutathione-Stransferase) would be more susceptible to the toxic effects of chloromethane.

Although the breakdown and elimination of chloromethane is expected to be the same in children as in

adults, more studies are needed to answer this and other questions concerning the movement of

chloromethane into the fetus or breast milk, and what levels might result in harmful effects. There are no

PBPK models for children, adults, or test animal models. There are no good biomarkers of exposure for

children (or adults), although clinical symptoms of drunkenness or food poisoning, and a sweet odor of the

breath may alert a physician. Attempts to use urinary levels of S-methylcysteine as an indicator of

chloromethane exposure have not been successful.

Only limited information is available from animal studies on potential effects in the developing young. In

one animal study, pregnant rats were exposed to 1,500 ppm chloromethane by inhalation during gestation.

Maternal toxicity, evidenced by decreased body weight gain and retarded development of fetuses, was

observed in rats exposed to 1,500 ppm chloromethane for 6 hours per day during gestational days (Gd) 7-19

(Wolkowski-Tyl et al. 1983a). The fetal effects consisted of reduced fetal body weight and crown-rump
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length and reduced ossification of metatarsals and phalanges of the anterior limbs, thoracic centra in the

pubis of the pelvic girdle, and metatarsals of the hindlimbs.

In a mouse study, dams were exposed by inhalation to chloromethane during gestation days 6-17

(Wolkowski-Tyl et al. 1983a). The investigators found increased incidences of heart malformations in the

fetuses of mouse dams exposed to 500 ppm chloromethane during Gd 6-17. The heart malformations

consisted of absence or reduction of atrioventricular valves, chordae tendineae, and papillary muscles.

Heart malformations, however, were not found in fetuses of mouse dams exposed to higher concentrations of

chloromethane during Gd 11 S-12.5, which they considered to be the critical period for development of the

embryonal heart (John-Greene et al. 1985). John-Greene et al. (1985) suggested that the heart anomaly

reported by Wolkowski-Tyl et al. (1983) may have been an artifact of the sectioning technique, due to the

examination of the fixed as opposed to unfixed fetal tissue, or a misdiagnosis. They also found much interanimal variability in the appearance of the papillary muscles in control mice. However, Wolkowski-Tyl

(1985) countered that the inability of John-Greene et al. (1985) to detect the abnormality was due to the

different exposure protocol, and that the critical period is more appropriately gestational day 14. The

developmental toxicity of chloromethane in mice is, therefore, controversial; it is not known whether

chloromethane could produce developmental effects in humans.

Acute-, intermediate-, and chronic-duration inhalation exposures of male rats to chloromethane have resulted

in such reproductive effects as inflammation of the epididymis and sperm granuloma formation in

epididymides, disruption of spermatogenesis, decreased fertility at about 500 ppm, and sterility at higher

concentrations of 1,000 or 3,000 ppm (Burek et al. 1981; Chapin et al. 1984; Chellman et al. 1986a, 1986b,

1987; CIIT 1981; Hamm et al. 1985; Morgan et al. 1982; Working and Bus 1986; Working et al. 1985a,

1985b). Testicular effects of chloromethane have been manifested as preimplantation loss in unexposed

female rats mated with males exposed to chloromethane (Working et al. 1985a). Testicular lesions were

also observed in mice after 18 months of exposure to chloromethane (CIIT 1981). Studies on the

mechanism of chloromethane-induced testicular effects suggested that preimplantation loss was due to

cytotoxicity of chloromethane to sperm in the testes at the time of exposure, rather than to a genotoxic effect

on the sperm (Chellman et al. 1986a, 1986c, 1987; Working and Bus 1986; Working et al. 1985a, 1985b).

Chloromethane exposure consistently produced dominant lethal mutations in the sperm of rats, as measured

by postimplantation loss in females mated to exposed males (Chellman et al. 1986c; Rushbrook 1984;

Working et al. 1985a). Because of the known transit times for sperm in the epididymis and the resulting

observed times of the postimplantation losses, Working et al. (1985a) observed that the timing of the genetic

damage to the sperm coincided with their location in the chloromethane-induced inflammation of the
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epididymis. Since concurrent exposure of male rats to chloromethane and BW755C, an anti-inflammatory

agent, greatly reduced the amount of postimplantation loss, the dominant lethal mutations probably resulted

secondary to the epididymal inflammatory response (Chellman et al. 1986c; Working and Chellman 1989).

The activation of phagocytic cells during the inflammatory process may result in the production of

potentially genotoxic chemical species including the superoxide anion radical, hydrogen peroxide, and lipid

peroxide decomposition products (Fridovich 1978; Goldstein et al. 1979, 1981; Working et al. 1985a).

Chloromethane has been tested for genotoxicity in a number of in vitro and in vivo systems (see Tables 2-4

and 2-5). Chloromethane gave positive results for gene mutation, sister chromatid exchange, and

transformation in cultured mammalian cells, including human lymphoblast cells (Fostel et al. 1985; Hatch

et al. 1982, 1983; Working et al. 1986); and appears to be a direct-acting genotoxicant in vitro. The

ability of inflammatory cells (human phagocytes) to produce superoxides capable of genetic damage has

been demonstrated (Weitzman and Stossel 1981). Although chloromethane produced genotoxic effects in

human lymphocytes in culture, it is not known whether chloromethane could produce dominant lethal

mutations or other genotoxic effects in humans exposed by any route. No information was available on the

distribution of chloromethane or metabolites to parental reproductive organs or germ cells in humans that

could lead to genetic or epigenetic damage to germ cells. It is also not known whether chloromethane

produces a sublethal level of genetic or epigenetic damage to sperm that would, in turn, be sufficiently viable

to form an embryo and subsequently be detrimental (at clinical or subclinical levels) to the developing

young.

2.7 BIOMARKERS OF EXPOSURE AND EFFECT

Biomarkers are broadly defined as indicators signaling events in biologic systems or samples. They have

been classified as markers of exposure, markers of effect, and markers of susceptibility (NAS/NRC 1989).

Due to a nascent understanding of the use and interpretation of biomarkers, implementation of biomarkers as

tools of exposure in the general population is very limited. A biomarker of exposure is a xenobiotic

substance or its metabolite(s), or the product of an interaction between a xenobiotic agent and some target

molecule(s) or cell(s) that is measured within a compartment of an organism (NAS/NRC 1989). The

preferred biomarkers of exposure are generally the substance itself or substance-specific metabolites in

readily obtainable body fluid(s) or excreta. However, several factors can confound the use and

interpretation of biomarkers of exposure. The body burden of a substance may be the result of exposures

from more than one source. The substance being measured may be a metabolite of another xenobiotic

substance (e.g., high urinary levels of phenol can result from exposure to several different aromatic
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compounds). Depending on the properties of the substance (e.g., biologic half-life) and environmental

conditions (e.g., duration and route of exposure), the substance and all of its metabolites may have left the

body by the time samples can be taken. It may be difficult to identify individuals exposed to hazardous

substances that are commonly found in body tissues and fluids (e.g., essential mineral nutrients such as

copper, zinc, and selenium). Biomarkers of exposure to chloromethane are discussed in Section 2.7.1.

Biomarkers of effect are defined as any measurable biochemical, physiologic, or other alteration within an

organism that, depending on magnitude, can be recognized as an established or potential health impairment

or disease (NAS/NRC 1989). This definition encompasses biochemical or cellular signals of tissue

dysfunction (e.g., increased liver enzyme activity or pathologic changes in female genital epithelial cells), as

well as physiologic signs of dysfunction such as increased blood pressure or decreased lung capacity. Note

that these markers are not often substance specific. They also may not be directly adverse, but can indicate

potential health impairment (e.g., DNA adducts). Biomarkers of effects caused by chloromethane are

discussed in Section 2.7.2.

A biomarker of susceptibility is an indicator of an inherent or acquired limitation of an organisms ability to

respond to the challenge of exposure to a specific xenobiotic substance. It can be an intrinsic genetic or

other characteristic or a preexisting disease that results in an increase in absorbed dose, a decrease in the

biologically effective dose, or a target tissue response. If biomarkers of susceptibility exist, they are

discussed in Section 2.9, Populations That Are Unusually Susceptible.

2.7.1 Biomarkers Used to Identify or Quantify Exposure to Chloromethane

Several studies have unsuccessfully attempted to correlate exposure levels of chloromethane in air with

urinary excretion of S-methylcysteine. In a group of 6 workers exposed to TWA g-hour workroom

concentrations of 30-90 ppm the excretion of S-methylcysteine in urine showed wide variations, with little

correlation with exposure levels (van Doorn et al. 1980). On the basis of variable excretion of S-methylcysteine in 6 male volunteers exposed to 10 or 50 ppm chloromethane for 6 hours, Nolan et al. (1985)

concluded that measurement of S-methylcysteine in urine is not a valid method for monitoring exposure to

chloromethane.

In an evaluation of the use of blood and breath analysis of chloromethane to monitor exposure in volunteers

exposed to up to 150 ppm chloromethane, breath levels immediately after exposure to 20 or 100 ppm

correlated with exposure, but subsequent samples were difficult to interpret (Stewart et al. 1980). Exposure

to 100 ppm could not be distinguished from exposure to 150 ppm. The excretion patterns following
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prolonged exposure will differ from those observed in these experiments (Morgan et al. 1970), which

followed single breath exposure (see Section 2.3.4.1); therefore, the data are not useful for monitoring

occupational exposure. This conclusion probably applies to prolonged environmental exposure as well.

Symptoms resembling drunkenness and food poisoning, along with a sweet odor of the breath, may alert

physicians that a person has been exposed to chloromethane.

Xu et al. (1990) evaluated whether covalent binding of chloromethane to hemoglobin would be a viable

measure for monitoring exposure. In comparison to the other monohalomethanes tested (methyl bromide

and methyl iodide), chloromethane had the lowest reactivity with hemoglobin. The authors support further

assay development for methyl bromide, but make no mention of the usefulness of a covalent binding assay

for chloromethane, presumably because its reactivity was too low.

2.7.2 Biomarkers Used to Characterize Effects Caused by Chloromethane

Attempts to correlate blood levels and expired air concentrations of chloromethane with health effects of

occupational and experimental inhalation exposure have been unsuccessful. In a study of 73 behavioral

measures of task performance, 4 indices of exposure and 8 indicators of neurological function in workers

exposed to a mean concentration of 34 ppm chloromethane, effects on cognitive time-sharing and finger

tremor were found, but correlation coefficients indicated that chloromethane in breath was not a sensitive

indicator of performance (Repko et al. 1977). Although volunteers exposed to 200 ppm chloromethane for

3 hours had a 4% decrement in their performance on behavioral tests, blood and alveolar air levels of

chloromethane were too variable to be of practical use (Putz-Anderson et al. 1981a). The decrement in

performance was also small and not statistically significant.

For more information on biomarkers for renal and hepatic effects of chemicals see ATSDR/CDC

Subcommittee Report on Biological Indicators of Organ Damage (1990) and for information on biomarkers

for neurological effects see OTA (1990).

2.8 INTERACTIONS WITH OTHER CHEMICALS

Inhalation exposure of volunteers to 200 ppm chloromethane along with oral dosing with 10 mg diazepam

produced an additive impairment in performance on behavioral tests (Putz-Anderson et al. 1981a). Since

both of these compounds are known to be central nervous system depressants, workers who are exposed to
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chloromethane in industry or during cleanup of hazardous waste sites, or people who live near hazardous

waste sites where chloromethane is present and are treated with diazepam or exposed to other central

nervous system depressants, including alcohol, may have aggravated symptoms.

Minami et al. (1992) report on a patient in Japan exposed simultaneously to chloromethane and chloramine

gas. The exposure resulted from the patient first cleaning a porcelain toilet with sodium hypochlorite

(NaOCl) in an alkaline solution then, without first rinsing off the hypochlorite, spraying a hydrochloric acid

(HCl) solution to remove hard salt adhesions. The toilet was connected directly to a sewage storage tank.

The resulting fumes produced a toxic response in the patient 30 minutes after cleaning. The patient

recovered from the acidosis after bicarbonate transfusion, plasmapheresis, and plasma exchange; but

permanent blindness ensued 3 days postexposure. In a follow-up study, Minami et al. (1993) demonstrated

an increase in formate excretion in mice dosed with chloramine after exposure to chloromethane. The

authors ascribe this increase to an inhibitory effect of chloramine on formyl tetrahydrofolate dehydrogenase

and formaldehyde dehydrogenase. More recently, Wang and Minami (1996) extended their proposed

mechanism to include a potentiation of formaldehyde on chloramine inhibition of acetycholinesterase

activity.

The only other studies that show an effect of other compounds on the toxicity of chloromethane are those in

which the effects of BW755C, an anti-inflammatory agent, and BSO, a depleter of glutathione, were

administered to rats or mice exposed to chloromethane by inhalation to study the mechanism of

chloromethane-induced toxicity (Chellman et al. 1986a, 1986b). These studies are discussed in Section 2.2.

It is unlikely that these compounds would be found with chloromethane at hazardous waste sites.

2.9 POPULATIONS THAT ARE UNUSUALLY SUSCEPTIBLE

A susceptible population will exhibit a different or enhanced response to chloromethane than will most

persons exposed to the same level of chloromethane in the environment. Reasons may include genetic

makeup, age, health and nutritional status, and exposure to other toxic substances (e.g., cigarette smoke).

These parameters may result in reduced detoxification or excretion of chloromethane, or compromised

function of target organs affected by chloromethane. Populations who are at greater risk due to their

unusually high exposure to chloromethane are discussed in Section 5.7, Populations With Potentially High

Exposure.
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In general, people who have kidney or liver disease, anemia, or neurological deficits may be more

susceptible to the toxic effects of chloromethane.

Two distinct populations of humans with differences in elimination of chloromethane have been identified.

Some of the volunteers exposed by inhalation to chloromethane had distinctly higher chloromethane

concentrations in alveolar breath samples than others (Stewart et al. 1980). In humans exposed to

chloromethane by inhalation, the chloromethane was eliminated from the blood and expired air more slowly

by the subjects who had higher venous blood and expired air concentrations than by those who had lower

concentrations (Nolan et al. 1985). This finding was believed to be due to differences in metabolic rate. In

six workers exposed to chloromethane occupationally, the excretion of S-methylcysteine showed wide

variations, and there was little or no correlation between exposure levels and excretion (van Doom et al.

1980). In four of the workers, all concentrations of S-methylcysteine were higher than in controls, and

appeared to increase during the course of the week. The other two workers had only small amounts of

S-methylcysteine in the urine, but these workers had experienced the highest exposure concentrations. These

results support the hypothesis that there are two distinct populations: fast eliminators, with lower body

burdens and higher excretion; and slow eliminators, with higher body burdens and lower excretion.

Because chloromethane is eliminated relatively rapidly, the observation of two distinct populations may have

no toxicological significance (Nolan et al. 1985). Based on studies in mice, the reaction of chloromethane

with glutathione, however, may lead to the formation of toxic compounds in humans that exert their action

before they are eliminated. If slow eliminators have a deficiency of glutathione- S-transferase, the enzyme

that catalyzes the conjugation of glutathione with chloromethane, or low levels of glutathione, they would be

expected to be less susceptible to the toxic effects of chloromethane. The extent to which chloromethane

reacts with glutathione in humans, however, is not known.

As discussed in Section 2.8, workers treated with diazepam and exposed to chloromethane had an additive

impairment in performing behavioral tests (Putz-Anderson et al. 1981a). These results imply that people

who are occupationally exposed to chloromethane and treated with diazepam, or perhaps other drugs that

depress the central nervous system, may have aggravated symptoms.

2.10 METHODS FOR REDUCING TOXIC EFFECTS

This section will describe clinical practice and research concerning methods for reducing toxic effects of

exposure to chloromethane. However, because some of the treatments discussed may be experimental and
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unproven, this section should not be used as a guide for treatment of exposures to chloromethane. When

specific exposures have occurred, poison control centers and medical toxicologists should be consulted for

medical advice. The following texts provide specific information about treatment following exposures to

chloromethane:

Goldfrank LR, Flomenbaum NE, Lewin NA, et al. 1994. Goldfrank’s Toxicologic Emergencies.

Fifth edition. Norwalk. CT: Appleton & Lange, 1231-1244.

Ellenhorn MJ, Barceloux DG. 1988. Medical Toxicology: Diagnosis and Treatment of Human

Poisoning. New York, NY. Elsevier, 982-983.

ATSDR. 1994. Agency for Toxic Substances and Disease Registry. Medical Management

Guidelines for Acute Chemical Exposures: Formaldehyde. Atlanta, GA.

2.10.1 Reducing Peak Absorption Following Exposure

Acute inhalation exposure to high levels of chloromethane primarily causes neurological effects with signs

and symptoms that can range from staggering and blurred vision to coma, convulsions, and death. Such

effects as abnormal gait, tremors, and personality changes may persist for several months or more, but

complete recovery may also occur eventually. Because chloromethane is so rapidly absorbed, metabolized,

and distributed; treatment to reduce absorption would have to be administered promptly. No treatments,

however, were located in the literature except the general indication of supportive treatment. This usually

consists of ensuring open airways, adequate supply of fresh air, and establishing and monitoring proper

cardiovascular function.

2.10.2 Reducing Body Burden

No information was located on reducing body burdens of absorbed chloromethane.

2.10.3 Interfering with the Mechanism of Action for Toxic Effects

The mechanism(s) of chloromethane toxicity remains unclear, and thus it is uncertain whether depletion or

protection of glutathione pools would be appropriate for any given exposure or target organ.
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Methanethiol and formaldehyde formation, and increased lipid peroxidation due to glutathione depletion

have been suggested as the toxic intermediates and mechanism responsible for the toxicity of chloromethane

(Dekant et al. 1995; Jager et al. 1988; Kombrust and Bus 1983, 1984; Ristau et al. 1989, 1990).

Dodd et al. (1982) also proposed possible mechanisms for the toxicity of chloromethane related to

glutathione depletion including enhancement of the toxicity of chemicals that are detoxified via conjugation

with GSH; prevention of GSH from acting as a cellular reducing agent, thereby interfering with a variety of

physiological functions; or an increase in chloromethane-glutathione conjugates that are then further

metabolized to putative toxic metabolite (e.g., formaldehyde or methanethiol).

Chellman et al. (1986b), however, concluded that the depletion of GSH protected mice from cerebellar

damage due to exposure to chloromethane. The mechanism may involve conjugation of chloromethane with

glutathione in the liver, followed by biliary excretion and enterohepatic circulation of the glutathione

conjugate or possibly a cysteine conjugate and further metabolism by kidney and/or gut flora beta-lyase to

methanethiol. Methanethiol produces similar central nervous system symptoms (tremors, convulsion, coma)

as seen in animals or humans acutely intoxicated with chloromethane (Chellman et al. 1986b).

There is only a limited amount of information available from animal studies on interfering with putative

mechanism of chloromethane-induced toxicity. Interference with specific toxic events has been

demonstrated for BW755C, an anti-inflammatory agent, and for BSO, a depleter of glutathione, when

administered to rats or mice that have been exposed to chloromethane by inhalation (Chellman et al. 1986a,

1986b). BW755C protected rats from chloromethane-induced epididymal or testicular lesions, but did not

alter chloromethane metabolism, tissue distribution, or excretion of 14C-chloromethane, or decrease hepatic

glutathione content. An alternate mechanism for BW755C’s protective effects against testicular damage

could be an inhibition of leukotriene and prostaglandin synthesis.

2.11 ADEQUACY OF THE DATABASE

Section 104(i)(5) of CERCLA, as amended, directs the Administrator of ATSDR (in consultation with the

Administrator of EPA and agencies and programs of the Public Health Service) to assess whether adequate

information on the health effects of chloromethane is available. Where adequate information is not

available, ATSDR, in conjunction with the National Toxicology Program (NTP), is required to assure the

initiation of a program of research designed to determine the health effects (and techniques for developing

methods to determine such health effects) of chloromethane.
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The following categories of possible data needs have been identified by a joint team of scientists from

ATSDR, NTP, and EPA. They are defined as substance-specific informational needs that if met would

reduce the uncertainties of human health assessment. This definition should not be interpreted to mean that

all data needs discussed in this section must be filled. In the future, the identified data needs will be

evaluated and prioritized, and a substance-specific research agenda will be proposed.

2.11.1 Existing Information on Health Effects of Chloromethane

The existing data on health effects of inhalation, oral, and dermal exposure of humans and animals to

chloromethane are summarized in Figure 2-5. The purpose of this figure is to illustrate the existing

information concerning the health effects of chloromethane. Each dot in the figure indicates that one or

more studies provide information associated with that particular effect. The dot does not necessarily imply

anything about the quality of the study or studies, nor should missing information in this figure be

interpreted as a “data need.” A data need, as defined in ATSDR’s Decision Guide for Identifying

Substance-Specific Data Needs Related to Toxicological Profiles (ATSDR 1989), is substance-specific

information necessary to conduct comprehensive public health assessments. Generally, ATSDR defines a

data gap more broadly as any substance-specific information missing from the scientific literature.

As shown in Figure 2-5, information on the health effects in humans exposed to chloromethane is available

only for inhalation or occupational exposures. Accidental leaks of chloromethane from refrigeration units or

from occupational sources involves dermal as well as inhalation exposure; however, the primary exposure

route during an accidental spill or leak is inhalation exposure. The organs or systems adversely affected in

humans after exposure to chloromethane include the liver, kidney, neurological system (including behavioral

alterations), and the cardiovascular and gastrointestinal systems (possibly secondary to the neurological

effects). Death may occur at sufficiently high doses. Information on the adverse health effects of

chloromethane has been presented for occupational exposures of acute, intermediate, and chronic duration.

One epidemiological study found no association between exposure to chloromethane and cancer at any site.

One epidemiological study found a slight excess of mortality from all cancers, and more specifically, from

lung cancers, 32 years following an acute high level exposure to inhaled chloromethane. No information

was available regarding immunological, developmental, reproductive, or genotoxic effects in humans

exposed to chloromethane by any route.

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There have been no studies to determine if children are more or less susceptible than adults to adverse health

effects from a given amount or duration of exposure to chloromethane, or if chloromethane affects the

developing fetus or the development of young children. There is no information on the potential movement

of chloromethane or its metabolites across the placenta and into the developing young. We also do not know

if chloromethane or its metabolites can migrate into breast milk.

A number of studies have evaluated the health effects of chloromethane exposure in animals for the

inhalation route, although only a single comprehensive chronic study in rats and mice has been performed.

Health effects of acute, intermediate, and chronic inhalation exposure in animals include increased mortality,

liver damage, kidney damage and tumors, neurological damage; and adverse reproductive, genotoxic and

possibly developmental effects. In the only oral study in animals, an attempt was made to compare the

hepatotoxicity of chloromethane with that of carbon tetrachloride and chloroform. The administered dose of

chloromethane, however, was too low to produce hepatic effects, and the use of a higher dose was precluded

due to neurotoxicity.

2.11.2 Identification of Data Needs

Chloromethane is highly volatile, and chloromethane in water or soil will likely evaporate to the air

(Chapter 5). Given the volatility of chloromethane, inhalation exposures and toxicity are of primary concern

and have been the most studied. The oral and dermal routes of exposure are also of concern because

chloromethane is ubiquitous in the environment; yet, with the exception of a single-dose oral study

(Reynolds and Yee 1967) and ocular effects from a presumptive dermal exposure in whole-body inhalation

chambers (CIIT 1981; McKenna et al. 1981a, 1981b; Mitchell et al. 1979), no information was located

regarding the health effects of chloromethane in humans or animals after oral or dermal exposure. It is not

possible to predict whether effects following oral or dermal exposure to chloromethane would be similar to

those following inhalation exposure, partially because the pharmacokinetic disposition of chloromethane has

not been compared for the three routes of exposure. Differences in absorption, distribution, and metabolic

pathways could lead to differences in toxic response and different target organs following the three routes of

exposure. Therefore, additional studies using oral and dermal routes of exposure are also needed.

Acute-Duration Exposure. Case reports of humans exposed acutely to high concentrations of

chloromethane have described severe neurological effects, sometimes followed by death (Baird 1954;

Battigelli and Perini 1955; Borovska et al. 1976; Gudmundsson 1977; Jones 1942; Kegel et al. 1929;
CHLOROMETHANE 136

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Lanham 1982; McNally 1946; Spevak et al. 1976; Thordarson et al. 1965). Effects on the cardiovascular

system, liver, and kidney have also been described in case reports of humans exposed for brief periods, or

occupationally for more prolonged periods (Gummert 1961; Hansen et al. 1953; Kegel et al. 1929; McNally

1946; Rafnsson and Gudmundsson 1997; Schamweber et al. 1974; Spevak et al. 1976; Verriere and Vachez

1949). Only one epidemiology study addressed cancer following an acute exposure (Rafnsson and

Gudmundsson 1997). The results indicate a slight elevation in death from all cancers, and a clear increase

in deaths due to cardiovascular disease, but the usefulness of the study conclusions are limited due to

assumptions about similar lifestyle factors between the exposed population and the reference group,

including smoking and drinking habits.

Acute inhalation exposure levels of chloromethane causing death in animals are available for rats and mice

(Burek et al. 1981; Chellman et al. 1986a, 1986b, 1987; Jiang et al. 1985; Landry et al. 1985; Morgan et al.

1982; Smith and von Oettingen 1947a, 1947b; von Oettingen et al. 1949, 1950; Wolkowski-Tyl et al.

1983a, 1983b). Numerous acute inhalation studies have identified the liver and kidney as target organs in

rats and mice (Burek et al. 1981; Chapin et al. 1984; Chelhnan et al. 1986a; Jiang et al. 1985; Landry et al.

1985; Morgan et al. 1982); the spleen as a target organ in mice (Landry et al. 1985); the central nervous

system as a target system in rats, mice, and dogs (Chellman et al. 1986a, 1986b; Jiang et al. 1985;

McKenna et al. 1981a; Smith and von Oettingen 1947a, 1947b); and the testes and epididymides as target

organs in rats (Chapin et al. 1984; Chellman et al. 1987; Morgan et al. 1982; Working et al. 1985b). The

respiratory and cardiovascular systems may be targets in dogs (Dunn and Smith 1947; Smith 1947; Smith

and von Oettingen 1947a, 1947b; von Oettingen et al. 1949, 1950). These studies have shown that species

differ in susceptibility, and that lower levels are needed when administered continuously to produce toxicity

compared with the higher levels needed in intermittent exposures. Some information on the mechanism of

hepatic, renal, neurological, and reproductive effects in mice is available, but more is needed.

The data for acute effects in animals were sufficient to derive an acute inhalation MRL for chloromethane

based on a NOAEL for neurological effects in mice.

Only one acute oral study was reported, and this was not sufficient to derive an MRL. In this study, rats

were dosed orally with chloromethane, and livers were examined for pathology (Reynolds and Yee 1967).

The administered dose was too low to cause hepatic effects, and higher doses were not administered because

of the neurotoxic effects of chloromethane.
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No studies were located regarding effects in humans or animals after dermal exposure to chloromethane.

Pharmacolcinetic data are insufficient to identify target organs of chloromethane after oral and dermal

exposure and more studies are needed. As discussed above, the potential for humans to be exposed to

chloromethane is greater for the inhalation route than for the oral and dermal routes, however,

chloromethane is ubiquitous in the environment. Therefore, acute studies in animals exposed by oral or

dermal routes are needed to identify target organs and dose-response relationships for these routes.

Intermediate-Duration Exposure. Information regarding effects in humans after intermediateduration exposure to chloromethane is limited to findings of neurological symptoms in humans

occupationally exposed. Inhalation studies conducted in rats, mice, and dogs have identified the liver as a

target organ in rats and mice (CIIT 1981; Mitchell et al. 1979; Smith and von Oettingen 1947a); the testes

as a target organ in rats (CIIT 1981; Hamm et al. 198.5); and the kidney, spleen, and central nervous system

as targets in mice (CIIT 1981). The data were sufficient to derive an intermediate-duration inhalation MRL.

No studies were located regarding effects in humans or animals after intermediate-duration oral or dermal

exposure, and pharmacokinetic data are insufficient to identify or predict target organs of chloromethane for

these routes of exposure. As discussed above, although the potential for humans to be exposed to

chloromethane is greater for the inhalation route than for the oral and dermal routes, chloromethane is

ubiquitous in the environment. Intermediate-duration studies in animals exposed by oral or dermal routes

are needed to identify target organs and dose-response relationships for these routes.

Chronic Duration Exposure and Cancer. Only one study was located regarding effects of

chloromethane in humans after chronic inhalation exposure. No studies were located for other routes.

A 2-year inhalation study in animals has been conducted in which both sexes of rats and mice were exposed

to several concentrations of chloromethane (CIIT 1981). The liver, kidney, spleen, and brain were identified

as target organs in mice, and the testes were identified as target organs in rats and mice. Data were

sufficient to derive a chronic inhalation MRL. No studies were located regarding effects in animals after

chronic oral or dermal exposure to chloromethane. Pharmacokinetic data are insufficient to identify or

predict target organs of chloromethane for these routes of exposure. Although the potential for humans to

be exposed to chloromethane is greater for the inhalation route than for the oral and dermal routes,

chloromethane is ubiquitous in the environment. Therefore, chronic-duration studies in animals exposed by

oral or dermal routes are needed to identify target organs and dose-response relationships for these routes.
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The carcinogenic effects of chloromethane were observed in male, but not female mice nor in rats of either

sex. Male mice had increased incidences of kidney tumors at the highest exposure level. The rats and mice

were exposed to the same concentrations, but differences in ventilation rate, the ability to conjugate

chloromethane with glutathione, the further metabolism of the glutathione conjugate, and body weight

effects make it probable that mice received a higher internal dose than rats. It is possible, therefore, that the

exposure concentration was not sufficient in rats to produce kidney tumors. Additional chronic inhalation

studies are needed to provide more information on differences in species susceptibility and to further

evaluate the potential for and the mechanisms of chronic and carcinogenic effects of chloromethane in

humans.

Genotoxicity. Chloromethane has been shown to be genotoxic (Chellman et al. 1986c; Ristau et al.

1990; Rushbrook 1984; Working et al. 1985a). DNA strand breaks have been evaluated in human

lymphoblasts (Fostel et al. 1985). Genotoxic effects have also been evaluated for mutations in S.

typhimurium (Andrews et al. 1976; DuPont 1977; Simmon et al. 1977), sister-chromatid exchange (Fostel

et al. 1985) unscheduled DNA synthesis in rat hepatocytes (Working et al. 1986), effects on spermatocytes

and tracheal epithelial cells (Working et al. 1986), and DNA viral transformation in primary hamster

embryo cells (Hatch et al. 1982, 1983). Studies of the mechanism of dominant lethal mutations in rat sperm

resulting from inhalation exposure of male rats to chloromethane suggest that the dominant lethal effects

may be secondary to inflammation of the epididymis (Chellman et al. 1986c). There remains, however,

some controversy about chloromethane’s alkylating and genotoxic potential, and additional studies are

needed to evaluate the genotoxic risks to humans.

Reproductive Toxicity. No information was available regarding reproductive effects of chloromethane

in humans.

Several inhalation studies, however, have demonstrated that chloromethane is a reproductive toxicant in

male rats (Burek et al. 1981; Chapin et al. 1984; Chellman et al. 1986a, 1986b, 1987; CIIT 1981; Hamm et

al. 1985; Morgan et al. 1982; Working and Bus 1986; Working et al. 1985a, 1985b). The mechanism of

this reproductive toxicity has been studied extensively only in rats because testicular lesions in mice

occurred at lower incidences and later time periods than in rats in the 2-year inhalation study by CIIT

(1981). Testicular effects were not observed in male dogs and cats exposed to chloromethane by inhalation

(McKenna et al. 1981a), but the exposure concentrations may not have been high enough. Species

differences in sensitivity exist for other end points as well. No studies were located regarding the
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reproductive effects of chloromethane in animals after oral or dermal exposure, and pharmacokinetic data

are insufficient to support the potential for reproductive effects across routes of exposure. Therefore,

additional inhalation, oral, and dermal studies for reproductive effects in other species at higher exposure

levels are needed to further evaluate the potential adverse reproductive effects in humans from exposure to

chloromethane.

Developmental Toxicity. No information was located regarding developmental effects in humans after

exposure to chloromethane by any route.

The teratogenicity of inhalation exposure to chloromethane has been studied in rats and mice

(Wolkowski-Tyl et al. 1983a). In rats, delayed fetal development was found at a concentration that also

resulted in maternal toxicity. Positive results in mice have been reported (Wolkowski-Tyl 1985); however

there is some controversy related to conflicting results reported from other laboratories (John-Greene et al.

1985). Additional studies are needed to further evaluate the pharmacokinetics and the potential teratogenic

effects of exposure to chloromethane.

No studies were located regarding the developmental effects of chloromethane in animals after oral and

dermal exposure, and the pharmacokinetic data are insufficient to extrapolate to these routes of exposure.

Additional studies in mice and other species are needed to evaluate the potential developmental risks to

humans from these routes of exposure.

Immunotoxicity. No information was located regarding immunotoxic effects in humans after exposure

to chloromethane by any route.

The immunotoxic effects reported in the literature from exposure to chloromethane were lymphoid depletion

of the spleen and splenic atrophy observed in mice exposed by inhalation to chloromethane for 2 years (CIIT

1981). Cats exposed continuously to chloromethane for 3 days had higher incidences of brain lesions than

the control (McKenna et al. 1981a), but the lesions were consistent with infection or post-vaccinal reaction

(the cats were vaccinated for panleukopenia by the supplier). Exacerbation of viral-induced central nervous

system disease could not be ruled out. Additional studies are needed to further evaluate the potential

immunotoxicity of chloromethane to humans.
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Neurotoxicity. The neurotoxic effects in humans from inhalation exposure to chloromethane are

described in numerous case studies (Baird 1954; Battigelli and Perini 1955; Gudmundsson 1977; Hansen et

al. 1953; Hartman et al. 1955; Jones 1942; Kegel et al. 1929; Lanham 1982; MacDonald 1964; McNally

1946; Raalte and van Velzen 1945; Spevak et al. 1976; Wood 1951), but the mechanism is unclear.

S-methylcysteine appears to be a metabolite in humans (Kornbrust and Bus 1983), and mechanisms

involving conjugation with glutathione are likely to be relevant to human toxicity. Methanethiol produces

similar central nervous system effects as seen in humans and animals exposed to chloromethane (Jager et al.

1988; Kornbrust and Bus 1983, 1984).

The neurotoxic effects of inhalation exposure to chloromethane are also well defined in animals (Burek et al.

1981; Chelhnan et al. 1986a, 1986b; CIIT 1981; Kolkmann and Volk 1975; Landry et al. 1985; McKenna

et al. 1981a; Morgan et al. 1982; Smith and von Oettingen 1947b). The mechanism for the induction of

cerebellar lesions in mice exposed by inhalation may involve conjugation of chloromethane with glutathione,

with further metabolism leading to production of methanethiol (Chellman et al. 1986b). The relative

importance of conjugation with glutathione in other species has not been determined.

Monkeys provide a better animal model compared with rodents when evaluating neurobehavioral effects in

humans. Neurobehavioral studies in monkeys and additional mechanistic studies in rodents are needed to

further evaluate the mechanism and dose-response relationships of chloroform-induced neurotoxicity in

humans.

No studies were located regarding the neurotoxic effects of chloromethane in animals after oral and dermal

exposure, and pharmacokinetic data are insufficient to extrapolate to other routes of exposure.

Epidemiological and Human Dosimetry Studies. A retrospective epidemiological study was

conducted in workers exposed to chloromethane in a butyl rubber manufacturing facility (Holmes et al.

1986). No association was found between chloromethane exposure and death due to cardiovascular disease

or cancer at any site. In a study of workers from fabricating plants, occupational exposure to

chloromethane below 100 ppm produced subtle, quantifiable behavioral effects, but the threshold for

changes in functional capacity could not be determined precisely (Repko et al. 1977). An experimental

study by Stewart et al. (1980) found no effects on pulmonary function, cardiac function or ECG, and no

hematological, neurological, or behavioral effects in human volunteers exposed by inhalation to

chloromethane, but the protocol was too confusing to clearly define the exposures. A slight decrement in
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performance of behavioral tasks was found in human volunteers exposed to 200 ppm for 3 hours

(Putz-Anderson et al. 1981a). An epidemiology study on a cohort of 24 Icelandic fishermen reported a

slight increase in excess mortality from all cancers (more specifically, lung cancer) and a clear increase in

death from cardiovascular disease (Rafnsson and Gudmundsson 1997). The study was conducted 32 years

after an acute (i.e., 2 days) high level exposure to chloromethane from a leaking refrigerator (although no

estimates of exposure levels were reported). The usefulness of these results are limited because confounding

factors for lifestyle and smoking were not explicitly controlled, but assumed to be similar based on controls

for age, social class, and occupation. Exposure levels were also not quantified. Additional epidemiology

and dosimetry studies are therefore needed to further evaluate the occupational and environmental health risk

from exposure to chloromethane.

Biomarkers of Exposure and Effect.

Exposure. A number of studies have unsuccessfully tried to relate blood and alveolar air levels of

chloromethane and urinary levels of S-methylcysteine with exposure (DeKok and Antheunius 1981; Nolan et

al. 1985; Stewart et al. 1980; Van Doorn et al. 1980). The blood and alveolar air levels of chloromethane

and the urinary levels of S-methylcysteine are highly variable. Symptoms resembling drunkenness and food

poisoning, along with a sweet odor on the breath, may alert a physician that a person has been exposed to

chloromethane, but such symptoms could easily be mistaken for the conditions they resemble.

Although Xu et al. (1990) reported low chloromethane reactivity with hemoglobin, protein adducts may still

hold promise as potential biomarkers for chloromethane exposure. In view of chloromethane’s genotoxicity

in short-term assays, an assay for a DNA adduct or indicator of oxidative damage to DNA from

chloromethane exposure might also be pursued. Further studies are, therefore, needed to identify a

metabolite or biomarker that can be used to monitor chloromethane exposure.

Effect. Attempts to correlate blood levels and expired air concentrations of chloromethane with health

effects of occupational and experimental inhalation exposures of humans have also been unsuccessful

(Putz-Anderson et al. 1981a; Repko et al. 1977). Blood and alveolar levels are highly variable and are not

sensitive indicators of neurological function or behavior. Further studies are needed to identify a metabolite

or biomarker that can be correlated with the known toxic end point and that would lead to early detection

and possibly treatment.
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Absorption, Distribution, Metabolism, and Excretion. Experimental inhalation studies in animals

and humans indicate that chloromethane is rapidly taken up from the lungs into the blood, widely distributed

throughout the body and extensively metabolized, incorporated into macromolecules, and excreted as CO2

or other metabolites in the urine (Dekant et al. 1995; Dodd et al. 1982; Heck et al. 1982; Jager et al. 1988;

Kornbrust and Bus 1983, 1984; Kornbrust et al. 1982; Landry et al. 1983a, 1983b; Putz-Anderson et al.

1981a, 1981b; Redford-Ellis and Gowenlock 1971a, 1971b; Van Doorn et al. 1980; von Oettingen et al.

1949, 1950). Differences in the rate and extent of absorption, metabolic pathways, and disposition will have

a profound effect on the toxicity of chloromethane. Oral and dermal routes of exposure may be of particular

concern because chloromethane is ubiquitous in the environment. Additional pharmacokinetic studies are

needed to evaluate the potential for delivery of toxic levels of chloromethane to human target tissues from

different routes of exposure and durations of exposure.

Comparative Toxicokinetics. Studies on the pharmacokinetics of chloromethane following inhalation

exposure have been conducted in rats, mice, dogs, and humans (Dekant et al. 1995; Dodd et al. 1982; Heck

et al. 1982; Jager et al. 1988; Kombrust and Bus 1983, 1984; Kombrust et al. 1982; Landry et al. 1983a,

1983b; Putz-Anderson et al. 1981a, 1981b; Redford-Ellis and Gowenlock 1971a, 1971b; Van Doorn et al.

1980; von Oettingen et al. 1949, 1950). The kinetics of chloromethane in humans were similar to those in

rats and dogs, with data for each species consistent with a 2-compartment model. Some species differences

can be explained by differences in respiratory minute volumes and basal metabolic rates (rat > dog >

human). Additional pharmacokinetic studies in different species and with different routes of exposure are

needed to further evaluate the target tissues and the differences in potential toxic metabolites. Additional

studies are especially needed to resolve the relative importance of glutathione conjugation and P-450

oxidation to the toxicity of chloromethane. These studies should be performed in different tissues, species,

and sexes to resolve potential differences. Additional studies are needed to evaluate the importance of

varying levels of human endogenous erythrocyte, glutathione transferase (as has been recently shown to

exist) to the toxicity of chloromethane and to the identification of potentially susceptible populations.

Methods for Reducing Toxic Effects. Additional studies are needed to further define the mechanism

of chloromethane’s toxicity. Especially important are studies to determine whether depletion or protection

of glutathione pools is needed to protect against toxicity for any given exposure route or target organ. The

mechanisms and the beneficial or detrimental contribution of glutathione may be different for different end

points or target tissues.
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Children’s Susceptibility. There have been no studies on whether children are more or less susceptible

than adults to adverse health effects from a given amount or duration of exposure to chloromethane, or if

chloromethane affects the developing fetus or the development of young children. There have also been no

studies in which young animals were exposed to chloromethane.

Only limited information is available from rat and mouse studies on potential effects in the developing young

(see above in Data Needs for Developmental Toxicity). In one rat study (Wolkowski-Tyl et al. 1983a), at

levels that also produced maternal toxicity, fetal effects consisted of reduced fetal body weight and crownrump

length and reduced ossification of metatarsals and phalanges of the anterior limbs, thoracic centra in

the pubis of the pelvic girdle, and metatarsals of the hindlimbs. Wolkowski-Tyl et al. (1983a) also found

increased incidences of heart malformations in the fetuses of mouse dams exposed to 500 ppm

chloromethane during Gd 6-17; however, heart malformation were not found in fetuses of mouse dams

exposed to higher concentrations of chloromethane during Gd 11.5-12.5 (John-Greene et al. 1985). The

developmental toxicity of chloromethane in mice is, therefore, controversial, and further studies are needed

to determine potential adverse effects on development from maternal and fetal exposure to chloromethane.

There is no information on the movement of chloromethane or its metabolites across the placenta or into the

developing young. There is no information on the movement of chloromethane or its metabolites into a

nursing women’s milk. Chloromethane is broken down and eliminated from the body very quickly in adults

(Nolan et al. 1985) and animals (Landry et al. 1983a; von Oettingen et al. 1949, 1950). Thus, it is unlikely

that chloromethane would be stored in maternal tissues or be mobilized (i.e., released from stores) during

pregnancy or lactation. However, further studies are needed to answer these questions.

In adults, there appear to be two distinct populations with regard to metabolism and elimination of

chloromethane. One population has higher amounts of the metabolizing enzyme, glutathione-S-transferase,

and thus a higher rate of elimination of chloromethane from the body. The toxicity of chloromethane,

however, is thought to result from toxic metabolites formed following the conjugation with glutathione

(Chellman et al. 1986b; Jager et al. 1988; Kombmst and Bus 1983, 1984; Nolan et al. 1985; Stewart et al.

1980; Warholm et al. 1995). It is anticipated that children would have a polymorphism similar to the adult

population, although no specific data have been collected to test this hypothesis. If a polymorphism is

present in children, then some children (i.e., those with higher levels of glutathione-S-transferase) would be

more susceptible to the toxic effects of chloromethane. Moreover, cytochrome P-450 dependent metabolism

of methanethiol may yield formaldehyde and formic acid whose carbon atoms can then enter the one-carbon
CHLOROMETHANE 144

2. HEALTH EFFECTS

pool for incorporation into macromolecules or formation of CO2 (Heck et al. 1982; Jager et al. 1988;

Kombrust and Bus 1983). Guengerich and Shimada (1991) suggest that the human cytochrome P-450

enzyme 2El is a major catalyst in the oxidation of chloromethane. Formaldehyde may also be a direct

product of chloromethane via oxidative dechlorination. Studies are therefore needed to evaluate the

differences among and between children and adults for P-450 and transferase levels and isoforms, and for

differences in chloroform metabolism.

There are no PBPK models for children, adults, or test animal models. There are no good biomarkers of

exposure for children (or adults), although clinical symptoms of drunkenness or food poisoning, and a sweet

odor of the breath may alert a physician. Attempts to use urinary levels of S-methylcysteine as an indicator

of chloromethane exposure have not been successful. Further studies are needed to evaluate the

toxicokinetics of chloromethane and its metabolites in children and to develop better biomarkers of exposure

and effects.

Child health data needs relating to exposure are discussed in Section 5.8.1, Data Needs: Exposures of

Children.

2.11.3 Ongoing Studies

No ongoing studies were found that address the health effects of chloromethane.

The National Science Foundation is sponsoring a study to analyze the degradation products of a methane

oxidizing bacteria (methanotrophic degradation) for selected contaminants including chloromethane to

demonstrate that no toxic products are formed. A laboratory scale treatment column will also be used to

optimize conditions for the removal of chlorinated aliphatics from contaminated waters. The principal

researcher is Samuel Fogel, Cambridge Analytical Associates, Inc., Boston, Massachusetts.
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3. CHEMICAL AND PHYSICAL INFORMATION

3.1 CHEMICAL IDENTITY

Information regarding the chemical identity of chloromethane is located in Table 3-1.

3.2 PHYSICAL AND CHEMICAL PROPERTIES

Information regarding the physical and chemical properties of chloromethane is located in Table 3-2.



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4.1 PRODUCTION

Table 4-1 lists the facilities in each state that manufacture or process chloromethane, the intended use, and

the range of maximum amounts of chloromethane that are stored on site. The data listed in Table 4-l are

derived from the Toxics Release Inventory (TRI96 1998). Only certain types of facilities were required to

report. Therefore, this is not an exhaustive list. Based on the most current TRI information, there are

currently 96 facilities that produce or process chloromethane in the United States.

Chloromethane (also commonly known as methyl chloride) is both an anthropogenic and naturally occurring

chemical. Anthropogenic sources include industrial production, polyvinyl chloride burning, and wood

burning; natural sources include the oceans, microbial fermentation, and biomass fires (e.g., forest fires,

grass fires). Chloromethane is produced industrially by reaction of methanol and hydrogen chloride (HCl)

or by chlorination of methane (Edwards et al. 1982a; Holbrook 1992; Key et al. 1980). While the reaction

of methanol with HCl is the most common method, the choice of process depends, in part, on the HCl

balance at the site (the methane route produces HCl, the methanol route uses it) (Edwards et al. 1982a;

Holbrook 1992). Typically, manufacturing plants that produce chloromethane also produce higher

chlorinated methanes (methylene chloride, chloroform, and carbon tetrachloride).

The methanol-HCl process involves combining vapor-phase methanol and HCl at 180-200 °C, followed by

passage over a catalyst where the reaction occurs (Holbrook 1992; Key et al. 1980). Catalysts include

alumina gel, gamma alumina, and cuprous or zinc chloride on pumice or activated carbon. The exit gases

from the reactor are quenched with water to remove unreacted HCl and methanol. The quench water is

stripped of the dissolved methanol and chloromethane, and the remaining dilute HCl solution is used inhouse

or treated and discharged (Holbrook 1992; Key et al. 1980). The chloromethane is then dried by

treatment with concentrated sulfuric acid, compressed, cooled, and stored.

In the methane chlorination process, a molar excess of methane is mixed with chlorine, and the mixture is

then fed to a reactor, which is operated at 400 °C and 200 kPa pressure (Holbrook 1992; Key et al. 1980).

The exit gases can then be scrubbed with chilled chloromethanes (mono- to tetrachloromethane) to remove

most of the reaction chloromethanes from unreacted methane and HCl. The by-product HCl is removed by



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4. PRODUCTION, IMPORT/EXPORT, USE, AND DISPOSAL

water wash, stripped of any chloromethanes, and either used in-house or sold; the unreacted methane is

recycled through the process. The condensed chloromethanes are scrubbed with dilute NaOH to remove any

HCl, dried, compressed, cooled, and then fractionally distilled to separate the four chloromethanes. While

there are some variations to this process, including the use of catalysts, this is a general overview of the

basic steps in the process.

It is difficult to estimate the total production levels for chloromethane at specific plants because many of the

producers consume their output internally as a feedstock for other chemicals, including silicones and higher

chlorinated methanes. Current production capacity in the United States is estimated to be in the

neighborhood of 920 million pounds (417.3 million kg) per year (CMR 1995). The seven facilities with the

largest production capacities are: (1) Dow Chemical Company plant at Freeport, Texas; (2) Dow Chemical

Company plant at Plaquemine, Louisiana; (3) Dow Corning Corporation plant at Carrolton, Kentucky; (4)

Dow Corning Corporation plant at Midland, Michigan; (5) GE Plastics Company plant at Waterford, New

York; (6) Vulcan Chemical Company plant at Geismar, Louisiana; and (7) Vulcan Chemical Company

plant at Wichita, Kansas (CMR 1995). All these facilities have production capacities in excess of 50

million pounds per year. At the GE Plastics facility and the two Dow Corning facilities, all the

chloromethane generated is used on-site in silicone production; a large percentage of the output from the

Dow plant in Freeport, Texas, and the two Vulcan facilities are also used on-site as feedstocks in the

manufacture of other chemicals and products (CMR 1995).

Available estimates for annual production show a growth in output from the early 1980s through the mid1990s. These production trends are documented in Table 4-2 (C&EN 1992, 1995). In addition to direct

manufacture, chloromethane is also produced naturally and from a number of human industrial activities

(e.g., the manufacture of vinyl chloride) that can lead to the inadvertent production and release of

chloromethane to environmental media. These releases are discussed in Chapter 5.

4.2 IMPORT/EXPORT

In the period from 1990 through 1994, U.S. imports of chloromethane showed considerable fluctuations,

with annual import levels ranging from 2,241,040 kg (4,930,288 lbs) in 1990 to a low value of 119,171 kg

(262,176 lbs) in 1991. During 1992, imports rebounded to 657,612 kg (1,446,746 lbs); more recently,

imports have increased to 1,682,383 kg (3,701,242 lbs) in 1993 and 1,916,523 kg (4,216,350 lbs) in 1994

(USDOC 1996). During the same period, exports also showed considerable volatility, with export levels

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4. PRODUCTION, IMPORT/EXPORT, USE, AND DISPOSAL

outpacing imports by a factor of about 2. In the period from 1991 through 1995, export levels ranged from

5,092,969 kg (11,204,532 lbs) in 1992 to 7,107,860 kg (15,637,292 lbs) in 1991 (USDOC 1996).

4.3 USE

Chloromethane is used mainly (72%) in the production of silicones (CMR 1986; Holbrook 1992).

Chloromethane has also been used in the production of agricultural chemicals (8%), methyl cellulose (6%),

quaternary amines (5%), butyl rubber (3%), and for miscellaneous uses including tetramethyl lead (2%)

(CMR 1986). It has been used in the past as a component or propellant in some cleansers and industrial

solvents (Howard 1990). It has also apparently been used in the past as a foam blowing agent and as an

agricultural pesticide or fumigant (HSDB 1998). At the present time, virtually all of the commercial uses

for chloromethane are consumptive in that the chloromethane is reacted to form another product during use.

Thus, almost all chloromethane will be consumed when used and will no longer be available for release,

disposal, or reuse.

4.4 DISPOSAL

Limited information was located in the literature concerning the disposal of chloromethane. Since most

chloromethane is used consumptively, little remains to be disposed. Nonetheless, some chloromethane is

present in waste, and chloromethane has been detected in hazardous waste landfills. Its presence in

hazardous waste sites may result from the landfilling of still bottoms or other residues from the manufacture

and use of chloromethane. Its presence in municipal waste landfills suggests that consumer products

containing chloromethane were landfilled (e.g., propellants for aerosol cans, old refrigerators). Since

chloromethane is an impurity in vinyl chloride, the disposal of vinyl chloride may also lead to chloromethane

contamination. Like other chlorinated hydrocarbons, chloromethane can inhibit the combustion of such

fuels as methane. Chloromethane has a considerable inhibitory effect on combustion when mixed with

methane, the principal component of natural gas (Philbrick et al. 1993). Changes in the amounts of

chloromethane added to the methane fuel stock did not produce well-defined relations with the combustion

characteristics. Such phenomena would complicate the disposal of chloromethane using incineration

technologies. When incineration was attempted under oxygen-starved conditions (Taylor and Dellinger

1988), chloromethane was shown to combine with other components of the combustion mixture to form,

among other compounds, chlorinated ethanes, hexachlorobenzene, and octachlorostyrene.
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4. PRODUCTION, IMPORT/EXPORT, USE, AND DISPOSAL

Chloromethane is listed as a toxic substance under Section 313 of the Emergency Planning and Community

Right to Know Act (EPCRA) under Title III of the Superfund Amendments and Reauthorization Act

(SARA). Disposal of wastes containing chloromethane is controlled by a number of federal regulations (see

Chapter 7).
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5. POTENTIAL FOR HUMAN EXPOSURE

5.1 OVERVIEW

Chloromethane has been identified in at least 172 of the 1,467 current or former EPA National Priorities

List (NPL) hazardous waste sites (HazDat 1998). However, the number of sites evaluated for

chloromethane is not known. The frequency of these sites within the United States can be seen in

Figure 5-1. Of these sites, 171 are located in the United States and 1 is located in the Commonwealth of

Puerto Rico (not shown).

Chloromethane (also commonly known as methyl chloride) is a natural and ubiquitous constituent of the

oceans and atmosphere (both the troposphere and the stratosphere). It is a product of biomass combustion

and is also created from biogenic emissions by wood-rotting fungi. Chloromethane has been detected in

surface waters, drinking water, groundwater, and soil. Chloromethane is a constituent of municipal and

industrial solid waste leachate; it is a component of industrial waste discharges, and is also present in the

effluents of publicly owned treatment works (POTWs). It is an impurity in vinyl chloride (Zaidman et al.

199 l), so chloromethane could be released to the environment during the manufacture of vinyl chloride or

introduced into NPL sites from vinyl chloride wastes. Chloromethane in air has a half-life of about 1 year

(see Table 3-2) with various estimates in the range of 0.6-3 years (see Section 5.3.2.1 below).

Chloromethane is the dominant organochlorine species in the atmosphere. In the upper atmosphere,

chloromethane, through its sheer abundance, plays a role in chemical reactions that remove ozone from the

upper troposphere and stratosphere (Crutzen and Gidel 1983; Gidel et al. 1983; Singh et al. 1983). Since

these processes are believed to be largely part of natural background cycles, chloromethane has not been the

focus of ozone depletion control efforts under the Clean Air Act (CAA) and the Montreal Protocol, which

are targeted at such anthropogenic halogenated compounds as chlorofluorocarbons (EPA 1996b; FinlaysonPitts and Pitts 1986; IPCC 1995).

In water, chloromethane is expected to volatilize rapidly (Mabey and Mill 1978). It is not expected to sorb

to sediments or to bioconcentrate. Chemical hydrolysis and biodegradation are not expected to be

significant processes. In soil, chloromethane is expected to volatilize from the surface, but when present in a

landfill, it will probably leach into groundwater. In groundwater, hydrolysis may be the only removal

mechanism available to chloromethane, with an estimated half-life of ~4 years based on available data

CHLOROMETHANE 159

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(Elliott and Rowland 1995; Mabey and Mill 1978). Air concentrations of chloromethane are generally in

the low per billion range, but urban locations appear to have elevated concentrations compared to

background concentrations. Although detailed information is lacking, water concentrations are likely to

vary considerably depending on the season and the geographic location. Very little information is available

concerning chloromethane concentrations in soil. The general population is not expected to be exposed to

concentrations of chloromethane much above 3 ppb in urban locations. In rural locations, the exposure

concentration is expected to be ≈0.7-0.9 ppb. Occupational exposure to chloromethane may result in

exposures of ≈ 10 parts per million (ppm); however, the database for occupational exposure is outdated (late

1980s or earlier) and not sufficiently comprehensive to allow reliable predictions of average or probable

occupational exposure levels. The population with the highest potential exposures probably would include

those people who work in chloromethane manufacturing or use industries.

5.2 RELEASES TO THE ENVIRONMENT

According to the Toxics Release Inventory (TRI), in 1996, a total of 4,827,803 pounds (2,189,855 kg) of

chloromethane was released to the environment from 96 processing facilities (TRI96 1998). This total

consists of chloromethane released to air (4,457,775 pounds), water (803 pounds), soil (80 pounds), and via

underground injection (99,705 pounds). Table 5-l lists the amounts released to the environment by each

site. In addition, an estimated 9,758 pounds (4,426 kg) were released by manufacturing and processing

facilities to POTWs and an estimated 259,682 pounds (117,790 kg) were transferred off-site (TRI96 1998).

The TRI data should be used with caution because only certain types of facilities are required to report this

information. This is not an exhaustive list.

Chloromethane has been identified in a variety of environmental media (air, surface water, groundwater,

soil, and sediment) collected at 172 of the 1,467 current and former NPL hazardous waste sites (HazDat

1998).

5.2.1 Air

According to the TRI, in 1996, the estimated release of chloromethane of 4,457,775 pounds (2,022,013 kg)

into the air from at least 95 processing facilities accounted for about 92.3% of total anthropogenic

environmental releases (TRI96 1998). Table 5-l lists the amounts released from these facilities. The TRI



CHLOROMETHANE 163

5. POTENTIAL FOR HUMAN EXPOSURE

data should be used with caution, however, since only certain types of facilities are required to report this

information. This is not an exhaustive list.

Chloromethane has been identified in air samples collected at 16 of the 172 NPL hazardous waste sites

where it was detected in some environmental media (HazDat 1998).

Most releases of chloromethane will be to air, since it is a gas at ambient temperatures, and manufacturing

practices suggest that little will be discharged by any other route. Chloromethane discharged to water will

volatilize rapidly, based on the Henry’s law constant; however, the amount volatilized will vary depending

on a number of factors, including the temperature, turbulence, and depth of the receiving water.

Chloromethane will be released from manufacturing and use (fugitive emissions) as well as from production

resulting from human and natural activities. Chloromethane present in waste waters also may be released to

air during aeration (Pincince 1988). Release from all sources amounts to 7-18 billion pounds (3.2-8.2x109

kg) annually on a worldwide basis. Sources include the oceans, forest fires, burning wood, burning coal,

volcanoes, burning plastic (Chopra 1972; Crutzen et al. 1979; Edgerton et al. 1984, 1986; Edwards et al.

1982a, 1982b; Khalil et al. 1985; Kleindienst et al. 1986; Palmer 1976; Rasmussen et al. 1980; Singh et al.

1979, 1981a, 1981b, 1982, 1983; Tassios and Packham 1985; Yung et al. 1975), fungal activity (Fabian

1986; Harper 1985; Harper and Hamilton 1988; Harper et al. 1988), and release from some trees (Isidorov

et al. 1985). It is estimated that biomass burning in grasslands and forested areas accounts for about 20%

(range, 10-40%) of the total global budget of chloromethane, with emissions from the oceans making

another significant contribution (Rudolph et al. 1995). Various estimates of average global annual

production rates, and significantly different estimates of the contributions from different natural production,

sources have been made. Estimates from terrestrial ecologists tend to emphasize the role of such sources as

biomass burning, while oceanographers may emphasize the role of biogenic emissions from marine

phytoplankton. The global budget figures presented below are based on a study by Edwards et al. (1982b)

and are used primarily to emphasize the overwhelming contributions from nonindustrial production.

In comparison with an estimated total global budget of 7-18 billion pounds (3.2-8.2x109

 kg) annually,

1980 worldwide production of chloromethane was ≈ 794 million pounds (3.6x108

 kg) (Edwards et al.

1982b), of which ≈6% was released into the environment from production, storage, transport, and use

emissions (Edwards et al. 1982a; Singh et al. 1981a, 1981b). This amounts to worldwide releases of

47.6 million pounds (2.1x107

 kg) from manufacturing and use activities in 1980. U.S. production capacity
CHLOROMETHANE 164

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of chloromethane in 1995 was around 920 million pounds (417.3 million kg), with total releases to

environmental media estimated from the 1996 TRI at around 4.8 million pounds (2.2 million kg) (CMR

1995; TRI96 1998). Thus, well over 90% (perhaps up to 99%) of ambient air concentrations of

chloromethane on a global scale appear to come from releases from natural sources rather than from

manufacturing or other emissions from anthropogenic processes or uses. Releases associated with

manufacturing and production processes in the United States would constitute less than 1% of the global

budget.

Typical estimates for the natural background concentrations of chloromethane in ambient air are ≈1 ppb

(Harper et al. 1990). Chloromethane concentrations are often in excess of rural background concentrations

in the ambient air of cities in the United States (Singh et al. 1982, 1983) (see Section 5.1). The authors

suggested that this elevation may be the result of manufacturing or other anthropogenic emission sources in

the urban areas, over and beyond releases from combustion or other background sources that would

determine the levels in more rural areas. Other than data from the TRI or rough estimates based on global

budgets, no studies were identified that attempt to make quantitative estimates for natural or anthropogenic

releases of chloromethane to the air in the United States.

5.2.2 Water

According to the TRI, in 1996, there were estimated releases of chloromethane of 803 pounds (364 kg) to

water from 15 documented processing facilities. These releases accounted for less than 0.1% of total

anthropogenic environmental releases (TRI96 1998). Table 5-l lists the amounts released from these

facilities. The TRI data should be used with caution, however, since only certain types of facilities are

required to report this information. This is not an exhaustive list.

Chloromethane is released into the water from a number of sources, including industrial discharges and

effluents from municipal waste treatment plants, but insufficient information is available to quantify the

releases. During the manufacture of chloromethane, process water contacts the reaction mixtures (see

Section 4.1) (Edwards et al. 1982a; Key et al. 1980). This water is stripped during manufacture and

treatment to remove most of the dissolved chloromethane and then discharged (some chloromethane

manufacturing plants use the process water on-site as a source of dilute hydrochloric acid [HCl] rather than

discharging it). Data regarding the use and fate of process water in use applications were not found in the

available literature; however, spent process water is probably treated (including aeration) prior to discharge.
CHLOROMETHANE 165

5. POTENTIAL FOR HUMAN EXPOSURE

Nonetheless, chloromethane has been found in waste water effluents, possibly as a result of its formation

(Coleman et al. 1976; Gould et al. 1983) or incomplete removal during industrial waste water treatment

(Snider and Manning 1982). Chloromethane has been detected in the leachate of both municipal (Gould et

al. 1983; Sabel and Clark 1984) and hazardous waste landfills (Brown and Donnelly 1988; Kosson et al.

1985; Venkataramani et al. 1984). Chloromethane has been identified in 21 surface water and 100

groundwater samples collected at the 172 NPL hazardous waste sites where it was detected in some

environmental media (HazDat 1998).

5.2.3 Soil

According to the TRI, in 1996, the estimated release of chloromethane of 80 pounds (36.3 kg) to soil from

four processing facilities accounted for less than 0.1% of total anthropogenic environmental releases (TRI96

1998). Table 5-l lists the amounts released from these facilities. The TRI data should be used with

caution, however, since only certain types of facilities are required to report this information. This is not an

exhaustive list.

Chloromethane is probably released into the soil during the landfilling of sludges and other wastes (e.g., still

bottoms) generated from industrial processes and municipal sewage treatment; however, no specific

information concerning chloromethane-containing wastes was located in the literature. Chloromethane has

been detected in the leachate of both municipal (Sabel and Clark 1984) and hazardous waste landfills

(Brown and Donnelly 1988; Kosson et al. 1985; Venkataramani et al. 1984), indicating that disposal of

these materials apparently results in contamination of soils. Chloromethane has been identified in 34 soil

and 13 sediment samples collected at the 172 NPL hazardous waste sites where it was detected in some

environmental media (HazDat 1998).

5.3 ENVIRONMENTAL FATE

5.3.1 Transport and Partitioning

Most chloromethane discharged into the environment will be released into the air, where it will be subjected

to transport and diffusion into the stratosphere (Singh et al. 1979, 1982, 1983). The relatively uniform

concentration of chloromethane in the northern and southern hemispheres (Singh et al. 1979, 1982, 1983)

indicates its widespread distribution and the importance of transport processes in its distribution. The water
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5. POTENTIAL FOR HUMAN EXPOSURE

solubility of chloromethane is high enough that small amounts may be removed from the atmosphere by

precipitation; however, no information confirming this environmental pathway was located in the literature.

The dominant transport process from water will be volatilization. The results of two EXAMS model runs

and the value of the Henry’s law constant (calculated from the solubility and the vapor pressure) suggest that

volatilization will be significant in surface waters. EXAMS is an environmental model that predicts the

behavior of a chemical in surface waters. Using the code test data for a pond developed by the Athens

Environmental Research Laboratory of the EPA, the half-life for volatilization was calculated to be

2.5 hours. For a lake, the half-life was calculated to be 18 days. Input data included the molecular weight,

the vapor pressure, Henry’s law constant, the octanol/water partition coefficient, the sediment sorption

coefficient, and the water solubility. The volatilization rates predicted by the EXAMS model appear to be in

agreement with the observation of Lurker et al. (1983) who reported chloromethane concentrations in waste

water and in the air above the waste water at the Memphis North Wastewater Treatment Plant in Memphis,

Tennessee. Based on the log octanol/water partition coefficient (Hansch and Leo 1985) and the sorption

coefficient and BCF calculated from it (see Table 3-2), chloromethane is not expected to concentrate in

sediments or in biota.

In soil, the dominant transport mechanism for chloromethane present near the surface probably will be

volatilization (based on its Henry’s law constant, water solubility, and vapor pressure), but no experimental

information was located in the literature to confirm this. The actual volatilization rate for a chemical in soil

is influenced by a number of factors, including surface roughness, soil type, rainfall, leaching, depth of

incorporation, temperature, and ground cover (Jury et al. 1987). Since chloromethane is not expected to

sorb to soils, any chloromethane present in lower layers of the soil will be expected to leach to lower

horizons as well as to diffuse to the surface and volatilize. The presence of chloromethane in groundwater

confirms the importance of leaching as a transport route (Greenberg et al. 1982c; Jury et al. 1987; Page

1981).
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5. POTENTIAL FOR HUMAN EXPOSURE

5.3.2 Transformation and Degradation

5.3.2.1 Air

The dominant tropospheric removal mechanism for chloromethane is generally thought to be hydrogen

abstraction by hydroxyl radical (Dilling 1982; Fabian 1986; Gusten et al. 1984; Lovelock 1975; Rasmussen

et al. 1980; Robbins 1976; Singh et al. 1979). The hydroxyl radical reaction with chloromethane has been

experimentally determined in a number of studies (Butler et al. 1978; Cox et al. 1976; Davis et al. 1976a;

Howard and Evenson 1976; Jeong and Kaufman 1980, 1982; Jeong et al. 1984; Paraskevopoulos et al.

1981; Perry et al. 1976). The data of Howard and Evenson (1976) (discharge flow-laser magnetic

resonance), Perry et al. (1976) (flash photolysis-resonance fluorescence), Davis et al. (1976a) (flash

photolysis-resonance fluorescence), Paraskevopoulos et al. (1981) (flash photolysis-resonance adsorption),

and Jeong and Kaufman (1980, 1982) (discharge flow-resonance fluorescence) are in agreement (Atkinson

1985; NASA 1981).

Using the measured rate constants for the chloromethane reaction with hydroxyl radicals, several

researchers have made estimates of tropospheric total lifetimes or half-lives (Crutzen and Gidel 1983;

Dilling 1982; Fabian 1986; Khalil and Rasmussen 1981; Singh et al. 1979). The various half-life estimates

are in the neighborhood of 1 year (see Table 3-2), with values ranging from 0.6 to 3 years. The differences

in the estimated half-lives are associated mainly with differences in assumptions on the levels of hydroxyl

free radical concentrations in the upper troposphere.

5.3.2.2 Water

In water, chloromethane can degrade by hydrolysis or by biodegradation. Although few data are available

on the biodegradation of chloromethane in water, neither hydrolysis nor biodegradation in surface waters

appears to be rapid when compared with volatilization. Chloromethane hydrolysis proceeds via an SN2

mechanism (bi-molecular) in which no intermediate ions are formed, and methanol and HCl are the only

products. The kinetics of chloromethane hydrolysis have been measured by Heppolette and Robertson

(1959) and Laughton and Robertson (1956) by bubbling chloromethane into water and following the

reaction by measuring the conductance of the water. The rate constant for hydrolysis of chloromethane at

50 °C was reported to be 7.6x10-7 sec-1, with a half-life of 10.6 days. When extrapolated to 20 °C and

neutral conditions using the thermodynamic constants calculated by Heppolette and Robertson (1959), a rate
CHLOROMETHANE 168

5. POTENTIAL FOR HUMAN EXPOSURE

constant was calculated of 1.04x10-8 sec-1 with a half-life of ≈ 2.1 years. More recent hydrolysis data from

Elliot and Rowland (1995) are in good agreement with the estimates of Mabey and Mill (1978) and the

measurements of Zafiriou (1975). Actual measurements conducted at 22 and 9 °C in pure water, sea water,

and salt solution yield the same values of k (not listed), from which the Arrhenius relation was derived:

k(in s-1)=9.5x1010e

-12,800/T. This relation was used to estimate the values at 25 and 15 °C given in Table 3-2.

These rates are expected to be unaffected by pH ranges normally encountered in the environment (Mabey

and Mill 1978). The hydrolysis half-lives are too long to be of environmental significance in surface waters,

considering the rapid volatilization of chloromethane from surface water (Mabey and Mill 1978). In

groundwater, however, hydrolysis may be the only degradation mechanism available and, hence, may be a

more significant factor. Biodegradation may also occur in groundwater, but rates are thought to be highly

variable.

Very little information is available concerning the biodegradation of chloromethane in water. In studies

involving such bacteria as Methylococcus capsulatus, formaldehyde was a product of chloromethane

biodegradation (Stirling and Dalton 1979). In pure culture conditions, some microbial strains can degrade

chloromethane. Hartmans et al. (1986) reported that pure cultures of a Hyphomicrobium sp. were obtained

with a chloromethane-minima1 medium. Abiotic hydrolytic dehalogenation was not significant, so that the

observed cell growth and chloride formation confirmed biodegradation as the predominant transformation

process (Hartmans et al. 1986). Since these laboratory conditions do not commonly occur in the

environment, these same species may not degrade chloromethane in the environment to any significant

degree. Biodegradation of chloromethane, however, cannot be ruled out based on the available information.

As with reactions of other chloroalkanes, chloromethane may degrade anaerobically via reductive

dechlorination to form methane (Vogel et al. 1987).

5.3.2.3 Sediment and Soil

Very limited information concerning soil transformation and degradation of chloromethane was located in

the literature. In lower soil horizons, hydrolysis may be the only relevant abiotic process since no other nonbiological removal mechanisms have been identified. Biological processes, especially from some fungi, can

release chloromethane (Fabian 1986; Harper 1985; Harper and Hamilton 1988; Harper et al. 1988).

Research also suggests that members of the so-called white rot fungus family may degrade (mineralize)

chloromethane (Harper et al. 1990). These same fungi (especially Phanerochaete chrysosporium) can also

dehalogenate aliphatic halocarbons such as chloroform, dichloromethane, and carbon tetrachloride
CHLOROMETHANE 169

5. POTENTIAL FOR HUMAN EXPOSURE

(Khindaria et al. 1995) possibly forming chloromethane as an intermediate product that, in turn, could be

further dehalogenated.

Doronina et al. (1996) isolated eight strains of non-methane-utilizing bacteria that are able to grow on

chloromethane as the carbon and energy source. The new isolates were classified as Hyphomicrobium spp.

(strains CMl, CM2, CM9, CM29,CM35) and Methylbacterium spp. (strains CM4, CM30, CM34). All

strains possessed an inducible but unknown enzyme that catalyzed the conversion of chloromethane to HCI

and formaldehyde. The formaldehyde was oxidized via formate to CO2 or assimilated through icl+

 or iclvariants of the serine pathway. Vanelli et al. (1998) found that Methylobacterium sp. (strain CM4)

metabolized chloromethane quantitatively with a molar yield of 2.8 g of whole-cell protein/mol of C. Based

on the protein yield data and the properties of the transposon mutants, they proposed a pathway for

chloromethane metabolism that depends on methyltransferase and dehydrogenase activities.

Under anaerobic conditions as encountered in deeper soil profiles or in many sediments, a bacterial strain

called MC isolated from municipal anaerobic digester sludge flora seems capable of metabolizing

chloromethane into acetate (Messmer et al. 1993; Zitomer and Speece 1995). It is not clear, however, that

such anaerobic biodegradation processes are common around waste sites with chloromethane site

contamination. The biochemistry of chloroaliphatics degradation in the newer aerobic isolates is largely

unexplored, but progress has been made in understanding some of the anaerobic dehalogenation reactions

(Leisinger 1996).

5.4 LEVELS MONITORED OR ESTIMATED IN THE ENVIRONMENT

Reliable evaluation of the potential for human exposure to chloromethane depends in part on the reliability

of supporting analytical data from environmental samples and biological specimens. In reviewing data on

chloromethane levels monitored or estimated in the environment, it should also be noted that the amount of

chemical identified analytically is not necessarily equivalent to the amount that is bioavailable.

5.4.1 Air

Chloromethane has been the subject of numerous studies conducted to determine the atmospheric chloride

balance. In the development of a database for ambient air monitoring, more than 242 sites in the United

States were monitored for chloromethane during a 5-year period (Eichler and Mackey 1986).



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5. POTENTIAL FOR HUMAN EXPOSURE

In accordance with provisions of the Clean Air Act Amendments (CAAAs) of 1990, chloromethane (or

methyl chloride) was among 189 compounds designated as hazardous air pollutants (HAPS). Aside from the

public health impacts from direct exposures to these chemicals, most of the HAPS are VOCs that, in

combination with other air pollutants, can lead to the formation of ozone and photochemical smog. The

EPA has collected available ambient measurements to compile an HAP database (Kelly et al. 1994). This

database adds monitoring information to earlier databases that focused on VOCs. The national median

ambient air concentration from the HAP database for chloromethane is 1.3 μg/m3

 (629 ppt [v/v]).

5.4.2 Water

Chloromethane has been detected in surface water, groundwater, drinking water, municipal and hazardous

waste landfill leachate, and industrial effluents (Table 5-3). When detected, concentrations appear to be in

the ppb-ppt range, possibly due to the rapid volatilization of chloromethane. Chloromethane apparently is

formed during the chlorination of drinking water. It was 1 of 13 compounds found in the drinking water of

all five cities (Philadelphia, Pennsylvania; Miami, Florida; Seattle, Washington; Ottumwa, Iowa; and

Cincinnati, Ohio) studied as part of the EPA National Organics Reconnaissance Survey (NORS) (Coleman

et al. 1976). Most of the compounds detected were reported to be highly specific to the locality and raw

water supply. Those compounds found in all supplies studied may be widespread.

No specific information concerning sources of chloromethane in fresh surface water was located in the

literature. Chloromethane concentrations in surface water may be the result of rain as well as human

activity (e.g., industrial effluents, chlorinated secondary effluent from POTWs). Industrial effluents may be

a significant source. Seven positive detections of chloromethane in industrial effluents out of more than

4,000 samples from 46 industrial categories and subcategories were reported in the EPA database (Bursey

and Pellizzari 1982). Concentrations ranged from 6 to 4,194 mg/L in these effluents. Thirty-four species of

fungi can produce chloromethane biosynthetically (Harper et al. 1988). The presence of these fungi near

lakes and streams may be a source of chloromethane. The significance of this source to surface water,

however, cannot currently be estimated.

In a study of groundwater samples from 479 active waste disposal sites, chloromethane was detected at 20

of these sites (Plumb 1991). Information from HazDat (1998) documents at least 100 current or past NPL

sites with detections in groundwater. There is virtually no reporting of actual concentration values or ranges

for groundwater detections in the available literature. The presence of chloromethane in groundwater may


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5. POTENTIAL FOR HUMAN EXPOSURE

result from both natural and anthropogenic sources. Since chloromethane has been detected in the

groundwater near municipal waste sites containing the chemical (Sabel and Clark 1984), waste deposits of

chloromethane on land may lead to groundwater contamination. Chloromethane appears to be a constituent

of both municipal and industrial waste landfills. In these landfills, volatilization may be hindered and

leaching to groundwater could become an important transport pathway. Chloromethane may also be a

product from the anaerobic metabolism of higher chlorinated methanes present in the soil (Vogel et al.

1987).

5.4.3 Sediment and Soil

Information from HazDat (1998) documents the presence of chloromethane in soils at 34 waste sites and in

sediments at 13 waste sites. Information on background levels in soils and sediments is very limited in the

available literature. The only information located in the literature concerning the presence of chloromethane

in soil was the natural formation of chloromethane by a number of fungi (Harper et al. 1988) and its

presence in both landfill leachate and groundwater.

5.4.4 Other Environmental Media

As presented in Section 5.2.1, chloromethane is released from wood smoke, burning coal, volcanoes, and

burning plastic (Chopra 1972; Crutzen et al. 1979; Edgerton et al. 1984, 1986; Fabian 1986; Kadaba et al.

1978; Khalil et al. 1985; Kleindienst et al. 1986; Palmer 1976; Rasmussen et al. 1980; Singh et al. 1982;

Tassios and Packham 1985). Palmer (1976) suggested that 1 cm3 of chloromethane gas (2.2 mg) was

produced for each gram of cellulose burned (glowing combustion). Concentrations of chloromethane in

smoke from combustion processes, however, are highly variable and depend on both the fuel (i.e., the

amount of inorganic chlorine present in the fuel) and the temperature of the bum. Thus, quantification of

chloromethane in these media will be representative of the specific source and the exact conditions of the

burn rather than of general emission levels. Chloromethane has not been detected in auto exhaust (detection

limit of 1 ppm) (Hasanen et al. 1979).

Chloromethane was present in the expired air of all 3 tested groups of 62 nonsmoking adults, including a

control, a prediabetic, and a diabetic group (Krotoszynski and O’Neill 1982). Since chloromethane is a

ubiquitous constituent of air, it is reasonable that it would be found in the expired air of virtually all
CHLOROMETHANE 177

5. POTENTIAL FOR HUMAN EXPOSURE

humans. The chlorine solutions used to chlorinate drinking water did not contain chloromethane, but other

higher chloromethanes were present (Otson et al. 1986).

5.5 GENERAL POPULATION AND OCCUPATIONAL EXPOSURE

Chloromethane is a ubiquitous low-level constituent of air and is probably found at very low concentrations

in many drinking water supplies that have used chlorine treatment for disinfection. As such, the general

population will be exposed to low background levels at all times, while those living in urban centers may be

exposed to slightly higher levels.

According to one report, persons living in Los Angeles, California; Phoenix, Arizona; and Oakland,

California; would have daily intakes of ≈ 140.4, 108.6, and 59.7 μg/day, respectively (Singh et al. 1981a),

based on a total respirable air volume of 23 m3

/day at 25 °C and 1 atm pressure. Using the data of Shah

and Singh (1988) for remote, rural, suburban, and urban air masses, daily intakes are estimated to be = 31,

40, 28, and 35 μg/day, respectively. The intakes for rural and remote air masses are based on very small

sample sizes and may be inaccurate. Dermal exposure and exposures from drinking water containing

chloromethane are more difficult to estimate from the available information. Drinking water concentrations

are not well described in the literature and may vary considerably both seasonally and geographically.

Historically (30 years ago or longer), large exposures could have been associated with leaking refrigerators

that used chloromethane as a refrigerant. While refrigeration-grade chloromethane may still be available, it

is not known whether it is currently used to any significant degree in refrigeration equipment. Without this

information, potential exposures cannot be estimated.

Chloromethane is an impurity in vinyl chloride when the vinyl chloride is produced from the thermal

dehydrochlorination of 1,2-dichloroethane (Zaidman et al. 1991). Exposures to chloromethane could take

place during the manufacture of vinyl chloride or when vinyl chloride wastes have been released to the

environment or to waste sites. Information is lacking to make any firm estimates of such exposure

potentials. Of the 172 current or past NPL sites in HazDat (1998) showing site contamination with

chloromethane, 128 of these sites (about 75%) also showed site contamination related to vinyl chloride.

Current and empirically based estimates of exposures to chloromethane in various occupations are lacking.

Some insights can be gleaned from the National Institute for Occupational Safety and Health’s (NIOSH’s)
CHLOROMETHANE 178

5. POTENTIAL FOR HUMAN EXPOSURE

National Occupational Hazard Survey (NOHS) database (the NOHS database is also called the National

Occupational Exposure Survey or NOES database) that estimates the number of potentially exposed

workers in a variety of manufacturing jobs (Sieber et al. 1991). Based on conditions typical of the mid1970s it was estimated that 39,343 workers had potential exposures to chloromethane (NOES 1991). The

majority of these potential exposures involved occupations where chloromethane could have been used as a

cleaner or pest control fumigant. There is virtually no mention in NOHS of current applications such as use

as a process chemical in the manufacture of silicone rubbers. While the NOHS data are of some historical

value, it is therefore doubtful whether they accurately reflect the potential number of workers subject to

current occupational exposures. A number of regulations, however, are in place to protect workers from

exposure to levels of chloromethane that are considered harmful.

5.6 EXPOSURES OF CHILDREN

This section focuses on exposures from conception to maturity at 18 years in humans and briefly considers

potential pre-conception exposure to germ cells. Differences from adults in susceptibility to hazardous

substances are discussed in Section 2.6, Children’s Susceptibility.

Children are not small adults. A child’s exposure may differ from an adult’s exposure in many ways.

Children drink more fluids, eat more food, and breathe more air per kilogram of body weight, and have a

larger skin surface in proportion to their body volume. A child’s diet often differs from that of adults. The

developing human’s source of nutrition changes with age: from placental nourishment to breast milk or

formula to the diet of older children who eat more of certain types of foods than adults. A child’s behavior

and lifestyle also influence exposure. Children crawl on the floor; they put things in their mouths; they may

ingest inappropriate things such as dirt or paint chips; they spend more time outdoors. Children also are

closer to the ground, and they do not have the judgement of adults in avoiding hazards (NRC 1993).

Children are members of the general population and encounter the same exposures that are described in

Section 5.5. No data were found on the measurement of chloromethane or its metabolites in amniotic fluid,

meconium, cord blood, or neonatal blood that would indicate prenatal exposure. It is not known whether

chloromethane in the body can cross the placenta and enter into the developing young. Since chloromethane

is broken down and eliminated from the body quickly in adults, it is unlikely that chloromethane would be

stored in maternal tissues or mobilized during pregnancy or lactation. Chloromethane was present in 2 of 8

samples of mothers’ milk from Bayonne and Jersey City, New Jersey; Bridgeville, Pennsylvania; and Baton
CHLOROMETHANE 179

5. POTENTIAL FOR HUMAN EXPOSURE

Rouge, Louisiana (Pellizzari et al. 1982). No concentrations were reported and no information was given

concerning the source of the chloromethane in the milk.

The levels that children could be exposed to through accidents involving chloromethane may be higher than

levels affecting adults because chloromethane is heavier than air (i.e., greater concentrations near the

ground).

Parents can inadvertently carry certain hazardous materials home from work on their clothes, skin, hair,

tools and in their vehicles. However, since chloromethane is so volatile, it is unlikely that children would be

exposed by this route. No incidents of home contamination by chloromethane were reported in the Workers’

Home Contamination Study conducted under the Workers’ Family Protection Act (29 U.S.C. 671a) (DHHS

1995).

5.7 POPULATIONS WITH POTENTIALLY HIGH EXPOSURES

All humans are probably exposed to low concentrations of chloromethane. Those with potentially higher

than average exposures include workers employed in the manufacturing and use (by analogy) industries. In

addition to individuals occupationally exposed to chloromethane (see Section 5.5), there are several groups

within the general population that could have exposures higher than background levels. These populations

include individuals living in proximity to sites where chloromethane was produced or disposed, and

individuals living near one of the 172 NPL hazardous waste sites where chloromethane has been detected in

some environmental media (HazDat 1998). Chloromethane may also be a constituent in other materials

such as vinyl chloride. Chloromethane exposure risks may be of concern to individuals working or living in

the vicinity of sites where vinyl chloride was produced or where there is evidence vinyl chloride has been

disposed.

People with very old refrigeration equipment in which chloromethane is used as a refrigerant are a

population with potentially very high exposures. These refrigerators can leak and result in very high local

air concentrations of chloromethane. This population is, however, likely to be small since the number of

refrigerators using chloromethane has been decreasing.
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5. POTENTIAL FOR HUMAN EXPOSURE

5.8 ADEQUACY OF THE DATABASE

Section 104(i)(5) of CERCLA, as amended, directs the Administrator of ATSDR (in consultation with the

Administrator of EPA and agencies and programs of the Public Health Service) to assess whether adequate

information on the health effects of chloromethane is available. Where adequate information is not

available, ATSDR, in conjunction with the NTP, is required to assure the initiation of a program of research

designed to determine the health effects (and techniques for developing methods to determine such health

effects) of chloromethane.

The following categories of possible data needs have been identified by a joint team of scientists from

ATSDR, NTP, and EPA. They are defined as substance-specific informational needs that if met would

reduce the uncertainties of human health assessment. This definition should not be interpreted to mean that

all data needs discussed in this section must be filled. In the future, the identified data needs will be

evaluated and prioritized, and a substance-specific research agenda will be proposed.

5.8.1 Identification of Data Needs

Physical and Chemical Properties. Data regarding physical and chemical properties are essential

for estimating the partitioning of a chemical in the environment. Most of the necessary data on physical and

chemical properties are available for chloromethane, and many of these have experimental descriptions

accompanying them so that accuracy can be evaluated. The data on known physical and chemical

properties form the basis of many of the input requirements for environmental models that predict the

behavior of a chemical under specific conditions including hazardous waste landfills.

Production, Import/Export, Use, Release, and Disposal. Production methods for chloromethane

are well-described in the literature (including the patent literature) and there does not appear to be a need for

further information. Uses of chloromethane have been documented, although a detailed description of all

uses is not available. This information is useful for estimating the potential for environmental releases from

manufacturing and use industries as well as the potential environmental burden; however, it is difficult to

obtain this information in the detail desired since generally it is considered to be confidential business

information (CBI) for those industries that manufacture chloromethane. Release information, which can be

used to estimate environmental burdens and potentially exposed populations, is also not obtained easily.
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5. POTENTIAL FOR HUMAN EXPOSURE

According to the Emergency Planning and Community Right-to-Know Act of 1986,42 U.S.C. Section

11023, industries are required to submit chemical release and off-site transfer information to the EPA. The

Toxics Release Inventory (TRI), which contains this information for 1996, became available in May of

1998. This database will be updated yearly and should provide a list of industrial production facilities and

emissions.

Environmental Fate. The fate of chloromethane in air is well-described because extensive air

photolysis and photo-oxidation studies are available that characterize these processes. Biodegradation

studies in surface water and groundwater are not as complete. These kinds of studies are important because

they would provide information about fundamental removal mechanisms for chloromethane in the

environment and might aid in understanding the behavior of chloromethane at hazardous waste sites or

municipal landfills. The vapor pressure of chloromethane and its presence in groundwater suggest that these

processes are important, particularly at hazardous waste sites, and may account for some of the losses of

chloromethane from the site. Limited research suggests that common soil fungi may be able to generate

chloromethane as well as to dehalogenate, and thus degrade, it. Since these wood rot fungi can also break

down other halogenated aliphatic compounds, there is the possibility that some of the chloromethane found

at waste sites could have been produced through the action of such fungi on other waste compounds. More

research is needed to document the importance of these biodegradation mechanisms and to determine

whether the net effects tend toward a progressive reduction in the levels of chloromethane found in

contaminated soils and sediments at waste sites.

Bioavailability from Environmental Media. Experimental inhalation studies in animals and humans

indicate that chloromethane is bioavailable from the atmosphere. Studies for the oral and dermal routes of

exposure may be of lesser research importance than studies on inhalation pathways and the bioavailability of

chloromethane from water, soil, and other environmental media.

Food Chain Bioaccumulation. The log Kow for chloromethane is in the range of 0.91 to 1.086 (see

Chapter 3, Table 3-2). Such low values generally mean that the BCF will be low, suggesting that

chloromethane will not tend to concentrate in aquatic organisms. However, no information was identified on

experimental determinations of BCF levels for chloromethane. Determinations of BCF values for

organisms at various trophic levels are needed to estimate human dietary intake of chloromethane.
CHLOROMETHANE 182

5. POTENTIAL FOR HUMAN EXPOSURE

Exposure Levels in Environmental Media. Extensive environmental monitoring data are available

for chloromethane in air, while the available data are very limited for drinking water, surface water, and

groundwater. The air monitoring data describe the concentrations that populations are exposed to through

inhalation of ambient air. The data for water are not sufficient to accurately characterize the concentrations

of chloromethane present in drinking water, surface water, or groundwater. Almost no data are available for

soils. These data are needed to determine the ambient concentrations of chloromethane so that exposure of

the general population as well as of terrestrial and aquatic organisms can be estimated.

Reliable monitoring data for the levels of chloromethane in contaminated media at hazardous waste sites are

needed to assess the potential risk of adverse health effects in populations living in the vicinity of hazardous

waste sites.

Exposure Levels in Humans. The database for chloromethane exposure levels in humans is limited to

determinations of chloromethane in breast milk. A more complete database is needed to determine the

current exposure levels and to estimate the average daily dose associated with various scenarios (e.g., living

near a hazardous waste site). An environmental media monitoring program may provide the necessary

information for estimating environmental exposures, while workplace monitoring at use sites, using personal

dosimeters and remote sensing devices, would probably provide useful workplace information. The

available NOES database of potential occupational exposures was assembled in the late 1980s and is

becoming outdated. An update to this statistically based database of potential occupational exposures is

needed.

Exposures of Children. Chloromethane was present in 2 of 8 samples of mothers’ milk from Bayonne

and Jersey City, New Jersey; Bridgeville, Pennsylvania; and Baton Rouge, Louisiana (Pellizzari et al. 1982).

No concentrations were reported and no information was given concerning the source of the chloromethane

in the milk. Studies to determine current chloromethane residues and sources in breast milk of women in the

general population and in the work force are needed. Well water surveys should be conducted in areas near

landfills where chloromethane has been detected at significant levels. Ingestion of chloromethanecontaminated

drinking water could be an important route of exposure in children.

Current information on whether children are different in their weight-adjusted intake of chloromethane via

oral and dermal exposures was not available. A study to determine this information is needed.
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5. POTENTIAL FOR HUMAN EXPOSURE

Exposure Registries. An exposure registry for chloromethane is not available. The development of a

registry of exposures is needed to assess exposure levels and frequency. In addition, a registry would allow

assessment of variations in exposure resulting from such variables as geography, season, regulatory actions,

presence of hazardous waste landfills, or presence of manufacturing and use facilities.

Although chloromethane is not currently one of the compounds for which a subregistry has been established

in the National Exposure Registry, it will be considered in the future. The information that is amassed in the

National Exposure Registry facilitates the epidemiological research needed to assess adverse health

outcomes that may be related to exposure to this substance.

5.8.2 Ongoing Studies

A project carried out at Cambridge Analytical Associates, Inc., under the direction of Dr. Samuel Fogel with

NSF support will study the biodegradation of chlorinated aliphatic compounds by methane-utilizing bacteria

(FEDRIP 1998).

CHLOROMETHANE 185

6. ANALYTICAL METHODS

The purpose of this chapter is to describe the analytical methods that are available for detecting, and/or

measuring, and/or monitoring chloromethane, its metabolites, and other biomarkers of exposure and effect to

chloromethane. The intent is not to provide an exhaustive list of analytical methods. Rather, the intention is

to identify well established methods that are used as the standard methods of analysis. Many of the

analytical methods used for environmental samples are the methods approved by federal agencies and

organizations such as EPA and the National Institute for Occupational Safety and Health (NIOSH). Other

methods presented in this chapter are those that are approved by groups such as the Association of Official

Analytical Chemists (AOAC) and the American Public Health Association (APHA). Additionally,

analytical methods are included that modify previously used methods to obtain lower detection limits, and/or

to improve accuracy and precision.

6.1 BIOLOGICAL SAMPLES

Methods used to analyze biological samples for chloromethane are summarized in Table 6-1. S-methylcysteine may be a urinary metabolite of chloromethane in some humans (Nolan et al. 1985; van Doorn et al.

1980). S-methylcysteine can be analyzed by diluting urine with water and treating the resulting solution

with a buffer and a phthaldialdehyde solution to derivatize the S-methylcysteine (DeKok and Antheunius

1981) Analysis is performed on a reversed-phase high-performance liquid chromatography (HPLC) column

using methanol and sodium hydrogen phosphate buffer gradient elution with a fluorescence detector. The

reported detection limit is 1 mg/L. S-methylcysteine, along with other methylthio- compounds, can also be

analyzed as methanethiol following alkaline hydrolysis and acidification (van Doom et al. 1980).

Breast milk was analyzed for chloromethane by expressing a 60 mL sample into a wide-mouth bottle and

then freezing until analysis (Pellizzari et al. 1982). Analysis was performed by warming the sample and

then purging it with helium and directing the chloromethane and other volatilized compounds through a

Tenax adsorbant. The analytes were thermally desorbed from the Tenax onto a gas chromatography (GC)

column and analyzed by mass spectrometry (MS). No recovery or accuracy information was reported. A

headspace analysis for chloromethane in blood has been described (Landry et al. 1983a) as has a method for

chloromethane in exhaled air (Nolan et al. 1985). No limits of detection (LODs) or recovery information

were available for these methods.

CHLOROMETHANE 187

6. ANALYTICAL METHODS

6.2 ENVIRONMENTAL SAMPLES

Methods for the determination of chloromethane in environmental samples are presented in Table 6-2. In

air, chloromethane can be analyzed by NIOSH Method 1001 (NIOSH 1994). This method involves drawing

a 0.4-3 L sample through a coconut charcoal tube followed by methylene chloride desorption and analysis

by GC with flame ionization detection (FID). The method has a working range of 66-670 mg/m3

 for a

1.5 L sample and an LOD of 0.01 mg/tube. The method of Oliver et al. (1996) also uses a preconcentration

approach, but analyte recovery is accomplished via thermal desorption. The large sample concentration

factor combined with the sensitivity of the ion trap detector (ITD) provides for an LOD of less than 1 ppb.

Chloromethane can also be trapped cryogenically from an aliquot of air collected into an evacuated canister

followed by determination using GC with either electron capture or mass spectrometric detection (EPA

19888). LODs were reported to be in the low ppb range. Loss of chloromethane from air samples stored in

canisters can impact the accuracy of the determination. Kelly and Holdren (1995) reported a 17% loss for

chloromethane at 2.1 ppb stored for 33 days. On the other hand, Brymer et al. (1996) showed a loss of

approximately 5% over a 30-day period for chloromethane in a canister at 2.3 ppb (v/v). They also

reported a method detection limits of 0.82 ppbv and a recovery of 124%. Potential changes in analyte

concentration as function of time after sample collection indicates that field control samples should be used.

Field controls are always appropriate regardless of the collection approach used. Fukui and Doskey (1996)

reported using a canister-based approach to collect chloromethane and other volatile compounds emitted

from grasslands. Extreme care must be taken, especially at very low air concentrations, to ensure that no

contamination is introduced into the sampling and analysis method; method blanks must always be used to

verify the cleanliness of the sample collection and analysis system.

Chloromethane can be analyzed in municipal and industrial waste water by EPA Test Method 601-

Purgeable Halocarbons or EPA Test Method 624Purgeables (EPA 1982a). Both methods are adequate for

measuring chloromethane in waste waters. However, care must be exercised during sample collection

because chloromethane is volatile and some of the chemical might be lost during the sampling process.

Method 601 involves purging the sample with an inert gas and passing the gas through a trap containing

2,6-diphenylene oxide polymer (Tenax GC), silica gel, and coconut charcoal to adsorb the purged

chloromethane and other halocarbons (called the “purge and trap” method). After the purging is complete,

the trap is heated to desorb the chloromethane. The desorbed chloromethane is analyzed by GC using an

electrolytic conductivity (EC) or microcoulometric detector. Method 624 is similar to Method 601, but the

trap material is made of 3% methyl silicone (OV-1) on packing material, 2,6-diphenylene oxide polymer


CHLOROMETHANE 190

6. ANALYTICAL METHODS

(Tenax GC), and silica gel; analysis is made by GC/MS. Overpurging the sample may result in loss of

some chloromethane. The average recovery from reagent water and effluents was 91.4±13.4% for Method

601 and 99±24% from waste water for Method 624. The Contract Laboratory Program analytical method

involves screening the sample for component concentrations by rapidly transferring the room temperature

sample to a volumetric flask; adding hexadecane; extracting the volatiles, including chloromethane, for

1 minute; and then qualitatively analyzing the sample by GC/FID (EPA 1988a). The quantitative analysis

method for the sample is by GC/MS and is essentially identical to EPA Method 624 (EPA 1982a).

Three additional purge-and-trap approaches with LODs as low as 0.01 μg/L (0.01 ppb) have also been

described for drinking water: Standard Method 6210D (Greenberg et al. 1992a), Method 502.1 (EPA

1989a), and Method 524.2 (EPA 1989b). A purge-and-trap approach to the determination of chloromethane

in an aqueous culture medium provided an LOD of 0.35 ppt (Tait and Moore 1995). A technique known as

solid-phase microextraction (SPME) has been demonstrated to be applicable to low ppb chloromethane

concentrations in a water matrix (Shirey 1995). In this method, a polymer-coated fiber is equilibrated in a

water sample until the chloromethane partitions into the polymer coating. The fiber is withdrawn and

inserted into the hot injection port of a GC, where the analyte is thermally desorbed onto the GC column.

EPA Method 5030 for analysis of chloromethane in soil and solid waste (EPA 1986b) involves the direct

purge-and-trap method for low-level samples or the methanolic extraction for high-level samples, based on a

hexadecane extraction as described above. For low-level samples, the soil and solid waste are placed in a

purge impinger, mixed with water, purged with an inert gas, and trapped on a Tenax GC and silica gel (EPA

1988a) or on a OV-1, Tenax GC, and silica gel column (EPA 1986b). The trap column is heated and

purged to desorb the chloromethane and other volatiles onto the GC column. For medium-level samples, the

soil and solid waste are mixed with methanol and shaken. An aliquot of the methanol is removed, diluted

with water, and purged as described above for water samples. Overpurging the sample may result in loss of

some chloromethane. Analysis is performed by EPA Method 8000 (Gas Chromatography/Mass

Spectrometry for Volatile Organics) and Method 8010B (Halogenated Volatile Organics) or by Method

8240 (GC/MS for Volatile Organics) (EPA 1986b). Method 8010 uses GC with an electrolytic conductivity

detector. EPA Method 8021A uses analysis by GC with photoionization detection and electron capture

detection in series (EPA 1986c). LODs range from 0.03 μg/L with chloromethane in water (Method

8021A) (EPA 1986c) to 12.5 μg/kg for high-concentration soils and sludges (Method 8010B) (EPA 1986b).

Other method characteristics are shown in Table 6-2.
CHLOROMETHANE 191

6. ANALYTICAL METHODS

No methods for chloromethane in foods were found. However, a purge-and-trap method applicable to the

determination of trihalomethanes in liquid and viscous foods has been published by researchers at the U.S.

Food and Drug Administration (FDA) (McNeal et al. 1995). This method is a modification of EPA

Method 524.2 (EPA 1989b) and should be applicable to the determination of chloromethane in foods.

However, this method has not been validated for chloromethane.

6.3 ADEQUACY OF THE DATABASE

Section 104(i)(5) of CERCLA, as amended, directs the Administrator of ATSDR (in consultation with the

Administrator of EPA and agencies and programs of the Public Health Service) to assess whether adequate

information on the health effects of chloromethane is available. Where adequate information is not

available, ATSDR, in conjunction with the NTP, is required to assure the initiation of a program of research

designed to determine the health effects (and techniques for developing methods to determine such health

effects) of chloromethane.

The following categories of possible data needs have been identified by a joint team of scientists from

ATSDR, NTP, and EPA. They are defined as substance-specific informational needs that if met would

reduce the uncertainties of human health assessment. This definition should not be interpreted to mean that

all data needs discussed in this section must be filled. In the future, the identified data needs will be

evaluated and prioritized, and a substance-specific research agenda will be proposed.

6.3.1 Identification of Data Needs

Methods for Determining Biomarkers of Exposure and Effect. No biomarker that can be

associated quantitatively with exposure to chloromethane has been identified (see Section 2.6). Methods are

available for the analysis of chloromethane in blood, expired air, and breast milk. In addition, a method

exists for the analysis of the metabolite S-methylcysteine in urine. Quantitative relationships have not been

established between exposure and measurement of chloromethane or S-methylcysteine in these biological

media. The observed variability of metabolism (see the discussion of the metabolism of chloromethane in

Section 2.3.3) suggests that a correlation of chloromethane levels in tissues with levels of chloromethane

exposure is not likely to be found. It may be possible to use levels of yet unidentified metabolites in blood or

urine as biomarkers of exposure. If reliable biomarkers of exposure were available, it would allow both

investigators and reviewers to assess the accuracy and uncertainty of the methods used in toxicological
CHLOROMETHANE 192

6. ANALYTICAL METHODS

studies. Furthermore, the ready availability of tested analytical methods for the biomarkers, including

sample preservation, would permit a standardized approach to the analysis of biological materials to assist

in measuring human exposure and monitoring effects in humans. Thus, methods for biomarkers of exposure

and effect are needed.

Methods for Determining Parent Compounds and Degradation Products in Environmental

Media. Methods appear to be available for the analysis of chloromethane in all environmental media.

Methods for drinking water, groundwater, surface water, and waste water (Bauer and Solyom 1994; EPA

1982, 1989a, 1989b; Greenberg et al. 1992a, 1992b; Shirey 1995) have LODs as low as 0.01 ppb; methods

for soil and solid waste (EPA 1989b, 1989c), and for workplace and ambient air (EPA 19888; NIOSH

1994; Oliver et al. 1996) have LODs in the 0.5 to 1.5 ppb range. The MRL for chronic inhalation exposure

to chloromethane is 0.05 ppm and all of the methods reported for air are adequate. No MRLs have been

established for ingestion exposures. No methods were identified for chloromethane in foods; the need for

analytical methods would be driven by oral MRLs. Chloromethane degrades to a number of products in the

environment, including methanol and formaldehyde, both of which are natural products. While analytical

methods exist for these compounds, they cannot be used as indicators of chloromethane degradation since

methanol and formaldehyde have large natural sources.

6.3.2 Ongoing Studies

No ongoing studies were located in which new methods for chloromethane might be developed.
CHLOROMETHANE 193

7. REGULATIONS AND ADVISORIES

The international, national, and state regulations and guidelines regarding chloromethane in air, water and

other media are summarized in Table 7-1.

An acute inhalation MRL of 0.5 ppm was derived from a NOAEL of 50 ppm for motor coordination and

damage to the cerebellar granule cells in a study by Landry et al. (1985).

An intermediate inhalation MRL of 0.2 ppm was derived from a LOAEL of 51 ppm for increased liver

enzymes in male mice at the 6-month time point in a 2-year study by CIIT (1981).

A chronic inhalation MRL of 0.05 ppm was derived from a LOAEL of 51 ppm for axonal swelling in male

mice in a 2-year study by CIIT (1981).

The risk assessments for establishing a reference concentration (RfC) for chronic inhalation exposures and a

reference dose (RfD) for chronic oral exposures to chloromethane are undergoing review by an EPA work

group (IRIS 1997). However, the EPA Office of Water reports an RfD of 0.004 mg/kg/day (EPA 1996a).

The EPA has not assigned a carcinogenicity classification for chloromethane (IRIS 1997). Health

advisories published by the EPA Office of Water assign chloromethane to cancer group C, which indicates

that the substance is a possible human carcinogen (EPA 1996a). The International Agency for Research on

Cancer (IARC) has classified chloromethane as Group 3; not classifiable as to its carcinogenicity to humans

(IARC 1987). The National Toxicology Program (NTP) has not classified the chemical for carcinogenicity.

The National Institute for Occupational Safety and Health (NIOSH) recommends that chloromethane be

treated as a potential occupational carcinogen (NIOSH 1992).

Chloromethane is on the list of chemicals subject to the requirements of “The Emergency Planning and

Community Right-to-Know Act of 1986 (EPCRA) (EPA 1988c). Section 313 of Title III of EPCRA,

requires owners and operators of certain facilities that manufacture, import, process, or otherwise use the

chemicals on this list to report annually their release of those chemicals to any environmental media (U.S.

Congress 1986).
CHLOROMETHANE 194

7. REGULATIONS AND ADVISORIES

OSHA requires employers of workers who are occupationally exposed to chloromethane to institute

engineering controls and work practices to reduce and maintain employee exposure at or below permissible

exposure limits (PELs). The employer must use controls and practices, if feasible, to reduce exposure to or

below an g-hour time-weighted average (TWA) of 100 ppm (OSHA 1974). The acceptable ceiling

concentration for chloromethane is 200 ppm. The acceptable maximum peak above this ceiling

concentration is 300 ppm. Therefore, during an g-hour work shift a person may be exposed to a

concentration of chloromethane measuring 200 ppm or greater, but never more than 300 ppm and only for a

maximum period of 5 minutes within any 3-hour period. An exposure such as this must be compensated by

exposures to concentrations less than 100 ppm so that the cumulative exposure for the g-hour shift does not

exceed the 100 ppm exposure limit (OSHA 1974).

The EPA regulates chloromethane under the Clean Air Act (CAA) and has designated chloromethane as a

hazardous air pollutant (HAP). The major source category for which chloromethane emissions are

controlled is the synthetic organic chemicals manufacturing industry (SOCMI) and includes equipment leaks

(EPA 1983b) distillation operations (EPA 1990), and reactor processes (EPA 1993a).

Chloromethane is regulated by the Clean Water Effluent Guidelines in Subchapter N of Title 40 of the Code

of Federal Regulations. Electroplating is the points source category for which chloromethane is controlled

as a total toxic organic (EPA 1981a). The point source categories for which chloromethane has specific

regulatory performance standards include organic chemicals, plastics, and synthetic fibers (EPA 1987b,

1987c, 1987d, 1987e, 1987f, 19878, 1987h, 19871, 1987j, 1987k), steam electric power generators (EPA

1982c), metal finishing (EPA 1983c).

The Resource Conservation and Recovery Act (RCRA) identifies chloromethane as a hazardous waste from

non-specific sources and has assigned it the hazardous waste numbers F024 and F025 (EPA 1981c).

Under the Comprehensive Environmental Response, Compensation, and Liability Act (CERCLA), owners

of vessels or facilities are required to immediately report release of chloromethane equal to or greater than

the reportable quantity of 100 pounds (45.4 kg) (EPA 1985).








CHLOROMETHANE 203

8. REFERENCES

*ACGIH. 1996. TLVs Threshold Limit values and biological exposure indices for 1995-1996. American

Conference of Governmental Industrial Hygienists, Cincinnati, OH, 26.

*Adinolfi M. 1985. The development of the human blood-CSF-brain barrier. Developmental Medicine &

Child Neurology 27:532-537.

*Ahman PK, Dittmer DS. 1974. In: Biological handbooks: Biology data book, Volume III, second edition.

Bethesda, MD: Federation of American Societies for Experimental Biology, 1987-2008, 2041.

Andersen ME, Gargas ML, Jones RA, et al. 1980. Determination of the kinetic constants for metabolism

of inhaled toxicants in vivo using gas uptake measurements. Toxicol Appl Pharmacol 54:100-116.

*Andersen ME, Krishman K. 1994. Relating in vitro to in vivo exposures with physiologically-based tissue

dosimetry and tissue response models. In: H. Salem, ed. Current concepts and approaches on animal test

alternatives. U.S. Army Chemical Research Development and Engineering Center, Aberdeen Proving

Ground, Maryland.

*Andersen ME, MacNaughton MG, Clewell HJ, et al. 1987. Adjusting exposure limits for long and short

exposure periods using a physiological pharmacokinetic model. Am Ind Hyg Assoc J 48(4):335-343.

*Andrews AW, Zawistowski ES, Valentine CR. 1976. A comparison of the mutagenic properties of vinyl

chloride and methyl chloride. Mutat Res 40:273-276.

Anger WK. 1985. Neurobehavioral tests used in NIOSH-supported worksite studies, 1973-1983.

Neurobehav Toxicol Teratol 7:359-368.

Anger WK, Johnson BL. 1985. Chemicals affecting behavior. In: O’Donoghue JL, ed. Volume I:

Neurotoxicity of industrial commercial chemicals. Boca Raton, FL: CRC Press, Inc., 51-148.

Anonymous. 1977. TSCA (Toxic Substances Control Act) interagency testing committee. Initial report to

the Administrator, Environmental Protection Agency. Federal Register 42:55026-55080.

*Atkinson R. 1985. Kinetics and mechanisms of the gas-phase reactions of hydroxyl radical with organic

compounds under atmospheric conditions. Chem Rev 85:69-201.

Atkinson R, Darnall KR, Lloyd AC, et al. 1979. Kinetics and mechanisms of the reactions of the hydroxyl

radical with organic compounds in the gas phase. Adv Photochem 11:375-488.

*ATSDR. 1989. Decision guide for identifying substance-specific data needs related to toxicological

profiles. Agency for Toxic Substances and Disease Registry, Division of Toxicology, Atlanta, GA.

*ATSDR/CDC. 1990. Subcommittee report on biological indicators of organ damage. Agency for Toxic

Substances and Disease Registry, Centers for Disease Control and Prevention, Atlanta, GA.

 

*Cited in text
CHLOROMETHANE 204

8. REFERENCES

Axelson O. 1985. Halogenated alkanes and alkenes and cancer: Epidemiological aspects. In: Fishbein L,

O’Neill IK, eds. Volume 7: Environmental carcinogens selected methods of analysis. Lyon, France: IARC.

*Baird TT. 1954. Methyl chloride poisoning. Br Med J 2:1353.

*Baker HM. 1927. Intoxication with commercial methyl chloride. Report of a series of cases. J Am Med

Assoc 88:1137-l 138.

Barassin J, Combourieu J. 1974. Kinetic study of reactions between atomic oxygen and the chlorinated

derivates of methane. II. Reactions CH3CL+O, CHCL3+0, CCL4+0 and CH4+0. Bull Sot Chim

1974:1-5.

*Barnes DG, Dourson M. 1988. Reference dose (RfD): Description and use in health risk assessments.

U.S. Environmental Protection Agency. Regul Toxicol Pharmacol 8:471-486.

Barrie LA. 1986. Arctic air pollution: An overview of current knowledge. Atmos Environ 20:643-663.

*Battigelli MC, Perini A. 1955. [Two cases of acute methyl chloride intoxication]. Medicina de1 Lavoro

46:646-652. (Italian).

*Bauer S, Solyom d. 1994. Determination of volatile organic compounds at the parts per trillion level in

complex aqueous matrices using membrane introduction mass spectrometry. Analytical Chemistry

66(24):4422-4431.

Belanger PL. 1980. Health hazard evaluation--determination report no. HE 79-31-699. University

Corporation for Atmospheric Research, Mauna Loa Observatory, Hilo, Hawaii. Cincinnati, OH: U.S.

Department of Health and Human Services, Public Health Service, Centers for Disease Control, National

Institute for Occupational Safety and Health.

Bentur Y, Koren G. 1991. The three most common occupational exposures reported by pregnant women:

An update. American Journal of Obstetrics and Gynecology 165(2):429-437.

*Bolt HM, Ganswendt B. 1993. Mechanisms of carcinogenicity of methyl halides. Critical Reviews in

Toxicology 23(3):237-253.

Bolt HM, Laib RJ, Pater H, et al. 1986. DNA adducts of halogenated hydrocarbons. J Cancer Res Clin

Oncol 112:92-96.

*Borovska D, Jindrichova J, Klima M. 1976. [Methyl chloride intoxications in the East Bohemia district.]

Z Gesamte Hyg 22:241-245. (German).

*Brown KW, Donnelly KC. 1988. An estimation of the risk associated with the organic constituents of

hazardous and municipal waste landfill leachates. Haz Waste Haz Mater 5:1-30.

Browning G. 1985. Notes of meeting (February 20) between G. Browning, General Electric Silicone

Products Division, Waterford, NY 12188, and M. Price, Test Rules Development Branch, Office of Toxic

Substances, U. S. Environmental Protection Agency, Washington, DC.
CHLOROMETHANE 205

8. REFERENCES

*Burek JD, Potts WJ, Gushow TS, et al. 1981. Methyl chloride:48 and 72 hour continuous inhalation

exposure in rats followed by up to 12 days of recovery. Unpublished study. Toxicology Research

Laboratory, Dow Chemical USA, Midland, MI. OTS Submission Document ID 40-8120723. Microfiche

511317.

*Burmaster DE. 1982. The new pollution-groundwater contamination. Environ 24:6-13, 33-36.

*Bursey JT, Pellizzari D. 1982. Analysis of industrial wastewater for organic pollutants in consent decree

survey. Env Research Lab Office Research Devel, U.S. Environmental Protection Agency, Athens GA.

Printout of Database.

Bus JS. 1982. Integrated studies of methyl chloride toxicity. Chem Ind Inst Toxicol Activ 2:3-4.

*Butler R, Solomon IJ, Snelson A. 1978. Rate constants for the reaction of OH with halocarbons in the

presence of 02 + N2. J Air Pollut Cont Fed 28:1131-1133.

*C&EN. 1992. Production by the U.S. chemistry industry. Chemical & Engineering News 23

(June 29):34-40

*C&EN. 1995. Production by the U.S. chemistry industry. Chemical & Engineering News 26

(June 26):36-44.

*Cammann K, Hubner K. 1995. Trihalomethane concentrations in swimmers’ and bath attendants’ blood

and urine after swimming or working in indoor swimming pools. Arch Environ Health 50(1):61-65.

*CAS. 1988. Chemical Abstract Services. December 6, 1988.

*Chapin RE, White RD, Morgan KT, et al. 1984. Studies of lesions induced in the testis and epididymis of

F-344 rats by inhaled methyl chloride. Toxicol Appl Pharmacol 76:328-343.

*Chellman GJ, Bus JS, Working PK. 1986c. Role of epididymal inflammation in the induction of dominant

lethal mutations in Fischer 344 rat sperm by methyl chloride. Proc Natl Acad Sci USA 83:8087-8091.

*Chellman GJ, Hurtt ME, Bus JS, et al. 1987. Role of testicular versus epididymal toxicity in the induction

of cytotoxic damage in Fischer-344 rat sperm by methyl chloride. Repro Toxicol 1:25-35.

*Chellman GJ, Morgan KT, Bus JS, et al. 1986a. Inhibition of methyl chloride toxicity in male F-344 rats

by the anti-inflammatory agent BW755C. Toxicol Appl Pharmacol 85:367-379.

*Chellman GJ, White RD, Norton RM, et al. 1986b. Inhibition of the acute toxicity of methyl chloride in

male B6C3F1 mice by glutathione depletion. Toxicol Appl Pharmacol 86:93-104.

Chenoweth MB, Hake CL. 1962. The smaller halogenated aliphatic hydrocarbons. Ann Rev Pharmacol

2:363-398.

*Chopra NM. 1972. Breakdown of chlorinated hydrocarbon pesticides in tobacco smokes: A short review.

In: Tahori AS, ed. Proceedings of the 2nd International IUPAC Congress of Pesticide Chemistry, Vol VI.

New York, NY: Gordon and Breach Science Publishers, 245-261.
CHLOROMETHANE 206

8. REFERENCES

*CIIT. 1981. Final report on a chronic inhalation toxicology study in rats and mice exposed to methyl

chloride. Unpublished study prepared by Battelle-Columbus Laboratories, Columbus, OH. OTS

Submission Document ID 40-8120717. Microfiche 511310.

*Clewell HJ III, Andersen M. 1985. Risk assessment extrapolations and physiological modeling. Toxicol

IndHealth 1(4):111-131.

*CLPSDB. 1987. Contract Laboratory Program Statistical Data Base. April 13, 1987.

*CMR. 1986. Chemical profile: Chloromethane. Chemical Marketing Reporter, March 3, 1986.

*CMR. 1995. Chemical profile: Methyl chloride. Chemical Marketing Reporter (March 6):44-45.

Cohen J. 1979. Methyl chloride survey final report, task III. Conoco Chemicals, Westlake, Louisiana.

NTIS PB83-156299. (microfiche)

Cohen JM. 1980. Extent-of-exposure survey of methyl chloride. Report. NTIS PB81-223547.

(microfiche)

Cohen N. 1986. Structure-reactivity relationships for predicting environmentally hazardous chemicals.

Report. EPA 600/3-86-072. NTIS PB87-140497/GAR. (microfiche)

*Cole RH, Frederick RE, Healy RP, et al. 1984. Preliminary findings of the priority pollutant monitoring

project of the nationwide urban runoff program. J Water Pollut 56:898-908.

*Coleman WE, Lingg RD, Melton RG, et al. 1976. The occurrence of volatile organics in five drinking

water supplies using gas chromatography/mass spectrometry. In: Keith L, ed. Analysis and identification

of organic substances in water. Ann Arbor, MI: Ann Arbor Science, 305-327.

Cowie M, Watts H. 1971. Diffusion of methane and chloromethanes in air. Can J Chem 49:74-77.

*Cox RA, Derwent RG, Eggleton AEJ, et al. 1976. Photochemical oxidation of halocarbons in the

troposphere. Atmos Environ 10:305-308.

Crandall MS, McCammon CS, Fajen J, et al. 1980. Industrial hygiene report in-depth survey of

monochlorobenzene and methyl chloride exposure at the Dow Chemical Company, Midland, Michigan.

Report. NTIS PB80-192933. (microfiche)

Cronn DR, Harsch DE. 1976. Rapid determination of methyl chloride in ambient air samples by GC-MS.

Anal Lett 9:1015-1023.

*Cronn DR, Rasmussen RA, Robinson E, et al. 1977. Halogenated compound identification and

measurement in the troposphere and lower stratosphere. J Geophys Res 82:5935-5944.

*Crosley DR. 1997. 1993 Tropospheric OH photochemistry experiment: A summary and perspective.

Journal of Geophysical Research Atmospheres 102(5):6300-6700.
CHLOROMETHANE 207

8. REFERENCES

*Crutzen PJ, Gidel LT. 1983. A two-dimensional photochemical model of the atmosphere. 2: The

tropospheric budgets of the anthropogenic chlorocarbons,carbon monoxide, methane, chloromethane and the

effect of various nitrogen oxides sources on the tropospheric ozone. J Geophys Res 88:6641-6661.

*Crutzen PJ, Heidt LE, Krasnec JP, et al. 1979. Biomass burning as a source of atmospheric gases carbon

monoxide, hydrogen, nitrous oxide, nitric oxide, methyl chloride and carbonyl sulfide. Nature (London)

282:253-256.

*Crutzen PJ, Isaksen ISA, McAfee JR. 1978. The impact of the chlorocarbon industry on the ozone layer.

J Geophys Res 83:345-363.

Daubert TE, Danner RP. 1985. Data compilation tables of properties of pure compounds. Am Inst Chem

Eng 450.

Davis DD, Chameides WL, Kiang CS. 1982. Measuring atmospheric gases and aerosols. Nature 295:186.

*Davis DD, Machado G, Conaway B, et al. 1976. A temperature dependent kinetics study of the reaction

of OH with CH3C1, CH2C12, CHC13 and CH3Br. J Chem Phys 65:1268-1274.

Davis DD, Watson R, McGee T, et al. 1976. Tropospheric residence times for several halocarbons based

on chemical degradation via hydroxyl radicals. Paper presented at National Meeting: Division

Environmental Chemistry, American Chemical Society, 16:189-191.

DeCesar RT, Edgerton SA, Khalil MAK, et al. 1985. Sensitivity analysis of mass balance receptor

modeling: Methyl chloride as an indicator of wood smoke. Chemosphere 14:1495-1501.

DeGroot WF. 1989. Methyl chloride as a gaseous tracer for wood burning? Environ Sci Technol 23:252.

*Dekant W, Frischmann C, Speerschneider P. 1995. Sex, organ and species specific bioactivation of

chloromethane by cytochrome P4502El. Xenobiotica. 25(11):1259-1265.

*DeKok AC, Antheunius WS. 1981. S-Methylcysteine no human metabolite of methylchloride.

Unpublished study. Dow Chemical USA, Midland MI. OTS 8D Submission. Document ID 878221209.

Microfiche 215176.

DeMeyer CL, Whitehead LW, Jacobson AP, et al. 1986. Potential exposure to metal fumes, particulates,

and organic vapors during radiotherapy shielding block fabrication. Med Phys 13:748-750.

Derwent RG, Eggleton AEJ. 1978. Halocarbon lifetimes and concentration distributions calculated using a

two-dimensional tropospheric model. Atmos Environ 12:1261-1269.

*DHHS. 1995. Report to Congress on workers’ home contamination study conducted under the workers’

family protection act (29 U.S.C. 671a). U.S. Department of Health and Human Services, Public Health

Service, Centers for Disease Control and Prevention, National Institute for Occupational Safety and Health

(Cincinnati, OH). September 1995.

Dilling WL. 1977. Interphase transfer processes. II. Evaporation rates of chloromethanes, ethanes,

ethylenes, propanes, and propylenes from dilute aqueous solutions. Comparisons with theoretical

predictions. Environ Sci Technol 11:405-409.
CHLOROMETHANE 208

8. REFERENCES

*Dilling WL. 1982. Atmospheric environment, Chapter 5. In: Conway RA. ed. Environmental risk

analysis for chemicals. New York, NY: Van Nostrand Reinhold Co., 154-197.

Dilling WL, Goersch HK. 1980. Organic photochemistry. XVI. Tropospheric photodecomposition of

methylene chloride. In: Haque R, ed. Dynamics, exposure and hazard assessment of toxic chemicals. Ann

Arbor, MI: Ann Arbor Science.

Dilling WL, Tefertiller NB, Kallos GJ. 1975. Evaporation rates and reactivities of methylene chloride,

chloroform, 1,1,l -trichloroethane, trichloroethylene, tetrachloroethylene and other chlorinated compounds in

dilute aqueous solutions. Environ Sci Technol 9:833-838.

*Dodd DE, Bus JS, Barrow CS. 1982. Nonprotein sulfhydryl alterations in F-344 rats following acute

methyl chloride inhalation. Toxicol Appl Pharmacol 62:228-236.

*Doronina N V, Sokolov A P, Trotsenko YA. 1996. Isolation and initial characterization of aerobic

chloromethane-utilizing bacteria. Ferns Microbiology Letters 142(2-3):179-183.

*DOT. 1990a. Hazardous materials table special provisions, hazardous materials commuications,

emergency response information and training requirements. Department of Transportation. Code of

Federal Regulations. 49 CFR 172.101.

*DOT. 1990b. List of hazardous substances and reportable quantities. Department of Transportation.

Code of Federal Regulations. 49 CFR 172.101.

*Dunn RC, Smith WW. 1947. Acute and chronic toxicity of methyl chloride. Arch Pathol 43:296-300.

*DuPont. 1977. Mutagenic activity of methane chloro- in the Salmonella/microsome assay. Unpublished

study. OTS 8D Submission. E.I. Du Pont de Nemours and Co., Inc., Wilmington, DE. Document

878220403. Microfiche 215036.

Edgerton SA. 1985. Gaseous tracers in receptor modeling: Methyl chloride emission from wood

combustion. Diss Abstr Int B 46(Part 1):4284.

*Edgerton SA, Khalil MAK, Rasmussen RA. 1984. Estimates of air pollution from backyard burning. J

Air Pollut Contr Fed 34:661-664.

Edgerton SA, Khalil MAK, Rasmussen RA. 1985. Methodology for collecting short-period integrated gas

samples: Estimating acute exposure to woodburning pollution. J Environ Sci Health Part A A20:563-581.

*Edgerton SA, Khalil MAK, Rasmussen RA. 1986. Source emission characterization of residential

wood-burning stoves and fireplaces: Fine particle/methyl chloride ratios for use in chemical mass balance

modeling. Environ Sci Technol 20:803-807.

Edgerton SA, Khalil MAK, Rasmussen RA. 1987. Diurnal variations in residential woodburning pollution

in Portland, Oregon (USA). Chemosphere 16:155-160.

*Edwards PR, Campbell I, Milne GS. 1982a. The impact of chloromethanes on the environment. Part 1.

The atmospheric chlorine cycle. Chem Ind (London) 16:574-578.
CHLOROMETHANE 209

8. REFERENCES

*Edwards PR, Campbell I, Milne GS. 1982b. The impact of chloromethanes on the environment. Part 2.

Methyl chloride and methylene chloride. Chem Ind (London) 17:619-622.

Egan E, Boeniger M, Meinhardt T. 1976. Industrial hygiene walk-through report No. IWS-60-11.

Diamond Shamrock Chemical Company, Belle, West Virginia. NTIS PB88-237-276. (microfiche)

*Eichler DL, Mackey JH. 1986. The levels of certain volatile organic compounds in the ambient air of the

United States. In:79th annual meeting: Air Pollution Control Assoc, 6:l-17.

*Elliot S, Rowland FS. 1995. Methyl halide hydrolysis rates in natural waters. Journal Of Atmospheric

Chemistry 20(3):229-236.

*EPA. 1973. Guidelines establishing test procedures for th analysis of pollutants. U. S. Environmental

Protection Agency. Code of Federal Regulations. 40 CFR 136, App A.

EPA. 1975. U.S. Environmental Protection Agency. Preliminary assessment of suspected carcinogens in

drinking water. Interim report to Congress, June, 1975. Washington, DC.

*EPA. 1980. U. S. Environmental Protection Agency. Ambient water quality criteria for halomethanes.

Washington, DC: Office of Water Regulations and Standards. EPA 440/5-80-051.

*EPA. 1981a. Electroplating point source category. U. S. Enviornmental Protection Agency. Code of

Federal Regulations. 40 CFR 413.02.

*EPA. 198 lb. General pretreatment regulations for existing and new sources of pollution. U. S.

Environmental Protection Agency. Code of Federal Regulations. 40 CFR 403, App B.

*EPA. 198 lc. Identification and listing of hazardous waste. U. S. Environmental Protection Agency.

Code of Federal Regulations. 40 CFR 261.31.

*EPA. 1981d. Hazardous constituents for which listed. U. S. Environmental Protection Agency. Code of

Federal Regulations. 40 CFR 261 App VII.

*EPA. 1982a. U.S. Environmental Protection Agency. Methods for organic chemical analysis of

municipal and industrial wastewater. Methods 601 and 624. EPA-600/4-82-057. Cincinnati, OH:

Environmental Monitoring and Support Laboratory. (microfiche)

*EPA. 1982b. U.S. Environmental Protection Agency. Errata: Halomethanes. Ambient water quality

criterion for the protection of human health. Prepared by Environmental Criteria and Assessment Office,

Cincinnati, OH, for the Office of Water Regulations, Washington, DC.

*EPA. 1982c. Chemical information rules. U. S. Environmental Protection Agency. Code of Federal

Regulations. 40 CFR 712.30.

*EPA. 1982d. Steam electric power generating point source category. U. S. Environmental Protection

Agency. Code of Federal Regulations. 40 CFR 423.17.

*EPA. 1982e. Steam electric power generating point source category. U. S. Enviornmental Protection

Agency. Code of Federal Regulations. 40 CFR 423.17 App A.
CHLOROMETHANE 210

8. REFERENCES

EPA. 1983a. U.S. Environmental Protection Agency. Reportable quantity document for methyl chloride.

Prepared by Environmental Criteria and Assessment Office, Cincinnati, OH, for the Office of Solid Waste

and Emergency Response, Washington, DC. ECAO-CIN-R 155.

*EPA. 1983b. Subpart W-Standards of performance for equipment leaks of VOC in the synthetic organic

chemicals manufacturing industry. U. S. Envionmental Protection Agency. Code of Federal Regulations.

40 CFR 60.489.

*EPA. 1983c. Chemical analysis test methods. U. S. Environmenal Protection Agency. Code of Federal

Regulations. 40 CFR 266, App III.

*EPA. 1983d. EPA administered permit programs: The national pollutant discharge elimination system.

Environmental Protection Agency. Code of Federal Regulations. 40 CFR 122, App D.

*EPA. 1983e. Applicability description of the metal finishing point source category. U. S. Environmental

Protection Agency. Code of Federal Regulations. 40 CFR 433.10.

*EPA. 1985. Designation, reportable quantities, and notification. U. S. Environmental Protection Agency.

Code of Federal Regulations. 40 CFR 302.4.

*EPA. 1986a. U.S. Environmental Protection Agency. Reference values for risk assessment. Prepared by

The Office of Health and Environmental Assessment, Environmental Criteria and Assessment Office,

Cincinnati, OH, for the Office of Solid Waste, Washington, DC.

*EPA. 1986b. Method 8010b, Halogenated volatile organics by gas chromatography, test methods for

evaluating solid waste, Volume 1B: Laboratory manual physical/chemical methods, SW-846.

*EPA. 1986c. Method 8021A, Halogenated volatiles by gas chromatography using photoionizationand

electrolytic conductivity detectors in series: capillary column technique, test methods for evaluating solid

waste, Volume 1B: Laboratory Manual Physical/Chemical Methods, SW-846.

*EPA. 1987a. National primary drinking water regulations. U. S. Environmental Protection Agency.

Code of Federal Regulations. 40 CFR 141.40.

*EPA. 1987b. U.S. Environmental Protection Agency. Hazardous substances: Reportable quantity

adjustments. Proposed rules. Federal Register 50:8140-8186.

*EPA. 1987c. Organic chemicals, plastics, and synthetic fibers. U. S. Environmental Protection Agency.

Code of Federal Regulations. 40 CFR 414.25.

*EPA. 1987d. U.S. Environmental Protection Agency. Health effects assessment for chloromethane. EPA

600/8-88-024. Cincinnati, OH: Office of Research and Development, Office of Health and Environmental

Assessment, Environmental Criteria and Assessment Office. NTIS PB88-279932.

*EPA. 1987e. Applicability description of the other fibers subcategory. U. S. Environmental Protection

Agency. Code of Federal Regulations. 40 CFR 414.35.

*EPA. 1987f. Themosetting resins. U. S. Environmetnal Protection Agency. Code of Federal

Regulations. 40 CFR 414.55.
CHLOROMETHANE 211

8. REFERENCES

*EPA. 1987g. Thermoplastic resins. U. S. Environmental Protection Agency. Code of Federal

Regulations. 40 CFR 414.45.

EPA. 1987h. Pretreatment standards for existing sources (PSES). U. S. Environmental Protection Agency.

Code of Federal Regulations. CFR 414.65.

*EPA. 1987i. Applicability description of the bulk organic chemicals subcategory. U. S. Environmental

Protection Agency. Code of Federal Regulations. 40 CFR 414.70.

*EPA. 1987j. Pretreatment standards for existing sources. U. S. Environmental Protection Agency. Code

of Federal Regulations. 40 CFR 414.75.

*EPA. 1987k. Direct discharge point sources that use end-of-pipe biological treatment. U. S

Environmental Protection Agency. Code of Federal Regulations. 40 CFR 414.90.

*EPA. 19871. Direct discharge point sources that do not use end-of-pipe biological treatment. U. S.

Environmental Protection Agency. Code of Federal Regulations 40 CFR 414.100.

*EPA. 1987m. Toxic pollutant effluent limitations and standards for direct discharge point sources that do

not use end-of-pipe biological treatment. U. S. Environmental Protection Agency. Code of Federal

Regulations 40 CFR 414.101.

*EPA. 1987n. Standards for owners and operators of hazardous waste treatment storage, and disposal

facilities. U. S. Environmental Protection Agency. Code of Federal Regulations. 40 CFR 264, App IX.

*EPA. 1988a. Contract Laboratory Program Statement of Work for Organics Analysis Multi-Media

Multi-Component 2/88. U.S. Environmental Protection Agency.

*EPA. 1988b. Land disposal restrictions. U. S. Environmental Protection Agency. Code of Federal

Regulations. 40 CFR 268.30.

*EPA. 1988c. Specific Toxic Chemical Listings. U. S. Environmental Protection Agency. Code of

Federal Regulations. 40 CFR 372.65.

*EPA. 1988d. Health and safety data reporting. U. S. Environmental Protection Agency. Code of Federal

Regulations. 40 CFR 716.120.

*EPA. 1988e. U.S. Environmental Protection Agency. Analysis of clean water act effluent guidelines

pollutants. 40 CFR Parts 400-475.

*EPA. 1988f. U.S. Environmental Protection Agency. Designation, reportable quantities and notifications.

40 CFR 302.4.

*EPA. 1988g. Method TO-14 Determination of Volatile Compounds (VOCs) in Ambient Air using

SUMMA passivated canister sampling and Gas Chromatographic ANalysis, Compendium of Methods for

the Determination of Toxic Organic Compounds in Ambient Air EPA 600/4-89/017.
CHLOROMETHANE 212

8. REFERENCES

*EPA. 1988h. Recommendations for and documentation of biological values for use in risk assessment.

Environmental Criteria and Assessment Office, Office of Health and Environmental Assessment,

Environmental Protection Agency. NTIS No. PB88-179874. (microfiche)

*EPA. 1989a. Method 502.1 Volatile halogenated organic compounds in water by purge and trap gas

chromatography, methods for the determination of organic compounds in drinking water,

EPA-600/4-88/039.

*EPA. 1989b. Method 524.2 Measurement of purgeable organic compounds in water by capillary column

gas chromatography/mass spectrometry, methods for the determination of organic compounds in drinking

water, EPA-600/4-88/039.

*EPA. 1989c. Direct discharge point sources that use end-of-pipe biological treatment. U. S.

Environmental Protection Agency. Code of Federal Regulations. 40CFR 414.75.

*EPA. 1990. Standards of Performance for volatile organic compound (VOC) emissions from synthetic

organic chemical manufacturing industry (SOCMI) distillation operations. U. S . Environmental Protection

Agency. Code of Federal Regulations. 40 CFR 60.667.

*EPA. 1991a. Criteria for municipal solid waste landfills. U. S. Environmental Protection Agency. Code

of Federal Regulations. 40 CFR 258.

*EPA. 1991b. Criteria for municipal solid waste landfills. U. S. Environmental Protection Agency. Code

of Federal Regulations. 40 CFR 258 App II.

*EPA. 1991c. Drinking water health advisory. Volatile organic chemicals., United States Environmental

Protection Agency, Office of Drinking Water Health Advisories, Lewis Publishers, Inc., Michigan, 85-105.

*EPA. 1993a. Standards of performance for volatile organic compound emissions from synthetic organic

chemical manufacturing industry (SOCMI) reactor processes. U. S. Environmental Protection Agency.

Code of Federal Regulations. 40 CFR 60.707.

*EPA. 1993b. Identification of test procedure. U. S. Environmental Protection Agency. Code of Federal

Regulations. 40 CFR 455.50.

*EPA. 1993c. Land disposal restrictions for newly identified and listed hazardous wastes and hazardous

soil. U. S. Environmental Protection Agency. Federal Register 58 FR 48092.

*EPA. 1994a. National emission standards for organic hazardous air pollutants from the synthetic organic

chemical manufacturing industry. U. S. Environmental Protection Agency. Code of Federal Regulations.

40 CFR 63.106.

*EPA. 1994b. Methods for derivation of inhalation reference concentrations and applications of inhalation

dosimetry. U.S. Environmental Protection Agency, Office of Research and Development. Washington D.C.

EPA/600/8-90/066F.

*EPA. 1996a. Drinking water regulations and health advisories. Office of Water, U. S. Environmental

Protection Agency.
CHLOROMETHANE 213

8. REFERENCES

*EPA. 1996b. Ozone science fact sheet. U.S. EPA Office of Air and Radiation, Stratospheric Protection

Division. http://www.epa.gov/docs/ozone/science/sc_fact.html

*EPA. 1997. Land disposal restrictions: Correction of tables; Treatment standards for hazardous wastes

and universal treatment standards. Technical amendment of final rule. Federal Register. 62 FR 7502.

*Eriksson L, Jonsson J, Hellberg S, et al. 1991. A strategy for ranking environmentally occurring

chemicals. Part V: The development of two genotoxicity QSARs for halogenated aliphatics. Environ

Toxicol Chem 10(5):585-596.

*Eriksson Ll, Jonsson J, Berglind R. 1993. External validation of a QSAR for the acute toxicity of

halogenated aliphatic hydrocarbons. Environ Toxicol Chem 12(7):1185-l 191.

*Fabian P. 1986. Halogenated hydrocarbons in the atmosphere. In: Hutzinger O, ed. The handbook of

environmental chemistry, Vol. 4, Part A. Berlin: Springer-Verlag, 23-51.

*Fazzalari FA. 1978. Odor threshold (ot): odor recognition in air:1.00x +lppm(chemically pure).

compiliation of odor and taste threshold values data. ASTM Data Series DS 48 A Commettee E-18.

Philadelphia, AP American Society for Testing and Materials.

*FEDRIP. 1998. FEDRIP literature search (references and abstracts) for chloromethane. Federal Research

in Progress. Dialog Information Service.

*Finlayson-Pitts BJ, Pitts JN Jr. 1986. Atmospheric chemistry: fundamentals and experimental techniques.

NY: John Wiley & Sons.

Fishbein L. 1979. Potential halogenated industrial carcinogenic and mutagenic chemicals. 2. Halogenated

saturated hydrocarbons. Sci Total Environ 11:163-195.

*Foman SJ. 1966. Body composition of the infant (Part I: The male reference infant). In: Falkner F, ed.

Human development. Philadelphia, PA: WB Saunders, 239-246.

*Foman, SJ, Haschke F, Ziegler EE et al. 1982. Body composition of reference children from birth to age

10 years. American Journal of Clinical Nutrition 35:1169-l 175.

*Fostel J, Allen PF, Bermudez E, et al. 1985. Assessment of the genotoxic effects of methyl chloride in

human lymphoblasts. Mutat Res 155:75-81.

*Fridovich I. 1978. The biology of oxygen radicals. Science 201:875-880.

*FSTRAC. 1990. Summary of state and federal drinking water standards and guidelines. Federal-State

Toxicology and Regulatory Alliance Committee. U. S. Environmental Protection Agency.

Gargas ML, Clewell III HJ, Andersen ME. 1990. Gas uptake inhalation techniques and the rates of

metabolism of chloromethanes, chloroethanes, and chloroethylenes in the rat. Inhalation. Toxicology

2(3):295-319.
CHLOROMETHANE 214

8. REFERENCES

*Gidel LT, Crutzoen PJ, Fishman J. 1983. A two-dimensional photchemical model of the atmosphere; 1:

Chlorocarbon emissions and their effect on stratospheric ozone. Journal of Geophysical Research

88:6622-6640.

*Goldstein BD, Witz G, Amoruso M, et al. 1979. Protease inhibitors antagonize the activation of

polymorphonuclear leucocyte oxygen consumption. Biochem Biophys Res Commun 88:854-860.

*Goldstein BD, Witz G, Amoruso M, et al. 1981. Stimulation of human polymorphonuclear leucocyte

superoxide anion radical production by tumor promotors. Cancer Letters 11:257-262.

Gorman RW, Froneburg B. 1981. Health hazard evaluation--report No. HHE-80-106-963. Union

Carbide, Sistersville, West Virginia. Cincinnati, OH: U.S. Department of Health and Human Services,

Public Health Service, Centers for Disease Control, National Institute for Occupational Safety and Health.

*Gossett JM. 1987. Measurement of Henry’s law constants for Cl and C2 and chlorinated hydrocarbons.

Environ Sci Tech 21:202-208.

*Gould JP, Ramsey RE, Giabbai M, et al. 1983. Formation of volatile haloorganic compounds in the

chlorination of municipal landfill leachates. In: Water Chlorination Environ Impact Health Eff 4:525-539.

*Granstrom ML, Ahlert RC, Wiesenfeld J. 1984. The relationships between the pollutants in the sediments

and in the water of the Delaware and Raritan Canal. Water Sci Tech 16:375-380.

Grasso P, Sharratt M, Davies DM, et al. 1984. Neurophysiological and psychological disorders and

occupational exposure to organic solvents. Food Chem Toxicol 22:819-852.

*Great Lakes Water Quality Board. 1983. An inventory of chemical substances identified in the Great

Lakes ecosystem. Volume I - Summary. Report to the Great Lakes Water Quality Board, Windsor,

Ontario, Canada, l-8, 11, 59, 90-91.

*Greenberg AE, Clesceri LS, Eaton AD. 1992a. Method 6210 Volatile Organics, Purge and Trap Gas

Chromatographic/Mass Spectrometric Method, Standard Methods for the Examination of Waste and

Wastewater, Eighteenth Edition, American Public Health Association, Washington, DC.

*Greenberg AE, Clesceri LS, Eaton AD. 1992b. Method 6230 Volatile Halocarbons, Purge and Trap Gas

Chromatographic Method, Standard Methods for the Examination of Waste and Wastewater, Eighteenth

Edition, American Public Health Association, Washington, DC.

*Greenberg M, Anderson R, Keene J, et al. 1982c. Empirical test of the association between gross

contamination of wells with toxic substances and surrounding land use. Environ Sci Technol 16:14-19.

Grirnsrud EP, Miller DA. 1978. Oxygen doping of carrier gas in measurement of halogenated methanes by

gas chromatography with electron capture detection. Anal Chem 50:1141-1145.

*Grimsrud EP, Rasmussen RA. 1975. Survey and analysis of halocarbons in the atmosphere by gas

chromatography-mass spectrometry. Atmos Environ 9:1014-1017.

*Gudmundsson G. 1977. Methyl chloride poisoning 13 years later (letters to the editor). Archives of

Environmental Health 32(5):236-237.
CHLOROMETHANE 215

8. REFERENCES

*Guengerich FP, Shimada T. 1991. Oxidation of toxic and carcinogenic chemicals by human cytochrome

P-450 enzymes. Chemical Research in Toxicology 4(4):391-407.

Guenther FR, Chesler SN. 1986. Post column solvent trapping technique for the analysis of very volatile

halocarbons. Govt Rep Announce Ind, Issue 16.

*Gummert M. 1961. [The Wilson Block after methyl chloride intoxication.] Zeitschrift fuer die Gesamte

Innere Medizin und ihre Grenzgebiete 16:677-680. (German).

Gunther FA, Westlake WE, Jaglan PS. 1968. Reported solubilities of 738 pesticide chemicals in water.

Res Rev 20:1-148.

*Gusten H, Klasinc L, Marie D. 1984. Prediction of the abiotic degradability of organic compounds in the

troposphere. J Atmos Chem 2:83-94.

*Guzelian PS, Henry CJ, Olin SS. 1992. Similarities and differences between children and adults:

Implications for risk assessment. International Life Sciences Institute Press, Washington, D.C.

*Hallier E, Deutschmann S, Reichel C, et al. 1990. A comparative investigation of the metabolism of

methyl bromide and methyl iodide in human erythrocytes. Int Arch Occup Environ Health 62(3):221-225.

Hallier E, Peter H. 1988. Methyl chloride metabolism by human erythrocyte glutathione transferases. In:

29th spring meeting: German Society for Pharmacology and Toxicology, Mainz, West Germany, March

8-l 1, 1988. Naunyn- Schmiedeberg’s Arch Pharmacol 337(Suppl):R20.

*Hamm TE Jr., Raynor TH, Phelps MC, et al. 1985. Reproduction in Fischer-344 rats exposed to methyl

chloride by inhalation for two generations. Fund Appl Toxicol 5:568-577.

Hampson RF. 1980. Chemical kinetic and photochemical data sheets for atmospheric reactions.

Washington, DC: U.S. Department of Transportation. FAA-EE-80-17.

Hansch C, Leo AJ. 1985. Medchem project. Claremont, CA: Pomona College. Issue No. 26.

*Hansen H, Weaver NK, Venable FS. 1953. Methyl chloride intoxication. Am Med Assoc Arch Ind Hyg

Occ Med 8:328-334.

Hao WM. 1986. Industrial sources of atmospheric nitrous oxide, chloromethane, and bromomethane. Diss

Abstr Int B 47:2424.

*Harper DB. 1985. Halomethane from halide ion a highly efficient fungal conversion of environmental

significance. Nature (London) 315:55-57.

*Harper DB, Buswell JA, Kennedy JT, et al. 1990. Chloromethane, methyl donor in veratryul alchohol

biosynthesis in Phanerochaete chrysosporium and other l&run-degrading fungi. Appl Environ Microbial

56(11):3450-3457.

*Harper DB, Hamilton JTG. 1988. Biosynthesis of chloromethane in Phellinus pomaceus. J Gen

Microbial 134:283 l-2839.
CHLOROMETHANE 216

8. REFERENCES

*Harper DB, Kennedy JT, Hamilton JTG. 1988. Chloromethane biosynthesis in poroid fungi.

Phytochemistry 27:3147-3153.

Harsch DE, Cronn DR, Slater WR. 1979. Expanded list of halogenated hydrocarbons measurable in

ambient air. J Air Pollut Contr Assoc 29:975-976.

*Hartman TL, Wacker W, Roll RM. 1955. Methyl chloride intoxication. New Eng J Med 253:552-554.

*Hartmans S, Schmuckle A, Cook AM, et al. 1986. Methyl chloride: Naturally occurring toxicant and C-l

growth substrate. J Gen Microbial 132:1139-l 142.

*Hasanen E, Soininen V, Pyysalo H, et al. 1979. On the occurrence of aliphatic chlorine and bromine

compounds in automobile exhaust. Atmos Environ 13:1217-1219.

*Hatch GG, Mamay PD, Ayer ML, et al. 1982. Methods for detecting gaseous and volatile carcinogens

using cell transformation assays. Environ Sci Res 25:75-90.

*Hatch GG, Mamay PD, Ayer ML, et al. 1983. Chemical enhancement of viral transformation in Syrian

hamster embryo cells by gaseous and volatile chlorinated methanes and ethanes. Cancer Res 43:1945-1950.

*HazDat. 1998. Database. Agency for Toxic Substances and Disease Registry (ATSDR), Atlanta, GA.

*Heck HD, White EL, Casanova-Schmitz M. 1982. Determination of formaldehyde in biological tissues by

gas chromatography/mass spectrometry. Biomed Mass Spectrom 9:347-353.

Heicklen JP, Sanhueza E, Hisatsune IC, et al. 1975. Oxidation of halocarbons. Washington, DC: U.S.

Environmental Protection Agency. EPA 650/3-75-008.

*Heppolette RL, Robertson RE. 1959. The neutral hydrolysis of methyl halides. Proc Royal Sot London,

Ser A. 252:273-285.

Heppolette RL, Robertson RE. 1966. Effect of alpha-methylation on the parameters characterizing

hydrolysis in water for a series of halides and sulfonates. Can J Chem 44:677-684.

Herron JT, Huie RE. 1973. Rate constant for the reactions of atomic oxygen (03P) with organic

compounds in the gas phase. J Phys Chem Ref Data 2:467-518.

*Holbrook MT. 1992. Chlorocarbons, hydrocarbons (CHC13). In: Kroschwitz JI and Howe-Grant M eds.

Kirk-Othmers encyclopedia of chemical technology, Fourth Edition. New York, NY: John Wiley & Sons,

Inc.. 5:1028-1040.

*Holmes TM, Buffler PA, Holguin AH, et al. 1986. A mortality study of employees at a synthetic rubber

manufacturing plant. Am J Ind Med 9:355-362.

*Horvath AL. 1982. Halogenated hydrocarbons. Solubility - miscibility with water. New York: Marcel

Dekker, Inc., 483.

*Howard CJ, Evenson KM. 1976. Rate constants for the reactions of hydroxyl with methane and fluorine,

chlorine and bromine substituted methanes at 296 deg. K. J Chem Phys 64:197-202.
CHLOROMETHANE 217

8. REFERENCES

*Howard PH. 1990. Methyl chloride: Handbook of environmental fate and exposure data for organic

chemicals: Volume 1: Large production and priority pollutants. Chelsea, MI: Lewis Publishers, Inc.

394-400.

*HSDB. 1998. Hazardous substance data bank (Chloromethane). National Library of Medicine. National

Toxicology Program. Bethesda, MD.

*Hue1 G, Mergler D, Bowler R. 1990. Evidence for adverse reproductive outcomes among women

microelectronic assembly workers. British Journal of Industrial Medicine 47(6):400-404.

IARC. 1986. IARC monographs on the evaluation of carcinogenic risk of chemicals to humans. Vol. 41:

Some halogenated hydrogenated and pesticide exposures: Methyl chloride. Lyon, France, WHO, 161-186.

*IARC. 1987. IARC monographs on the evaluation of carcinogenic risks to humans. International Agency

for the Research on Cancer. World Health Organization.

Infante PF, Tsongas TA. 1982. Mutagenic and oncogenic effects of chloromethanes, chloroethanes and

halogenated analogs of vinyl chloride, In: Genotoxic effects of airborne agents. Environ Sci Res

25:301-327.

*IPCC. 1995. Climate change 1995: The science of climate change. Cambridge: Cambridge Univ. Press

for the Intergovernmental Panel on Climate Change.

*Isidorov VA, Zenkevich IG, Ioffe BV. 1985. Volatile organic compounds in the atmosphere of forests.

Atmos Environ 19:1-8.

IT Corporation. 1985a. Preliminary site assessment, Broadview, Illinois Plant, Amphenol Products

Division, Industrial and Technology Sector. 8D submission 878216382. TSCA Health and Safety Studies.

IT Corporation. 1985b. Phase II Site Assessment, Broadview, Illinois Plant. 8D submission 878216377.

TSCA Health and Safety Studies.

Jager R. 1988. Differences in metabolic activities of methyl chloride metabolizing enzymes

glutathione-S-transferases and cytochrome P-450 in various strains of mice. In:29th Spring Meeting:

German Society for Pharmacology and Toxicology, Mainz, West Germany, March 8-l 1, 1988. NaunynSchmiedeberg’s Arch Pharmacol 337(Suppl.):R-20.

*Jager R, Peter H, Sterzel W, et al. 1988. Biochemical effects of methyl chloride in relation to its

tumorigenicity. J Cancer Res Clin Oncol 114:64-70.

Janssen DB, Scheper A, Kijkhuizen L, et al. 1985. Degradation of halogenated aliphatic compounds by

Xanthobacter autotrophicus GJlO. Appl Environ Microb 49:673-677.

*Jeong K-M, Kaufman F. 1980. Manuscript in preparation, as cited in NASA 1981. Apparently published

as Joeng and Kaufman 1982.

*Jeong K-M, Kaufman F. 1982. Kinetics of the reaction of hydroxyl radical with methane and with nine

Cl- and F-substituted methanes. 1. Experimental results, comparisons, and applications. J Phys Chem

86:1808-1815.
CHLOROMETHANE 218

8. REFERENCES

*Jeong KM, Hsu KJ, Jeffries JB, et al. 1984. Kinetics of the reactions of OH with C2H6, CH3CC13,

CH2ClCClF2, and CH2FCF3. J Phys Chem 88:1222-1226.

*Jiang XZ, White R, Morgan KT. 1985. An ultrastructural study of lesions induced in the cerebellum of

mice by inhalation exposure to methyl chloride. Neurotoxicology 6:93-104.

*Johanson CE. 1980. Permeability and vascularity of the developing brain: Cerebellum vs cerebral cortex.

Brain Research 190:3-16.

*John-Greene JA, Welsch F, Bus JS. 1985. Comments on heart malformations in B6C3F1 mouse fetuses

induced by methyl chloride: Continuing efforts to understand the etiology and interpretation of an unusual

lesion. Teratology 32:483-487.

*Jones MA. 1942. Methyl chloride poisoning. Quart J Med 41:29-43.

Junk GA, Ford CS. 1980. A review of organic emissions from selected combustion processes.

Chemosphere 9:187-230.

*Jury WA, Winer AM, Spencer WF, et al. 1987. Transport and transformation of organic chemicals in the

soil-air-water ecosystem. Rev Environ Contam Toxicol 99:119-164.

*Kadaba PK, Bhagat PK, Goldberger GN. 1978. Application of microwave spectroscopy for simultaneous

detection of toxic constituents in tobacco smoke. Bull Environ Cont Toxicol 19:104-112.

*Kegel AH, McNally WD, Pope AS. 1929. Methyl chloride poisoning from domestic refrigerators. J Am

Med Assoc 93:353-358.

*Kelly TJ, Holdren MW. 1995. Applicability of canisters for sample storage in the determination of

hazardous air pollutants. Atmos Environ 29(19):2595-2608.

*Kelly TJ, Spicer CW, Pollack AJ. 1994. Concentrations and transformations of hazardous air pollutants.

Environ Sci Technol. 28(8):380A-387A.

*Kempkes M, Wiebel FA, Golka K et al. 1996. Comparative genotyping and phenotyping of glutathione

s-transferase gsttl. Arch Toxicol 70:306-309.

*Key JA, Stuewe CW, Standifer RL, et al. 1980. Organic chemical manufacturing. Vol. 8: Selected

processes. EPA-450/3-80-028a. Research Triangle Park, NC: Office of Air, Noise, and Radiation, U.S.

Environmental Protection Agency. (microfiche)

Khalil MAK, Edgerton SA, Rasmussen RA. 1983. A gaseous tracer model for air pollution from

residential wood burning. Environ Sci Technol 17:555-559.

*Khalil MAK, Rasmussen RA. 1981. Atmospheric methylchloride (CH3Cl). Chemosphere 10:1019-1023.

Khalil MAK, Rasmussen RA. 1983. Gaseous tracers of arctic haze. Environ Sci Technol 17:157-164.

*Khalil MAK, Rasmussen RA, Edgerton SA. 1985. Gaseous tracers for sources of regional scale

pollution. J Air Pollut Cont Assoc 35:838-840.
CHLOROMETHANE 219

8. REFERENCES

*Khindaria A, Grover TA, Aust SD. 1995. Reductive dehalogenation of aliphatic halocarbons by lignin

peroxidase of Pharnerochaete chrysosporium. Environ Sci Technol 29(3):719-725.

*Kleindienst TE, Shepson PB, Edney EO, et al. 1986. Wood smoke: Measurement of the mutagenic

activities of its gas and particulate-phase photooxidation products. Environ Sci Technol 20:493-501.

Knackmuss HJ. 1980. Degradation ofhalogenated and sulfonated hydrocarbons. In: Microbial

degradation of xenobiotics and recalcitrant compounds, Sept. 15-17, 1980, 189-212.

Kobaysahi H, Rittmann BE. 1982. Microbial removal of hazardous organic compounds. Environ Sci

Technol 16:170A-182A.

*Koketsu M. 1979. Methyl chloride survey report. E.1 DuPont Corporation, Deepwater, New Jersey.

NTIS PB83-136440. (microfiche)

*Kolkmann FW, Volk B. 1975. [Necroses in the granular cell layer of cerebellum due to methylchloride

intoxication in guinea pigs.] Exp Pathol 10:298-308. (German).

*Komori M, Nishio K, Kitada M et al. 1990. Fetus-specific expression of a form of cytochrome P-450 in

human liver. Biochemistry 29:4430-4433.

*Kopfler FC, Melton RG, Mullaney JL, et al. 1977. Human exposure to water pollutants. Adv Environ

Sci Technol 8:419-433.

*Kornbrust DJ, Bus JS. 1982. Metabolism of methyl chloride to formate in rats. Toxicol Appl Pharmacol

65:135-143.

*Kornbrust DJ, Bus JS. 1983. The role of glutathione and cytochrome P-450 in the metabolism of methyl

chloride. Toxicol Appl Pharmacol 67:246-256.

*Kornbrust DJ, Bus JS. 1984. Glutathione depletion by methyl chloride and association with lipid

peroxidation in mice and rats. Toxicol Appl Pharmacol 72:388-399.

*Kombrust DJ, Bus JS, Doerjer G, et al. 1982. Association of inhaled [14C]methyl chloride with

macromolecules from various rat tissues. Toxicol Appl Pharmacol 65:122-134.

*Kosson DS, Dienemann EA, Ahlert RC. 1985. Characterization and treatability studies of an industrial

landfill leachate (KIN-BUC I). Proc Ing Waste Conf 39:329-341.

*Krishnan K, Andersen ME. 1994. Physiologically-based pharmacokinetic modeling in toxicology. In:

Wallace Hayes, ed. Principles and methods of toxicology. 3rd edition. New York, NY: Raven Press, Ltd.

*Krishnan K, Andersen ME, Clewell HJ III, et al. 1994. Physiologically-based pharmacokinetic modeling

of chemical mixtures. In: R.S.A. Yang, ed. Toxicology of chemical mixtures. New York, NY: Academic

Press.

Krishnan K, Haddad S, Pelekis M. 1995. A simple index for representing the discrepancy between

simulations of physiological pharmacokinetic models and experimental data. Toxicology and Industrial

Health 11(4):413-421.
CHLOROMETHANE 220

8. REFERENCES

*Krotoszynski BK, O’Neill HJ. 1982. Involuntary bioaccumulation of environmental pollutants in

nonsmoking heterogeneous human population. J Environ Sci Health Part A-Environ Sci Eng 17:855-883.

*Landry TD, Gushow TS, Langvardt PW, et al. 1983a. Pharmacokinetics and metabolism of inhaled

methyl chloride in the rat and dog. Toxicol Appl Pharmacol 68:473-486.

*Landry TD, Quast JF, Gushow TS. 1985. Neurotoxicity of methyl chloride in continuously versus

intermittently exposed female C57BL/6 mice. Fund Appl Toxicol 5:87-98.

*Landry TD, Ramsey JC, McKenna MJ. 1983b. Pulmonary physiology and inhalation dosimetry in rats:

Development of a method and two examples. Toxicol Appl Pharmacol 71:72-83.

*Lanham JM. 1982. Methyl chloride: An unusual incident of intoxication [letter]. Can Med Assoc J

126:593.

*Laughton PM, Robertson RE. 1956. Solvolysis in deuterium and hydrogen oxide. Can J Chem

34:1714-1718.

*Leeder JS, Kearns GL. 1997. Pharmacogenetics in pediatrics: Implications for practice. Pediatric Clinics

of North America 44:55-77.

*Leisinger T. 1996. Biodegradation of chlorinated aliphatic compounds. Current Opinion in

Biotechnology 7(3):295-300.

*Leung H. 1993. Physiologically-based pharmacokinetic modeling. In: Ballantine B, Marro T, Turner T,

eds. General and applied toxicology, Vol. 1. New York, NY: Stockton Press, 153-164.

Li JCM, Rossini FD. 1953. Vapor pressures and boiling points of the l- fluoroalkanes, 1-chloroalkanes,

I-bromoalkanes and 1-iodoalkanes, Cl to C20. J Chem Eng Data 6:268-270.

Lillian D, Singh HB, Appleby A, et al. 1975. Atmospheric fates of halogenated compounds. Environ Sci

Technol 9:1042-1048.

Lingaard-Joergensen P, Jacobsen BN. 1986. A data base on behavior and effects of organic pollutants in

waste water treatment processes. In: Comm Eur Communites, Eur 10388. Org Micropollut Aquat Environ

429-439.

*Lovelock JE. 1975. Natural halocarbons in the air and in the sea. Nature 256:193-194.

Lovelock JE. 1977. Halogenated hydrocarbons in the atmosphere. Ecotoxicol Environ Safety 1:399-406.

*Lurker PA, Clark CS, Elia VJ. 1983. Worker exposure to chlorinated organic compounds from the

activated-sludge wastewater treatment process. Am Ind Hyg Assoc J 44:109-l 12.

*Lyman WJ. 1982. Handbook of chemical property estimation methods. New York, NY:

McGraw-Hill,960, 4.1-4.33.

*Mabey W, Mill T. 1978. Critical review of hydrolysis of organic compounds in water under

environmental conditions. J Phys Chem Ref Data 7:383-415.
CHLOROMETHANE 221

8. REFERENCES

*MacDonald JDC. 1964. Methyl chloride intoxication report of 8 cases. J Occ Med 6:81-84.

Mackay D, Shiu WY. 1981. A critical review of Henry’s law constants for chemicals of environmental

interest. J Phys Chem Ref Data 19:1175-l 199.

*Mackie IJ. 1961. Methyl chloride intoxication. Med J Australia 1:203-205.

MacPhail RC, Berman E, Elder JA, et al. 1995. A multidisciplinary approach to toxicological screening:

IV. Comparison of results. Journal of Toxicology and Environmental Health 45(2):21l-220.

Markel HL, Froneberg B. 1983. Health hazard evaluation--report no. HETA 80-010-l 199. Cities Service

Company, Butyl Rubber Plant, Lake Charles Louisiana. Cincinnati, OH: U.S. Department of Health and

Human Services, Public Health Service, Centers for Disease Control, National Institute for Occupational

Safety and Health.

Mayo D, Collins J, Riordan B. 1980. Economic impact analysis of proposed testing regulations for

chloromethane and chlorobenzenes. Govt Rep Announce Ind, Issue 25.

McClenny WA, Fortune CR. 1995. Superfund contract laboratory program method evaluation--ambient

air volatile organic compounds from canisters. J Environ Sci Health A 30(4):901-919.

McConnell G, Ferguson DM, Pearson CR. 1975. Chlorinated hydrocarbons and the environment.

Endeavour 34:13-38.

*McKenna MJ, Burek JD, Henck JW, et al. 1981b. Methyl chloride: A 90-day inhalation toxicity study in

rats, mice and beagle dogs. Toxicology Research Laboratory, Dow Chemical USA, Midland MI. OTS

submission document 40-8120723. Microfiche 511317.

*McKenna MJ, Gushow TS, Bell TJ, et al. 1981a. Methyl chloride: A 72-hour continuous (-23-l/2

hr/day) inhalation toxicity study in dogs and cats. Unpublished study. Toxicology Research Laboratory,

Dow Chemical USA, Midland MI. OTS submission document 40-8120723. Microfiche 511317.

*McNally WD. 1946. Eight cases of methyl chloride poisoning with three deaths. J Ind Hyg Toxicol

28:94-97.

*McNeal TP, Hollifield HC, Diachenko GW. 1995. Survey of trihalomethanes and other volatile chemical

contaminants in processed foods by purge-and-trap capillary gas chromatography with mass selective

detection. J Aoac Int 78(2):391-397.

*Merck. 1989. The Merk index, an encyclopedia of chemicals, drugs, and biologicals, Eleventh Edition.

Rahway, NJ: Merck and Co., Inc.

*Messmer M, Wohlfarth G, Dickert G. 1993. Methyl chloride metabolism of the strictly anaerobic, methyl

chloride-utilizing homoacetogen strain MC. Arch Microbial 160:383-387.

Mill T. 1982. Hydrolysis and oxidation processes in the environment. Environ Toxicol Chem 1:135-141.

Mill T, Winterle JS, Davenport JE. 1982. Validation of estimation techniques for predicting environmental

transformation of chemicals. Prepared for U.S. Environmental Protection Agency, Washington, DC.
CHLOROMETHANE 222

8. REFERENCES

Miller DL, Senser DW, Cundy VA, et al. 1984. Chemical considerations in the incineration of chlorinated

methanes: I-methyl chloride. Hazard Waste 1:l-18.

*Minami M, Inagaki H, Katsumata M, et al. 1993. Inhibitory action of chloramine on

formate-metabolizing system. Studies suggested by an unusual case record. Biochem Pharmacol

45(5):1059-1064

*Minami M, Katsumata M, Miyake K, et al. 1992. Dangerous mixture of household detergents in an

old-style toilet: A case report with simulation experiments of the working enviroment and warning of

potentioal hazard relevant to the general environment. Humans Experimental Toxicology 11:27-34.

*Mitchell RI, Pavkov K, Everett RM, Holzworth DA. 1979. A 90-day inhalation toxicology study in

F-344 rats and B6C3F1 mice exposed to atmospheric methyl chloride gas. Unpublished study. Battelle

Columbus Laboratory, Columbus, OH, for Chemical Industry Institute of Toxicology, Research Triangle

Park, NC. Microfiche 205952.

Molton PM, Hallen RT, Payne JW. 1987. Study of vinyl chloride formation at landfill sites in California:

Report. NTIS PB87-161279/GAR.

Morgan A, Black A, Belcher DR. 1972. Studies on the absorption of halogenated hydrocarbons and their

excretion in breath using 38Cl tracer techniques. Ann Occ Hyg 15:273-282.

*Morgan A, Black A, Bercher DR. 1970. The excretion in breath of some aliphatic halogenated

hydrocarbons following administration by inhalation. Ann Occ Hyg 13:219-233.

*Morgan KT, Swenberg JA, Hamm TE Jr., et al. 1982. Histopathology of acute toxic response in rats and

mice exposed to methyl chloride by inhalation. Fund Appl Toxicol 2:293-299.

*Morselli PL, France-Morselli R, Bossi L. 1980. Clinical Pharmacokinetics in Newborns and Infants.

Clinical Pharmacokinetics 5:485-527.

Murray AJ, Riley JP. 1973. The determination of chlorinated aliphatic hydrocarbons in air, natural waters,

marine organisms, and sediments. Anal Chim Acta 65:261-270.

Narotsky MG, Kavlock RJ. 1995. A multidisciplinary approach to toxicological screening: II.

Developmental toxicity. Journal of Toxicology and Environmental Health 45(2):145-171.

*NAS/NRC. 1989. Biological markers in reproductive toxicology. National Research Council. Board of

Environmental Studies and Toxicology. Committee on Biological Markers, 15-35.

*NASA. 1981. Chemical kinetic and photochemical data for use in stratospheric modeling evaluation

number 4: NASA panel for data evaluation. NASA-CR-163973. JPL-BUP-81-3. Pasadena, CA: National

Aeronautics and Space Administration, Jet Propulsion Lab, 131.

NATICH. 1988. National Air Toxics Information Clearinghouse. Database report of state, local and EPA

air toxics activities. Office of Air Quality Planning and Standards, U.S. Environmental Protection Agency,

Research Triangle Park, NC.

*NATICH. 1992. Database. National Air Toxics Information Clearinghouse.
CHLOROMETHANE 223

8. REFERENCES

Neely WB. 1976. Predicting the flux of organics across the air/water interface. In:3rd National

Conference: Control of Hazardous Material Spills, 197-200.

Nelson E. 1992. Determination of mercapturic acid excretions in exposure control of toxicants. Critical

Reviews in Toxicology 22(5-6):371-389.

NFPA. 1994. Fire protection guide to hazardous materials, Eleventh Edition. Quincy, MA: National

Fire Protection Association.

NIOSH. 1984. Monohalomethanes: Methyl chloride CH3CL, methyl bromide CH3BR, methyl iodide

CH3I. In: Current intelligence bulletin 43. Cincinnati, OH: Cincinnati, OH: U. S. Department of Health

and Human Services, Public Health Service,Centers for Disease Control, National Institute for Occupational

Safety and Health, 22.

NIOSH. 1985. NIOSH pocket guide to chemical hazards. Washington, DC: National Institute for

Occupational Safety and Health.

NIOSH. 1988. National occupational exposure survey as of May 10, 1988. Washington, DC: U.S.

Department of Health and Human Services, National Institute for Occupational Safety and Health, 11.

NIOSH. 1991. National occupational exposure survey 1981 -1983. U.S. Department of Health and

Human Services, National Institute for Occupational Safety and Health, Cincinnti, OH.

*NIOSH. 1992. NIOSH recommendations for occupational safety and health. Compendium of policy

documents and statements. Division of Standards Developmental and Technology Transfer, National

Institute for Occupational Safety and Health, Centers for Disease Control, Public Health Service, U. S

Department of Health and Human Services.

*NIOSH. 1994. Method 1011, methyl chloride. NIOSH manual of analytical methods (NMAM), Fourth

Edition. National Institute for Occupational Safety and Health, Centers for Disease Control, Public Health

Service, U. S Department of Health and Human Services.

Nisbet ICT, Siegel DM, Paxton MB, et al. 1984. Carcinogenic risk assessment for occupational exposure

to monohalomethanes. Final report. U.S. Department of Health and Human Services, Division of

Standards Development and Technology Transfer, National Institute for Occupational Safety and Health,

Cincinnati, OH.

*Nolan RJ, Rick DL, Landry TD, et al. 1985. Pharmacokinetics of inhaled methyl chloride (CH3Cl) in

male volunteers. Fund Appl Toxicol 5:361-369.

*NPLTDB. 1989. National Priority List Technical Data Base. BASE IV format, 2/89 version.

*NRC. 1993. Pesticides in the Diets of Infants and Children. National Research Council. Washington DC:

National Academy Press.

O’Donoghue JL. 1985. Aliphatic halogenated hydrocarbons, alcohols, and acids and thioacids. In:

O’Donoghue, ed. Volume 2: Neurotoxicity of industrial and commercial chemicals. Boca Raton, FL: CRC

Press, Inc., 99-126.
CHLOROMETHANE 224

8. REFERENCES

*OHM-TADS. 1988. Oil and Hazardous Materials - Technical Assistance Data System. U.S.

Environmental Protection Agency, National Institute of Health. Computer database on-line: December 5,

1988.

*Oliver KD, Adams JR, Daughtrey EH, JR. 1996. Technique for monitoring toxic vocs in air: Sorbent

preconcentration, closed-cycle cooler cryofocusing, and GC/MS analysis. Environ Sci Technol

30(6):1939-1945.

Oomens AC, Noten LG. 1984. Picomole amounts of methyl chloride (chloromethane) by reaction gas

chromatography. J High Resolut Chromatogr Chromatogr 7:280-281.

Osborne JS, Adamek S, Hobbs ME. 1956. Some components of gas phase of cigarette smoke. Anal Chem

28:211-215.

*OSHA. 1974. Occupational Safety and Health Standards. 29 CFR 1910.1000.

*OTA. 1990. Neurotoxicology: Identifying and controlling poisons of the nervous system. Office of

Technology Assessment, Washington, DC. OTA-BA-438.

*Otson R. 1987. Purgeable organics in Great Lakes raw and treated water. Int J Environ Anal Chem

31:41-53.

*Otson R, Polley GL, Robertson JL. 1986. Chlorinated organics from chlorine used in water treatment.

Water Res 20:775-779.

*Owen GM, Brozek J. 1966. Influence of age, sex, and nutrition on body composition during childhood

and adolescence. In: Falkner F, ed. Human development. Philadelphia, PA: Saunders, 222-238.

*Page GW. 1981. Comparison of groundwater and surface water for patterns and levels of contamination

by toxic substances. Environ Sci Technol 15:1475-1481.

*Palmer TY. 1976. Combustion sources of atmospheric chlorine. Nature (London) 263:44-46.

Pankow JF, Rosen ME. 1988. Determination of volatile compounds in water by purging directly to a

capillary column with whole column cryotrapping. Environ Sci Technol 22:398-405.

*Paraskevopoulos G, Singleton DL, Irwin RS. 1981. Rates of OH radical reactions. 8. Reactions with

CH2FC1, CHF2C1, CHFC12, CH3CF2C1, CH3C1, and C2H5Cl at 297 K. J Phys Chem 85:561-564.

Peers AM. 1985. The determination of methyl chloride in air. IARC Sci Pub168:219-225.

*Pellizzari ED, Hartwell TD, Harris BSH, et al. 1982. Purgeable organic compounds in mother’s milk.

Bull Environ Cont Toxicol 28:322-328.

Penkett SA, Derwent RG, Fabian P. 1980. Methyl chloride in the stratosphere. Nature 283:58-60.

*Perry RA, Atkinson R, Pitts JN Jr. 1976. Rate constants for the reaction of OH radicals with CHFC12

and CH3Cl over the temperature range 298-423 K and with CH2C12 at 298 K. J Chem Phys

64:1618-1620.
CHLOROMETHANE 225

8. REFERENCES

*Peter H, Deutschman S, Muelle A, et al. 1989b. Different affinity of erythrocyte glutathione-S-transferase

to methyl chloride in humans. Arch Toxicol Suppl 13:128-132.

*Peter H, Deutschmann S, Reichel C, et al. 1989a. Metabolism of methyl chloride by human erythrocytes.

Arch Toxicol 63(5):351-355.

*Peter H, Laib RJ, Ottenwalder H, et al. 1985. DNA-binding assay of methyl chloride. Arch Toxicol

57:84-87.

Petros JK, Alsop GM, Conway RA. 1984. Rapid extraction methods for organics in soil. ASTM Spec

Tech Publ 851:92-99.

*Philbrick CA, Aggarwal SK, Puri IK. 1993. The extinction of methan/methyl chloride nonpremixed

flames. Hazardous Waste & Hazardous Materials 10(1):71-79.

Phillips D. 1978. Gas-phase photoprocesses. Photochemistry 9:140-192.

*Pincince AB. 1988. Estimating volatile organic emissions from publicly owned treatment works. J Water

Pollut Cont Fed 59:119-121.

Pleil JD, Oliver KD, McClenny WA. 1988. Ambient air analyses using nonspecific flame ionization and

electron capture detection compared to specific detection by mass spec. J Air Poll Cont Assoc

38:1006-1010.

*Plumb RH, Jr. 1991. The occurrence of Appendix IX organic constituents in disposal site ground water.

Ground Water Monitoring Review 12:157-64.

Politis MJ, Schaumburg HH, Spencer PS. 1980. Neurotoxicity of selected chemicals. In: Spencer PS,

Schaumburg HH, eds. Experimental and clinical neurotoxicology. London, UK: Williams and Wilkins,

613-630.

*Poulin P, Krishnan K. 1996. A tissue composition-based algorithm for predicting tissue: Air partiton

coefficients of organic chemicals. Toxicol Appl Pharmacol 136(1):126-130.

*Putz-Anderson V, Setzer JV, Croxton JS. 1981b. Effects of alcohol, caffeine and methyl chloride on man.

Psycho1 Rep 48:715-725.

*Putz-Anderson V, Setzer JV, Croxton JS, et al. 1981a. Methyl chloride and diazepam effects on

performance. Stand J Work Environ Health 7:8-13.

*Raalte HGS, van Velzen HGECT. 1945. Methyl chloride intoxication. Ind Med 14:707-709.

*Rafnsson V, Gudmundsson G. 1997. Long-term follow-up after methyl chloride intoxication. Archives of

Environmental Health 52(5):355-359.

Rao PSC, Hornsby AG, Jessup RE. 1985. Indices for ranking the potential for pesticide contamination of

groundwater. Soil Crop Sci Sot FL Proc 44:1-8.
CHLOROMETHANE 226

8. REFERENCES

*Rasmussen RA, Khalil MAK. 1983. Natural and anthropogenic trace gases in the lower troposphere of

the arctic. Chemosphere 12:371-375.

*Rasmussen RA, Rasmussen LE, Khalil MAK. 1980. Concentration distribution of methyl chloride in the

atmosphere. J Geophys Res 85:7350-7356.

Reddy SR, Anandakumar R, Satyanarayan A. 1973. Vapor pressure of low boiling organic compounds.

Chem Ind Dev 7:21-25.

*Redford-Ellis M, Gowenlock AH. 1971a. Studies on the reaction of chloromethane with preparations of

liver, brain and kidney. Acta Pharmacol Toxicol 30:49-58.

*Redford-Ellis M, Gowenlock AH. 1971b. Reaction of chloromethane with human blood. Acta Pharmacol

Toxicol 30:36-48.

Reinhard TE, Ward DE. 1995. Factors affecting methyl chloride emissions from forest biomass

combustion. Env Sci Technol 29:825-832.

Repko JD. 1981. Neurotoxicity of methyl chloride. Neurobehav Toxicol Teratol 3:425-429.

*Repko JD, Jones PD, Garcia LS Jr., et al. 1977. Behavioral and neurological effects of methyl chloride.

Behavioral and neurological evaluation of workers exposed to industrial solvents: Methyl chloride.

Cincinnati, OH: National Institute for Occupational Safety and Health, Centers for Disease Control, Public

Health Service, Department of Health and Human Services. NIOSH publication 77-125.

Repko JD, Lasley SM. 1979. Behavioral, neurological, and toxic effects of methyl chloride: A review of

the literature. CRC Crit Rev Toxicol 6:283-302.

*Reynolds ES, Yee AG. 1967. Liver parenchymal cell injury. V. Relationships between patterns of

chloromethane-14C incorporation into constituents of liver in vivo and cellular injury. Lab Invest

16:591-603.

*Riddick JA, Bunger WB, Sakano TK. 1986. Organic solvents: Physical properties and methods of

purification. Techniques of chemistry. 4th ed. New York, NY: Wiley-Interscience, 1325.

*Ristau C, Bolt HM, Vangala RR. 1989. Detection of DNA-protein crosslinks in the kidney of male

B6C3F1 mice after exposure to methly chloride. Arch Toxicol Supp 13 243:244-245.

*Ristau C, Bolt HM, Vangala RR. 1990. Formation and repair of DNA leisons in kidneys of male mice

after acute exposure to methyl chloride. Arch Toxicol. 64:254-256.

*Robbins DE. 1976. Photodissociation of methyl chloride and methyl bromide in the atmosphere. Geophys

Res Lett 3:213-216.

*Robertson RE, Heppolette RL, Scott JMW. 1959. A survey of thermodynamic parameters for solvolysis

in water. Can J Chem 37:803-824.

Robinson E, Rasmussen RA, Krasnec J, et al. 1977. Halocarbon measurements in the Alaskan troposphere

and lower stratosphere. Atmos Environ 11:215-223.
CHLOROMETHANE 227

8. REFERENCES

*RTECS. 1988. Registry of Toxic Effects of Chemical Substances. December 5, 1988.

*Rudolph J, Khedim A, Koppmann R, et al. 1995. Field study of the emissions of methyl chloride and

other halocarbons from biomass burning in western Africa. J Atmos Chem 22:67-80.

Ruhe RL. 1976. Health hazard evaluation--toxicity determination report no. 75180-311. The Foxboro

Company, Highland Plant, Bridgewater, Massachusetts. Cincinnati, OH: U.S. Department of Health and

Human Services, Public Health Service, Centers for Disease Control, National Institute for Occupational

Safety and Health.

*Rushbrook CJ. 1984. Evaluation of toxicological test methods used in estimating potential human health

hazards. Dominant lethal study of chloromethane in rats. Unpublished study. Prepared by SRI

International, Menlo Park, CA, for HERD, U.S. Environmental Protection Agency. OTS submission

document 40-8420732. Microfiche 511320.

*Sahel GV, Clark TP. 1984. Volatile organic compounds as indicators of municipal solid waste leachate

contamination. Waste Manag Res 2:119-130.

Sanhueza E. 1977. The chlorine atom sensitized oxidation of HCCL3, HCF2CL + HCF3. J Photochem

7:325-334.

Sanhueza E, Heicklen J. 1975. Chlorine-atom sensitized oxidation of dichloromethane and chloromethane.

J Phys Chem 79:7-11.

*SANSS. 1988. Structure and Nomenclature Search System. Chemical Information Systems, Inc.

Sayers RR, Yant WP, Thomas BGH, et al. 1929. Physiological response attending exposure to vapors of

methyl bromide, methyl chloride, ethyl bromide and ethyl chloride. Public Health Bulletin 185.

Washington, DC: Treasure Department, United States Public Health Service.

*Scharnweber HC, Spears GN, Cowles SR. 1974. Chronic methyl chloride intoxication in six industrial

workers. J Occ Med 16:112-l 13.

Schroder KR, Hallier E, Meyer DJ, et al. 1996. Purification and characterization of a new glutathione

S-transferase, class O, from erythrocytes. Arch Toxicol 70(9):559-566.

Schwartz BS, Ford P, Bolla KI, et al. 1990. Solvent-association decrements in olfactory function in paint

manufacturing workers. American Journal of Industrial Medicine 18(6):697-706.

Schwetz BA. 1995. Use of mechanistic and pharmacokinetic data for risk assessment at the National

Institute of Environmental Health Sciences (NIEHS). Toxicology Letters79(l-3):29-32.

*Setchell BP, Waites GMH. 1975. The blood testis barrier. In: Creep RO, Astwood EB, eds., Geiger SR,

executive ed. Handbook of physiology: Endocrinology V (Chapter 6). Washington DC: American

Physiological Society.

*Shah JJ, Singh HB. 1988. Distribution of volatile organic chemicals in outdoor and indoor air. Environ

Sci Tech 22:1381-1388.
CHLOROMETHANE 228

8. REFERENCES

*Shirey RE. 1995. Rapid analysis of environmental samples using solid-phase microextraction SPME and

narrow bore capillary columns. Hrc Journal of High Resolution Chromatography 18(8):495-499.

Shold DM, Rebbert RE. 1978. The photochemistry of methyl chloride. J Photochem 9:499-517.

*Shuckrow AJ, Pajah AP, Touhill CJ. 1982. Hazardous waste leachate management manual, Appendix A.

Noyes Data Corporation, Park Ridge, NJ, 126-149.

*Sieber WK Jr., Sundin DS, Frazier TM, et al. 1991. Development, use, and availability of a job exposure

matrix based on National Occupational Hazard Survey data. Am J Ind Med 20:163-174.

Simmon VF. 1978. Structural correlations of carcinogenic and mutagenic alkyl halides. Department of

Health, Education and Welfare, Washington, DC, 163-171.

Simmon VF. 1981. Applications of the Salmonella/microsome assay. Short-term Tests Chem Carcinogen

120-126.

Simmon VF, Kauhanen K, Tardiff RG. 1977. Mutagenic activity of chemicals identified in drinking water.

Dev Toxicol Environ Sci 2:249-258.

Simmon VF, Tardiff RG. 1978. Mutagenic activity of halogenated compounds found in chlorinated

drinking water. In: Conference: Water Chlorination: Environ Impact Health Effects 2:417-431.

Singh HB. 1977. Atmospheric halocarbons: Evidence in favor of reduced average hydroxyl radical

concentration in the troposphere. Geophys Res Lett 5:101-104.

*Singh HB, Salas JL, Shigeishi H, et al. 1979. Atmospheric halocarbons, hydrocarbons and sulfur

hexafluoride: Global distributions, sources and sinks. Science 203:899-903.

*Singh HB, Salas JL, Stiles RE. 1982a. Distribution of selected gaseous organic mutagens and suspect

carcinogens in ambient air. Environ Sci Technol 16:872-880.

*Singh HB, Salas L, Shigeishi H, et al. 1977a. Urban-nonurban relationships of halocarbons, sulfur

hexafluoride, nitrous oxide, and other atmospheric trace constituents. Atmos Environ 11:819-828.

Singh HB, Salas LJ, Cavanagh LA. 1977b. Distribution sources and sinks of atmospheric halogenated

compounds. J Air Pollut Cont Assoc 27:332-336.

*Singh HB, Salas LJ, Smith AJ, et al. 1981a. Measurements of some potentially hazardous organic

chemicals in urban environments. Atmos Environ 15:60l-612.

*Singh HB, Salas LJ, Stiles R. 1981b. Trace chemical in the clean troposphere. Environmental Sciences

Research Laboratory, U.S. EPA, Research Triangle Park, NC. EPA 600/3-81-055. NTIS PB82-249202.

(microfiche)

*Singh HB, Salas LJ, Stiles RE. 1983. Methyl halides in and over the eastern Pacific (40 deg N -32 deg

S). J Geophys Res 88:3684-3690.
CHLOROMETHANE 229

8. REFERENCES

Sizemore OJ, Amler RW. 1996. Characteristics of ATSDR’s adult and pediatric environmental

neurobehavioral test batteries. NeuroToxicology 17(1):229-236.

*Smith WW. 1947. The acute and chronic toxicity of methyl chloride. III. Hematology and biochemical

studies. J Ind Hyg Toxicol 29:185-188.

*Smith WW, von Oettingen. 1947b. The acute and chronic toxicity of methyl chloride. II.

Symptomatology of animals poisoned by methyl chloride. J Ind Hyg Toxicol 29:123-128.

*Smith WW, von Oettingen WF. 1947a. The acute and chronic toxicity of methyl chloride. I. Mortality

resulting from exposures to methyl chloride in concentrations of 4,000 to 300 parts per million. J Ind Hyg

Toxicol 29:47-52.

*Snider EH, Manning FS. 1982. A survey of pollutant emission levels in waste waters and residuals from

the petroleum refining industry. Environ Int 7:237-258.

Spence JW, Hanst PL, Gay BW, Jr. 1976. Atmospheric oxidation of methyl chloride, methylene chloride

and chloroform. J Air Pollut Cont Assoc 76:994-996.

Sperling F, Macri FJ, Von Oettingen WF. 1950. Distribution and excretion of intravenously administered

methyl chloride. Am Med Assoc Arch Ind Hyg Occ Med. 215-224.

*Spevak L, Nadj V, Felle D. 1976. Methyl chloride poisoning in four members of a family. Br J Ind Med

33:272-274.

*SRC. 1994. Henry’s Law Constant Program (HENRYWIN, version 2.50, serial H0142). Syracuse

Research Center, Chemical Assessment Division, Environmental Chemistry Center, Syracuse, NY.

*SRC. 1995. Octanol-Water Partition Coefficient Program (KOWWIN, version 1.37, serial LO148).

Syracuse Research Center, Chemical Hazard Assessment Division, Environmental Chemistry Center,

Syracuse, NY.

Staples CA, Werner A, Hoogheem T. 1985. Assessment of priority pollutant concentrations in the United

States using STORET database. Environ Toxicol Chem 4:131-142.

*State of Kentucky. 1986. New or modified sources emitting toxic air pollutants. Department for

Environmental Protection. 401 KAR 63:022.

*Stewart RD, Hake CL, Zvu A, et al. 1980. Methyl chloride: Development of a biologic standard for the

industrial worker by breath analysis. Prepared for National Institute for Occupational Safety and Health,

Cincinnati, OH. NTIS PB81-167686. (microfiche)

*Stirling DI, Dalton H. 1979. The fortuitous oxidation and cometabolism of various carbon compounds by

whole-cell suspensions of Methylococcus capsulatus (Bath). Ferns Microbial Lett 5:315-318.

Sujbert L. 1967. [Studies on the degradation of methyl chloride in mice.] Arch Toxicol (Germany, West)

22:233-235. (German).
CHLOROMETHANE 230

8. REFERENCES

*Tait VK, Moore RM. 1995. Methyl chloride (CH3Cl) production in phytoplankton cultures. Limnology

and Oceanography 40(1):189-195.

*Tassios S, Packham DR. 1985. The release of methyl chloride from biomass burning in Australia. J Air

Pollut Contr Assoc 35:41-42.

*Taylor PH, Dellinger B. 1988. Thermal degradation characteristics of chloromethane mixtures. Environ

Sci Technol 22:438-447.

*Thordarson 0, Gudmundsson G, Bjamason O, et al. 1965. Metylkloridforgiftning. Nord Med

18:150-154. (Norwegian, English abstract).

*Traunecker J, Preuss A, Diekert G. 1991. Isolation and characterization of a methyl chloride utilizing,

strictly anaerobic bacterium. Arch. Microbial. 156:416-421.

*TRI96. 1998. Toxic Chemical Release Inventory. National Library of Medicine, National Toxicology

Information Program, Bethesda, MD.

*U. S. Congress. 1986. Superfund admendment and reauthorization act of 1986. Title III-emergency

planning in community right to know. Ninty-ninth congress of the United States of America.

*U.S. Congress 1990. Clean Air Act Amendments. Title III, Hazardous Air Pollutants, Section 112,

Harzardous Air Pollutents as amended, October 26, 1990. 101 Congress of the United States of America,

Second session report 101-952.

Umbreit GR, Grob RL. 1980. Experimental application of gas chromatographic headspace. J Environ Sci

Health Part A Environ Sci Eng 15:429-466.

*USDOC. 1996. U.S. Merchandise Import and Export Trade. Retrieved from National Trade Data bank.

United States Department of Commerce, Bureau of Census, June 29, 1996.

USITC. 1985. U.S. International Trade Commission. Synthetic organic chemicals, United States

production and sales, 1984. Publication no. 1745. Washington, DC: U.S. Government Printing Office,

258, 259.

USITC. 1987. U.S. International Trade Commission. Synthetic organic chemicals, United States

production and sales, 1987. Publication no. 2118. Washington, DC: U.S. Government Printing Office,

15-7, 15-29, 15-36, 15-37, 15-38.

*van Doom R, Borm PJA, Leijdekkers Ch-M, et al. 1980. Detection and identification of s-methylcysteine

in urine of workers exposed to methyl chloride. Int Arch Occup Environ Health 46:99-109.

*Vannelli T, Studer A, Kertesz M, et al. 1998. Chloromethane metabolism by Methylobacterium sp. strain

cm4. Applied and Environmental Microbiology 64(5):1933-1936.

Vaughn P, Lindahl T, Sedgwick B. 1993. Induction of the adaptive response of Escherichia coli to

alkylation damage by the environmental mutagen, methyl chloride. Mutation Research, DNA Repair

293(3):249-257.
CHLOROMETHANE 231

8. REFERENCES

*Venkataramani ES, Ahlert RC, Corbo P. 1984. Biological treatment of landfill leachates. CRC Crit Rev

Environ Cont 14:333-376.

*Verrihe MP, Vachez M. 1949. [Severe acute nephritis after methyl chloride poisoning.] Lyon Med

1:296-297. (French).

Vidal-Madjar C, Gonnord MF, Benchah F, et al. 1978. Performances of various adsorbents for the

trapping and analysis of organohalogenated air pollutants by gas chromatography. J Chromatogr Sci

16:190-196.

*Vieira I, Sonnier M, Cresteil T. 1996. Developmental expression of CYP2El in the human liver:

hypermethylation control of gene expression during the neonatal period. European Journal of Biochemistry

238:476-483.

*Vogel TM, Criddle, CS, McCarty PL. 1987. Transformations of halogenated aliphatic compounds.

Environ Sci Technol 21:722-736.

von Oettingen WF. 1964. Halogenated hydrocarbons of industrial and toxicological importance. New

York, NY: Elsevier Publishing Co.

*van Oettingen WF, Powell CC, Sharpless NE, et al. 1949. Relation between the toxic action of

chlorinated methanes and their chemical and physicochemical properties. Health Bulletin 191. Washington,

DC: Public Health Service, National Institutes of Health.

*van Oettingen WF, Powell CC, Sharpless NE, et al. 19.50. Comparative studies of the toxicity and

pharmacodynamic action of chlorinated methanes with special reference to their physical and chemical

characteristics. Arch Int Pharmacodyn Ther 81:17-34.

*Wang Z, Minarni M. 1996. Effects of chloramine on neuronal cholinergic factors. Biogenic Amines

12(3):213-223.

*Warhlom M, Rane A, Alexandrie AK, et al. 1995. Genotypic and phenotypic determination of

polymorphic glutathione transferase Tl in a Swedish population. Pharmacogenetics 5:252-254.

*Warholm M, Alexandrie AK, Hogberg J, et al. 1994. Polymorphic distribution of glutathione transferase

activity with methyl chloride in human blood. Pharmacogenetics 4:307-311.

Waters MD, Stack HF, Jackson MA, et al. 1994. The performance of short-term tests in identifying

potential germ cell mutagens: A qualitative and quantitative analysis. Mutation Research 341(2):109-131.

Watts H. 1971. Temperature dependence of the diffusion of carbon tetrachloride, chloroform, and

methylene chloride vapors in air by a rate of evaporation method. Can J Chem 49:67-73.

*Weast RC. 1988. CRC handbook of chemistry and physics, 69th Edition. Boca Raton, FL: CRC Press.

*Weinstein A. 1937. Methyl chloride (refrigerator) gas poisoning. J Am Assoc 108:1603-1605.

*Weitzman SA, Stossel TP. 1981. Mutation caused by human phagocytes. Science 212:546-547.
CHLOROMETHANE 232

8. REFERENCES

*West JR, Smith HW, Chasis H. 1948. Glomerular filtration rate, effective renal blood flow, and maximal

tubular excretory capacity in infancy. J of Pediatrics 32a:10-18.

White JL, Somers PP. 1931. The toxicity of methyl chloride for laboratory animals. J Ind Hyg

13:213-275.

*WHO 1984. Guidelines for drinking-water quality. Volume 1: Recommendations. World Health

Organization.

*Widdowson EM, Dickerson JWT. 1964. Chapter 17: Chemical composition of the body. In: Comar CL

and Bronner F, eds. Mineral metabolism: An advanced treatise, Volume II - The elements part A. New

York: Academic Press.

Wilkes BE, Priestley LJ Jr., Scholl LK. 1982. An improved thermal desorption gas chromatography-mass

spectrometry method for the determination of low parts-per-billion concentrations of chloromethane in

ambient air. Microchem J 27:420-424.

Willson KS, Walker WO. 1944. Methyl chloride and mixtures of methyl chloride with dichlorodifluoromethane. Ind Eng Chem 36:466-468.

Willson KS, Walker WO, Rinelli WR, et al. 1943. Liquid methyl chloride. Chem Eng News

21:1254-1261.

*Wolkowski-Tyl R. 1985. Response to comments on heart malformations in B6C3F1 mouse fetuses

induced by methyl chloride: Continuing efforts to understand the etiology and interpretation of an unusual

lesion. Teratology 32:489-492.

*Wolkowski-Tyl R, Lawton AD, Phelps M, et al. 1983b. Evaluation of heart malformations in B6C3F1

mouse fetuses induced by in utero exposure to methyl chloride. Teratology 27:197-206.

*Wolkowski-Tyl R, Phelps M, Davis JK. 1983a. Structural teratogenicity evaluation of methyl chloride in

rats and mice after inhalation exposure. Teratology 27:181-195.

*Wood MWW. 1951. Cirrhosis of the liver in a refrigeration engineer, attributed to methyl chloride.

Lancet 1:508-509.

*Working PK, Bus JS. 1986. Failure of fertilization as a cause of preimplantation loss induced by methyl

chloride in Fischer 344 rats. Toxicol Appl Pharmacol 86:124-130.

*Working PK, Bus JS, Hamm TE Jr. 1985a. Reproductive effects of inhaled methyl chloride in the male

Fischer 344 rat. I. Mating performance and dominant lethal assay. Toxicol Appl Pharmacol 77:133-143.

*Working PK, Bus JS, Hamm TE Jr. 1985b. Reproductive effects of inhaled methyl chloride in the male

Fischer 344 rat. II. Spermatogonial toxicity and sperm quality. Toxicol Appl Pharmacol 77:144-157.

*Working PK, Chellman GJ. 1989. The use of multiple endpoints to define the mechanism of action of

reproductive toxicants and germ cell mutagens. Progress in Clinical and Biological Research.

302:21l-224.
CHLOROMETHANE 233

8. REFERENCES

*Working PK, Doolittle DJ, Smith-Oliver T, et al. 1986. Unscheduled DNA synthesis in rat tracheal

epithelial cells, hepatocytes and spermatocytes following exposure to methyl chloride in vitro and in vivo.

Mutat Res 162:219-224.

*Xu D, Peter H, Hallier E, et al. 1990. Hemoglobin adducts of monohalomethanes. Industrial Health

28:121-123.

Yoshida K, Shigeoka A, Yamauchi F. 1983. Relationship between molar refraction and N-octanol/water

partition coefficient. Ecotox Environ Saf 7:558-565.

*Yung YL, McElroy MB, Worfy SC. 1975. Atmospheric halocarbons: A discussion with emphasis on

chloroform. Geophys Res Lett 2:397-399.

Yurteri C, Ryan DF, Callow JJ, et al. 1987. The effect of chemical composition of water on Henry’s law

constant. Water Poll Cont Fed J 59:950-956.

*Zafiriou OC. 1975. Reaction of methyl halides with seawater and marine aerosols. J Mar Res 33:75-81.

*Zaidman OA, Sadogurskii MN, Krishstal NF, et al. 1991. Treatment of vinyl chloride to remove methyl

chloride by esterification with alcohol solutions of sodium hydroxide. Kimimicheskaya Promyshlennost

(English Editiion) 23(11):643-648.

*Ziegler EE, Edwards BB, Jensen RL et al. 1978. Absorption and retention of lead by infants. Pediatr Res

12:29-34.

*Zitomer DH, Speece R. 1995. Methanethiol in nonacclimated sewage sludge after addition of chloroform

and other toxicants. Environ Sci Technol 29:762-768.

CHLOROMETHANE 235

9. GLOSSARY

Absorption-The taking up of liquids by solids, or of gases by solids or liquids.

Acute Exposure-Exposure to a chemical for a duration of 14 days or less, as specified in the

Toxicological Profiles.

Adsorption-The adhesion in an extremely thin layer of molecules (as of gases, solutes, or liquids) to the

surfaces of solid bodies or liquids with which they are in contact.

Adsorption Coefficient (Koc)-The ratio of the amount of a chemical adsorbed per unit weight of organic

carbon in the soil or sediment to the concentration of the chemical in solution at equilibrium.

Adsorption Ratio (Kd)-The amount of a chemical adsorbed by a sediment or soil (i.e., the solid phase)

divided by the amount of chemical in the solution phase, which is in equilibrium with the solid phase, at a

fixed solid/solution ratio. It is generally expressed in micrograms of chemical sorbed per gram of soil or

sediment.

Benchmark Dose (BMD)-is usually defined as the lower confidence limit on the dose that produces a

specified magnitude of changes in a specified adverse response. For example, a BMD,, would be the dose

at the 95% lower confidence limit on a 10% response, and the benchmark response (BMR) would be 10%.

The BMD is determined by modeling the dose response curve in the region of the dose response relationship

where biologically observable data are feasible.

Benchmark Dose Model-is a statistical dose-response model applied to either experimental toxicological

or epidemiological data to calculate a BMD.

Bioconcentration Factor (BCF)-The quotient of the concentration of a chemical in aquatic organisms at a

specific time or during a discrete time period of exposure divided by the concentration in the surrounding

water at the same time or during the same period.

Biomarkers-are broadly defined as indicators signaling events in biologic systems or samples. They have

been classified as markers of exposure, markers of effect, and markers of susceptibility.

Cancer Effect Level (CEL)-The lowest dose of chemical in a study, or group of studies, that produces

significant increases in the incidence of cancer (or tumors) between the exposed population and its

appropriate control.

Carcinogen-A chemical capable of inducing cancer.

Case-Control Study-A type of epidemiological study which examines the relationship between a

particular outcome (disease or condition) and a variety of potential causative agents (such as toxic

chemicals). In a case-controlled study, a group of people with a specified and well-defined outcome is

identified and compared to a similar group of people without outcome.

Case Report-describes a single individual with a particular disease or exposure. These may suggest some

potential topics for scientific research but are not actual research studies.
CHLOROMETHANE 236

9. GLOSSARY

Case Series-describes the experience of a small number of individuals with the same disease or exposure.

These may suggest potential topics for scientific research but are not actual research studies.

Ceiling Value-A concentration of a substance that should not be exceeded, even instantaneously.

Chronic Exposure-Exposure to a chemical for 365 days or more, as specified in the Toxicological

Profiles.

Cohort Study-A type of epidemiological study of a specific group or groups of people who have had a

common insult (e.g., exposure to an agent suspected of causing disease or a common disease) and are

followed forward from exposure to outcome. At least one exposed group is compared to one unexposed

group.

Cross-sectional Study-A type of epidemiological study of a group or groups which examines the

relationship between exposure and outcome to a chemical or to chemicals at one point in time.

Data Needs-substance-specific informational needs that if met would reduce the uncertainties of human

health assessment.

Developmental Toxicity-The occurrence of adverse effects on the developing organism that may result

from exposure to a chemical prior to conception (either parent), during prenatal development, or postnatally

to the time of sexual maturation. Adverse developmental effects may be detected at any point in the life

span of the organism.

Dose-Response Relationship--the quantitative relationship between the amount of exposure to a toxicant

and the incidence of the adverse effects.

Embryotoxicity and Fetotoxicity-Any toxic effect on the conceptus as a result of prenatal exposure to a

chemical; the distinguishing feature between the two terms is the stage of development during which the

insult occurs. The terms, as used here, include malformations and variations, altered growth, and

in utero death.

Environmental Protection Agency (EPA) Health Advisory-An estimate of acceptable drinking water

levels for a chemical substance based on health effects information. A health advisory is not a legally

enforceable federal standard, but serves as technical guidance to assist federal, state, and local officials.

Epidemiology-refers to the investigation of factors that determine the frequency and distribution of disease

or other health-related conditions within a defined human population during a specified period.

Genotoxicity-A specific adverse effect on the genome of living cells that, upon the duplication of affected

cells, can be expressed as a mutagenic, clastogenic or carcinogenic event because of specific alteration of the

molecular structure of the genome.

Half-life-A measure of rate for the time required to eliminate one half of a quantity of a chemical from the

body or environmental media.
CHLOROMETHANE 237

9. GLOSSARY

Immediately Dangerous to Life or Health (IDLH)-The maximum environmental concentration of a

contaminant from which one could escape within 30 minutes without any escape-impairing symptoms or

irreversible health effects.

Incidence-The ratio of individuals in a population who develop a specified condition to the total number of

individuals in that population who could have developed that condition in a specified time period.

Intermediate Exposure-Exposure to a chemical for a duration of 15-364 days, as specified in the

Toxicological Profiles.

Immunological Effects-are functional changes in the immune response.

Immunologic Toxicity- The occurrence of adverse effects on the immune system that may result from

exposure to environmental agents such as chemicals.

In Vitro-Isolated from the living organism and artificially maintained, as in a test tube.

In Vivo-Occurring within the living organism.

Lethal Concentration(LO) (LCLO)-The lowest concentration of a chemical in air which has been reported

to have caused death in humans or animals.

Lethal Concentration(50) ( LC50)-A calculated concentration of a chemical in air to which exposure for a

specific length of time is expected to cause death in 50% of a defined experimental animal population.

Lethal Dose(LO) (LDLO)-The lowest dose of a chemical introduced by a route other than inhalation that has

been reported to have caused death in humans or animals.

Lethal Dose(50) (LD50)-The dose of a chemical which has been calculated to cause death in 50% of a

defined experimental animal population.

Lethal Time(50) (LT50)-A calculated period of time within which a specific concentration of a chemical is

expected to cause death in 50% of a defined experimental animal population.

Lowest-Observed-Adverse-Effect Level (LOAEL)-The lowest exposure level of chemical in a study, or

group of studies, that produces statistically or biologically significant increases in frequency or severity of

adverse effects between the exposed population and its appropriate control.

Lymphoreticular Effects-represent morphological effects involving lymphatic tissues such as the lymph

nodes, spleen, and thymus.

Malformations-Permanent structural changes that may adversely affect survival, development, or

function.

Minimal Risk Level (MRL) -An estimate of daily human exposure to a hazardous substance that is likely

to be without an appreciable risk of adverse noncancer health effects over a specified route and duration of

exposure.
CHLOROMETHANE 238

9. GLOSSARY

Modifying Factor (MF)-A value (greater than zero) that is applied to the derivation of a minimal risk

level (MRL) to reflect additional concerns about the database that are not covered by the uncertainty factors

The default value for a MF is 1.

Morbidity-State of being diseased; morbidity rate is the incidence or prevalence of disease in a specific

population.

Mortality-Death; mortality rate is a measure of the number of deaths in a population during a specified

interval of time.

Mutagen-A substance that causes mutations. A mutation is a change in the DNA sequence of a cell’s

DNA. Mutations can lead to birth defects, miscarriages, or cancer.

Necropsy-The gross examination of the organs and tissues of a dead body to determine the cause of death

or pathological conditions.

Neurotoxicity-The occurrence of adverse effects on the nervous system following exposure to a chemical.

No-Observed-Adverse-Effect Level (NOAEL)-The dose of a chemical at which there were no

statistically or biologically significant increases in frequency or severity of adverse effects seen between the

exposed population and its appropriate control. Effects may be produced at this dose, but they are not

considered to be adverse.

Octanol-Water Partition Coeffkient (Kow)-The equilibrium ratio of the concentrations of a chemical in

n-octanol and water, in dilute solution.

Odds Ratio-a means of measuring the association between an exposure (such as toxic substances and a

disease or condition) which represents the best estimate of relative risk (risk as a ratio of the incidence

among subjects exposed to a particular risk factor divided by the incidence among subjects who were not

exposed to the risk factor). An odds ratio of greater than 1 is considered to indicate greater risk of disease in

the exposed group compared to the unexposed.

Organophosphate or Organophosphorus Compound-A phosphorus containing organic compound and

especially a pesticide that acts by inhibiting cholinesterase.

Permissible Exposure Limit (PEL)-An Occupational Safety and Health Administration (OSHA)

allowable exposure level in workplace air averaged over an &hour shift of a 40 hour workweek.

Pesticide--general classification of chemicals specifically developed and produced for use in the control of

agricultural and public health pests.

Pharmacokinetics-is the science of quantitatively predicting the fate (disposition) of an exogenous

substance in an organism. Utilizing computational techniques, it provides the means of studying the

absorption, distribution, metabolism and excretion of chemicals by the body.
CHLOROMETHANE 239

9. GLOSSARY

Pharmacokinetic Model-is a set of equations that can be used to describe the time course of a parent

chemical or metabolite in an animal system. There are two types of pharmacokinetic models: data-based

and physiologically-based. A data-based model divides the animal system into a series of compartments

which, in general, do not represent real, identifiable anatomic regions of the body whereby the

physiologically-based model compartments represent real anatomic regions of the body.

Physiologically Based Pharmacodynamic (PBPD) Model-is a type of physiologically-based doseresponse

model which quantitatively describes the relationship between target tissue dose and toxic end

points. These models advance the importance of physiologically based models in that they clearly describe

the biological effect (response) produced by the system following exposure to an exogenous substance.

Physiologically Based Pharmacokinetic (PBPK) Model-is comprised of a series of compartments

representing organs or tissue groups with realistic weights and blood flows. These models require a variety

of physiological information: tissue volumes, blood flow rates to tissues, cardiac output, alveolar ventilation

rates and, possibly membrane permeabilities. The models also utilize biochemical information 4such as

air/blood partition coefficients, and metabolic parameters. PBPK models are also called biologically based

tissue dosimetry models.

Prevalence-The number of cases of a disease or condition in a population at one point in time.

Prospective Study-A type of cohort study in which the pertinent observations are made on events

occurring after the start of the study. A group is followed over time.

q1*-The upper-bound estimate of the low-dose slope of the dose-response curve as determined by the

multistage procedure. The q1* can be used to calculate an estimate of carcinogenic potency, the incremental

excess cancer risk per unit of exposure (usually μg/L for water, mg/kg/day for food, and μg/m3

 for air).

Recommended Exposure Limit (REL)-A National Institute for Occupational Safety and Health

(NIOSH) time-weighted average (TWA) concentrations for up to a lo-hour workday during a 40-hour

workweek.

Reference Concentration (RfC)-An estimate (with uncertainty spanning perhaps an order of magnitude)

of a continuous inhalation exposure to the human population (including sensitive subgroups) that is likely to

be without an appreciable risk of deleterious noncancer health effects during a lifetime. The inhalation

reference concentration is for continuous inhalation exposures and is appropriately expressed in units of

mg/m3

 or ppm.

Reference Dose (RfD)-An estimate (with uncertainty spanning perhaps an order of magnitude) of the

daily exposure of the human population to a potential hazard that is likely to be without risk of deleterious

effects during a lifetime. The RfD is operationally derived from the No-Observed-Adverse-Effect Level

(NOAEL- from animal and human studies) by a consistent application of uncertainty factors that reflect

various types of data used to estimate RfDs and an additional modifying factor, which is based on a

professional judgment of the entire database on the chemical. The RfDs are not applicable to nonthreshold

effects such as cancer.
CHLOROMETHANE 240

9. GLOSSARY

Reportable Quantity (RQ)-The quantity of a hazardous substance that is considered reportable under the

Comprehensive Environmental Response, Compensation, and Liability Act (CERCLA). Reportable

quantities are (1) 1 pound or greater or (2) for selected substances, an amount established by regulation

either under CERCLA or under Section 311 of the Clean Water Act. Quantities are measured over a

24-hour period.

Reproductive Toxicity-The occurrence of adverse effects on the reproductive system that may result from

exposure to a chemical. The toxicity may be directed to the reproductive organs and/or the related endocrine

system. The manifestation of such toxicity may be noted as alterations in sexual behavior, fertility,

pregnancy outcomes, or modifications in other functions that are dependent on the integrity of this system.

Retrospective Study-A type of cohort study based on a group of persons known to have been exposed at

some time in the past. Data are collected from routinely recorded events, up to the time the study is

undertaken. Retrospective studies are limited to casual factors that can be ascertained from existing records

and/or examining survivors of the cohort.

Risk-the possibility or chance that some adverse effect will result from a given exposure to a chemical.

Risk Factor-An aspect of personal behavior or lifestyle, an environmental exposure, or an inborn or

inherited characteristic, that is associated with an increased occurrence of disease or other health-related

event or condition.

Risk Ratio-The ratio of the risk among persons with specific risk factors compared to the risk among

persons without risk factors. A risk ratio greater than 1 indicates greater risk of disease in the exposed

group compared to the unexposed.

Short-Term Exposure Limit (STEL)-The American Conference of Governmental Industrial Hygienists

(ACGIH) maximum concentration to which workers can be exposed for up to 15 min continually. No more

than four excursions are allowed per day, and there must be at least 60 min between exposure periods. The

daily Threshold Limit Value - Time Weighted Average (TLV-TWA) may not be exceeded.

Target Organ Toxicity-This term covers a broad range of adverse effects on target organs or

physiological systems (e.g., renal, cardiovascular) extending from those arising through a single limited

exposure to those assumed over a lifetime of exposure to a chemical.

Teratogen-A chemical that causes structural defects that affect the development of an organism.

Threshold Limit Value (TLV)-An American Conference of Governmental Industrial Hygienists

(ACGIH) concentration of a substance to which most workers can be exposed without adverse effect. The

TLV may be expressed as a Time Weighted Average (TWA), as a Short-Term Exposure Limit (STEL), or

as a ceiling limit (CL).

Time-Weighted Average (TWA)-An allowable exposure concentration averaged over a normal g-hour

workday or 40-hour workweek.

Toxic Dose(50) ( TD50)-A calculated dose of a chemical, introduced by a route other than inhalation, which

is expected to cause a specific toxic effect in 50% of a defined experimental animal population.
CHLOROMETHANE 241

9. GLOSSARY

Toxicokinetic-The study of the absorption, distribution and elimination of toxic compounds in the living

organism.

Uncertainty Factor (UF)-A factor used in operationally deriving the Minimal Risk Level (MRL) or

Reference Dose (RfD) or Reference Concentration (RfC) from experimental data. UFs are intended to

account for (1) the variation in sensitivity among the members of the human population, (2) the uncertainty

in extrapolating animal data to the case of human, (3) the uncertainty in extrapolating from data obtained in

a study that is of less than lifetime exposure, and (4) the uncertainty in using Lowest-Observed-AdverseEffect Level (LOAEL) data rather than No-Observed-Adverse-Effect Level (NOAEL) data. A default for

each individual UF is 10; if complete certainty in data exists, a value of one can be used; however a reduced

LF of three may be used on a case-by-case basis, three being the approximate logarithmic average of 10

and 1.

Xenobiotic-any chemical that is foreign to the biological system.

CHLOROMETHANE A-1

APPENDIX A

ATSDR MINIMAL RISK LEVELS AND WORKSHEETS

The Comprehensive Environmental Response, Compensation, and Liability Act (CERCLA) [42 U.S.C.

9601 et seq.], as amended by the Superfund Amendments and Reauthorization Act (SARA) [Pub. L.

99-4991, requires that the Agency for Toxic Substances and Disease Registry (ATSDR) develop jointly

with the U.S. Environmental Protection Agency (EPA), in order of priority, a list of hazardous substances

most commonly found at facilities on the CERCLA National Priorities List (NPL); prepare toxicological

profiles for each substance included on the priority list of hazardous substances; and assure the initiation of

a research program to fill identified data needs associated with the substances.

The toxicological profiles include an examination, summary, and interpretation of available toxicological

information and epidemiologic evaluations of a hazardous substance. During the development of

toxicological profiles, Minimal Risk Levels (MRLs) are derived when reliable and sufficient data exist to

identify the target organ(s) of effect or the most sensitive health effect(s) for a specific duration for a given

route of exposure. An MRL is an estimate of the daily human exposure to a hazardous substance that is

likely to be without appreciable risk of adverse noncancer health effects over a specified duration of

exposure. MRLs are based on noncancer health effects only and are not based on a consideration of cancer

effects. These substance-specific estimates, which are intended to serve as screening levels, are used by

ATSDR health assessors to identify contaminants and potential health effects that may be of concern at

hazardous waste sites. It is important to note that MRLs are not intended to define clean-up or action levels.

MRLs are derived for hazardous substances using the no-observed-adverse-effect level/uncertainty factor

approach. They are below levels that might cause adverse health effects in the people most sensitive to such

chemical-induced effects. MRLs are derived for acute (1-14 days), intermediate (15-364 days), and

chronic (365 days and longer) durations and for the oral and inhalation routes of exposure. Currently,

MRLs for the dermal route of exposure are not derived because ATSDR has not yet identified a method

suitable for this route of exposure. MRLs are generally based on the most sensitive chemical-induced end

point considered to be of relevance to humans. Serious health effects (such as irreparable damage to the

liver or kidneys, or birth defects) are not used as a basis for establishing MRLs. Exposure to a level above

the MRL does not mean that adverse health effects will occur.
CHLOROMETHANE A-2

APPENDIX A

MRLs are intended only to serve as a screening tool to help public health professionals decide where to look

more closely. They may also be viewed as a mechanism to identify those hazardous waste sites that are not

expected to cause adverse health effects. Most MRLs contain a degree of uncertainty because of the lack of

precise toxicological information on the people who might be most sensitive (e.g., infants, elderly,

nutritionally or immunologically compromised) to the effects of hazardous substances. ATSDR uses a

conservative (i.e., protective) approach to address this uncertainty consistent with the public health principle

of prevention. Although human data are preferred, MRLs often must be based on animal studies because

relevant human studies are lacking. In the absence of evidence to the contrary, ATSDR assumes that

humans are more sensitive to the effects of hazardous substance than animals and that certain persons may

be particularly sensitive. Thus, the resulting MRL may be as much as a hundredfold below levels that have

been shown to be nontoxic in laboratory animals.

Proposed MRLs undergo a rigorous review process: Health Effects/MRL Workgroup reviews within the

Division of Toxicology, expert panel peer reviews, and agencywide MRL Workgroup reviews, with

participation from other federal agencies and comments from the public. They are subject to change as new

information becomes available concomitant with updating the toxicological profiles. Thus, MRLs in the

most recent toxicological profiles supersede previously published levels. For additional information

regarding MRLs, please contact the Division of Toxicology, Agency for Toxic Substances and Disease

Registry, 1600 Clifton Road, Mailstop E-29, Atlanta, Georgia 30333.
CHLOROMETHANE A-3

APPENDIX A

MINIMAL RISK LEVEL (MRL) WORKSHEET

Chemical name(s): Chloromethane

CAS number(s): 74-87-3

Date: November 1998

Profile status: Draft 2 Post-Public Comment

Route: [X] Inhalation [ ] Oral

Duration: [X] Acute [ ] Intermediate [ ] Chronic

Key to figure: 43

Species: Mouse

Minimal Risk Level: 0.5 [ ] mg/kg/day [X] ppm [ ] mg/m3

Reference: Landry DL, Quast JF, Gushow TS, Mattsson. 1985. Neurotoxicity of methyl chloride in

continuously versus intermittently exposed female C57BL/6 mice. Fundamental and Applied Toxicology

5:87-98.

Experimental design: An acute MRL of 0.5 ppm was derived from a NOAEL of 50 ppm for no effect on

motor coordination or damage to the cerebellar granule cells. Landry et al. (1985) evaluated the neurologic

effects of continuous versus intermittent chloromethane exposure in female C57BL/6 mice. Groups of 12

mice each were exposed to chloromethane in whole body inhalation chambers for 11 days either

continuously 22 hours/day at 0, 15, 50, 100, 150, 200, or 400 ppm or intermittently 5.5 hours/day at 0,

150, 400, 800, 1,600, or 2,400 ppm. The mice were subjected to neurofunctional testing (ability to stay on

a rotating 4 cm diameter rod) on days 4, 8, and 11. Mice were weighed prior to exposure, on exposure days

4 and 8, and at necropsy. Animals were sacrificed at various times during the experiment, and the following

tissues were collected, weighed, and prepared for histological evaluation: brain (cerebellum, cerebrum, brain

stem), sciatic nerve, vertebral bone with spinal cord, liver, kidneys, and thymus.

Effects noted in study and corresponding doses: The MRL was derived from effects observed in the

continuously exposed mice. The 400 ppm exposed mice died or were sacrificed by day 4, and the 200 ppm

group by day 5, due to severe toxicity. Mice exposed to 150 ppm were sacrificed in moribund condition by

day 10.5. At 200 ppm, the mice were ataxic and fell on their sides after 3 days. At 150 to 400 ppm, the

mice developed motor incoordination. Performance on a rotating rod was significantly decreased at 150 ppm

and greater. No effects were seen at 50 ppm or below. Histologically, degenerative changes in the

cerebellum granule cells were seen at ≥100 ppm, and consisted of nuclear pyknosis and karyorrhexis. At

150 ppm on day 4, there was a moderate intracellular and extracellular cerebellar vacuolation in the

Purkinje and/or molecular cell layer and in the white matter. This vacuolation was transient and not seen

after day 6 or later. These effects were more pronounced in the 400 ppm mice. Similar effects were seen in

mice exposed to higher concentrations intermittently (see separate entries). The apparent greater

susceptibility to continuous exposure may be related to the conversion of chloromethane to a toxic

metabolite, to decreased respiration at concentrations that are intolerable when exposure is continuous,

and/or to diurnal susceptibility.

15 and 50 ppm = No neurologic effects or histopathologic damage observed.

100 ppm = Slight degenerative changes in the cerebellum granule cells with nuclear pyknosis and

karyorrhexis.

150 ppm = Moderate cerebellar lesions and severe performance decrement on neuromotor tests.
CHLOROMETHANE A-4

APPENDIX A

200 ppm = Incapacitated after 4 days, severe cerebellar lesions.

400 ppm = Incapacitated after 2 days, severe cerebellar lesions.

Dose end ooint used for MRL derivation: 50 ppm; no neurological effects or histopathologic damage

observed

[X] NOAEL [ ]LOAEL

Uncertainty factors used in MRL derivation:

[ ]1 [ ]3 [ ] 10 (for use of a LOAEL)

[ ]1 [ ]3 [X] 10 (for extrapolation from animals to humans)

[ ]1 [ ]3 [X] 10 (for human variability)

Was a conversion factor used from prim in food or water to a mg/body weight dose?

If so explain: No conversion factor used.

Was a conversion used from intermittent to continuous exposure?

If so, explain: No adjustment made for the acute exposure NOAEL. Chloromethane is readily absorbed

from the lungs in humans and animals and rapidly (within 1 hour) reaches equilibrium with levels in blood

and expired air approximately proportional to the exposure concentrations (Landry et al. 1983a, 1983b;

Nolan et al. 1985; Putz-Andersen et al. 1981a, 1981b).

If an inhalation studv in animals, list conversion factors used in determining human equivalent dose:

The human equivalent dose (HEC) was calculated using Formula 4-48a from Methods for Derivation of

Inhalation Reference Concentrations and Application of Inhalation Dosimetry (EPA 1994b). Though

chloromethane is a category 2 gas, the formula in the EPA 1994b document for extrarespiratory effects of

category 2 gases is presently under review and the recommended equation is that for category 3 gases:

NOAEL[HEC] (ppm) = NOAEL[ADJ] (ppm) x (Hb/g)A

(Hb/g)H

= 50 ppm x [1] = 50 ppm

where,

NOAEL[HEC] = the NOAEL human equivalent concentration

NOAEL[ADJ] = the NOAEL adjusted for duration

Hb/g = the blood:gas (air) partition coefficient [the default value of 1.0 is used for the ratio of

(Hb/g),/(Hb/g), if these partition coefficients are not known]

A, H = the subscripts A and H refer to animal and human, respectively.

Additional studies or pertinent information that lend support to this MRL: Neurological effects have been

described in numerous case reports of humans exposed to chloromethane vapors as a result of industrial

leaks and leaks from defective refrigerators (Baird 1954; Gudmundsson 1977; Hansen et al. 1953; Hartman

et al. 1955; Kegel et al. 1929; MacDonald 1964; McNally 1946; Jones 1942; Raalte and van Velzen 1945;

Spevak et al. 1976; Wood 1951). Depending on the extent of exposure and the availability of medical
CHLOROMETHANE A-5

APPENDIX A

treatment, the signs and symptoms can range from staggering and blurred vision to coma, convulsions, and

death.

Severe neurological signs (ataxia, tremors, limb paralysis, incoordination, convulsions) have been observed

in rats, mice, rabbits, guinea pigs, dogs, cats, and monkeys exposed acutely by inhalation to high

concentrations of chloromethane (Burek et al. 1981; Chellman et al. 1986a, 1986b; Landry et al. 1985;

McKenna et al. 198 la; Morgan et al. 1982; Smith and von Oettingen 1947b). Cerebellar lesions have also

been observed microscopically in guinea pigs and rats (Kolkmann and Volk 1975; Morgan et al. 1982).

Mice are more susceptible than rats (Morgan et al. 1982; CIIT 1981), and more sensitive to neurological

effects after continuous exposure to low concentrations than after intermittent exposure to higher

concentrations of chloromethane (Landry et al. 1985). The greater sensitivity of mice to continuous

exposure makes the mouse a good model for the neurotoxicological effects seen in humans.

Agency Contact (Chemical Manager): Alfred Dorsey
CHLOROMETHANE A-6

APPENDIX A

MINIMAL RISK LEVEL (MRL) WORKSHEET

Chemical name(s): Chloromethane

CAS number(s): 74-87-3

Date: November 1998

Profile status: Draft 2 Post-Public Comment

Route: [X] Inhalation [ ] Oral

Duration: [ ] Acute [X] Intermediate [ ] Chronic

Key to figure: 73

Species: Mouse

Minimal Risk Level: 0.2 [ ] mg/kg/day [Xl ppm [ ] mg/m3

Reference: CIIT. 1981. Final report on a chronic inhalation toxicology study in rats and mice exposed to

methyl chloride. Unpublished study prepared by Battelle-Columbus Laboratories, Columbus, OH. OTS

Submission Document ID 408120717. Microfiche 511310.

Experimental design: An intermediate MRL of 0.2 ppm (rounded to one significant figure from 0.17) was

derived from a LOAEL of 51 ppm for significantly increased serum levels of alanine amino transferase

(indicative of hepatotoxicity) in male mice at the 6 month time point in a 2-year study. The objective of the

study was to evaluate the toxicologic and oncogenic effects of inhaled chloromethane in male and female

Fischer 344 rats and B6C3F1 mice. Animals (120 per sex per exposure level) were exposed to

chloromethane in whole body inhalation exposure chambers at target concentrations of 0 (control), 50, 225,

or 1,000 ppm, 6 hours/day, 5 days/week for up to two years. Necropsies were completed at 6, 12, 18, or

24 months after the initial exposure (n=10, 10, 20, 80 for rats; and n=10, 10, 10, 90 for mice; respectively).

Actual measured concentrations averaged for the 24-month exposure overall were 0.3±4, 51±9, 224±6, and

997±65 ppm. All animals were observed twice daily for signs of toxicity, abnormal behavior, anorexia, or

abnormal physical condition. Body weights were collected weekly for 6 months and biweekly thereafter.

Ophthalmic exams were performed at baseline and at sacrifice. Prior to the 18- and 24-month sacrifices,

neurofunction exams were performed. Blood samples were collected from selected animals at each

scheduled necropsy period for hematological and clinical chemistry evaluations; 16-hour urine samples were

collected from the same animals for urinalysis. At necropsy, a gross pathology examination was performed,

organs (heart, brain, gonads, liver, kidneys, and lungs) were weighed and tissue samples were collected.

Histological evaluation of tissues was performed only on tissues collected from the high dose and control

animals. Target organ tissues in rats (reproductive tissues, kidney liver, lung) and mice (liver, kidney,

spleen) were histologically evaluated in animals of all dose groups.

Effects noted in study and corresponding doses: A dose-response effect for liver toxicity was observed in

male mice. Females also had increased ALT, but the increase was not associated with treatment-related

histopathological changes in the liver. Liver necrosis and other pathological changes in the liver of high

dose male mice was also observed at 12, 18, and 24 months.

51 ppm = Increased ALT levels in male mice; no histopathological changes in the liver.

224 ppm = Increased ALT levels in male mice; no histopathological changes in the liver.

997 ppm = Increased ALT levels; histopathological changes including necrosis, karyomegaly,

polykarocytes.
CHLOROMETHANE A-7

APPENDIX A

Dose end point used for MRL derivation:51 ppm; increased ALT levels.

[ ] NOAEL [X] LOAEL

Uncertainty factors used in MRL derivation:

[ ] 1 [ X ] 3 [ ] 10 (for use of a minimal LOAEL)

[ ] 1 [ ] 3 [ X ] 10 (for extrapolation from animals to humans)

[ ] 1 [ ] 3 [ X ] 10 (for human variability)

Was a conversion factor used from ppm in food or water to a mg/bodv weight dose?

If so explain: No conversion factor used.

Was a conversion used from intermittent to continuous exposure?

If so, explain: No adjustment made for the intermediate exposure LOAEL. Chloromethane is readily

absorbed from the lungs in humans and animals and rapidly (within 1 hour) reaches equilibrium with levels

in blood and expired air approximately proportional to the exposure concentrations (Landry et al. 1983a,

1983b; Nolan et al. 1985; Putz-Andersen et al. 1981a, 1981b). The LOAEL[ADJ] = LOAEL = 51 ppm.

If an inhalation study in animals, list conversion factors used in determining human equivalent dose:

The human equivalent dose (HEC) was calculated using Formula 4-48a from Methods for Derivation of

Inhalation Reference Concentrations and Application of Inhalation Dosimetry (EPA 1994b). Though

chloromethane is a category 2 gas, the formula in the EPA 1994b document for extrarespiratory effects of

category 2 gases is presently under review and the recommended equation is that for category 3 gases:

LOAEL[HEC] (ppm) = LOAEL[ADJ] (ppm) x (Hb/g)A

(Hb/g)H

= 51 ppm x [1] = 51 ppm

LOAEL[HEC] = the LOAEL human equivalent concentration

LOAEL[ADJ] = the LOAEL adjusted for duration (see above)

Hb/g = the blood:gas (air) partition coefficient [the default value of 1.0 is used for the ratio of

 (Hb/g),/(Hb/g), if these partition coefficients are not known]

A H = the subscripts A and H refer to animal and human, respectively.

Additional studies or pertinent information that lend support to this MRL:

Case reports of humans exposed to chloromethane vapors have described clinical jaundice and cirrhosis of

the liver (Kegel et al. 1929; Mackie 1961; Weinstein 1937; Wood 195 l), but exposure concentrations were

not known.

Hepatic effects have been observed in animals exposed by inhalation to chloromethane at concentrations

>l,000 ppm in acute, intermediate, and chronic duration experiments (Burek et al. 1981; Chellman et al.

1986a; CIIT 1981; Landry et al. 1985; Mitchell et al. 1979; Morgan et al. 1982). Milder liver effects
CHLOROMETHANE A-8

APPENDIX A

occurred in mice exposed acutely to an intermittent but relatively high concentration than to a low but

continuous concentration (Landry et al. 1985). The greater susceptibility to continuous exposure may result

from relatively greater metabolism to a toxic intermediate or from diurnal susceptibility. Hepatic effects

were more severe in mice (necrosis and degeneration) than in rats (cloudy swelling, fatty infiltration,

increased ALT and AST with no necrosis). Furthermore, no hepatic lesions were observed in rats over the

course of 2 years of inhalation exposure to 1,000 ppm, while mice similarly exposed had necrotic lesions

after 6 months (CIIT 1981). The greater susceptibility of mice to the hepatotoxic effects of chloromethane

may be related to the greater ability of chloromethane to conjugate with hepatic glutathione in mice than in

rats (Dodd et al. 1982; Kornbrust and Bus 1984). The reaction of chloromethane with glutathione appears

to be toxifying rather than detoxifying (Chellman et al. 1986b). While the exact mechanism for the

hepatotoxic effects of chloromethane is unclear, chloromethane can elicit lipid peroxidation as a secondary

consequence of depletion of glutathione (Kornbrust and Bus 1984). Comparison of lipid peroxidation in the

S-9 fraction from mouse and rat livers revealed much greater lipid peroxidation in mouse liver than in rat

liver. The finding that mice exposed to 2,500 ppm chloromethane expired ethane to an extent comparable to

that produced by 2 mL/kg carbon tetrachloride, and developed moderate to severe hepatocellular hydropic

degeneration provide further evidence that the mechanism of hepatotoxicity may involve lipid peroxidation.

Agency Contact (Chemical Manager): Alfred Dorsey
CHLOROMETHANE A-9

APPENDIX A

MINIMAL RISK LEVEL (MRL) WORKSHEET

Chemical name(s): hloromethane

CAS number(s): 74-87-3

Date: November 1998

Profile status: Draft 2 Post-Public Comment

Route: [X] Inhalation [ ] Oral

Duration: [ ] Acute [ ] Intermediate [X] Chronic

Key to figure: 115

Species: Mouse

Minimal Risk Level: 0.05 [ ] mg/kg/day [X] ppm [ ] mg/m3

Reference: CIIT. 1981. Final report on a chronic inhalation toxicology study in rats and mice exposed to

methyl chloride. Unpublished study prepared by Battelle-Columbus Laboratories, Columbus, OH. OTS

Submission Document ID 40-8120717. Microfiche 511310.

Experimental design: A chronic MRL of 0.05 ppm (rounded to one significant figure from 0.051) was

derived from a LOAEL of 51 ppm for neurological effects (swelling and degeneration of the axons of the

spinal cord) in male and female mice at 18 months in a 2-year study. The objective of the study was to

evaluate the toxicologic and oncogenic effects of inhaled chloromethane in male and female Fischer 344 rats

and B6C3F1 mice. Animals (120 per sex per exposure level) were exposed to chloromethane in whole body

inhalation exposure chambers at target concentrations of 0 (control), 50, 225, or 1,000 ppm, 6 hours/day,

5 days/week for up to 2 years. Necropsies were completed at 6, 12, 18, or 24 months after the initial

exposure (n=10, 10, 20, 80 for rats; and n=10, 10, 10, 90 for mice; respectively). Actual measured

concentrations averaged for the 24-month exposure overall were 0.3±4, 51±9, 224±16, and 997±65 ppm.

All animals were observed twice daily for signs of toxicity, abnormal behavior, anorexia, or abnormal

physical condition. Body weights were measured weekly for 6 months and biweekly thereafter.

Ophthalmic exams were performed at baseline and at sacrifice. Prior to the 18- and 24-month sacrifices,

neurofunction exams were performed. Blood samples were collected from selected animals at each

scheduled necropsy period for hematological and clinical chemistry evaluations; 16-hour urine samples were

collected from the same animals for urinalysis. At necropsy, a gross pathology examination was performed,

organs (heart, brain, gonads, liver, kidneys, and lungs) were weighed and tissue samples were collected.

Histological evaluation of tissues was performed only on tissues collected from the high dose and control

animals. Target organ tissues in rats (reproductive tissues, kidney liver, lung) and mice (liver, kidney,

spleen) were histologically evaluated in animals of all dose groups.

Effects noted in study and corresponding doses: There was a consistent dose-response for neurological

effects in male and female mice. At the high dose, there was a mild reduction in the number of neurons in

the granular cell layer of the cerebellum with decreased width of the granular cell layer. In the high, mid,

and low dose groups, axonal swelling and degeneration of minimal severity was observed in the spinal

nerves and the cauda equina associated with the lumbar spinal cord.

51 ppm = Swelling and degeneration of axons in the spinal cord.

224 ppm = Swelling and degeneration of axons in the spinal cord.
CHLOROMETHANE A-10

APPENDIX A

997 ppm = Tremor, paralysis, mild reduction in the number of cerebellar neurons in the granular cell

layer.

Dose end point used for MRL derivation:51 ppm; axonal swelling and slight degeneration of axons in the

spinal cord

[ ] NOAEL [X] LOAEL

Uncertainty factors used in MRL derivation:

[ ] 1 [ ] 3 [ X ] 10 (for use of a LOAEL)

[ ] 1 [ ] 3 [ X ] 10 (for extrapolation from animals to humans)

[ ] 1 [ ] 3 [ X ] 10 (for human variability)

Was a conversion factor used from ppm in food or water to a mg/bodv weight dose?

If so explain: No conversion factor used.

Was a conversion used from intermittent to continuous exposure?

If so, explain: No adjustment made for the chronic exposure LOAEL. Chloromethane is readily absorbed

from the lungs in humans and animals and rapidly (within 1 hour) reaches equilibrium with levels in blood

and expired air approximately proportional to the exposure concentrations (Landry et al. 1983a, 1983b;

Nolan et al. 1985; Putz-Andersen et al. 1981a, 1981b).

If an inhalation study in animals, list conversion factors used in determining human equivalent dose:

The human equivalent dose (HEC) was calculated using Formula 4-48a from Methods for Derivation of

Inhalation Reference Concentrations and Application of Inhalation Dosimetry (EPA 1994b). Though

chloromethane is a category 2 gas, the formula in the EPA 1994b document for extrarespiratory effects of

category 2 gases is presently under review and the recommended equation is that for category 3 gases:

LOAEL[HEC] (ppm) = LOAEL[ADJ] (ppm) x (Hb/g)A

(Hb/g)H

= 51 ppm x [1] = 51 ppm

where,

LOAEL[HEC] = the LOAEL human equivalent concentration

LOAEL[ADJ] = the LOAEL adjusted for duration (see above)

Hb/g = the blood:gas (air) partition coefficient [the default value of 1.0 is used for the ratio

of (Hb/g),/(Hb/g), if these partition coefficients are not known]

A,H = the subscripts A and H refer to animal and human, respectively.

Additional studies or pertinent information that lend support to this MRL: Neurological effects have been

described in numerous case reports of humans exposed to chloromethane vapors as a result of industrial
CHLOROMETHANE A-11

APPENDIX A

leaks and leaks from defective home refrigerators (Baird 1954; Hansen et al. 1953; Hartman et al. 1955;

Kegel et al. 1929; MacDonald 1964; McNally 1946; Jones 1942; Raalte and van Velzen 1945; Spevak et al.

1976; Wood 1951). Depending on the extent of exposure and the availability of medical treatment, the signs

and symptoms can range from staggering and blurred vision to coma, convulsions, and death.

Severe neurological signs (ataxia, tremors, limb paralysis, incoordination, convulsions) have been observed

in rats, mice, rabbits, guinea pigs, dogs, cats, and monkeys exposed acutely by inhalation to high

concentrations of chloromethane (Burek et al. 1981; Chellman et al. 1986a, 1986b; Landry et al. 1985;

McKenna et al. 1981a; Morgan et al. 1982; Smith and von Oettingen 1947b). Cerebellar lesions have also

been observed microscopically in guinea pigs and rats (Kolkmann and Volk 1975; Morgan et al. 1982).

Mice are more susceptible than rats (Morgan et al. 1982; CIIT 1981), and more sensitive to neurological

effects after continuous exposure to low concentrations than after intermittent exposure to higher

concentrations of chloromethane (Landry et al. 1985). The greater sensitivity of mice to continuous

exposure makes the mouse a good model for the neurotoxicological effects seen in humans.

Agency Contact (Chemical Manager): Alfred Dorsey

CHLOROMETHANE B-1

APPENDIX B

USER’S GUIDE

Chapter 1

Public Health Statement

This chapter of the profile is a health effects summary written in non-technical language. Its intended

audience is the general public especially people living in the vicinity of a hazardous waste site or chemical

release. If the Public Health Statement were removed from the rest of the document, it would still

communicate to the lay public essential information about the chemical.

The major headings in the Public Health Statement are useful to find specific topics of concern. The topics

are written in a question and answer format. The answer to each question includes a sentence that will

direct the reader to chapters in the profile that will provide more information on the given topic.

Chapter 2

Tables and Figures for Levels of Significant Exposure (LSE)

Tables (2-1, 2-2, and 2-3) and figures (2-l and 2-2) are used to summarize health effects and illustrate

graphically levels of exposure associated with those effects. These levels cover health effects observed at

increasing dose concentrations and durations, differences in response by species, minimal risk levels (MRLs)

to humans for noncancer end points, and EPA’s estimated range associated with an upper-bound individual

lifetime cancer risk of 1 in 10,000 to 1 in 10,000,000. Use the LSE tables and figures for a quick review of

the health effects and to locate data for a specific exposure scenario. The LSE tables and figures should

always be used in conjunction with the text. All entries in these tables and figures represent studies that

provide reliable, quantitative estimates of No-Observed-Adverse- Effect Levels (NOAELs),

Lowest-Observed-Adverse-Effect Levels (LOAELs), or Cancer Effect Levels (CELs).

The legends presented below demonstrate the application of these tables and figures. Representative

examples of LSE Table 2-1 and Figure 2-1 are shown. The numbers in the left column of the legends

correspond to the numbers in the example table and figure.

LEGEND

See LSE Table 2-1

(1) Route of Exposure One of the first considerations when reviewing the toxicity of a substance using

these tables and figures should be the relevant and appropriate route of exposure. When sufficient

data exists, three LSE tables and two LSE figures are presented in the document. The three LSE

tables present data on the three principal routes of exposure, i.e., inhalation, oral, and dermal (LSE

Table 2-1, 2-2, and 2-3, respectively). LSE figures are limited to the inhalation (LSE Figure 2-1) and

oral (LSE Figure 2-2) routes. Not all substances will have data on each route of exposure and will not

therefore have all five of the tables and figures.
CHLOROMETHANE B-2

APPENDIX B

(2) Exposure Period Three exposure periods - acute (less than 15 days), intermediate (15-364 days), and

chronic (365 days or more) are presented within each relevant route of exposure. In this example, an

inhalation study of intermediate exposure duration is reported. For quick reference to health effects

occurring from a known length of exposure, locate the applicable exposure period within the LSE

table and figure.

(3) Health Effect The major categories of health effects included in LSE tables and figures are death,

systemic, immunological, neurological, developmental, reproductive, and cancer. NOAELs and

LOAELs can be reported in the tables and figures for all effects but cancer. Systemic effects are

further defined in the “System” column of the LSE table (see key number 18).

(4) Key to Figure Each key number in the LSE table links study information to one or more data points

using the same key number in the corresponding LSE figure. In this example, the study represented

by key number 18 has been used to derive a NOAEL and a Less Serious LOAEL (also see the 2 “18r”

data points in Figure 2-l).

(5) Species The test species, whether animal or human, are identified in this column. Section 2.5,

“Relevance to Public Health,” covers the relevance of animal data to human toxicity and Section 2.3,

“Toxicokinetics,” contains any available information on comparative toxicokinetics. Although

NOAELs and LOAELs are species specific, the levels are extrapolated to equivalent human doses to

derive an MRL.

(6) Exposure Frequency/Duration The duration of the study and the weekly and daily exposure regimen

are provided in this column. This permits comparison of NOAELs and LOAELs from different

studies. In this case (key number 1 S), rats were exposed to 1,1,2,2-tetrachloroethane via inhalation

for 6 hours per day, 5 days per week, for 3 weeks. For a more complete review of the dosing regimen

refer to the appropriate sections of the text or the original reference paper, i.e., Nitschke et al. 1981.

(7) System This column further defines the systemic effects. These systems include: respiratory,

cardiovascular, gastrointestinal, hematological, musculoskeletal, hepatic, renal, and dermal/ocular.

“Other” refers to any systemic effect (e.g., a decrease in body weight) not covered in these systems.

In the example of key number 18, 1 systemic effect (respiratory) was investigated.

(8) NOAEL A No-Observed-Adverse-Effect Level (NOAEL) is the highest exposure level at which no

harmful effects were seen in the organ system studied. Key number 18 reports a NOAEL of 3 ppm

for the respiratory system which was used to derive an intermediate exposure, inhalation MRL of

0.005 ppm (see footnote “b”).

(9) LOAEL A Lowest-Observed-Adverse-Effect Level (LOAEL) is the lowest dose used in the study that

caused a harmful health effect. LOAELs have been classified into “Less Serious” and “Serious”

effects. These distinctions help readers identify the levels of exposure at which adverse health effects

first appear and the gradation of effects with increasing dose. A brief description of the specific

endpoint used to quantify the adverse effect accompanies the LOAEL. The respiratory effect reported

in key number 18 (hyperplasia) is a Less serious LOAEL of 10 ppm. MRLs are not derived from

Serious LOAELs.

(10) Reference The complete reference citation is given in chapter 8 of the profile.
CHLOROMETHANE B-3

APPENDIX B

(11) CEL A Cancer Effect Level (CEL) is the lowest exposure level associated with the onset of

carcinogenesis in experimental or epidemiologic studies. CELs are always considered serious effects.

The LSE tables and figures do not contain NOAELs for cancer, but the text may report doses not

causing measurable cancer increases.

(12) Footnotes Explanations of abbreviations or reference notes for data in the LSE tables are found in the

footnotes. Footnote “b” indicates the NOAEL of 3 ppm in key number 18 was used to derive an MRL

of 0.005 ppm.

LEGEND

See Figure 2-l

LSE figures graphically illustrate the data presented in the corresponding LSE tables. Figures help the

reader quickly compare health effects according to exposure concentrations for particular exposure periods.

(13) Exposure Period The same exposure periods appear as in the LSE table. In this example, health

effects observed within the intermediate and chronic exposure periods are illustrated.

(14) Health Effect These are the categories of health effects for which reliable quantitative data exists.

The same health effects appear in the LSE table.

(15) Levels of Exposure concentrations or doses for each health effect in the LSE tables are graphically

displayed in the LSE figures. Exposure concentration or dose is measured on the log scale “y” axis.

Inhalation exposure is reported in mg/m3

 or ppm and oral exposure is reported in mg/kg/day.

(16) NOAEL In this example, 18r NOAEL is the critical endpoint for which an intermediate inhalation

exposure MRL is based. As you can see from the LSE figure key, the open-circle symbol indicates to

a NOAEL for the test species-rat. The key number 18 corresponds to the entry in the LSE table. The

dashed descending arrow indicates the extrapolation from the exposure level of 3 ppm (see entry 18 in

the Table) to the MRL of 0.005 ppm (see footnote “b” in the LSE table).

(17) CEL Key number 38r is 1 of 3 studies for which Cancer Effect Levels were derived. The diamond

symbol refers to a Cancer Effect Level for the test species-mouse. The number 38 corresponds to the

entry in the LSE table.

(18) Estimated Upper-Bound Human Cancer Risk Levels This is the range associated with the

upper-bound for lifetime cancer risk of 1 in 10,000 to 1 in 10,000,000. These risk levels are derived

from the EPA’s Human Health Assessment Group’s upper-bound estimates of the slope of the cancer

dose response curve at low dose levels (q1*).

(19) Key to LSE Figure The Key explains the abbreviations and symbols used in the figure.


CHLOROMETHANE B-6

APPENDIX B

Chapter 2 (Section 2.5)

Relevance to Public Health

The Relevance to Public Health section provides a health effects summary based on evaluations of existing

toxicologic, epidemiologic, and toxicokinetic information. This summary is designed to present interpretive,

weight-of-evidence discussions for human health end points by addressing the following questions.

1. What effects are known to occur in humans?

2 . What effects observed in animals are likely to be of concern to humans?

3 . What exposure conditions are likely to be of concern to humans, especially around

hazardous waste sites?

The section covers end points in the same order they appear within the Discussion of Health Effects by

Route of Exposure section, by route (inhalation, oral, dermal) and within route by effect. Human data are

presented first, then animal data. Both are organized by duration (acute, intermediate, chronic). In vitro

data and data from parenteral routes (intramuscular, intravenous, subcutaneous, etc.) are also considered in

this section. If data are located in the scientific literature, a table of genotoxicity information is included.

The carcinogenic potential of the profiled substance is qualitatively evaluated, when appropriate, using

existing toxicokinetic, genotoxic, and carcinogenic data. ATSDR does not currently assess cancer potency

or perform cancer risk assessments. Minimal risk levels (MRLs) for noncancer end points (if derived) and

the end points from which they were derived are indicated and discussed.

Limitations to existing scientific literature that prevent a satisfactory evaluation of the relevance to public

health are identified in the Data Needs section.

Interpretation of Minimal Risk Levels

Where sufficient toxicologic information is available, we have derived minimal risk levels (MRLs) for

inhalation and oral routes of entry at each duration of exposure (acute, intermediate, and chronic). These

MRLs are not meant to support regulatory action; but to acquaint health professionals with exposure levels

at which adverse health effects are not expected to occur in humans. They should help physicians and

public health officials determine the safety of a community living near a chemical emission, given the

concentration of a contaminant in air or the estimated daily dose in water. MRLs are based largely on

toxicological studies in animals and on reports of human occupational exposure.

MRL users should be familiar with the toxicologic information on which the number is based. Chapter 2.5,

“Relevance to Public Health,” contains basic information known about the substance. Other sections such

as 2.8, “Interactions with Other Substances,” and 2.9, “Populations that are Unusually Susceptible” provide

important supplemental information.

MRL users should also understand the MRL derivation methodology. MRLs are derived using a modified

version of the risk assessment methodology the Environmental Protection Agency (EPA) provides (Barnes

and Dourson 1988) to determine reference doses for lifetime exposure (RfDs).
CHLOROMETHANE B-7

APPENDIX B

To derive an MRL, ATSDR generally selects the most sensitive endpoint which, in its best judgement,

represents the most sensitive human health effect for a given exposure route and duration. ATSDR cannot

make this judgement or derive an MRL unless information (quantitative or qualitative) is available for all

potential systemic, neurological, and developmental effects. If this information and reliable quantitative data

on the chosen endpoint are available, ATSDR derives an MRL using the most sensitive species (when

information from multiple species is available) with the highest NOAEL that does not exceed any adverse

effect levels. When a NOAEL is not available, a lowest-observed-adverse-effect level (LOAEL) can be

used to derive an MRL, and an uncertainty factor (UF) of 10 must be employed. Additional uncertainty

factors of 10 must be used both for human variability to protect sensitive subpopulations (people who are

most susceptible to the health effects caused by the substance) and for interspecies variability (extrapolation

from animals to humans). In deriving an MRL, these individual uncertainty factors are multiplied together.

The product is then divided into the inhalation concentration or oral dosage selected from the study.

Uncertainty factors used in developing a substance-specific MRL are provided in the footnotes of the LSE

Tables.