Reference

NBS

PUBLICATIONS

N A 1 L

III NilIII

AlllDb 03^306

NBSIR 85-3248

Acrylonitrile-Butadiene-Styrene

Copolymers (ABS): Pyrolysis and

Combustion Products and Their

Toxicity - A Review of the Literature

Joseph V. Rutkowski

Barbara C. Levin

U.S. DEPARTMENT OF COMMERCE

National Bureau of Standards

National Engineering Laboratory

Center for Fire Research

Gaithersburg, MD 20899

December 1985

QC100

• U56

85-3248

1985

onsored in part by:

S. Consumer Product Safety Commission

thesda, Maryland 20207

NBSIR 85-3248

• i ACRYLONITRILE-BUTADIENE-STYRENE

COPOLYMERS (ABS): PYROLYSIS AND

COMBUSTION PRODUCTS AND THEIR

TOXICITY - A REVIEW OF THE LITERATURE

MBS RESEARCH INFORMATION CENTER

ClCs/bo

,UC&

Joseph V. Rutkowski

Barbara C. Levin

U S. DEPARTMENT OF COMMERCE

National Bureau of Standards

National Engineering Laboratory

Center for Fire Research

Gaithersburg, MD 20899

December 1985

Sponsored in part by:

U.S. Consumer Product Safety Commission

Bethesda, Maryland 20207

U.S. DEPARTMENT OF COMMERCE, Malcolm Baldrige, Secretary

NATIONAL BUREAU OF STANDARDS, Ernest Ambler. Director

TABLE OF CONTENTS

List of Tables . iv

List of Figures . . . . . v

Abstract 1

1. Introduction 2

2. Chemical Structure and Thermophysical Properties 2

3. Thermal Decomposition 6

3.1 Thermal Degradation in Inert Atmospheres 8

3.2 Thermooxidative Degradation .... 10

3.2.1 Carbon Monoxide 10

3.2.2 Hydrogen Cyanide 12

3.2.3 Carbon Dioxide 13

3.2.4 Organic Volatiles 14

4. Combustion Product Toxicity 16

4.1 National Bureau of Standards (NBS) Toxicity Test Method ... 17

4.2 University of Michigan Test Method 19

4.3 University of Pittsburgh (PITT) Method 22

4.4 DIN 53 436 Method - Federal Republic of Germany 23

4.5 University of San Francisco (USF) Method 26

5. Summary 29

6. Conclusions 31

7 . Acknowledgements 32

8. References 33

iii
List of Tables

Page

Table 1. Degradation Products of ABS 37

Table 2. Thermal Degradation Products of Two Types of ABS

Decomposed in Nitrogen 38

Table 3. Primary Toxicants from Experimental ABS

Thermooxidative Degradation 39

Table 4. Organic Volatiles from Experimental ABS

Thermooxidative Degradation 40

Table 5. Thermal Oxidative Degradation Products of Two

Types of ABS 41

Table 6. ABS Toxicity Data - NBS Toxicity Test Method 42

Table 7. ABS Toxicity Data - NBS Toxicity Test Method - Carbon monoxide, COHb and HCN 43

Table 8. Relative Toxicity of ABS and Douglas Fir - NBS Test Method 44

Table 9. Toxicity Data - University of Michigan Test Method .... 45

Table 10. ABS Toxicity Data - DIN 53 436 Method 46

Table 11. ABS Mortality and Toxicity Data - DIN 53 436 Method .... 47

Table 12. ABS Toxicity Data - USF Method 48

Table 13. Time to Death Dependency on Sample Size - USF Test Method 49

Table 14. Relative Toxicity of ABS Compared to Various Woods .... 50
List of Figures

Page

Figure 1. Chemical Structures of ABS Monomers 51

Figure 2. Representative Chemical Structure of ABS Polymer 52

Figure 3. Relative Toxicity of ABS - PITT Method 53

v
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Acrylonitrile-Butadiene-Styrene Copolymers (ABS)t Pyrolysis and Combustion

Products and Their Toxicity - A Review of the Literature

Joseph V. Rutkowski

Barbara C. Levin

Abstract

A review of the literature was undertaken to ascertain the current knowledge

of the nature of the thermal decomposition products generated from ABS and

the toxicity of these evolved products ijl toto. The literature review

encompasses English language publications available through June 1984.

This literature surveyed showed that the principal ABS thermooxidative

degradation products of toxicologic importance are carbon monoxide and

hydrogen cyanide. The experimental generation of these and other volatile

products is principally dependent upon the combustion conditions and the

formulation of the plastic. The toxicity of ABS thermal degradation products

has been evaluated by five methods. The LC^^ (30 min. exposure + 14 day post

exposure period) values for flaming combustion ranged from 15.0 mg /2 to 28.5

mg/2. In the non-flaming mode of combustion, the LC,-q values ranged from

19.3 mg/ 2, to 64.0 mg/ 2. Therefore, no apparent toxicological difference

exists between the flaming mode and the non-flaming mode. The toxicity of

ABS degradation products was found to be comparable to the toxicity of the

thermal decomposition products of other common polymeric materials.

Keywords*. ABS plastics; carbon monoxide; combustion products; hydrogen

cyanide; literature reviews; thermal decomposition; toxicity.

1
1. Introduction

Although the hazard posed by toxic gases and vapors generated in a fire

environment has long been recognized [1]*, information regarding the toxic

agent(s) generated from ABS which are responsible for fire deaths not

attributable to burns is relatively sparse. The growth of the science of

combustion toxicology over the last ten years has resulted in the generation

of a large quantity of information regarding the thermal decomposition

products of many natural and synthetic materials, and the relative toxicity

of those materials' decomposition products in toto . This paper is a review

of the English literature, available through June 1984, on the thermal

decomposition products from acrylonitrile-butadiene-styrene (ABS)

terpolymers, and an evaluation of the toxicity data from animals exposed to

those products.

The ABS plastics are of particular interest since they are found in numerous

household items, such as telephones, appliances, luggage and piping, as well

as in automobile and aircraft interior structures.

2. Chemical Structure and Thermophysical Properties

ABS polymers are synthesized from three monomeric chemicals: acrylonitrile,

butadiene, and styrene (Figure 1); from which the acronym is derived. The

^•Numbers in brackets refer to the literature references listed at the

end of this report.

2
atomic components of these three chemical compounds are, exclusively, carbon,

nitrogen, and hydrogen with carbon being the predominant atomic species

(atomic weight /molecular weight). The only source of nitrogen in the plastic

is acrylonitrile which contains approximately 26% nitrogen. The weight

percentage of hydrogen is relatively small.

Acrylonitrile is a colorless liquid characterized by a strong odor. The

boiling point of acrylonitrile is 77.3°C and its freezing point is approximately -83.55°C. Acrylonitrile is soluble in most solvents, both polar and

non-polar. Water solubility increases with temperature [2]. Acrylonitrile

is capable of undergoing many chemical reactions, the majority of which occur

at the carbon-carbon double bond. It is at this site that the homopolymerization of the acrylonitrile monomer occurs. This reaction takes place

readily in the presence of initiators through either a free radical mechanism

or an anionic mechanism of polymerization [3]. The resultant polymer,

polyacrylonitrile, is a crystalline- type compound, which is not soluble in

most common solvents, e.g., acids, greases, oils, water and hypochlorite

solutions. It will, however, degrade when exposed to concentrated cold or

hot dilute alkaline solutions, as well as warm 50% sulfuric acid. Although

the acrylonitrile monomer is significantly toxic by either ingestion of the

liquid or inhalation of the vapor, the homopolymer is considered essentially

non-toxic [3].

1,3-Butadiene is a colorless gas. The boiling point of butadiene is -4.5°C

and its freezing point is -108.96°C. It is soluble in organic solvents [4].

3
Due to the presence of two double bonds, butadiene is a very reactive compound, allowing a variety of polymer structures to be formed. All polymerizations require either an initiator or catalytic factor and occur by a freeradical, an ionic, or a coordinate mechanism. The end result, polybutadiene,

is a rubber polymer formed by addition polymerization [5].

Styrene is a colorless to yellowish, oily liquid which has a penetrating

odor. The boiling point range of styrene is 145 to 146°C and the freezing

point is -30.6°C. Styrene is only slightly soluble in water; however, it is

soluble in alcohol, ether, methanol, acetone and carbon disulfide. Styrene

is not considered very toxic upon ingestion but is a significant irritant

when applied to the skin, eyes and mucous membranes. The rate of polymerization of the styrene monomer is slow at room temperature and increases with

heat. Since the polymerization is an exothermic process, the reaction can

become self -accelerating. Styrene homopolymerization can occur either by

free-radical or ionic reactions. The resultant polymer, polystyrene, is a

clear, crystalline- type compound [6,7,8].

ABS polymers (Figure 2) can be produced by two general methods, each of which

generates a different type of plastic. Type A ABS polymers are produced by a

mechanical blending of a styrene-acrylonitrile copolymer resin with a

butadiene-based elastomer (butadiene-acrylonitrile rubber). The production

of Type B ABS involves a grafting of styrene and acrylonitrile onto polybutadiene. The type B polymer also contains styrene-acrylonitrile copolymer and

ungrafted polybutadiene. The types of plastics are varied further by

differences in the relative proportions of the monomer components. The

4
styrene-acrylonitrile copolymer, for either type of production procedure, can

be composed of 65 to 76% styrene and 24 to 35% acrylonitrile [9,10]. Since

the formulations of ABS plastics are rarely the same and poorly defined in

most of the studies examined for this review, it is difficult to generalize

or compare ABS samples.

The temperatures at which ABS processing occurs range from 325 to 550°C

depending upon the type and grade of plastic being produced as well as the

technique being used. The melting point range for extrusion grades of ABS is

88 to 120°C and for the injection molding grades of ABS, 110 to 125°C [11].

The autoignition temperature of the finished products, generally termed ABS,

has been reported as 466°C [12] and between 500 and 575°C [13]. ABS polymers

burn readily with the generation of dense smoke which is characteristic of

polymers containing aromatic rings [14].

In general, the ABS plastics exhibit good durability and resilience, as well

as mechanical strength. In addition, these thermoplastic polymers demonstrate a favorable combination of thermal, electrical and mechanical properties. The different properties may be selectively enhanced for specific

applications by modification of the composition and/or relative proportions

of the components. Such selective production is usually at the expense of

one or more of the other properties [9,10,15].

5
3, Thermal Decomposition

The type and quantity of the thermal degradation products from ABS plastics

depends upon the combustion chamber utilized and the existing combustion

conditions, as well as the composition of the plastic. The majority of the

studies of the chemical analysis of the decomposition products of ABS has

employed a combustion tube with a ring furnace to decompose the material.

This type of combustion system is similar to that used in the DIN 53 436

toxicity test method (see Section 4.4). This apparatus has the advantages of

being easy to set up and operate and requiring only a small sample for

testing. The combustion atmosphere is easily changed, allowing for pyrolysis

studies under inert conditions as well as thermooxidative degradation experiments. This type of furnace may be programmed either to provide a constant

temperature zone or to heat at a fixed rate. The disadvantages within this

type of system also must be considered. One of the most important

limitations is the large internal surface area on which combustion products

may adsorb or react. In addition, the small sample size, listed as an

advantage above, may also be considered a disadvantage since it does not

provide enough material to be conducive to a flaming test mode. During the

actual combustion, air and/or other gases are fed into the system in a manner

which is contrary to the natural convective flow of air observed under

natural combustion conditions [16].

6
Other furnace systems have been used less frequently in combustion product

generation and analysis. Therefore, their pertinent advantages and limitations will be addressed when the experiments conducted in these particular

systems are initially discussed.

In the following sections, the results of the chemical analyses of the

combustion atmospheres of ABS are separated according to the prevailing

experimental conditions; i.e., inert or oxidative atmospheres. Although real

fires occur normally under oxidative conditions, very often (especially in

large fires), little or no O 2 reaches the polymer surface. Therefore, the

study of the volatile products generated under inert atmospheres provides

information on the molecular mechanisms of thermal degradation under controlled experimental conditions. Also, information may be obtained on

potential decomposition products that could be generated under vitiated

atmospheres or at the polymer surface in real fires.

A summary of all the decomposition products of ABS identified under all the

described experimental conditions is presented in Table 1 in which the

combustion atmosphere (inert or oxidative) is indicated as are the studies

which identified each product. The data indicate that the majority of the

products generated are characteristic of both inert and oxidative conditions.

7
3.1 Thermal Degradation in Inert Atmospheres

This section will cover experiments performed in atmospheres devoid of

oxygen. This experimental atmosphere, in effect, limits the type of degradation products formed, as oxidative decomposition is prevented.

Sumi and Tsuchiya [17] measured the amount of hydrogen cyanide (HCN) generated when chopped ABS pipe was exposed to a temperature of 800°C in a

combustion tube furnace with a nitrogen flow of 1 2,/min. The evolved HCN was

collected in a 0.4% sodium hydroxide (NaOH) trap and quantified with a

cyanide ion (CN“) specific electrode. The maximum concentration of HCN

generated under these experimental conditions was 0.034 g HCN/g ABS sample.

The generation of HCN under nitrogen did not differ quantitatively from that

generated under oxidative conditions (see Section 3.2).

The amount of carbon monoxide (CO) generated by pyrolysis of an ABS sample in

a helium atmosphere was determined by Michal [18]. A horizontal combustion

tube was used with a moving ring oven set at 550°C. Helium gas was fed into

the combustion chamber at a flow rate of 30 ml/min. The ABS used was

identified as Forsan 752E (Kaucuk, Kralupy, Czechoslovakia)^. The results

indicated that CO (as measured by gas chromatography) was not detectable when

this ABS sample was decomposed under the described inert pyrolysis conditions .

^Certain commercial equipment, instruments, or materials are identified

in this paper in order to adequately specify the experimental procedure. In no case does such identification imply recommendation or endorsement by the

National Bureau of Standards, nor does it imply that the equipment or material identified is necessarily the best available for the purpose.

8
Hoff et al. [19] analyzed by gas chromatography-mass spectrometry the

volatile products generated from two different ABS samples decomposed under

an inert atmosphere. The two ABS samples were identified as Ugikral RA 10331

(Ugine Kulman; referred to as ABS-1) and Cycolac AM 25139 (Borg-Warner

;

referred to as ABS-2). ABS-1 and ABS -2 were pyrolyzed at 210°C in a Pyrex

glass degradation tube with a nitrogen gas flow of 20 to 30 ml/min. The two

ABS polymers demonstrated different properties upon thermal degradation.

ABS-2, the less thermostable of the two, decomposed considerably faster and

formed nearly three times as much styrene as ABS-1 (Table 2). ABS-2 also

released higher amounts of other volatiles common to both plastics as

degradation products, such as 2-phenyl-2-propanol, acetophenone, amethylstyrene and isopropylbenzene. ABS-1 did not generate any volatile

products other than styrene in quantities greater than 100 pg/g of ABS sample

pyrolyzed. Some of the degradation products from the ABS samples pyrolyzed

under inert conditions contain oxygen indicating the presence of oxygencontaining additives.

The extensive list of volatile products identified by Hoff et al. [19] (Table

2) may be a result of the experimental methodology. The decomposition

products evolved during the thermal degradation of the polymer were removed

from the furnace/ combustion site by the nitrogen gas flow (20 to 30 ml/min)

potentially reducing their further degradation. Also, the temperature used

is typical of those temperatures used in industrial processing and, at most,

may represent the temperature conditions during the early phase of a fire.

The different amounts of styrene evolved from the two ABS plastics may be

9
related to a difference in the acrylonitrile content of the plastic as it has

been shown that an increase in acrylonitrile content of styreneacrylonitrile polymers favors a higher styrene yield during degradation [20].

3.2 Thermooxidative Degradation

When sufficient oxygen (

O

2

) is present in the atmosphere, the primary gases

formed during the combustion of most materials, including ABS, are CO and

carbon dioxide (CO2

). Hydrogen cyanide generation from nitrogen-containing

materials occurs during thermooxidative degradation as well as during thermal

degradation under inert atmospheres. Other thermooxidative products from ABS

are listed in Table 1.

Table 3 summarizes the quantitative data in the literature on the generation

of CO, CO2 and HCN from ABS decomposed under oxidative conditions. Although

variations in test methods and ABS samples do not allow for direct,

quantitative comparisons between studies, generally more CO and CO2 were

generated in the flaming mode than in the non-flaming mode. The production

of HCN is approximately the same in both modes. The following sections will

discuss the experimental studies on each of these primary gases separately.

3.2.1 Carbon Monoxide

Gross et al. [21] measured the amount of CO generated during the combustion

of two generic samples of ABS. The composition ratio of the monomers in the

plastics was the same for both samples; however, the samples did differ in

10
their physical characteristics and appearance. ABS sample 1 was 0.045 inches

thick, weighed 1.33 kg/m^, and was a semi-rigid sheet with a dark gray matte

finish. The second ABS sample was 0.08 inches thick, weighed 2.35 kg/m^, and

was a rigid sheet with a green polished surface. Each ABS sample was placed

in an 18 ft.^ chamber and was subjected to thermal irradiation at a level of

25 kW/m^ to the normal-use exterior (or front) surface. Gas analysis during

the course of experimentation was performed using colorimetric indicator

tubes^. The maximum value from two separate determinations was reported; if

these values differed by a factor of two, additional measurements were

performed. A ten-fold increase in the maximum generation of CO was

demonstrated under flaming conditions as compared with the CO levels

generated in the non-flaming or smoldering conditions (Table 3).

Similar findings are evident in the data from the interlaboratory evaluation

(ILE) of the National Bureau of Standards (NBS) Toxicity Test Method (Table

3) [13]. Four laboratories used the same ABS material and essentially the

same combustion conditions. However, variations in the results can be

attributed to individual laboratory modifications of the designed

experimental protocol. An ABS copolymer in pellet form was thermooxidatively

degraded in a crucible (or cup) furnace. The amount of air flow around the

test sample in the furnace is unknown and not controlled. This may affect

the formation of secondary combustion products and the completeness of

combustion of evolved products. In the ILE of this test system, toxic gas

-^Indicator tubes, such as Draeger Tubes, do provide a convenient and

inexpensive indication of the presence of measurable amounts of individual

combustion products; however, if interfering gases are present in the test

atmosphere, a high degree of precision and accuracy is not attainable [22].

11
analysis was performed by continuous flow, non-dispersive infra-red analysis

or gas chromatography for CO and CO2 and either gas chromatography or

specific ion electrodes were used for HCN measurement. The observed CO

levels generated in the flaming mode generally exceeded levels measured in

the non-flaming mode of combustion of the ABS; however, the differences were

not as great as those found by Gross et al. (i.e.

,

ten-fold) [21]. One of the

four ILE participating laboratories who examined ABS reported no significant

difference in mean CO levels (laboratory #3). The reason for the differences

between the data of Gross et al. [21] and of Levin et al. [13] is unknown.

Sumi and Tsuchiya [17] used gas chromatography to measure the amount of CO

generated from chopped ABS pipe subjected to a series of increasing

temperatures in a combustion tube furnace (Table 3). An initial increase in

CO production was observed when the temperature was raised from 500 to

600°C. Further elevation of temperature in 100° increments up to a maximum

of 800 °C resulted in a decrease in CO levels. However, when the O

2

concentration was decreased by 50% by nitrogen, the CO level increased twofold over that found at 800°C in air alone. The authors provide no

indication of whether or not the specimens flamed during their tests.

However, as noted above (see Section 3), the quartz tube furnace is not

conducive to flaming combustion.

3.2.2 Hydrogen Cyanide

The generation of HCN, like that of CO, is dependent upon the combustion

conditions. The data from the previously described work of Gross et al. [21]

12
and Levin et al. [13] (laboratory #6 of the ILE) demonstrate no difference

between the evolution of HCN gas during flaming combustion and during nonflaming thermal degradation (Table 3). However, some data (laboratories 1 &

3 of the ILE) indicate a somewhat greater product of HCN in the flaming mode

of combustion than in the non-flaming mode (Table 3) [13]. Sumi and Tsuchiya

[17] demonstrated an increase in HCN production as the temperature increased

from 500 to 800°C. The incidence of flaming combustion, however, was not

noted. For the 300 °C increase in temperature, the generation of HCN

increased approximately two-fold. At 800°C, a 50% decrease in the O 2 content

of the combustion atmosphere increased HCN production by approximately 20%.

3.2.3 Carbon Dioxide

Sumi and Tsuchiya [17] examined the effect of temperature on the production

of CO2. Carbon dioxide production was approximately five- to ten-fold

greater than CO production (Table 3). The CO2 production at all temperatures

was approximately the same, ranging from 223 to 297 mg/g sample. The

occurrence of flaming combustion was not reported. In a combustion

atmosphere of air and nitrogen (50/50; 10% O2

), the yields of CO and CO2 were

of the same order of magnitude (52 and 58 mg/g sample, respectively).

The data reported by Levin et al. [13] also demonstrated a preponderance of

CO2 over CO generated in the combustion of ABS (Table 3). Except for the

results reported by one of the participating laboratories (laboratory // 3),

CO2 production was greater in the flaming mode than in the non- flaming mode.

13
The mean CO2 values differed between combustion modes by a factor of two to

three

.

3. 2. A Organic Volatiles

The classes of organic volatiles and the summed quantities of the individual

agents generated during the experimental thermooxidative degradation of

various samples of ABS are presented in Table A and discussed below. Some of

these compounds, such as acrolein and styrene, have known irritant properties

and may be present in high enough concentrations to compound the hazard of

the fire environment by affecting the mucous membranes and respiratory tracts

of exposed individuals.

Zitting and Heinonen [23] measured the levels of styrene, benzaldehyde,

acrolein, and acrylonitrile when Cycolac T 10000 (Borg Warner) was decomposed

in air at 250, 300 and 350°C in a combustion tube furnace with an air flow of

0.5 2,/min. Styrene and benzaldehyde were measured by gas chromatography,

acrolein by high pressure- liquid chromatography (HPLC) of its 2,A-dinitrophenylhydrazone derivative and acrylonitrile by colorimetric indicator

tubes^. The aromatic hydrocarbon yield (in this case, styrene) increased

with each 50 °C increase in temperature, as did the aldehydes (benzaldehyde

and acrolein) and acrylonitrile (Table A). The amount of benzaldehyde

present exceeded the measured amount of acrolein one hundred fold.

Zitting and Savolainen [2A] determined the quantity of various organic

volatiles when Cycolac T 1000 was thermooxidatively degraded at temperatures

1A
of 300 and 330°C. Gas chromatographic analyses of styrene (listed as an

aromatic hydrocarbon in Table 4) indicated that the concentration doubled

with the 30°C increase in degradation temperature. The same relative

increase was seen with acrylonitrile and the organic acids which were

measured by back titration with NaOH. The aldehyde concentrations (acrolein,

formaldehyde and total aldehydes) also increased with the increase in

temperature; however, this increase was less than two-fold. Acrolein was

measured by the method of Cohen and Altshuller [25]. Formaldehyde concentration was determined by a chromatropic method [26] and total aldehydes by

sodium bisulfite titration.

Hoff et al. [19] thermooxidatively decomposed two ABS plastics, Ugikral RA

10331 (ABS-1) and Cycolac AM 25139 (ABS-2) at 208°C and 197°C, respectively,

and measured a number of organic volatiles (Tables 4 and 5). Styrene was the

principal degradation product measured. ABS-1 generated six times more

styrene than the total of all other combustion products combined and ABS-2

generated four times more styrene than the total of all the other volatiles.

Thus, the aromatic hydrocarbons were the predominant class of organic

volatiles. During the thermooxidative degradation of ABS-1, no other

measured compound appeared in the fire atmosphere in quantities equal to or

greater than 100 pg/g of sample. ABS-2 generated significant amounts

(greater than 100 pg/g of sample) of 2-phenyl-2-propanol, acetophenone, isopropylbenzene, benzaldehyde and a-methylstyrene in addition to styrene; the

other measured compounds appeared in quantities less than 100 pg/g of sample

(Table 5). Comparison of Tables 2 and 5 indicates that similar degradation

products evolved during the degradation of ABS-1 and ABS-2 under both inert

15
and oxidative conditions which demonstrates no significant oxidative effect

on the products. Therefore, either no oxidation occurs under the described

thermooxidative combustion conditions or the combustion apparatus prevented

oxidation from occurring.

4. Combustion Product Toxicity

In laboratory experiments designed to assess the toxicity of combustion

products of either natural or synthetic materials, a number of factors must

be considered, including the experimental design, the physical apparatus, the

combustion conditions and the material sample. A review of the literature on

ABS combustion product toxicity is presented below with appropriate

consideration given to these important factors.

The variety of ill-defined material formulations, experimental systems, and

conditions that have been used to assess ABS combustion product toxicity

makes inter laboratory comparison of data difficult. However, sufficient

toxicity data obtained using different test methods exist to compare the

toxicity of the thermal degradation products of ABS to those of other

materials such as Douglas fir. (Although it is recognized that Douglas fir

is not a substitute for ABS in commercial products, the large realm of

toxicological data on wood provides a point of reference with which the

relative toxicity of materials can be compared.) Certain other

characteristics of the combustion product toxicity can also be inferred. A

brief description of each test system will precede a discussion of the data.

16
4.1 National Bureau of Standards (NBS) Toxicity Test Method

The NBS test method [27] utilizes a static exposure system in which the

combustion products accumulate in the exposure chamber for the duration of

the exposure. The system employs a cup furnace which generates combustion

products directly into the 200 £ exposure chamber. The material to be tested

is decomposed at a cup furnace temperature 25°C above (flaming mode) and

below (non- flaming mode) the predetermined autoignition temperature of that

particular material. The experiments may also be performed at a furnace

temperature of 440°C if the autoignition temperature exceeds 490°C. The

design of the exposure chamber provides for head-only exposure of six rats,

as well as sampling of the chamber atmosphere for chemical analyses. Carbon

monoxide, CO2 and O 2 are monitored continuously. Hydrogen cyanide is

measured approximately every three minutes when a nitrogen- containing

material is tested.

The biological/toxicological endpoints that have been used with this test

method are incapacitation and lethality. Incapacitation is determined by the

hind limb flexion conditioned avoidance response for which an value is

determined. For lethality, an exposure LC^-q value (the mass loading of

material per unit volume of the chamber necessary to cause 50% of the test

animals to die) is determined, as well as an LC_q value for both the exposure

and post-exposure observation periods. The procedure also calls for the

observation of toxic signs during the 30-minute exposure period and the 14-

day post-exposure period, during which daily animal body weights are

recorded. Carboxyhemoglobin (COHb) levels are measured before exposure and

17
just before the end of the exposure period in two animals which are

cannulated 24 hours prior to exposure.

The toxicity data from Levin et al. [13] and Anderson et al. [28] show that

the degradation products from ABS may be more toxic when decomposed under

flaming thermooxidative conditions than non-flaming conditions (Table 6 ).

The within-exposure [LC^ (30 min)] and the within plus post-exposure [LC50

(30 min + 14 days)] results are equivocal in the comparison of toxicity under

the two modes of combustion. The animal deaths did occur during both the

exposure and post-exposure periods. The incapacitation data (EC^^)

demonstrate that the flaming mode and the non-flaming mode produced

combustion products of approximately equal toxicity. In addition, Anderson

et al. [28] reported that some animals demonstrated a degree of corneal

opacity when ABS was degraded in the non-flaming mode.

The concentrations of CO and HCN in the combustion atmosphere are measured

according to the protocol of the NBS test method. The results are presented

in Table 7. More CO was generated in the flaming than the non-flaming

exposure atmospheres and correspondingly higher COHb levels were noted in the

exposed animals; however, the amount of CO was not sufficient to account for

the lethality of the animals [29]. On the other hand, the measured HCN

concentrations in the exposure atmospheres were sufficient by themselves or

with the additional CO to account for the deaths that were observed in

laboratories 1, 3 and 6 in the flaming mode. In the non-flaming mode,

laboratory 1 reported HCN and CO levels that either individually or together

were too low to account for the observed within-exposure deaths. Whereas,

18
laboratories 3 and 6 reported HCN levels sufficiently high enough to have

caused within-exposure deaths, but in actuality no deaths were observed

(Table 7).

Under flaming conditions, the LC^ values for ABS were lower than those found

for Douglas fir by approximately a factor of two (Table 8). This difference

may not be regarded as toxico logically significant. There is no significant

difference in toxicity between ABS and Douglas fir when combusted in the nonflaming mode, even though the wood generates a significantly greater amount

of CO under both combustion conditions. These results support the earlier

implication of the involvement of another toxicant (presumably HCN) in the

toxic action of ABS combustion products.

4.2 University of Michigan Test Methods

Two test systems, one static and one dynamic, each with distinct characteristics, were developed by Cornish and coworkers [30-32]. The static system

consists of a 1500 Z stainless steel exposure chamber in which mice are

exposed in a whole-body fashion to the combustion products for a period of 4

hours. Combustion products are generated by placing the test material in a

Vycor tube wrapped with resistance wire which produces a combustion temperature of 700 to 800°C in 1 to 2 minutes. The LC^ is determined after a 7 day

observation period. Additional animals may be tested and sacrificed

following exposure for histological/pathological examination.

19
The dynamic University of Michigan test system consists of a flow-through

Pyrex glass tube chamber with side ports for the head-only exposure of rats.

The combustion products are generated from materials placed in a ceramic boat

in a combustion furnace. The furnace temperature is programmed to increase 3

to 5°C per minute to a maximum temperature of 700 to 800°C. Carrier air is

passed through the combustion apparatus at a rate of 1 2,/min and an additional diluting air stream of 2 2,/min is added before the combustion products

enter the exposure chamber. The exposure period parallels the time course of

combustion product generation during the degradation of the material sample.

The amount of material consumed which kills 50% of the exposed animals

(LA(-q)^ from a number of studies on ABS decomposed in both the static and the

dynamic test systems are listed in Table 9. The specimens were not

identified sufficiently to determine if the ABS material tested was identical

in all three studies. The data provide some information on the relative

toxicity of fire retardant (unspecified) treated ABS (ABS-FR) and non-fire

retarded ABS samples and other materials used in these studies. Because of

the great differences in design and operation of the static and dynamic

exposure systems, the specific toxicity of any one material in either system

should not be compared. However, the relative toxicities of different

materials studied within one system should be comparable to that found in

other systems. This does not always hold [32],

^ The use of the convention, LCj-q, by Cornish et al. to describe a value expressed in grams and not grams per unit volume is inappropriate. The

convention LA^ (lethal amount,^) is used as a more appropriate substitute in

the discussion of this data.

20
In the static exposure system, red oak is a factor of two more toxic than ABS

and ABS-FR (Table 9). However, the results of the experiments with the

dynamic exposure system rank both ABS and ABS-FR of approximately equal

toxicity with red oak (Table 9). When one considers the relative toxicities

of ABS and polypropylene in the static exposure system, polypropylene is

equal in toxicity to ABS; whereas, in the dynamic exposure system, it is more

toxic (Table 9) [32], Therefore, these data indicate that a change in

combustion systems will affect different materials differently.

The LA^q values from the experiments using both the dynamic system and the

static system [30,31] do not show much difference between the apparent

toxicities of the combustion products of ABS and those of ABS-FR (Table 9).

However, the specific mortality results, taken in a separate study [32], do

indicate a difference. For example, when rats were exposed in the static

system to the combustion products of a 20 gram sample of ABS-FR, 14 out of 15

animals (93%) died. Three of four rabbits died, as well, when subjected to

the same exposure conditions [32]. This mortality is somewhat greater than

anticipated since a 20 gram sample is essentially equivalent to the reported

LA[-q value [30,32]. In contrast, no rats or rabbits died from the exposure

when a 20 gram sample of non-fire retarded ABS was decomposed [32], although

the reported LA^q value is also approximately 20 g [30,31] or slightly

greater (33 grams) [32]. These inconsistencies which are evident between the

mortality data [32] and the LA^ values [30-32] for ABS and ABS-FR are not

explained.

21
4.3 University of Pittsburgh (PITT) Method

This dynamic test system was developed by Alarie and Anderson [33], A

Lindberg furnace programmed to heat at 20°C/min, starting at room temperature, is responsible for the generation of combustion products. The test

material starts in the non-flaming mode and will flame when the material's

autoignition temperature (under these combustion conditions) is exceeded.

Animal exposure begins in the non-flaming mode when 0.2% of the material has

decomposed. An air flow of 11 8,/min is maintained through the furnace during

the combustion of the material. Total air flow entering the exposure chamber

amounts to 20 2,/min following dilution of the combustion gases with cooling

air. The 2.3 2, glass exposure chamber accommodates four mice in the headonly exposure mode. The biological endpoints /parameters which are determined

include the RD^-q (i.e., the concentration of smoke that produces a 50%

decrease in respiratory rate), a sensory irritation stress index (SISI),

asphyxiant effects, lethality, and histopathological changes. Analyses of

the combustion atmosphere for primary toxicants and O

2 depletion are also

performed.

A very limited amount of ABS toxicity information derived from this test

system is available. Alarie and Anderson [34] determined an LC^q of 6.3 g

(10.5 mg/fc)5 where the LC,-q is the amount of material loaded in the furnace

^Alarie reports his toxicological results in grams of material. For

comparison purposes the gram units have been converted to mg/ 2, units by the

following equation:

x 1000 mg/g

chamber air flow rate (2,/min) x exposure time (min)

22
that is required to kill 50% of the animals within an exposure period of 30

minutes and a post-exposure period of 10 minutes. The ABS sample used was

only described as "standard acrylonitrile-butadiene-styrene". The LT^q, the

time at which 50% of the animals die at the sample weight killing 50% of the

animals (or the sample weight nearest above it), was recorded as 9 minutes.

According to the evaluation criteria incorporating both the concentrationresponse and time-response, the ABS is classified as being more toxic than

wood (i.e., Douglas fir) and toxic actions occur faster upon exposure to ABS

combustion products than upon exposure to the combustion products of wood.

Anderson et al. [28] also tested ABS using the PITT method in their report to

the New York State Office of Fire Prevention and Control. An LC^q value of

9.3 mg/ £.5 was obtained for the ABS sample used. The LT^q range during which

the deaths occurred was 0 to 40 minutes with an additional death reported

during the period of 49 hours to 14 days post exposure. Again, the ABS also

proved to be more toxic than Douglas fir.

4.4 DIN 53 436 Method - Federal Republic of Germany

This apparatus was developed in the Federal Republic of Germany and adopted

as a standard test method by the German Commission of Standards [35]. The

combustion apparatus consists of a silica tube with a ring oven which moves

along the combustion tube at a rate of 10 mm/min. In these flow experiments,

the key parameters are residence time in the heated zone and air/fuel (gas)

ratio. Air flow through the combustion tube is provided at a rate of 100

2,/hr in a direction counter to the movement of the oven. The combustion

23
products are diluted, cooled and carried into the exposure chamber by a total

air flow of 200 8,/hr. Various exposure chambers can be used to provide for

either whole body or head-only exposures. The toxicological end point is

animal death. In addition, the animals are observed for toxic signs during

and following the exposure. Gross pathological examinations are performed

when appropriate. The typical protocol consists of a 30 minute exposure

period and a 7 to 14 day post-exposure observation period.

Kimmerle [36] used the head-only exposure system to evaluate the toxicity of

two samples of ABS, a solid and a foam. The mortality data are presented in

Table 10. It appears that a substantial increase in mortality occurred when

the decomposition temperature of the solid ABS sample was increased from 350

to 400°C. Although the CO concentration at 400°C was increased more than 2-

fold in the atmosphere, the level was too low to account for the deaths. The

carboxyhemoglobin levels in the rats exposed to solid ABS being degraded at

400°C were also higher than the other groups but still well below toxic

levels, which were shown by Levin et al. to be above 80% [29], The increased

HCN concentration from 100 to 150 ppm, however, was enough to cause lethality

in 30 minutes [29].

An ABS foam differed from the above described solid ABS in that the increase

in mortality at the elevated temperature was much less for the foam. No

change in CO concentration was recorded when the foam was degraded at the

higher temperature, and the five-fold increase in HCN concentration resulted

in a final concentration of only 100 ppm. It is, therefore, not surprising

that fewer rats died in the 30 minute exposure to the combustion products of

24
the ABS foam as compared to the solid. These results show that the solid ABS

combustion products appear to be more toxic than those of the ABS foam when

exposed to temperatures of 400°C. At this temperature, lethal levels of HCN

are generated from the solid ABS sample while sublethal levels are produced

from the ABS foam. In both cases, HCN concentrations increased at the higher

temperature. The differences in toxicity between the two ABS samples can be

attributed to possible variations in the formulation of the solid and foam.

Herpol [37] also utilized the DIN test apparatus to evaluate the toxicity of

an ABS sheet. However, the chamber system was modified to allow for

individual whole-body exposure of the rats. This ABS sample was degraded at

three different temperatures 400, 600, and 800°C and the mortality found at

each temperature is given in Table 11. The toxicity of ABS increases with an

increase in combustion temperature. However, at the two higher temperatures,

more material degraded. This temperature phenomenon was also described to

some degree by Kimmerle [36] (see above). A significant mortality was

evident at 400°C and not at 350°C in the results for the ABS solid [36].

However, Herpol did not observe any animal deaths until a temperature of

600°C was reached [37]. This may reflect a difference in material

concentration, formulation, or any number of possible variations in the

experimental conditions. Herpol [37] demonstrated an increase in the CO and

CO2 indices as the temperature increased from 400 to 600°C. These indices

are calculated by summing the recorded values at each minute and indicate the

amount of gas liberated by the test material during the test period. A

slight decrease was evident when the temperature was further increased to

800°C (see Table 11). In pure CO experiments, Herpol [37] found that the CO

25
index necessary to cause death during a 30 minute exposure was 120,000

ppm*min (equivalent to a 30 minute exposure to A, 000 ppm). A CO2 index of

300%*min (equivalent to a 30 minute exposure to 100,000 ppm) will result in

the inhibition of respiration. It is evident from the data (Table 11) that

the CO was not present in amounts that can solely account for the observed

mortality. These data suggest, as has the work of other authors, that CO is

not the only toxicant involved.

A. 5 University of San Francisco (USF) Method

The apparatus for this method consists of a Lindberg horizontal tube furnace

which is either programmed to heat at a rate of A0°C/min from 200°C to a

maximum of 800°C or set at a fixed temperature. The toxic combustion

products which are generated are carried into the exposure chamber with or

without a forced air flow. The exposure chamber is a A. 2 8, hemisphere

constructed of polymethylmethacrylate and provides for whole-body exposure of

four mice. The biological endpoints which are used in this system are time

intervals to various observed signs of intoxication, such as incapacitation,

staggering, convulsions, collapse, or death. The mortality is recordedAnalysis of CO and CO2 in the chamber atmosphere is performed at the

conclusion of the experiment. Oxygen levels, however, are monitored

periodically during the exposure.

The principal disadvantage to this system is that all endpoints are based on

the subjective measurements of the one individual conducting the test. In

addition, these endpoints provide no insight into the cause of the observed

26
response. Since CO and CO2 are measured at the end of the exposure period,

limited inference can be made concerning the role of these gases in the

observed toxic effects. Moreover, time to effect is not a true toxicologic

parameter and, in this case, is related to both the time necessary for

material degradation and the time required for the toxic insult to take

effect. Toxicity is based on the quantity of a substance required to

elicit a certain measurable effect. The "time to effect" is more appropriately considered important in the overall hazard assessment of a material in

a particular use rather than being an index of toxicity.

Hilado and co-workers have amassed a sizeable amount of data on the toxicity

of materials, including ABS. Only selected representative work by Hilado et

al. [38,39] will be presented here in an effort to avoid redundancy.

The data for ABS toxicity are presented in Table 12. The endpoints used by

Hilado are the following: (1) time to incapacitation (the first observation

of staggering, prostration, collapse or convulsions), (2) time to staggering

(the initial observation of loss of equilibrium), (3) time to convulsions

(the first observation of convulsive- type movement), (A) time to collapse

(the first observation of muscular support loss), and (5) time to death (the

time at which cessation of movement and respiration are observed). The mean

values and standard deviations of times to specified animal responses

presented in the studies by Hilado et al. are derived from the means of two

or more replicate tests and reflect between- experiment variation, rather than

individual animal variability. The ABS material used by Hilado et al. was

identified as Dylel 702, natural, lot A5A000 from Sinclair-Koppers , Co.,

27
Kobuta, PA. The data in Table 12 compare various experimental conditions and

their influence on the toxicity of ABS. The amount of ABS pyrolyzed under

each set of experimental conditions was approximately 1.0 g. From these

results, it is evident that the determination of the relative toxicity of ABS

depends largely upon the test conditions used. With this test system, the

most toxic exposure condition is a fixed furnace temperature of 800°C with

forced air flow at which animals respond most rapidly. This short animal

response time is most likely due to the more rapid generation of toxic

decomposition products at this temperature. The addition of a forced air

flow through the combustion system into the exposure chamber also augments

the degree of toxicity as reflected in the shorter time to response at 600

and 800°C. The apparent CO concentration (ppm) in the animal chamber at the

end of the exposure period did not correlate with the time to response. In

fact, at 800°C with forced air flow, the amount of CO was lower at the

shorter response times, an observation that was not evident at a furnace

temperature of 600°C.

In another study of ABS by Hilado and Huttlinger [39], a material sample

size-dependent phenomenon was demonstrated under fixed an ramped temperature

conditions in the time to death of the animals (Table 13). Two samples of

ABS, Dylel 702 natural Lot A54000, Sinclair-Koppers Co., Kobuta, PA (ABS-1)

and Lustran, Monsanto Co., St. Louis, MO (ABS-2) were tested. As the mass of

the pyrolyzed sample increased, the mean time to death of the experimental

animals decreased, a result which is not surprising since the amount of toxic

gases produced is directly correlated with the amount of sample decomposed.

The decrease is directly correlated with the amount of sample decomposed.

28
The decrease in time of death observed with both samples under ramped and

fixed temperature conditions was comparable.

Hilado and Huttlinger compared the relative toxicity of ABS to various woods

under ramped temperature conditions and no air flow [41], The results are

presented in Table 14. The data presented by Hilado [41] show that the CO

concentration generated by the ABS sample at the time of death is less than

that generated by any of the nine wood samples tested under similar

conditions. Also, the concentration-time product for ABS is lower than that

of any wood sample tested. The concentration- time product of CO was

calculated to be 31,020 ppm’min indicating that the amount of CO generated by

the thermal decomposition of ABS was barely in the critical range (30,000 to

45,000 ppm*min for a 30 minute exposure period is characteristic of materials

whose principal toxicant is CO [41]). (Caution should be used, however, in

extrapolating concentration-time products to other exposure times since this

value is not a constant.) While CO was found to be an important contributor

to ABS combustion product toxicity [40], Hilado and Huttlinger [39] did not

consider it to be the sole toxicant.

5 . Summary

The processes of pyrolysis and combustion under various atmospheric conditions result in the production of many decomposition products, some which are

known toxicants and others whose toxicities have not been investigated. In

addition, there may be toxic products generated that have not been

identified. The conditions under which decomposition occurs are important in

29
determining which degradation products will be generated and at what concentrations .

In the case of ABS, twenty-seven chemical compounds have been identified as

combustion products [13,17,18,19,21,23,24]. It is obvious that more

combustion products are generated, but have not been identified or

investigated to date. The degradation products which appear to be of primary

toxicologic concern are CO and HCN [13,36]. These two decomposition products

have been detected under a wide variety of experimental conditions and are

likely to be generated under real fire situations. Although each toxicant

alone may not be present in adequate concentrations to pose a health threat,

recent studies at NBS on the interaction of CO and HCN indicate that these

two toxicants may act in an additive fashion [29]. The data presented in

this review have been evaluated to determine the extent to which CO and HCN

together could account for the combustion product toxicity. It appears that

the concomitant generation of CO and HCN is responsible for the toxic/ lethal

effects of the combustion products of ABS. However, the involvement of other

toxicants cannot be precluded prior to comprehensive analyses of the

degradation products.

In general, the degradation products of ABS from the flaming mode produced

LC^q values that were lower than those of wood (either Douglas fir or red

oak) (Figure 3) [13,32,34]; however, some findings to the contrary have been

noted [32]. The magnitude of the differences in LC^q values ranges from a

two-fold difference in a static exposure system [13] to a ten-fold difference

in a dynamic test system [34]. The ABS LC^q values for flaming combustion

30
ranged from 10.5 mg/2 [34] to 22.1 mg/ 8- [13] for a 30 minute exposure period

and 15.0 mg/2, [13] to 28.5 mg/ 2, [28] for the 30 minute exposure and 14 day

observation period. In the non-flaming mode, both ABS and Douglas fir

combustion products are equally toxic [13]. In the non-flaming mode of

combustion, the ABS LC,-q values ranged from 22.0 mg/ 2, [13] for a 30 minute

exposure to 64.0 mg/ 2 or greater [13,28] for the 30 minute exposure and 14

day observation period.

6. Conclusions

The currently available literature on ABS combustion product toxicity provide

a great deal of data; however, these results have only very limited usefulness. The full assessment of the relative toxicity of the combustion

products of ABS is complicated by a large number of potential variations in

the chemical formulations of ABS and a variety of test systems and experimental protocols. However, the following generalizations are possible:

(1) Many combustion products are generated during the decomposition

of ABS.

(2) The principal gases which appear to be responsible for the

observed toxicity are HCN and CO.

(3) The thermal degradation products of ABS plastics demonstrate a

measurable degree of toxicity. However, the toxicity of ABS

31
combustion products is comparable to the toxicity of the degradation products of other common polymeric materials.

7 . Acknowledgements

The authors gratefully acknowledge the help of Ms. N. Jason, Ms. M. Diephaus,

Ms. A. Durham and Ms. C. S. Bailey who performed the literature search and

compiled the references.

This experimental work was performed under Contract CPSC-IAG-74-25, Task

Order 84-8 from the U. S. Consumer Product Safety Commission, Dr. Rita Orzel,

Project Officer. The opinions expressed herein are those of the authors and

not those of CPSC.

32
8. References

[1] Ferguson, G. E., Fire gases. Nat. Fire Prot. Assoc. 27:110 (1933).

[2] The Merck Index. M. Windholz, ed. 10th edition, p. 20 (1983).

[3] Bamford, C. H. , and Eastmond, G. C., Acrylonitrile polymers. Encyclopedia of Polymer Science and Technology. H. F. Mark, N. G. Gaylord and

N. M. Bikales, eds., Interscience Publishers, New York, pp. 374-425

(1964).

[4] The Merck Index. M. Windholz, ed. 10th edition, Merck & Co., Inc.,

Rahway, NJ, p. 209 (1983).

[5] Saltman, W. M. , Butadiene polymers. Encyclopedia of Polymer Science

and Technology. H. F. Mark, N.G. Gaylord and N. M. Bikales, eds..

Interscience Publishers, New York, pp. 678-754 (1965).

[6] The Merck Index, M. Windholz, ed. 10th edition, Merck & Co., Inc.,

Rahway, NJ, p. 1270 (1983).

[7] Coulter, K. E. and Kehde, H. , Styrene polymers (monomers). Encyclopedia of Polymer Science and Technology. H. F. Mark, N. G. Gaylord and

N. M. Bikales, eds.. Interscience Publishers, New York, pp. 135-155

(1970).

[8] Platt, A. E., Styrene polymers (polymerization). Encyclopedia of

Polymer Science and Technology. H. F. Mark, N. G. Gaylord and

N. M. Bikales, eds.. Interscience Publishers, New York, pp. 156-206

(1970).

[9] Basdekis, C. H. , ABS Plastics. Reinhold Publishing Corporation, New

York (1964).

[10] Lebovits, A., Acrylonitrile-butadiene- styrene copolymers. Encyclopedia of Polymer Science and Technology. H. F. Mark, N. G. Gaylord

and N. M. Bikales, eds.. Interscience Publishers, New York, pp. 436-

444 (1964).

[11] Modern Plastics Guide to Plastics, McGraw-Hill, New York, pp. 4-5

(1983).

[12] Landrock, A. H. , Handbook of Plastics Flammability and Combustion

Toxicology. Noyes Publications, Park Ridge, NJ (1983).

[13] Levin, B. C., Paabo, M. and Birky, M. , An interlaboratory evaluation

of the 1980 version of the National Bureau of Standards test method

for assessing the acute inhalation toxicity of combustion products.

Nat. Bur. Stand. (U.S.) NBSIR 83-2378, April 1983. 82 p.

33
[14] Cullis, C. F. and Hirschler, M. M. , The combustion of organic polymers. The International Series of Monographs on Chemistry.

J. E. Baldwin, J. B. Goodenough, J. Halpern and J. S. Rowlinson, eds.

Clarendon Press, Oxford (1981).

[15] Lantz, J. M. , ABS. Modern Plastics Encyclopedia 198A-85. J.

Agranoff, ed., McGraw-Hill Inc., New York, pp. 6-7 (1984).

[16] Kaplan, H. L. , Grand, A. F. and Hartzell, G. E., Combustion

Toxicology-Principles and Test Methods, Technomic Publishing Co.,

Inc., Lancaster, PA (1983).

[17] Sumi, K. and Tsuchiya, Y. , Toxicity of decomposition productspolyacrylonitrile, nylon and ABS. Building Research Note No. Ill,

Division of Building Research, National Research Council of Canada,

April 1976, 3p.

[18] Michal, J., Determination of carbon monoxide in thermal degradation

products of polymeric materials. Fire & Matls. 5:149-152 (1981).

[19] Hoff, A., Jacobsson, S., Pfaffi, P., Zitting, A., Frostling, H.,

Degradation products of plastics: Polyethylene and styrene-containing

thermoplastics - Analytical, occupational and toxicologic aspects.

Scand. J. Work Environ. Health, Suppl.2 8:9-60 (1982).

[20] Grassie, N. and Bain, D. R. , Thermal degradation of copolymers of

styrene and acrylonitrile: I. preliminary investigation of changes in

molecular weight and the formation of volatile products.

J. Polym. Sci. A-l 8:2653-2664 (1970).

[21] Gross, D., Loftus, J. J., Lee, T. G. , and Gray, V. E., Smoke and gases

produced by burning aircraft interior materials. Nat. Bur. Stand.,

Washington, DC. Prepared for the Dept, of Trans, F.A.A., Report

No. NA-68-36 (DS-68-16) (June 1968).

[22] Standard Guide for Measurement of Gases Present or Generated During

Fires, ASTM E 800-81, American Society for Testing Materials,

Philadelphia, PA (1984).

[23] Zitting, A. and Heinonen, T., Decrease of reduced glutathione in

isolated rat hepatocytes cause by acrolein, acrylonitrile, and the

thermal degradation products of styrene copolymers. Toxicology

17:333-341 (1980).

[24] Zitting, A. and Savolainen, H. , Effects of single and repeated

exposures to thermooxidative degradation products of

poly( acrylonitrile-butadiene-styrene) (ABS) on rat lung, liver,

kidney, and brain. Arch. Toxicol. 46:295-304 (1980).

[25] Cohen, J. R. and Altshuller, A. P. , A new spectrophotometric method

for the determination of acrolein in combustion gases and in the

atmosphere. Anal. Chem. 33:726-733 (1961).

34
[26] NIOSH American Public Health Association, Washington (NIOSH manual of

analytical methods of air sampling and analysis), p. 194 (1972).

[27] Levin, B. C., Fowell, A. J., Birky, M. M. , Paabo, M. , Stolte, A. and

Malek, D. , Further development of a test method for the assessment of

the acute inhalation toxicity of combustion products. Nat. Bur.

Stand. (U.S.) NBSIR 82-2532, June 1982, 133p.

[28] Anderson, R. C., Croce, P. A., Feeley, F. G. and Sakura, J. D., Study

to assess the feasibility of incorporating combustion toxicity

requirements into building material and furnishing codes of New York

State. Final Report to Department of State, Office of Fire Prevention

and Control, Albany, NY, Reference 88712, Arthur D. Little,

Inc. (1983).

[29] Levin, B. C., Paabo, M. , Bailey, C., Harris, S. E., and Gurman, J. L.

,

Toxicological effects of the interactions of fire gases and their use

in a toxic hazard assessment computer model. The Toxicologist 5:127

(1985).

[30] Cornish, H. , Toxicity of thermal-degradation products of plastics.

Proceedings of Symposium on Products of Combustion of (Plastics)

Building Materials, Lancaster, PA (March 1973).

[31] Cornish, H. H. , Hahn, K. J., and Barth, M. L. , Experimental toxicology

of pyrolysis and combustion hazards. Environ. Health

Perspect. 11:191-196 (1975).

[32] Cornish, H. H. , Barth, M. L., and Kolman, L. H. , Comparative toxicology of plastics during thermodecomposition. Utah University

International Symposium (March 1976).

[33] Alarie, Y. C. and Anderson, R. C., Toxicologic and acute lethal hazard

evaluation of thermal decomposition products of synthetic and natural

polymers. Toxicol. Appl. Pharmacol. 51_:341-362 (1979).

[34] Alarie, Y. and Anderson, R. C., Toxicological classification of

thermal decomposition products of synthetic and natural polymers.

Toxicol. Appl. Pharmacol. 57:181-188 (1981).

[35] German Standards Institution, (January 1979). DIN 53 436, "Erzeugung

Thermischer Zersetzungsprodukte von Werkstoffen unter Luftzufuhr und

ihre Toxikologische Prufung. Part 1, Zersetzungserat und Bestimmung

der Versuchstemperatur . Part 2, Verfahren zur Thermischen Zersetzung"

(draft)

.

[36] Kimmerle, M. G. , Aspects and methodology for the evaluation of

toxicological parameters during fire exposure. J. Fire &

Flamm./Comb. Tox. 1:4-51 (1974).

35
[37] Herpol, C., Biological evaluation of toxicity caused by combustion of

building materials. Fire & Hatls. 4:127-143 (1980).

[38] Hilado, C. J., Gumming, H. J., Michado, A. M. and Schneider, J. E.

,

Comparison of animal responses to the combustion products generated by

two test procedures, the USF/NASA methodology and the FAA/CAMI

system. J. Comb. Tox. 4:325-359 (1977).

[39] Hilado, C. J. and Huttlinger, N. V. Concentration-response data on toxicity of pyrolysis gases from six synthetic polymers.

J. Comb. Tox. 5:81-100 (1978).

[40] Hilado, C. J. and Cumming, H. J., Studies with the USF/NASA toxicity

screening test method: Carbon monoxide and carbon dioxide concentrations. J. Comb. Tox. 4:376-384 (1977).

[41] Hilado, C. J., Carbon monoxide as the principal toxicant in the

pyrolysis gases from materials. J. Comb. Tox. 6:177-184 (1979).

36
Table 1

Degradation Products of ABS

Product Atmospherea References

acetophenone I, o 19

acids (-COOH) 0 24

acrolein I, o 19, 23, 24

acrylonitrile I, o 19, 23, 24

aldehydes (total) (HCHO) 0 24

benzaldehyde I, o 19, 23

carbon dioxide 0 13, 17

carbon monoxide 0 13, 17, 18, 21

cresol I, 0 19

dimethylbenzene I, 0 19

ethanal I, 0 19

ethylbenzene I, 0 19

ethylmethylbenzene I, 0 19

formaldehyde 0 24

hydrogen cyanide I, 0 13, 17, 21, : isopropylbenzene I, 0 19

a-methylstyrene I, 0 19

0-methylstyrene I, 0 19

nitric oxide 0 21

nitrogen dioxide 0 21

phenol I, 0 19

phenyl cyclohexane I, 0 19

2 -phenyl- 2 -propanol I, 0 19

3-phenyl-l-propene I, 0 19

n-propylbenzene I, 0 19

styrene I, 0 19, 23, 24

4-vinyl- 1 -cyclohexene I, 0 19

a

I = Inert pyrolysis atmosphere

0 = Oxidative combustion atmosphere

37
Table 2

Thermal Degradation Products of Two Types of ABS

Decomposed in Nitrogen [19]

Degradation Product ABS-l a ABS-2b

Styrene 2400 c 7400

2- phenyl- 2 -propanol*^ 20 580

Acetophenone^ 23 420

a-Methylstyrene 12 230

Iso-propylbenzene 42 190

4-vinyl-l -cyclohexane 13 88

Benzaldehyde^ 33 75

Ethylbenzene 23 54

Ethylmethylbenzene 11 39

n-propylbenzene 18 32

3 -methylstyrene <10 18

Acrylonitrile 15 <10

Cresol^ 48 - Phenol*^ 33 - PhenyIcyc lohexane 18 - Di-methylbenezene 14 - 3- Phenyl- 1-propene <10 -

aUgikral RA 10331, Ugine Kulman

bCycolac AM 25139, Borg-Warner

cValues are yg of product evolved per g of material pyrolyzed.

^Oxygen- containing products.

38
Primary

Toxicants

from

Experimental

ABS

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—

h

o •-* —

m o

+ I +I + I+I ! ! +1 + 1 O' (VI (v| o rv

O (VI

to I h n O' m oo in o rv n

O I (vi (vi in n n in o I

0) <

io in oo oo (vj^rs^H^NHn

+ I+I + I+I + I + I + I+I NNiooioinioin 'O-H(V|vOf>»^00(V|

0) X)o u ^ U* U- b«ZU<Z u- til In Uh bZ^ZhZbZ

(VIE

-*

in

(V|

U O U U U 0 0 0 0 0 O O O O O

O O O in o rv oo oo

uoo oooorvooo OUCJUOUOO

o o m o in o m m o N n i o (vi m m rv. m <? o m

ON

so

C 0) O Wj •H 0) u JZ

(A CL 3 W

-Q O

E E

o u u <

u

(G

(VI z om •• •• u u o *H •h m (« «

w

3

aJua

Cl <

U 00 c e

(0 *H -o Cfl (« a) Ui x

co

4J 0)

(0 JO 3 3

jO 4J SO

u

0

a

CL (0 3 C U u

3

0)uc

QJU

Q) VM

a) OZ

«r jo u

39

nambers

respond

to

the

label

atory

code

of

those

laboratories

participating

in

the

interlaboratory
Table

00 00

a. a. Ov OV

see

00 00 00 see E E a a a a 6 S a a a a

m o m m

X

"e "e "b s s

a. cu

O- CL

0) IS

in

CQ

0)CL £Sou

V)co a x>

•H Li U TTJ § uc O Li U T3 < >\

x:

00 00 a a.

in vo

inCM

cm oo

ess

00 00 00 EES

me e a a a a

oo

m

cn0)>» jz

0) T3

O

OO

m o m n n n o o o m m m

4J x: w a a vi xa o E E O 4J U <U

to

m S3

T3C

<0

0) T3

>> x:

0) *3

4J (0 •H rg c e c 3 E o o o H (0 H 0) •H 0) O T3

L> X3

U 0) 4J 0) T3 •H

l/>

a

M X) v) xa >s

a

a 4J

a

aaa

X • *0 Xa XI X» 4J 0) c e a e 01 T3 •H a o o o c 0) •H U U a 0) (0 H e

LiN o aJ c L< 00

4J 0)

OM

in CQ < O

*-« CM 1 1 <0 xa

a T3

40
Table 5

Thermal Oxidative Degradation Products of Two Types of ABS [19]

Degradation Product ABS -

1

a ABSStyrene 2300° 7800

2 - Pheny 1-2

- propano

1

< 10 700

Acetophenone 35 450

Iso-propylbenzene 35 190

Benzaldehyde 43 130

a -methylstyrene < 10 120

4-vinyl-l- cyclohexene 10 82

Ethylbenzene 20 56

Acrolein 15 50

Ethymethylbenzene 14 38

Ethanal 11 38

n-propylbenzene 18 35

B-methylstyrene < 10 17

Acrylonitrile 19 < 10

Cresol 37 - Phenol 25 - Phenylcyclohexane 16 - Di-methylbenzene 12 -

a Ugikral RA 10331, Ugine Kulman

b Cycolac AM 25139, Borg-Warner

c Values are yig of product per g of material pyrolyzed.

41
ABS

Toxicity

Data -

NBS

Toxicity

Test

Method

[13,28]

co o i • in o • CO o

CM 0cQ2 Co

*H

cd

cd>

0)>»ou

cdMO

JO

cd +c

*H6o

O'

vO

CM

CO I • ON

ON • ^ CO

CO o co

00COA

VO 00

CO

CM

oo r*. • CM O I CM ONCO CM • CM

ON I h r*

«d cm

NO •

in

in -d

<D JZu

CM CM CM I NO

CMI ON 0 • cm in 1

NO oo • H m • •H CM

CO

CO

O r-i • I on r>. ^d o • • co «d

00 CM • CM O I CM O'

pH• CM

CM I CM r-4

4J

VJ

Cda.uo

cdo

cd

0) T5Oo

cduo

ja

cd

•o

CDWd

0)a

a

cd

tx,

a)CM

NO • • m O pH

OO 00 • I in ooCM

CO I cm mi o o • • o r* cmo

in

a) T?

*oco

a*

<00)M

*o

01 V

CxJ

•o (D nm 00

X

42

952

confidence

limits.
ABS

Toxicity

Data

-

NBS

Toxicity

Test

Method

-

Carbon

monoxide,

COHb

and

HCN

[13]

43
z a u O, a ex

00c

•HIcoz

ro

/—

N o o o O a o o o o O 04 o O' < u cu m m < m V-/ A

/-s o o*

m

m o ir>^

• • • • O dO H e'- P O'

h-3 S CN en < CN A

00p

cd H

T3OPp

<3J zP

in

0) H

C/5 P

in

Cfl t—I

003oQ

X)Cm

C/5 3pXoH

0)>

•HP

03 rH

a) a

cn

CO

r—I

003oo

00c

00c

•HIcoz

C/5

00c Z 6 a a a as o a a a o oo p 6 z 6 u a, a a.a o o. u o. O 00 a a Pz a o a a o. p a o CX o a.

>>oop

(0MOP

,3 oo oo

cs

O' ooPcn

in

cnom

<r oo <n cn i oP Oo

<T

cn

O'

cnop

(\J /-N O O? <r

p 00

H • • • • O dO r*- in o (N p a r-H r-H CN CN m op o

cn

0) PpMOop

w

0) p3e

•HaomOP

0) ppp

cfl

Q)P3MO o o o o a

cn in CN o X

cn 00 -tf r- a) A A • a) P p O 3

•H

C o o o un •rt • • • • 0) a

CN 00 cn CN ex CN cn cn cn o A A 0) m h3 a) w P O p O O O ex

cn 00 i P X

a

p ?—

H

H 0) op

a) p P 3 a) o o o o C p o o o o •p4 cO O' in in 00 a H H r~H r—H 3

tOOo

CJ

0)00

(0M

(1) < 3P

44

NBS

large
Table 9

Toxicity Data - University of Michigan Test Method

LA 50 Values3

Material Static Dynamic Reference

ABS 18 1.7 30

22 1.8 31

33 2.2 32

ABS-FRb 20 2.2 30

21 2.3 32

Red Oak 9 3.6 32

Polypropylene 28 0.9 32

3 Amount (grams) of material consumed necessary to cause the death of

50% of the exposed animals.

b Fire-retarded treated sample.

45
Table 10

ABS Toxicity Data - DIN 53 436 Method [36]

Sample

Temp

(°c)

Mortality

(# dead/// tested)

CO

(ppm)

COHb

(%)

HCN

(ppm)

ABS solid 350 0/20 150 5.8 100

400 13/20 350 14.2 150

ABS foam 350 0/20 100 6.2 20

400 2/20 100 7.3 100

46
ABS

Mortality

and

Toxicity

Data -

DIN

53

436

Method

[35] o /-» x c

a) -h y s c • *h > O S'? Wo

JOXIwoOG

to

a) s

'V

0)

to >. o p a.

•H

x

rH Q) to P %PO -d

as «fl 0) T3X 10 wMo a> x to 00 to

1-4a) <4-1 » o

to0) 00

f—I '—

a1 p

cn ? u p

a> to X) a) 6 PU o

cs

O'o VO

00

X c

0) •H •d

d •d s o o o c • m in -o- •H 0 O' in O'

C4 cs O' r-H o a vO in

vO

IT) o

00 -O’ 04

O'04

00

-o- o

O' oO'

'd

a>

x:o

•H

x: oo oo oo m in oo oo

vO oo00

a) X!P

00G

•rl a) g -C | p W 00e

*d •H C p

to

G

X)

r-HtO •d > a) p p

a) tO P P c a) •H Xl

•H

0) rH Pd P c c

•rH to 0 u

•H x: X o o

top

a) 4H p o

tO

p

tO

C P 3 C o 1 8 P rH d tO 10 P

tO

O

0) P Q 0

0)

X

x:

p

p

4-1 S o oP <D 4-1 P

•q S

a) *h p p

to to

to rH 0)

r-H

d • (H o c x: Q rH (0 p

•P tO to G O (0 0)

to -d *d

a) -H

a)p > 4H

to tO o O o p

x: t0 CL, P p a) e

T) o to a)

(U 4H •h a) 0

00

O -d o o

|H

C iH 0

to (0 •H T3 • x: rH c "d a) o to d -H o JC > o •iH p

a) (0u a) P

r-H rH £ a)

p

CL -d

H

a <0 0 x> c

to

w to a)

X

to o • p a) o O tn d •d 4H u a) to G O c d o •H

to a) rH CL P a) -C tO X o 5 3C H > a) u

47
Table

12

O E u aa

m

r>. on

CM

ino

^d- CM

CM

in

*0

a>wo

>» P P X

•h a) qj JD Sfc

(o e^ P 3 TJ p z OS O 0) a: tj

j=

0) P E to •H (1) H Q + 1 +1 CM

00

00

oo00 o

+1m

in o

CM+ 1

vOH

vO

00

00

O' CO o m

-d-

—i + 1 +1 o+ 1 Q

cn+1wc

(0

(0 Q

a

a) to E -«

*H rH H 0UC

-t4B

tn o c p o

*H

a) to Q rH S 5coo o « p cr

•P

QJ P S 0) •H 0( H c*

(0 p

C/3 + 1 o

+1

%-

(M r-«

r**

w o cm

r^. +i o

+1

H o o H o o

-hi -hi -hi -hi -hi •hi -hi CO ON ON CO o CM V© m CO CO ON in

in 00 CO CM in

H

H

^»s CM CM -d- W w

<r CO ON

H

-d- 00 O'

W

NO CM CMH

-hi -hi 1 1 -hi i • H

00 o NO

^d- in

NO >o *dTJ

(1) W3

a)M

a)3

(AC

<0

a)0

0) -Cps5u

0)a.x

0)

(0 (0 p c c o

<U -P Si! P XI

0)

C

P- o r co O -P p p

to

a)p 0 i* •H U H <0a

(0c 5 .H P O 6

X)nO

<r+ 1

CM

v-/ o

CM+ 1

to 1 3 § H w| a

TJ

O

OO 00 >o +1 <T

O+ 1

TJ TJ O O o o

vO NO

--I oo

-H o

-hi

<0

a) si

TJ

aia

CDPa

<DPW

a)

a

c/3

-hi

V) za

TJ TJ O O o o

00 00

48

Fixed

heating

mode.
Time

to

Death

Dependency

on

Sample

Size

-

USF

Test

Method

[39]

XXh-HvOini/IH-^OO O' CO CM VO <—

i

N 00 00 n CM o < o o rH o rH vO rH

w- •Ha

rH <T o o r-H o o o rH o o rH O o

oH + I + I + I + I-H + I + I + I +1+1+1 +1+1+1

0) XX VO CM CM rH 00 00 00 vO rH 00 t". o m

a P vO m O <r CM m 00 O' in in CM r-H rH vO

•H (0 H 03 vO 00 o O' in o o O' O' CM CM m CM

T) CM rH H CM CM r-H

T> CO vO <r -y CM y C-l rH 00 O' CM

03 O —1 vO m o in rH CO O' y y

N o <r rH m r>. *H rH cn H <r vO CM in

a) >> in oo r» o 00 o O' O' O' in O' vO

r-H r-H O O' 00 rH O' o 00 O' O' O' O' r>* O'

a. o

CO P

>V 04 o <T o o CM y o rH y o •H y

01

ss

(0 p

3

XX

60 T3 m cn o y o rH CM H m y <3- rH o

•H 03 o 00 O' s

00 r>. vO rH in CM y 00 US

03 00 o CM m rH o CM CM o CO CM O' *H y

3 P in o o o o o o o o o o O' o o «k nS o o o o rH o o o o o o O' o o • X o o rH CM in o rH CM m rH CM m o CM m o

Ip

to p

o C

p

0)a

as •H

JO p

z

0)a

X

w

(S'Or-IHnNrHH *y '—l •—

t

(M CM CM

WP

(1) a

a

0

US

1p

COo

o

o-y<

o

x:

3

O

-3

p

o

a)

>43

p "O "O

cfl a) ai •o t

3

P

03O 1 1

03X

•H

0)X

•H 1H

p p P P

a) aJ o

rH *H CM rH CM i

1 CO

rO

l CO

rO

1 COrn

1 CO

CO 3 § 5 %

49

standard

deviation
Table 14

Relative Toxicity of ABS Compared to Various Woods [41]

Sample/material13

Time to

death

(min)

CO

(ppm)

Cone »time'

(ppm* min)

ABS 18.52 6,700 31,020

aspen poplar 14.06 15,000 52,720

beech 13.82 11,400 39,390

yellow birch 15.09 12,000 45,270

red oak 14.50 10,200 36,980

western red cedar . 14.91 9,100 33,920

Douglas fir 14.76 9,100 33,580

western hemlock 14.37 13,500 48,500

eastern white pine 15.42 10,300 39,710

southern yellow pine 15.56 9,200 35,790

a Concentration-time products (ppm*min) for CO.

b Samples were pyrolyzed with a ramped furnace temperature at

40°C/min to a maximum of 800°C with no forced air flow

through the system.

50
CHEMICAL

STRUCTURES

OF

ABS

MONOMERS CDc

CDM

“O2D

CQ

I-O" I

II 1-0I O - I

II I-O- I oo

in

ii $E Ii I-O

_a> z CO M

LOH

III o

00 c O in o>o i O - I

ii$ < II E H i 0 - 1

51

(m.w. =

104.14)
Figure

2.

N

1

x-°-0

1 1

1

1 1

x-o-x

i x-o-x

I X-O

II

o-x

1 J

1 1 x-o-x

I 2

x-o-o

I x-o-x

I I I

52
Figure 3.

Relative Toxicity of ABS - Pitt Method [33]

CONCENTRATION - RESPONSE

0.)

MUCH MORE

TOXIC THAN

j WOOD

1.0

MORE TOXIC

THAN WOOD

10.0

AS TOXIC

AS WOOD

100.0 10000

Each point represents the amount of materia] (gram on the X axis) *hich produced

sufficient smoke to kil] 50r? of the animaJs <LC50i and the time (minutes on the Y ax:s> required to

kill 509c of the animals (LT50) using that amount of material. Reading the graph %er*jca~\ each materia] is classified in terms of potency while each material is classified m terms of onset of action b>

reading horizontally. To combine both, parallel quadrants separate ciass A. B. C. and D

Reproduced with the permission of the authors.

Copyright 1981 Academic Press, Inc.

53
NBS-114A (rev. 2 -ec) U.s. DEPT. OF COMM. BIBLIOGRAPHIC DATA

SHEET (See instructions)

1. PUBLICATION OR

REPORT NO. NBSIR ^85/3248

2. Performing Organ. Report No 3. Publication Date

December 1985

4.

TITLE AND SUBTITLE

Acrylonitrile-Butadiene-Styrene Copolymers (ABS) : Pyrolysis and Combustion

Products and Their Toxicity - A Review of the Literature

5. AUTHOR(S)

Joseph V. Rutkowski and Barbara C. Levin

6. PERFORMING ORGANIZATION (If joint or other than NBS, see in struction s) 7 . Contract/Grant No. NATIONAL bureau of standards

DEPARTMENT OF COMMERCE 8 . Type of Report & Period Covered

WASHINGTON, D.C. 20234

9. SPONSORING ORGANIZATION NAME AND COMPLETE ADDRESS (Street. City. State. ZIP)

Consumer Product Safety Commission

Bethesda, MD 20207

10.

SUPPLEMENTARY NOTES

Document describes a computer program; SF-185, FIPS Software Summary, is attached.

11. ABSTRACT (A 200-word or less factual summary of most significant information. If document includes a significant

bibliography or literature survey, mention it here) A review of the literature was undertaken to ascertain the current knowledge of

the nature of the thermal decomposition products generated from ABS and the

toxicity of these evolved products in toto . The literature review encompasses

English language publications available through June 1984. This literature

surveyed showed that the principal ABS thermooxidative degradation products of

toxicologic importance are carbon monoxide and hydrogen cyanide. The

experimental generation of these and other volatile products is principally

dependent upon the combustion conditions and the formulation of the plastic.

The toxicity of ABS thermal degradation products has been evaluated by five

methods. The LC^ (30 min. exposure + 14 day post exposure period) values for

flaming combustion ranged from 15.0 mg/ 2. to 28.5 mg/2,. In the non-flaming mode

of combustion, the LC,-q values ranged from 19.3 mg/ 2, to 64.0 mg/ 2,. Therefore,

no apparent toxicological difference exists between the flaming mode and the

non-flaming mode. The toxicity of ABS degradation products was found to be

comparable to the toxicity of the thermal decomposition products of other common polymeric materials.

12.

KEY WORDS (Six to twelve entries; alphabetical order; capitalize only proper names; and separate key words by semicolons)

ABS plastics; carbon monoxide; combustion products;

literature reviews; thermal decomposition; toxicity.

13. AVAILABILITY

hydrogen cyanide;

14. NO. OF

PRINTED PAGES

325 Unlimited

| | For Official Distribution. Do Not Release to NTIS 59

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