NATL INST OF STAND & TECH

A111Q7 BTODDfl

NBSIR 83-2690

Priority Toxic Pollutants in Human

Urine: Their Occurrence and

Analysis

U.S. DEPARTMENT OF COMMERCE

National Bureau of Standards

National Measurement Laboratory

Center for Analytical Chemistry

Washington, DC 20234

April 1983

Final Report

Issued June 1 983

Prepared for Environmental Monitoring Systems Laboratory

U.S, Environmental Protection Agency

Las Vegas, NV 89114

NBSIR 83-2690

ft* PRIORITY TOXIC POLLUTANTS IN HUMAN

URINE: THEIR OCCURRENCE AND

ANALYSIS

NATIONAL BUREAU

OF ETANDAilOS

U8RARY

JUL 5 1983

r -rV as-<^

Oc

Alexander J. Fatiadi

U.S. DEPARTMENT OF COMMERCE

National Bureau of Standards

National Measurement Laboratory

Center for Analytical Chemistry

Washington, DC 20234

April 1983

Final Report

Issued June 1 983

Prepared for Environmental Monitoring Systems Laboratory

U.S. Environmental Protection Agency

Las Vegas, NV 89114

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

NATIONAL BUREAU OF STANDARDS. Ernest Ambler. Director
If

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1
I. INTRODUCTION

Table of Contents

Page

1

A. Handling of Samples of Human Urine 2

II. PENTACHLOROPHENOL IN HUMAN URINE (OCCURRENCE AND DETERMINATION) 2

A. General 2

B. Methods for the Analysis of PCP 3

C. Additional Analytical Methods for PCP 6

III. MONO-, DI-, TRI-, AND TETRA-CHLOROPHENOL IN HUMAN URINE 8

A. General 8

B. Analytical Methodology 10

C. Recent Methodology 12

IV. PHENOL, £_-CRES0L, CATECHOL, AND RELATED HYDROXYAROMATICS IN HUMAN URINE . 14

A. Phenol (General) . 14

B. Analysis of Phenol in Human Urine 15

C. Cresol , Catechol, Hydroquinone, and Other Benzenediols

(Polyhydric Phenols) . 18

V. 2.-NITR0PHEN0L IN HUMAN URINE 20

A. £-Nitrophenol , a Metabolite of the Pesticide Parathion 20

B. Analysis of £-Nitrophenol in Human Urine ...... . ... 22

C. Recent Methodology ...... 23

VI. HERBICIDES (2,4-D, 2,4, 5-T, SIVEX, DICAMBA, AND OTHERS) 24

A. Introduction 24

B. Toxicity of Pesticides 25

C. Toxic Substances in Human Urine 26

D. Pharmacology and Metabolism of Si 1 vex, Dicamba, and Related

Pesticides 28

E. Trace Analyses of Pesticides: 2,4-D, 2, 4, 5-T, Silvex, Dicamba, and

Others (General Overview) 28

F. Additional Recent Results on Analysis of Pesticides 30

VII. PHTHALATE ESTERS (PLASTICIZERS) IN HUMAN URINE 31

A. General 31

B. Toxicity of Phthalate Esters 32

C. Metabolism of Phthalate Esters 33

D. Determination of Plasticizers in Human Urine 34

References 37
List of Figures

Figure No. Page

1 Chromatography of chlorinated phenol standards (250 ng each)

on LiChrosorbidiol column. UV detector at 210 nm 13

List of Tables

Table No. Page

1 Comparison of PCP Levels Found in Human Urine Samples by

Different Methods 4

2 PCP Content of Urine of Non-exposed Persons 4

3 Levels of Pentachlorophenol (PCP) (Conjugated and Nonconjugated)

in Hydrolyzed, Test and Control Urine Samples 5

4 Comparison of Chlorophenol Levels Found in Human Urine by EC/LC

and EC/GC 7

5 Possible Origins of Various Chlorinated Phenols .’ 9

6 Accuracy, Precision, and Detection Limits for the Determination

of Chlorophenols in Human Urine 10

7 Chlorophenols in Human Urine Samples (Results in ppm) 11

8 Common, Mean Values for Toluene in Blood and Urinary

Metabolites from Exposure Experiments 19

9 Summary of Pesticides and Their Metabolites Detection in 267

Human Urine Samples 21

10 List of Chemicals Detectable in Human Urine, and Their

Pesticide Origin 26

11 Occurrence of Pesticide-related, Phenolic Residues in

Human Urine 27

12 Occurrence of Di alkyl Phosphate Residues in Human Urine . . . . 27

13 Urinary Excretion of DEHP 32

14 Detection Limits for Phthalate Esters 35
Priority Toxic Pollutants in Human Urine:

Their Occurrence and Analysis

Alexander J. Fatiadi

Center for Analytical Chemistry

National Bureau of Standards

Washington, DC 20234

This survey reviews and discusses the occurrence of priority

pesticides and industrial chemicals in human urine. An overview of some recent analytical methodology for determination of selected toxic

pollutants and their metabolites as they are found in human urine is

also presented. The review includes 427 references.

Key words: chemicals; exposure; human; industrial; methodology;

pollutants; survey; toxic; urine.

I. INTRODUCTION

The many benefits of our modern developing, industrial society are accompanied by certain existing and new, man-made environmental hazards. These

can arise from air pollution, non-ionizing radiation, environmental carcinogenesis, and also from toxic pesticides, the effects of their metabolites, as well as other chemical pollutants. Next to analysis of toxic substances in

human blood, plasma, or tissue (1), monitoring of human urine for toxic

Dollutants is of paramount importance. Human urine is a complex mixture con- taining hundreds of organic (and many inorganic) compounds (1), and its

composition is constantly changing due to changes in diets as well as human

environmental exposure. Consequently, addition of one or two new organic

compounds (or their metabolites) each year to the array of chemicals known to be

present in human urine is not surprising.

The aim of this survey is to assess human exposure to certain pesticides

and industrial chemicals, and particularly to discuss the occurrence of such

substances in human urine; an overview of some recent methodology for determination of selected toxic pollutants and their metabolites as they are found in

human urine is also presented. The priority toxic substances in human urine

that are discussed in this survey are: phenol, chlorinated phenols ( e.g .

,

mono-, di-, tri-, and penta-chlorophenol ) , £-nitrophenol , and hydroxybenzene

derivatives ( e.g . , cresol and catechol); also, the herbicides 2,4-D, 2,4,5-T,

Si 1 vex, and Dicamba; and certain phthalates, e.g. , bis (2-ethyl hexyl ) phthalate,

diethyl phthalate, and others. The literature cited covers, approximately, the

period of the past ten years, with emphasis on the most recent references

(1975 - mid 1982).

1
A. Handling of Samples of Human Urine

According to Dr. Robert Purcell, Chief of the Hepatitis Section at the

National Institutes of Health (2), urine samples are generally handled in his

laboratory with the same precautions as are used for other human samples. He

has indicated that transmission of hepatitis A is very unlikely, and is very

uncommon in the United States, also that hepatitis B is not transmitted by

urine. His studies, involving the inoculation of primates with urine from

hepatitis A carriers, did not reveal transmission of the virus. Normal safety

precautions are observed in handling these samples, to avoid hand-to-mouth

contact in the laboratory. Eating, drinking, or smoking are not allowed.

Pipetting by mouth is not allowed; work areas and instruments are cleaned and

disinfected after use. Working in a biohazard hood is not required, but such

hoods should be used if available.

II. PENTACHLOROPHENOL IN HUMAN URINE (OCCURRENCE AND DETERMINATION)

A. General

Pentachlorophenol (PCP) and its water-soluble sodium salt, sodium pentachlorophenoxide (Na-PCP) are used as biocides. Although they are mainly

employed for preservation and treatment of wood, their antimicrobial, antifungal, herbicidal , insecticidal, and moll uscicidal properties have led to

widespread application of PCP formulations. The literature up to 1967 on the

chemistry, toxicology, and environmental residues of PCP has been reviewed by

Bevenue and Beckman (3) and by Bevenue et al

.

(4-6).

A recent discussion on the uses, exposure, toxicology, pharmacology, and

environmental impact of PCP can be found in a review by Detrick (7), by Kunde

and Bohme (8), by Ahlborg (9), and in a comprehensive book by Rao (10), in a chapter by Dougherty (11), and in a recent Russian book by Fudel '-Osipova £t

al . (12). The analysis of PCP has been reviewed by Firestone (13), by Dahms

and Metzner (14), by Taylor (15), by Thompson (16), by Edgerton et al . (17),

by takings ^

(18), and in a recent methodology book by Eben~Tl^.

The environmental effect and the human-health risks resulting from the use of PCP as a wood preservative and pesticide have recently been discussed and

reviewed (20-23).

The estimated annual production of PCP is 90 x 10^ kg world-wide (24);

the majority of the material is used as a wood preservative by the lumber

industry, and as a fungicide and a bactericide. Commercial preparations of PCP

may be contaminated with extremely toxic, chlorinated dibenzo-£-dioxins (7,

25-27).

Potential sources of PCP in human urine can be paper products, beverages

and foods; also city water, beef, grain products, and produce (10,28-31) (as a residue from the application of herbicide). PCP in urine can also be a metabolite of such fungicides as hexachlorobenzene (32-34) or hexachlorocyclohexane (35). PCP has been shown (9,36) to be metabolized in mammals to

tetrachloro-£-hydroquinone. Evidence has also been presented that both PCP and

tetrachloro-£-hydroquinone in urine exist as conjugates with Q-glucuronide or as

a sulfate adduct (18).

2
PCP, although moderate in toxicity [8), can he hazardous, as demonstrated

by cases in which death resulted from intense exposure C10J1»37); several

studies have been conducted relative to dermal and gastric toxicity (38) or toxicity by inhalation C39). PCP is reportedly (40,41) mutagenic. However, in

their comprehensive review on the environmental effects of pollutants, Kozak ^

al . (42) dispute the alleged mutagenic and tumorigenic properties of 2-chloro-

]^enol , 2,4-dichlorophenol , 2,4,5-trichlorophenol , 2 ,4,6-trichlorophenol

,

tetrachlorophenol , and PCP; although some chlorophenol s may be embryotoxic. In

recent reviews (42,43) it is also pointed out that PCP is the most toxic of the

chlorophenol series, but that chronic toxicity of chlorophenol s to humans has

never been documented. From these phenols, however, 2-chlorophenol , 2,4-dichloro

phenol, 2,4,5-trichloropheno'' , and 2 ,4,6-trichlorophenol have been shown to be

carcinogenic in test animals (42-44).

The average, urinary concentration of PCP in non-occupational ly exposed

individuals is about 20 ug/L (5-7,18,30) or 6-23 ug/L (45); for individuals who

live in PCP-treated rooms, the range is 30-150 yg/L (45). The urine of exposed,

industrial workers may contain 1.20 - 2.40 mg of PCP/L (14,45); compare, however, additional data (15,18,46), and see also data in Table 1.

It has been reported that PCP (and phenol) in urine can be stabilized and

preserved by storage (47) at 4®C or by being frozen (83). It has been

reported (48) that urine samples (10-15 ml) can be preserved for up to 15 days

when treated with a few drops of saturated, 8-quinolinol sulfate solution.

Phenol, perhydrol , or formalin are less effective preservatives. The occurrence

of PCP (free or conjugated) (10,18,49,50) in human urine, or of PCP levels found

in human urine samples by the EPA Analytical Manual Method (15-17) are well

documented. The carbon-13 NMR chemical shifts for pentachlorophenol and pentachloroanisol e have been reported (50b).

B. Methods for the Analysis of PCP

Several methods for the determination of PCP in urine have been reported in

the literature (13-18). Bevenue ^

(5,6) and Rivers (51) acidified urine,

extracted with an organic solvent, and methylated the urine extract with diazomethane prior to electron-capture gas chromatography (EC-GC). Cranmer and

Freal (52) partitioned possible interfering compounds into a base prior to

acidification, and extracted PCP into an organic solvent. The urine extract was methylated with diazomethane, and analyzed by EC-GC. Shafik ^ (53)

determined PCP and other halo- and nitro-phenols in urine by acid reflux,

extraction with ethyl ether, derivatization with diazoethane, and separation on

a column of silica gel prior to EC-GC analysis.

On the average, 75 percent of the PCP in urine is conjugated; if the

conjugate is the Q-glucuronide or sulfate adduct (which are the most likely

adducts for PCP)

, "hydrolysis to the free compound can be accomplished by

enzymatic (aryl sulfatase, g-D-glucuronidase) or acid hydrolysis. The analysis

of a hydrolyzed urine provides a measure of the conjugated and unconjugated

levels of a compound (18).

3
Recently, Edgerton and Moseman (54), Edgerton ^

aj_. 07,55,56) and

Zimmerli ^

(45) found that, prior to derlvatlzation , hydrolysis of a urine sample at lOQ °C for 1 hr In a Teflon-lined screw-capped sealed vial,

gave a much higher level for Biologically incorporated PCP (free and conjugated)

than when methods not employing hydrolysis were used. After hydrolysis and

extraction, the sample was treated with diazomethane, to produce the methyl

ether of PCP, prior to analysis by EC-GC. An acid alumina column as a clean-up

system was developed [54,56) to remove interference from the sample extracts,

thus allowing detectability of 1 yg/L of PCP (55).

The hydrolysis procedure [45,54) thus permits a highly selective and more

quantitative method for the determination of PCP in urine, as may be seen from

a comparison of alternative methods, summarized in Tables 1--3.

Table 1: Comparison of PCP Levels Found in Human Urine Samples by

Different Methods (54)

PCP found (ppm)^ method

EPA manual Reported Hydrolysi

s

Sample method (17) methods (51 ,52) method (54)

general population <Q.01 <0.01 0.02

general population 0.02 0.02 0.08

general population 0.01 <0.01 0.04

general population <0.01 <0.01 0.02

exposed worker 0.54 0.21 3.68°

exposed worker 0.41 0.31 1 .71

^Average of three determinations.

“The method presented in this paper yields as much as a 17--fold higher PCP

level after hydrolysis than do the other methods used for compari son

.

Table 2: PCP Content of Urine of Non-exposed Persons (45)

PCP Content (yg/L)

Urine sample Hydrolyzed urine Non- hydrolyzed urine

(general population)

1 18.8^ 5.8

2 23.0 6.7

3 11.1 2.3

4 14.3 3.7

5 15.3 5.1

6 19.6 6.1

7 11.4 4.8

^PCP level was 3 to 4-fold higher after hydrolysis.

4
Table

3:

Levels

of

Pentachlorophenol

(PCP)

(Conjugated

and

Nonconjugated)

in

Hydrolyzed,

Test

and

Control

Urine

Samples

(18) oO 0) M N

M- -O 1— 0 0)0 N &- o >>-o

•I- I— >1 +J O -C

<a i~ I a; T3 c

>> o

3= z;

Q.

CL

U

CU

CL| O

&-oo

ns Mc

OJ O-

•o

(UM

>>

OJ

s-3

T3

(UN

>> "o

s- T3

>>

•MC +J 3 Q. o <u sc_) O 0) c JZ s O 4-> 3

CO r—

C

•r- rtj O O)

r^coocvj ooiincT)

r— r^CVJCJ r^r—

CO

CVJ Lf) CO

O cd- lo

00 CO CVJ in r— CVJ

CVJn CVJ

in 00 CO

00 o CO 00 I—

m 00 oo «:a- • • • • in CO 00 cn in r— I— V

<U 0) 0)

to CO to (0(0(0 0)000 </> (O I— r~ r— O (O (O (O

•r— *1— *r-

+-•

OO

O

bO 01 O) O)

OJ O. a. Q.

+J V) CO to o o o o

S- S- S- S- +J +J +-> +J c c c c O O O O JO O O I- I I I I I I I

«a: cc <c < cvi CO cn o

CVTO

O r- ^ CVJ CVJ CVJ

CO CO CO CO

«0- 00 'd- CVJ O !— O CVJ I— r— CVJ CVJ

cn

0)coOJN

>>o

s- •o

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&-oo

(O +Jc

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0) cc

>>

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>>

— S0) OJ ^ > > o. 0)0 0. _i o«^ 0) i-

-o I— 0J(O

OJ .a >•1- 0. OJ CO. Q.

_J to

OJ

ns tn I m CO » CD 00 I in ^ I C71 oo

COin CVJ CVJ 00m

r*. CO CVJ 00 00 I o o ) 00 CO I o o I CO 00

T3

JtC .S<C OJ c c c c c

ns (O ns ns ns T-

.a JO jQ o: .a to

OJ OJ OJ OJ OJ OJ C C 3 C C 3

•r- T- T- -r— C- S- S- S- C- SCT) 3

ci” o

Q.O

Q-

>»

JO

Q.

Q.

ns 3O

to3

O.O

Q.

ns

iOJ3

OJOS

0)o

s.

-o

OJ MO

OJou

to

OJ

nsto O

00

tno

+jo00 > «4-

•^ o

to3

OJto

CT) 33O

OJCL

CO M

Sns

CO.

to

ns3

ns

OJ3O

•o

OJto

ns JO

to +J

(O T3

>>

Sto3

II -I—

OJ

i- CL

JO 5

via

the

Health

and

Nutrition

Examination

Survey

II

(HANES

II);

81%

of

the

urines

showed a

positive

PCP

response,

with

11.6%

having a

trace

level;

the

highest

value

was

2,670

ppb

and

the

geometric

mean

was

<5.
In another, recent procedure (56), chlorinated phenols in urine are isolated by sorption onto a small column of the macroreticul ar resin, XAD-2,

followed by elution (2-propanol --hexane) , concentration, and detection by

EC-GC. Results for the human, general -popul ation samples show low-ppb

levels of PCP and certain di-, tri-, and tetra-chlorophenol s . Gas

chromatography (GC) and electron capture (EC) detection (57) have been extensively used for the analysis of chlorophenol s in human urine (14,53,58,59).

Recently, a new reference method has been described (59) for confirmation

of the presence of chlorophenols in human urine. A hydrolyzed urine sample is

analyzed by both gas chromatography (GC) with electron capture (EC) and liquid

chromatography (LC) with electrochemical detection (EC); the results compared

in Table 4. As shown (Table 4) (59) there is a general agreement between the

results obtained by two methods for pentachl orophenol , 2 ,4 ,5-trichlorophenol

,

and 2,4- or 2,5-dichlorophenol . The EC/GC analysis appears to give false

positives for 2,4- and 3 ,5-dichl orophenol while EC/LC gives false positives

for 2 ,3-dichlorophenol and 2,4,6-trichlorophenol . These data support the

complementary use of both EC/GC and EC/LC for identification and confirmation

of chlorophenols in human urine.

C. Additional Analytical Methods for PCP

Negative chemical -ionization (NCI) (60,61) mass spectrometry (analogous

to gas chromatography with an electron-capture detector) (52) is an effective

tool for detecting polyhalogenated orqanics ( e.g . , chlorophenols) and other

toxic compounds in urine (30,31,60-64); it shows high sensitivity (1--10 ng

is sufficient to produce a usable spectrum). The procedure generally requires

solvent extraction, hydrolysis of urinary conjugates, derivatization , and

chromatographic separation prior to NCI analysis. However, in many cases, the

NCI method offers the advantages of (a) direct analysis after evaporation,

which eliminates the need for derivatization, and (b) mass analysis, which

gives information that bears directly on the molecular weight of the residue.

In a recent, analytical procedure (65), PCP is extracted from urine by

acidifying the urine sample with citric acid, and then steam-distilling.

The distillate is treated with a pH 4.16 buffer, 4-ami noantipyrine, and

potassium hexacyanoferrate, and then extracted with xylene, and the xylene^

extract is measured spectrophotometrical ly at 570 nm. PCP could be determined

around the biological limit of 2 mg/L of urine by using the technique.

Additional analytical methods for PCP in human urine have been reported

for occupational (67-70) and household exposure (45).

6
Chlorophenols

^results

in

ppb)

7
III. MONO-, DI-, TRI-, AND TETRA-CHLORO PHENOL IN HUMAN URINE

A. General

Chi orophenol s constitute a group of pollutants commonly found in tPie

environment. TFiese compounds arise from degradation or metabolism of pesticides,

chlorination of the water supply, and direct introduction from industrial sources (9,10,42,71-75,81). The primary source of human exposure to chlorophenol s (except PCP] is likely to Be from the degradation of such chemically

related phenoxyal kanoic herbicides as 2,4-dichlorophenoxyacetic acid C2,4-D;

and 2,4,5-trichlorophenoxyacetic acid C2,4,5-T) C42) . Some of the chlorinated

phenols of environmental origin are listed in Table 5 (59), and a comparison of

their levels in human urine is given in Tables 6-7.

In addition to PCP (Section II), mono-, di-, tri-, and tetra-chlorophenol

s

may appear in the urine of humans as a result of direct exposure to environmental sources or to pesticides or other compounds that metabol ically give rise

to chlorinated phenols. Engst ^ al . (76) identified 2,3,4, 6- and 2, 3,5,6-

tetrachlorophenol , 2,4,6- and 2,3,7^trichlorophenol , and pentachlorobenzene as urinary metabolites from the fungicide hexachlorobenzene (HCB), and Angerer

et (77) and Koransky ^

(78) found 2 ,4-dichl orophenol , 2,4,5- and

2,4,6-trichlorophenol , and 2,3,4,5-tetrachlorophenol as urinary metabolities

from a-hexachlorocyclohexane.

Renner and Schuster (79) reported 2,4,5-trichlorophenol as a new urinary

metabolite of HCB. A recent claim (80) that 4-chl orophenol in urine is a metabolite of cl of i brie acid proved to be incorrect. 4-Chl orophenol is an artifact produced from clofibric acid by proton-catalyzed hydrolysis or thermolysis in the analytical processing of urine (81). The urinary metabolite

of chlorobenzene in man has been identified as 4-chlorocatechol (82).

Recently, Edgerton (83) studied the storage stability of chlorinated

phenol s e.g. , 2,5-dichloro-, 2,4,5-trichloro-, 2 ,4,5,6-tetrachloro-, and

pentachlorophenol in urine. A decrease of 40 percent was noted in urine

fortified with known amounts of chlorophenol s, e.g. , 2,4,6-trichlorophenol, and

analyzed over a 36-day period with repeated freezing and thawing. A samplestorage technique was presented that allowed for the stability of chlorophenol

s

in urine for over 40 days with little or no decomposition noted. This technique

involved subdividing all ‘urine samples into 5-mL aliquots when first received,

and keeping them frozen until analysis, to avoid repeated, freezing-and-thawing

cycles. The study (83) demonstrated the importance of proper sampling and

storage of urine samples when quantitatively analyzing for chlorophenol s over

an extended period of time. The stability studies of other potentially

degradable compounds in urine, e.g

.

, parathion, anilines, and 2,4-D have been

described in the literature (84-86) . A recent stability study (87) of some environmental compounds such as phthalate esters or polychlorinated biphenyl

present in the seawater samples showed that between 2.2 percent and 49.9 percent

of organic solutes were lost from the spiked solutions during storage; the

loss of the analyte was ascribed to vaporization, degradation or adsorption to

the glass container walls.

8
Table 5: Possllile Origins of Various CFilorlnated Phenols (59)

Meta hoi Ite Origin Type of Pesticide

2-Chlorophenol 2,4-D Herbicide

3-Chlorophenol POP Fungicide

4-Chlorophenol Chloroxuron Herbicide

2 ,6-Dlchlorophenol Lindane Insecticide

2,4-Dichlorophenol VC-13 Insecticide

m-Di chlorobenzene Fumigant

2,4-D Herbicide

2,3-Dichlorophenol Lindane Insecticide

o-Dichlorobenzene Fumigant

2,5-Dichlorophenol Lindane Insecticide

p-Dlchl orobenzene

2.4,5-T Herbicide

3,4-Dlchlorophenol PCP Fungicide

o-Dichlorobenzene Fumigant

Diuron Herbicide

3,5-Dichlorophenol Lindane Insecticide

PCP Fungicide

2,3,4-Trichlorophenol Lindane Insecticide

2,3,5-Trichlorophenol Lindane Insecticide

PCP Fungicide

2,3,6-Trichlorophenol Lindane Insecticide

2 ,4,5-Trichlorophenol Ronnel Insecticide

Tetrachlorvlnphos Insecticide

Erbon Herbicide

2,4, 5-T Herbicide

HCB Fungicide

2,4,6-Trlchlorophenol Lindane Insecticide

3 ,4 , 5-Tr ichl orophenol Lindane Insecticide

2,3,5,6-Tetrachlorophenol HCB Fungicide

PCP

2,3,4,6-Tetrachlorophenol PCP (Impurity) Fungicide

Lindane Insecticide

2,3,4,5-Tetrachlorophenol PCP Fungicide

Lindane Insecticide

HCB Fungicide

Pentachlorophenol PCP Fungicide

Lindane Insecticide

HCB Fungicide

PCNB Fungicide

9
Table 6: Accuracy, Precision, and Detection Limits for the Determination

of Chlorophenol s in Human Urine (77)

Chlorophenol Nominal

val ue Actual

Mean

value

Relative

standard

deviation

Average

recovery

Detection

1 imit

ug/L ug/L % % ug/L

2 ,6-dichlorophenol 174 151 10.1 87 10.0

2,4-dichlorophenol 194 203 8.3 105 8.3

2 ,3-dichlorophenol 220 231 9.4 105 16.8

3,4-dichlorophenol 151 139 10.1 92 18.6

2 ,4 ,6- trie hi orophenol 73 70 7.5 96 8.5

2 , 4, 5-trichl orophenol 58 58 5.1 100 14.8

3 ,4, 5-trichl orophenol 66 78 7.7 119 11.0

2,3,4,6-tetrachlorophenol 68 72 4.9 106 4.9

2 ,3,4, 5-tetrachl orophenol 133 156 5.2 117 7.1

pentachlorophenol 127 148 4.4 117 9.0

B . Analytical Methodology

The methodology for the chemical analysis of pesticides and their metabolites, has been reviewed (6,16,88), The most frequently employed analytical

procedures for measuring low levels of chlorinated phenols in urine involve

solvent extraction and either derivatization (often with toxic, derivatizing

reagents like diazomethane) to more chromatographabl e compounds (35,37,89-93),

or determination of the free phenol in various polyester, gas-chromatographic

columns (94-97). Recently, reports of analytical methods that use porous,

polymer resins as the sorbing agents for the removal of phenols from water

(90-100), have been published. The most widely used resin for this purpose is

Amberlite XAD-2.

The efficiency of recovery of pesticides (99) and phenols (98,99) from

water by using XAD-2 resin or the chemially identical XAD-4 resin has been

reported. The free phenols isolated can be separated by using columns of both

double support-bonded diethylene glycol succinate (DSB-DEGS) and supportbonded, 1 ,4-butanediol succinate (SB-BDS) (27-29).

A recent report by Lores, Edgerton, and Mosemann (59) described an efficient method for the confirmation of chi orophenol s in human urine by

liquid chromatography (LC) with an electrochemical detector. The method was sensitive to chlorophenol s at the low-ppb range (as encountered in most

general -population samples).

Advantages and disadvantages of liquid chromatography in industrial

medical technology have been discussed (107).

10
Table

7:

Chlorophenols

In

Human

Urine

Samples

(Results

In

ppm)

(111)

Pentam o i- o a% lo in 91 CO cn VO VO

2.3.S.6 CO

tn

CM

in in 00 VO

m cn Ov

m lo in

m

(Am

CM

CO CM

CM

V CM

inVm

in p*> 00o

CM

VD

CM o ooCM

mCM in

VO

Oo

in oo o

in

CM

m f** CM cn CM lO ocn

lOm

CM - m oCM mm

CM

CM

CM<n

mm ^ m CM 00

CM

m

O lO

VO

CD •->

m CD 9 *i» o

CM

fn

lO

m VO

91

VO CM

VO

IDCM CM

lO

um

CM

VO

m vo ^ m o m CO cn ^ p^CMVO VO

O CO m o m •— CM

9V 9^ 91

O 91 in

CM

in o CM CM

u

CMm

CMm om om o a^ CM

ov &in

CM o m

CM

Detection Method £ CO s: o £ C9 «i £ CO £ CO ^ £ CO £ CO £ CO <«J £ CO ^ £ CO -J

0)aS

fO

(/)

CM

m

m VO pNk 00 9v o O

(/I « S»o

•o

01 • w e

u. o o&0> u w 9 • 0) 9

>t

u £ <o &O lA ra W u

O)o 3 1 (/) 9

fO 01 E 9 o O u u 9 u 9 & a* •o <0 •— w 9 3 91 1 o 1 •«K> «Q 1 E O. 1 o ro

0»

w 9 w £ 9> 3 U O W 1 CL «/) « O <e s u 9) o 1 9 e 0) o 9 w 3 w •9 u a. •mo 0) « 3 U 9 o» 1 e u o 9 w 9O

CJ • A 01 «* >1 «£ Uj 9 & <a) MB 9 W • s 9V O O £ 9

CL 4^

«e lO 9 £ U O 9> a. u O lA c£u (Q «/1 1 E «/l lA o !9

fO k,

B

9> £ i u 1 9i 1 >»

t/1 <£ 3 a. 9> fQ9 « 9 9 u W o 1 3 <w e m o • CL E u >» (Q O U 9 u e 1 01 o c 9 o

01 l/i

u

Hu 3 3 9 9 CO 1/1 o; 9 ^z> • * w

>» >1 u u o w S s w 9 o o o > ^m E mm mJ o o 9 u u t/1 o 9

&.

u

w 9

i/i 01o>

</l t/i o {•

*/> 1 e O

«Q (/) s 1/1 1 «o o 9

>> £ e </i 1 9 & 1 fQ u o> U o t 9> im 1 O a. o w <Q S W £ . O B 91 u c o O •V 9 o <Q 1 a. u £ in o O • 9

•o

w CM

O 3 u1 S 9 9 •pv3 1 t n 9’ m £ CM CM

<o 9

11
C. Recent Methodology

An application of pyrolysis gas chromatography-mass spectrometry CPGS-MS)

to the study of untreated urine yielded a highly reproducible pattern of peaks

that may potentially be used to ''fingerprint" metabolic abnormalities. No

sample preparation Is necessary; analysis can be conducted with 5--15 yL of

urine (108).

Relative retention-times of the chlorinated phenols in a 2-pyrrol idlnone

column, and reversed-phase 1 Iquld-chromatography have been reported by Moury

and Siggia (109). The study showed that ortho -substituted chlorophenols are not

retained as strongly as the corresponding meta and para isomers; also 2,4,6-

trichl orophenol is not retained as strongly as the dichlorophenol s that are not

ortho- substituted gen- bonding effect).

Recently, Edgerton et al

.

(56) described the determination of traces of

chlorinated phenols in human urine by gas chromatography. The analytical i procedure involves extraction of the chlorinated phenols by passing hydrolyzed

urine through a column of XAD-4 resin. The chlorinated phenols are then eluted

from the column with 2-propanol --hexane. The eluate is concentrated, and

analyzed by electron-capture gas chromatography (EC-GC). Recoveries of

chlorinated phenols from fortified urine averaged better than 80 percent.

Method sensitivity is dependent upon the chlorine substitution and the elution

time of the phenol through the gas chromatograph. Sensitivity for di- and trichlorophenol s is 1 yg/L, and, for tetrachlophenol and pentachl orophenol , 2 yg/L.

In recent work, Angerer ^

al_. (77) described a sensitive, gas-chromatographici

method for the simultaneous determination of ten chlorinated phenols that appear

in the urine of persons exposed to a-hexachlorocyclohexane (see Table 6). The

phenolic compounds in the urinary samples are hydrolyzed in acid, and derivatized with acetic anhydride. This simple treatment permits routine application.

The stationary phase (8 percent of DC200 on ChromoSorb GAW-DMCS) possesses a | high separation capability for the acetic esters of the chlorophenols. The

detection limit lies between 4.9 and 18.6 yg/L and this allows determinations

even in the environmentally interesting concentration range. The recoveries

determined by using aqueous standards ranged between 87 and 119 percent, and

the relative standard deviations were between 4.4 and IQ.l percent. The

application of acetic anhydride for derivatization of chlorophenols in urine has

been confirmed by another laboratory 08). The simultaneous determination, by

gas chromatography, of phenol, 2-chlorophenol , 2,4- and 2,6-dichlorophenol

,

2 ,4, 6-trichl orophenol , and 2,3 ,5,6-tetrachlorophenol in the urine of industrially

exposed workers has recently been reported (110); the method does not require

derivatization. The phenolic compounds are separated by distillation, and then

extraction into isopropyl ether and analyzed by GC. The detection limits in

urine are Q.l mg/L for phenol to 1 mg/L for the di- and tri-chlorophenol s . The

coefficient of variation for each component was 4 percent. The naturally

occurring metabolites cresol and 2-heptanone are also isolated, and can be

quantified by this method.

12
Absorbance

Recently, Wright ^

(111) reported determination of the underivatized

chlorophenol s in human urine by combined liquid chromatography (LC)-mass

spectrometry, and selected-ion monitoring. The urine samples were hydrolyzed

by the method of Edgerton e^ al . (56) and LC was performed in a LiChrosorbdiol

column (UV detector at 210 nmTT the separation of chlorinated phenols is

illustrated in Fig. 1 (111).

h—0

Q

1 Q.

qT

•qn

Time (min)

Figure 1. Chromatography of chlorinated phenol standards (250 ng each) on LiChrosorbdiol column. UV detector at 210 nm.

The study of chlorophenols in human urine was approached by selected-ion monitoring because of the large number of interfering compounds. The results of a selected-ion monitoring —LC--mass spectrometric study of ten individual, humanurine samples are presented in Table 7. The results obtained from the same extracts by electron-capture 6C and electrochemical detector LC are presented

in the same Table for comparison. The specific details of the last two methods

are reported elsewhere (54-56). In many cases, the results are in reasonable

agreement; in others the disagreement is distinct. The EC/GC method, by the

nature of the detector, has a low sensitivity for monochlorophenol s ; the EC/LC

method requires a buffered mobile phase and does not permit solvent gradient,

and the LC-MS method requires two 23 min data collection runs per sample. Each

of the three methods was capable of low-ppb detection when tested against

mixtures of standards. When urine extracts were examined, severe backgroundinterference generally limited mass-spectral detection to 5 —25 ppm. Each urine

sample run was either preceded, or followed, by analysis of a standard mixture

containing 0.2 ng of each of the chlorophenols per mL. The method (111) could

thus detect 19 chlorinated phenols in human urine in 2--23-min runs, with a lower detection limit of 2--10 ng. In absolute terms, however, the mass spectrometer is less sensitive than either the electron capture detector, or the electrochemical detector, but it is the most selective of the three.

13
IV. PHENOL, £-CRES0L, CATECHOL, AND RELATED HYDROXYAROMATICS IN HUMAN URINE

A. Phenol (General

)

The principal, simple phenols reported to he present in human urine are phenol, £-cresol , catechol, resorcinol, and hydroquinone (quinol ) (112-114).

However, as recently found by Spiteller and Spiteller (115) and others Cl 16),

human urine is a complex mixture containing 'vSOO acidic compounds [including

phenol and £-cresol), and 2/6ths of these can be characterized by their mass

spectra [115).

Phenol is a normal constituent of urine. For the most part, it is found in

the conjugated form — either as the sulfate or as the glucuronide [117); very

little free phenol is found in human urine. Normal total -phenol level in

human urine is '>^50 mg/L [112,118); however, this value may vary with exposure,

or with the methods of measurement [119-124). Phenols in urine may be derived

not only from the dietary intake of proteins, fats, such smoked foods as smoked

meat, and water, but also from a wide variety of exogenous sources ( e.g .

,

tobacco smoke, mouth washes, ointments, and analgesics) and drugs [phenyl

salicylate [salol ) [125) , zinc phenyl sulfonate, and phenobarbital ]. Exposure to

benzene (126,127), which is of particular interest because of its known

hemopoietic toxicity (128), may give rise to the formation, and increased

excretion, of phenols (112,113) and this may be used as a measure for assessing

the degree of exposure of humans 118,126-129). The mechanism of this relationship is that the liver oxidizes benzene to phenol, and subsequently detoxifies

the phenol by conjugation with either sulfate or Q-glucuronic acid.

Industrial organic solvents are commonly used nowadays, and they are potentially injurious to health. It is specific for this group of compounds

that, according to the latest findings, it is often not the toxicological

compounds themselves but their metabolic products that are dangerous to

health (130).

In a cross-sectional investigation (131), the results of 6126 toxicological urine tests of persons exposed to such industrial solvents as benzene or toluene have been statistically evaluated. The solvent metabolites from benzene ^ phenol » and from toluene -» hippuric acid and £-cresol , have been defined as hazards in occupational medicine.

Williams 012,113) reviewed the metabolism of phenols. The relative amounts

of these vary with the individual , and abnormal patterns of phenol excretion by

the kidney may be due to antibiotic intake, gastrointestinal disorders, and

liver and kidney diseases 032).

a. Preservation of urine samples containing phenol

The urine samples to he analyzed for both free phenol and total phenol were

stored at -20 °C in sterilized, 2Q-mL bottles, or polyethylene, screw-capped

jars, within 30 min after collection, and were thawed immediately before

analysis. Control samples showed no change after several weeks (132). In a more-recent report [133), the urine specimens containing phenol were collected

in polyethylene bottles. Whereas no specific treatment appeared necessary to

preserve the integrity of the sample, 1 mL of 10 percent copper sulfate solution

14
was added to InKltiit hacterial acttylty, and samples were stored tn a refrigerator

at 4 °C until analyzed. Storage (47) at 4 °C, or freezing (33), is recommended

for preservation of urine samples, as reported earlier in tKis text. Urine

samples selected for total -plienol analysis were preserved b.y collecting tliem in

1 M Kydrodiloric acid and storing tKem at -20 °C until analysis (134). Urine

samples were also preserved adding a drop of cPiloroform to prevent microbial

growth (135)

.

B. Analysis of Phenol in Human Urine

The quantitation of total urinary phenol has only been practical from the

clinical standpoint for ''^50 years. Some early, and some recent, methods of

urinary phenol analysis had been limited to colorimetric methods using either

coupling of a diazonium chloride with phenol 036,137,185), or the Gibbs reagent

(indophenol test) 038,160), or color-producing reagents, e.g. , 4-amino-anti pyrene

produces a stable color with phenol (520 nm) if the pH is kept (139,140) at

10.0 +0.2. These methods, however, lack specificity, as the cresols present in

urine interfere with development of the color. The colorimetric methods of

urine analysis were reviewed, and criticized (132,141). Also, analyses for

urine phenol sulfates, either by paper chromatography (142) or paper electrophoresis (142-144), are inadequate, because urine contains large proportions of

salts and polyols (145).

Recently, however, Ragan and MacKinnon (146) used paired-ion, reversedphase, liquid chromatography (LC) for both qualitative and quantitative analysis

of phenol sulfates in these complex, biological mixtures; the urine mono- and

di -sulfate of resorcinol have also been determined by this method. The range

of detection (254 nm absorption) was from 30--125 ng to 5--10 yg, depending on the compound (e.g., phenol sulfates). The paired-ion, reversed-phase, method

(146) thus constitutes a considerable improvement over paper-chromatographic and

paper-electrophoretic analysis of phenol sulfates, particularly those occurring

in crude extracts of urine. Normal (polar), phase-adsorption LC (147-149)

usually leads to poor retention characteristics and poor resolution of such

strongly ionized compounds.

The conditions used for hydrolysis of conjugated phenols vary widely (150),

and range from 032,135,151) refluxing urine for 30 min after adjustment of the

pH to 1 to refluxing for 60 min with an equal volume of concentrated hydrochloric (135,1 50) or sulfuric 0 52) acid. Sulfate-conjugated phenols are

hydrolyzed by acid at 03 —95 °C at least 50 times as quickly as glucuronideconjugated phenols 050,153). The hydrolysis of the conjugated phenols can also

be performed enzymically by using a mixture of arylsulfatase or S-D-glucuronidase (1 54)

.

a. The Van Haaften—Sie gas chromatography method for the measurement of

phenol in urine

In 1965, Van Haaften and Sie 0 55) developed a gas-chromatographic (GC)

technique that enabled determination of the phenol concentration in urine

without interference by cresol . Their technique 055) requires special

injection-equipment and, furthermore, the volume of the sample injected must be

measured with great accuracy. The urine sample was mixed with an equal volume

of phosphoric acid, and injected into the gas chromatograph. Conjugates were

15
hydrolyzed in a precolumn containing coarse-glass powder, and the phenol was separated from other urinary components in an analytical column, and detected by

flame-ionization. A few parts per million of phenol in urine could be detected,

and this was a significant break-through in the analysis of urinary phenol. A

recent, critical appraisal of this method was presented in a paper by Baldwin

et (156). The authors (156) found that the method gives over 80 percent

Tactually 89 percent) of the response expected for conjugates of phenol. However, they found that the response was strongly dependent on instrumental

conditions, and that safeguards must be built into the method, in order to

ensure that hydrolysis of conjugates is satisfactory (or complete). Despite

some drawbacks, the Van Haaften-Sie method has found wide application as a measure of benzene exposure in humans; the method has been modified by several

research groups (125,128,132,134,135,1 54,157-164).

The use of an appropriate, internal standard in GC analysis is essential if

reliable results are to be achieved with the Van Haaften--Sie method (158).

However, an internal standard was not used originally and chromatograms

frequently showed a relatively high background, making quick chromatographic

analysis difficult. This method has been modified by introducing an internal

standard such as valeric acid (161), benzyl alcohol (154), o^-cresol (135),

2-ethyl phenol (133), 2,5-xylenol (162), or 2,4-dichlorobenzene (119). A

standardized procedure for a GC analysis of phenol in urine has been suggested

(135), and is detailed next; the steps involve hydrolysis of conjugates,

addition of o^-cresol as the internal standard, extraction with ether, and GC

analysis

.

Suggested procedure for a GC analysis of phenol in urine (135)

1. To the sample of urine (containing 1 —200 yg of phenol) in an ampoule,

add sufficient hydrochloric acid to give a final strength of 5 mol/L, flush the

ampoule with nitrogen, and seal.*

2. Heat the ampoule at 100 °C for 30 min; then cool.

3. To the opened ampoule, add a known amount of o-cresol , estimated as far

as possible to be similar in amount to the phenol in tFe sample, and mix.

4. Transfer to a small separatory funnel, rinsing with water as necessary,

and extract the mixture with about twice its volume of ether.

5. Centrifuge, and transfer the ether layer to a tapered, evaporating tube

by means of a Pasteur pipette.

6. Evaporate the ethereal solution to '^^50 yL on a water bath at 30 °C.

7. Inject 1--5 yL of the concentrate on to the GC column (4 ft x 1/2 in)

containing 3 percent of OV 25 on Chromosorb W-HP (80--100 mesh) at 100 ®C.

*Screw-cap vials are more convenient, see Ref. (56), Part II.

16
However, gas-chromatographic methods are not without their problems, mainly

at the sample-preparation stage. Firstly, the samples must be hydrolyzed to

decompose the glucuronide and sulfuric ester of phenol. This step is usually

conducted by heating with acid, and it carries the twin dangers of incomplete

hydrolysis and loss of the very volatile phenol from heated solutions. The

hydrolysis may also be performed enzymically. Secondly, the phenol must be

extracted from the hydrolyzed sample: simple extraction usually recovers only

50-60 percent of the available phenol, and even salt saturation of the aqueous

layer increases extraction efficiency (52,129) to only 80 percent. Unfortunately,

much extraneous material is simultaneously extracted, giving chromatograms

showing interference and rising baselines. Finally, the phenols are often

derivatized [ e.g . , trimethyl silyl (TMS) or acetate derivatives] before analysis,

requiring further, labor-intensive manipulations (132,133,164). According to

Fell and Lee (164), acetates are conveniently prepared following extraction

by treating dilute solutions of monohydric and dihydric phenols at room temperature with acetic anhydride in the presence of 4-(dimethylamino)pyridine (which

is a far more powerful catalyst than pyridine). The phenol acetates are then

analyzed by GC using wall-coated, glass-capillary columns.

A rapid GC microdetermination of urinary, volatile phenols (phenol, £-

cresol , and 4-ethyl phenol ) , following hydrolysis with hydrochloric acid and

steam-distillation, has recently -been described (134). A determination of

phenol and catechol with immobilized enzymes has recently been reported (164a).

b. Phenol in urine: additional sources; determination, and methods of

analysis in brief

Phenol in urine as a result of industrial exposure to benzene has been

reported from many laboratories throughout the world. One study (165) showed

that, within 4 h, an average of 40 percent of the benzene absorbed was excreted

as phenol. Other studies included detailed urinary monitoring (166), benzene

metabolites (167), and benzene exposure versus urinary-phenol level (129,168).

Exposure to benzene and the presence of its metabolite, phenol, in urine has

also been reported in workers in the shoe industry (170), the oil industry

(171,172); in workers in close contact with oil-shale tars (173) or shale

chemical -products (174), or in workers in contact with phenolic resins (175),

caprolactam (176), or plastics (176) production, and in filling-station

personnel (177).

Additional methods of analysis of phenol in human urine include GC

determination of phenol and £-cresol ; the values found in urine were

2.9 mg/L for phenol and 3.3 mg/L for £-cresol (178); the values for phenol and

£-cresol , however, were considerably lower than reported (112,118,120,121 ,182).

Also, phenol in urine was determined by thin-layer chromatography (t.l.c.)

(179,180), or t .1 .c.--color reaction (using 2,6-dichloroquinone-4-chloroimide as the color reagent) (179); also, by derivatization (dansyl derivatives) followed

by high-speed GC (181-183), or as direct separation as phenyl glucuronide and

phenyl sulfuric esters ( via multiple, liquid--! iquid partition) (184). Additional procedures involved the diazoti zation of £-nitroaniline, and subsequent

coupling of the diazonium chloride with urine phenolic compounds (185); application of mass spectroscopy (186,187); liquid, thermal diffusion (139); multicomponent GC (188-191) or LC (182) analyses; and use of a special color reagent

Ctnvolving sodium tungstate) (192,193).

17
C. Crasol , Catechol , Kydroquinone, and QtKer Benzenedtol s (Polyhydric

Phenols )

a. Cresols

The presence of cresols tn human arfne after exposure to toluene was first

suggested 5y Laham (194). Further insfght into the metahol ism of toluene in man was gained by detailed investigations using elaborate, analytical methods,

e.g. , liquid chromatography CLC) 055) and GC (182,183). o^-Cresol was established as a metabolite of toluene, and a detailed comparison between

normal persons and an exposed group were presented by Angerer 0 83), who stated

that '>-0.05 percent of the toluene retained was metabolized to o^-cresol

.

Experimental evidence on cresol in human urine following exposure to

toluene has recently been reported by Moiwode and Drysch (196). Ten healthy men were exposed, at rest, to '^'200 ppm of toluene in the air and concentrations of

toluene in blood and urinary metabolites were measured with time following

exposure. The results of this study are summarized in Table 8. Hippuric acid,

£-, m-, and £-cresol , and phenol were detected by capillary GC, thus confirming

formation of these metabolites of toluene. Also, as shown in Table 8, the mean

value for all metabolites in the urine, except- phenol, increased after 4-h

exposure; notable also was a dramatic increase in the toluene concentration in

blood for the same period of time, with practically no change in density of

urine samples.

Using modern, analytical methods, e.g. , capillary column, flame-ionization

GC, or GC-MS, £- , m-, and £-cresol in human urine were determined in industrial

(printing) (182,183,196-199) or refinery (200) workers, and in occupational

(197) or experimental (196) exposure to toluene. In one practical procedure

(201)

, a sample of urine was acidified with 0.5 mol/L HCl to pH S.5--6,

followed by extraction of phenol and cresol into ether, clean-up in an activated-alumina column, and flame-ionization GC using Carbowax--cyclohexanedimethanol succinate on Chromosorb W, and nitrogen as the carrier gas. The column

temperature was 170 °C. At 0.2--1.4 mg/L of phenol and 1 .4--3 mg/L of cresols,

the recovery was 90—96 percent.

Colorimetric determination of hydroquinone (202) or catechol (203) in

urine was achieved by using specialized reagents, e.gv , 3-methyl -1 -phenyl -5-

pyrazolone (antipyrine reagent, red color of the complex measured at 520 nm)

(202) or the Gibbs reagent C2,6-dichloroquinone chloroimide, red color of the

complex measured at 510 nm) (203).

GC (_204) or GC-MS (205) analysis of al kyl phenol s , al kyl catechol s , and

polyphenols in the urine of exposed workers (204), or in uremic serum (205),

has recently been reported.

18
Table

8:

Common,

Mean

Values

for

Toluene

in

Blood

and

Urinary

Metabolites

from

Exposure

Experiments

(196)

i-0} +JM- , (O

CO (U &- szz 3 LO CO o CO O o CO o 00 CO •K CM CO 'd* o. CO r-* CM o r— X o O cu o o O LO

s-(U +J

(dCO <u s. S- 3 3 LO 00 O CO LO r-^ CO o

o cn r'* cn CM cn o ,

Q. o 'd' LO

cn

cn o X r— o CM 0) CM ' o O CO CO '

(U +JM-

(d O)

CO

s- 3 00 •d- 3 CO CO o cn CO O O CO o cn cn f— r—

Q. CO 'd’ LO o

X CO o o

"d* <u LO ' o >d* «d" '

CO

S-3

O

<u

'd' s-3 O r^

s- CO m 00 CO o cn CO

cu o o o LO 00 r>.

+-> o. cn CM CO LO o 4- X m cn o

<c 0) •d" r~ o CO CO

(U

i-

<u 3 CO 00

s- CO CO oo o cn o o CM LO * CM CO o +j

Q. 00 CM 00

0) X o ,—

o E

CQ (U r— o o o CO r— •n“

'

c

^

o .

i —

J

_i •r“ -o —I ^

^

+J

^ . •r“ cn cn cn CD O

_J o oo £ £ E CU c —

.

(d —

— — — 4- •M

•1- CO O O) U O) r— OJ r-“ dJ ^ <U <U •o

•I- c O C o c o c c >> c S- •!- CO 'r- CO 't— CO •!— r" +J 3

<U "O 3 1- <U S- (U S- O) &. o s_ •r- O 3 O Q. 3 S- 3 S_ 3 3 C 3 CO r—

1— o a. O C_J C_3 (U C CU O 1— •1- c 1 C 1 C 1 C x: c CU 03 “t— 3: T- o •<- E •<- O.T- Q. -f- o K

19
b. Benzenedlol s Cpolybydric pKenola)

There are many methods for determining monohydric phenols in urine, but at

present only a few quantitative procedures exist for the dihydric phenols. For

semi-quantitative measurements by paper chromatography, the phenols are usually

extracted from neutral urine with organic solvents. Using more sensitive and

specific GC methods for quantitation, ETafcke and Sche.line Q58J found this

method of extraction to Be inefficient and irreproduci bl e; they extracted

acidified urine with ether, and then back-extracted the ether layer with aqueous

sodium hydrogencarbonate; this procedure gives poor recoveries of the dihydric

phenols, but is, nevertheless, the most satisfactory method available. Fell

and Lee 0^4) re-investigated, and improved, the extraction of phenols from

human urine; they also developed a new method for derivatization Chy preparing

the acetates). The urinary monohydric and dihydric phenols as acetates (or

trimethylsilyl derivatives) are then analyzed by capillary GC. GC of underivatized dihydric phenols Cl 58) is somewhat difficult.

c. Analysis of biological mixtures by negative chemical ionization

mass spectrometry

A recently developed alternative to chromatography- -mass spectrometry for

the analysis of mixtures is direct analysis in a two-stage, mass spectrometer

C206). The first stage functions as an ion separator, and the second, as an

ion identifier [207). Recently, McClusky, Kondrat, and Cooks C61 ) and Levsen

and Schulten C208) developed a direct, mixture analysis by mass-analyzed, ion

kinetic energy spectrometry CMIKES), using negative chemical ionization (NCI).

The NCI/MIKES method (61) is particularly useful for direct analysis of such

complex biological mixtures as are found in human urine, e.g. , mono- and dihydric phenols, hydroxybenzoic acids, and D-glucose. Because mass analysis does

not separate isomers C &-g « » and £-hydroxybenzoic acid), the MIKE spectrum of

(M + H) and CM - H)" fragment-ions offers important structural information.

The detection limit is lower in the MIKES method (sensitivity is better than

10~^°g) than in conventional, mass spectrometry, and this is accounted for by

the decreased chemical noise in MIKES.

V. £-nitrophenol in human urine

A. p- Nitrophenol , a Metabolite of the Pesticide Parathion

The methyl- and ethyl -parathlons, i .e. , Q,Q-dimethyl- and 0 ,0-diethyl

0-p - nitrophenyl phosphorothionates , respectively, have been among the most widely

used insecticides in U. S. agriculture during the past quarter century. The

ethyl form has accounted for a large proportion of poisoning among workers

exposed to insecticide-treated citrus and cotton (201,210.). These incidents

demonstrated a need for improved protection of agricultural workers exposed to

organophosphate pesticides C2Q9-).

It has been reported C211) that, in California in 1177, methyl parathion

,

followed by ethyl parathion, were the two most used organophosphorus pesticides.

Exposure to methyl - or ethyl -parathion Cor similar organophosphorus pesticidesl

leads to excretion of £-nitrophenol CPNPl in human urine; other metabolites of

20
parathton, such, as alkyl pfiosphates. Rave also Reen found in human urine, and

their analysts provides a measure of the extent of exposure. A recent survey by

Kutz et al_. (72) showed that residues of pesticides and their metabolites can be

found in various tissues and body fluids of the general population of the United

States, and this is indicative of the environmental distribution of these

chemical compounds. For example. Table 9 summarizes the result of the analysis

of specimens from a pilot human urine study for the years 197Q -- 1974; alkyl

phosphate and phenolic derivative were both detected in urine samples (see also

Tables 11-121. Interestingly, from this survey, it may he seen that the pesticides 2,4,-D or Silvex, or the metabolites 3,5,6-trichloro-2-pyridinol , or 2,4,5-trichlorophenol , were not detected duriiig the 1970 —1974 pilot-study.

Table 9: Summary of Pesticides and Their Metabolites Detected in 267

Human Urine Samples C72I

Pesticide or its

meta bol ite

Percent

positive

Percent of samples

^0.1 ppm

Dimethyl phosphate (DMP) 76.7 2,2

Diethyl phosphate CDEP) 94.

Q

3.4

Dimethyl phosphothionate (DETP) 70.8 7,9

Dimethyl phosphodithionate 38.2 4.5

Diethyl phosphodithionate CDEDTP) 0,4 0.4

Malathion 0.4 0

Pentachlorophenol 96.3 1 .5

A1 pha-naphthol 10.9 2.2

Paranitrophenol 6.7 1.9

2,4, 5-T 1.5 1.5

The polarographic determination of £-nitrophenol , as a urinary metabolite

of parathion and similar pesticides, has recently been reported C239). The

measurement was conducted by reduction of the polarographically active, nitro

group at a dropping-mercury electrode; the recovery was 98--1Q0 percent. The

method permits determination of £-nitrophenol without extraction from urine.

The application of pulse polarography to the determination of ^-substituted

nitrobenzenes (^e .

g

. , PNPl and other nitrogen-containing organic compounds, and

their potential metabolites, has recently been described C2401. The sensitivity

of pulse polarography was Q.Q6 mol/L for nitro compounds, and was decreased

MQ-fold in the presence of urine. PNP was determined directly while spiked in

urine.

An enzymic procedure for the determination of pesticides in urine has also

been described. This new, competitive-assay procedure, namely, enzyme-1 inked

,

immunosorbent assay C^LISAJ, has been developed for the analysis of pesticides,

using parathion as the model compound C241 ) . Parathion was reduced to its

amino derivative, and this was diazotized, and coupled to bovine serum albumin

21
(BSA), Approximately 21 —23 aminoparathion residues were conjugated to each

molecule of BSA. The ELISA procedure was performed by utilzing the antiserum

produced, which exhibited high specificity for parathion. Various pesticides

(methyl parathion , diazinon, dimethoate, and carbaryl ) and a metabolite of

parathion (£-nitrophenol ) showed inhibition of the antiserum. The lower limit

of detection of parathion by the ELISA procedure was found to be 5.0—10 ng/mL

(0.005--0. 01 0 ppm) in human serum, human urine, and bovine serum.

Correct diagnosis in parathion poisoning depends on the history of

exposure to parathion, and on association with the characteristic signs and

symptoms. Urinary £-nitrophenol , a metabolite of parathion, can be detected as early as one hour, and as long as 259 hours, after parathion ingestion. The

urinary £-nitrophenol of 23 patients with acute, oral parathion poisoning was determined (212). The concentrations of £-nitrophenol in urine in mild

parathion poisoning ranged from 1.4 ppm to 10.5 ppm with an average value of 3.9

ppm; in severe parathion-poi soning , the value was >26.7 ppm (212). The toxicity

of the pesticide has been inferred from the analysis of a parathion-suicide

victims; their urine contained 6.3 ppm of PNP by liquid chromatography, and

6.2 ppm by a confirmatory, spectrophotometric method (213). £-Nitrophenol

and £-aminophenol are excreted in the urine of workers involved in the production of nitrobenzene, particularly in cases of acute poisoning (214).

B. Analysis of p-Nitrophenol in Human Urine

The urinary level of phenolic compounds may be the key for establishing

an index of exposure to pesticides containing this moeity as a readily

hydrolyzed or metabolized portion of the molecule. £-Nitrophenol is excreted

entirely as glucuronide and sulfate conjugates in mammals, including humans

(215-217). PNP can be readily detected and quantified in biological samples by

virtue of its strong, visible absorption at 390 nm. This property makes PNP an excellent substrate for the study of phenolic-conjugation enzymes. Thin-layer

chromatography (217,218) and anion-exchange, liquid chromatography (219) have

been reported for separation of PNP conjugates; however, quantitation of the

separated compounds requires either time-consuming procedures (217,218) or use of a solution of extremely high ionic-strength (mol/L KCl ) (219).

The behavior of £-nitrophenol and p-nitrophenyl Q-glucuronide with

mineral acid has been investigated (220). With 33 percent sulfuric acid,

'^^93 percent of the glucuronide was hydrolyzed when the solution was heated in an open vessel for 15 s. With 6 percent hydrochloric acid, only '\^65 percent

of the conjugated £-nitrophenol was converted into the free form. No loss of

PNP occurred when free PNP was treated under the same conditions. Studies of

the hydrolysis of PNP conjugates, and determination of free PNP in urine, have

been reported (221-228).

£-Nitrophenol as a human-urinary metabolite is generally detected and

measured by the multi phenol method of Shafik e£ al_. (53) down to levels of

10 ng/mL. The method measures PNP as £-ethoxyni trobenzene . Analyses by this

method have been conducted for a number of years, in order to determine the

extent of invasion by PNP residues in the general population. The method (53)

is based on electron-capture GC (EC/GC) of ethyl ether derivatives of phenols.

22
The procedure involves acid hydrolysis, extraction, derivatization (diazoethane),

silica gel chromatography, and EC/GC. A mixture of ten phenols and three phenoxy

acids, namely 2,4-D, 2,4,5-T and Silvex can be determined in one sample. The

sensitivity of this method is comparable to that of recent findings OH); for

example, a limit of detection is o.Ol ppm for 2,4,5-trichlorophenol , 0.01 ppm

for pentachlorophenol and 0.02 ppm for £-nitrophenol (56).

The analysis of other metabolic products of parathion, e.g. , alkyl phosphates, has also been explored. Alkyl phosphates are metabolic end-products of

parathion and all other organophosphate pesticides, and may therefore be useful

in evaluating exposure to many more organophosphates than those yielding

£-nitrophenol (229-231). Urinary 0,0-diethyl phosphorothionate (DETP), a primary

alkylated metabolite of ethyl parathion (229), has been shown (85) to be

unstable in urine, even when the sample is kept at -18 °C. Acid hydrolysis of

DETP, to give ethyl phosphate, is used in a procedure for the determination of

the pesticide by Shafik et al_. (232). In this procedure, acidified (hydrochloric acid) urine is autoclaved, extracted with 1:1 acetonitril e--ether , and

the material in the extract is derivatized with diazoethane. Chromatography

on a column of silica gel is used for clean-up, and fractionation, of the alkyl

phosphates. A gas chromatograph equipped with a flame-photometric detector in

the phosphorus mode is used to quantitate the alkyl phosphates. Improved

methodology based on resin absorption (ion-exchange chromatography ) of urinary

alkyl phosphonates has been developed by Lores and Shafik et al . (229-233).

Recently, Bradway et al_. (230) effectively extracted the aTFyT^phosphates in

urine, as an ion-pair with a lipophilic, quaternary ammonium cation, into a nonpolar solvent such as dichloromethane containing an alkylating agent [ e.g ., (pentafluorophenyl )methyl bromide]

.

C. Recent Methodology

A high percentage of the chemical compounds encountered in the environment are eventually excreted in the urine as various polar metabolites.

Therefore, indices of exposure to these compounds may be established by monitoring the levels of urinary metabolites. Because many of the metabolites may

be classified into one of several broad categories ( e.g . , phenols, anilines, and

alkyl phosphates), a few fundamental methods permit the monitoring of a large

number of metabolites (230). Detection of £-nitrophenol as a urinary metabolite

may be related to pesticide exposure; for example, exposure to parathion or its

homologs (1 6,211 ,234).

Recently, several methods have been developed for confirmation of the

presence of £-nitrophenol as a human urinary metabolite. According to Kirby

e£ al_. (235), £-ethoxyni trobenzene (as reported by Shafik £t al_. (53)) in a benzene or hexane extract is reduced with aqueous chromous chloride to

p-phenetidine, which is then converted into the amide by reaction with heptafl uorobutanoic anhydride. Heptafl uorobutano-£-phenetide is then determined by

GC in an OV-1 column, using a ^^Ni detector. The method was applied to urine

samples containing 10 ppb of PNP.

23
Liquid chromatography (LC) with UV detection (254 nm) has been reported for

the determination of PNP in urine (236). Recently, Ott (213) improved this

procedure; acid hydrolysis, steam distillation, and LC separation (UV detector)

of urinary pesticide-metabolites were performed automatically. At the highest

rate, samples were analyzed every 24 min with a limit of detectability of 1--2

ppb of PNP in urine.

Recently, a rapid, sensitive method has been developed for the simultaneous

determination of PNP and its glucuronide and sulfate conjugates in biological

samples ( e.g . , urine) by using reversed-phase LC (237). The mobile phase,

consisting of 10 mmol/L K2HPO4, pH 2.75, containing 20 percent of acetonitrile,

provided excellent retention, and separation, of PNP and its Q-glucuronide and

sulfate conjugates.

A simple, rapid spectrophotometric method for the determination of urinary

£-ni trophenol has recently been described (238). The urine sample (10 mL) was mixed with HCl (1 mL), and 25 mL of an extractant (consisting of 4:1 petroleum

ether--ethyl ether and 1 percent of pentyl alcohol) and was thoroughly shaken

for 3 min. The ether phase was washed with water ('\^20 mL) and mixed with

14 mL of 3 mol/L NH4OH, 0.7 mL of 1 percent £-cresol , and 1.4 mL of 1 percent

TiCl3, and the reaction complex was measured spectrophotometrically at 620 nm. The reproducibility was good, and recovery of added PNP was 92 —100 percent.

A sample of PNP (>30 yg) can be detected.

VI. HERBICIDES (2,4-D*, 2,4,5-T**, SILVEX***, DICAMBA****, AND OTHERS)

IN HUMAN URINE

A. Introduction

The chlorophenoxy acid herbicides, e.g

.

, 2,4-D, 2,4,5-T, Silvex, and

Dicamba, are widely used in agriculture, commerce, and homes in order to control

terrestrial and aquatic, broadleaf weeds (242,243). The herbicides 2,4,-D

(244) and 2,4,5-T (245,246) have played an important role in improving the

forest and food-producing capability of the United States during the past

twenty years. Their effectiveness in controlling a wide spectrum of broadleaf,

woody plants, and their high rate of degradation when applied to soil, have

allowed these herbicides to be widely used (247). The world-wide consumption

of these herbicides is now enormous (12). In Sweden, '^2 x 10^ kg of 2,4-D and

2,45-T are used annually in forestry (248). On the Canadian prairies,

'vS X 10^ kg of 2,4-D formulations are applied annually for weed control (249).

Agent Orange (a herbicide containing equal parts of 2,4-D and 2,4,5-T) was used extensively in Vietnam as a defoliant (250). Due to widespread application of the herbicides, the environment contains a significant amount of 2,4-D

(1 2,16,23,42,43,251-254); small amounts of 2,4-D have been found in drinking

*(2,4-Dichlorophenoxy)acetic acid (2,4-D)

(2 ,4 ,5-Trichlorophenoxy)acetic acid (2,4,5-T)

*2-(2,4,5-Trichlorophenoxy)propanoic acid (Silvex)

. . 3,6-Dichloro-2-methoxybenzoic acid (Dicamba)

24
water (^0.04 yg/L) and marine environments Cl3-0 yg/L) (244,255). The solubilities of 2, 4, -5 and 2,4,5-T in water at 25 °C are 890 and 280 ppm, respectively

(256); the appreciable water-solubility of 2,4-D makes derivatization necessary

prior to analysis.

Studies with humans who have ingested 2,4-D indicated that the herbicide is

first found in the blood plasma, whereupon it is excreted into the urine at a rate dependent on the concentration in the blood (257-259). The intake of

2,4-D, 2,4,5-T, Silvex, or Dicamba can be through inhalation, absorption through

the skin C260-262), or other exposure C263); the herbicides are known to have

relatively short half-lives of retention (244,264,265) and are excreted largely

unmetabolized in urine within 24--48 h (53,266-268); the pesticide chloropyrifos

,

however, metabolizes in human urine. It is known that 97 percent of any absorbed

2,4,5-T is excreted within seven days (269). Trichlorophenol , a known metabolite

of pentachlorophenol (PCP), is also a probable metabolite of 2,4,5-T and other

trichlorophenoxy acid herbicides (269,270); however, this assumption needs

experimental verification.

The rapid elimination of 2,4-D has been attributed to renal, proximaltubular secretion (244,271). For this reason, urinalysis is useful qualitatively,

and quantitatively, for determining occupational and extraneous exposure to this

herbicide.

B. Toxicity of Pesticides

The "Atlas of Cancer Mortality" (272) provides the strongest evidence yet

available for the association of human cancer with environmental factors; human

mutagenicity may be associated with exposure to 1 ,2-dichloroethane (273) and

human fertility has recently been shown (274) to be adversely affected by

exposure to PCP, trichlorophenol, hexachlorobenzene, and many other toxic

substances

.

Various toxicological studies have been conducted with 2,4-D, 2,4,5-T, and

other herbicides and pesticides during the past twenty-five years (72,248,262,

275,276-279). A concerted effort has been made to minimize the level of an extremely toxic impurity, namely, 2,3,7,8-tetrachlorodibenzo-£-dioxin (TCDD), in

commercial 2,4,5-T (245). The herbicide 2,4,5-T currently contains less than

0.01 ppm of TCDD (280). The extreme toxicity of 2,3,7,8-TCDD necessitates

monitoring for it at parts per trillion ( 10" ^2 g/g) levels ’in food (281).

The occupational exposure to polychlorinated dioxins and dibenzofurans has

recently been reviewed (282). The toxicity and metabolism of pesticides in

animals and humans is the subject of two recent reviews (72,283) and a recent

book (284). In his assessment of the toxicity of 2,4,5-T and related agricultural chemicals, the author of the review (283) suggested that the most useful

approach to re-evaluating the presumed, potential risks of these chemicals would

be a combined experimental and clinical study. Analysis for £-nitrophenol in

human urine is recommended for parathion; the tentative, toxic level for £-

nitrophenol is 100 yg/L; for organochlorine pesticides, the proposed toxic level

ranges (283) from 20 to 500 yg/100 mL. No profound effects on animals (261 ,262) or humans (278) have been observed on oral administration of small quantities

(3 mg/kg/day) of 2,4,5-T.

25
C. Toxic Substances in Human Urine

A three-year study to assess the exposure of the general population of the

United States to residues of selected pesticides and their specific metabolites

through analysis of human urine has been presented by Kutz ^ (71,72), and

is briefly summarized (72) in Tables 10--12. The multi-residue approach used

for analyzing the samples of human urine permitted the detection of the many

chemicals shown in Table 10; the pesticidal origins of these chemicals are also

presented. The results of the urine analyses for pesticide residues and metabolites are shown in Tables 11 and 12. Among the pesticides detected,

pentachlorophenol (POP) is ubiquitous, as it has been found in 85 percent of

the urine samples analyzed (maximum concentration, 193.0 ppb) (see Table 11).

The next most-abundant phenolic residue in human urine is £-ni trophenol

(113.0 ppb), followed by the metabolite 3 ,5,6-trichloro-2-pyridinol (31.7 ppb)

and 2,4,5-trichlorophenol (32.4 ppb); very little Silvex (3.2 ppb) and only

traces of 2,4-D and 2,4,5-T were found (Table 11). The most abundant dialkyl

phosphate residues in human urine were such metabolites of parathion as diethyl

phosphothionate (DETP) (900 ppb) and diethyl phosphate (DEP) (420 ppb), followed

by dimethyl phosphothionate (DMTP) (360 ppb) (see Table 12). The herbicides

2,4-D, 2,4,5-T, Silvex, and Dicamba are not found in human urine but the pesticide chloropyrifos is metabolized to yield 3 ,5,6-trichloro-2-pyridinol

.

Table 10: List of Chemicals Detectable in Human Urine, and Their Pesticide Origin

Chemical Pesticidal Origin

(Multi phenol Method)

£-Ni trophenol

2,4-D

2,4,5-T

Si 1 vex

3 ,5,6-Trichl oro-2-pyridi nol

Pentachlorophenol

(3,5,6-TC-2-P)

Pentachlorophenol, lindane,

and hexachlorobenzene

Methyl- and ethyl -parathion

2,4-D

2,4,5-T

Sil vex Chloropyrifos

2,4,5-Trichlorophenol 2 ,4 ,5-Trichlorophenol , metabolite

of certain organochlorine

i nsecticides

Dicamba Dicamba

(Dialkyl Phosphate Method)

Dimethyl phosphate (DMP)

Diethyl phosphate (DEP)

Dimethyl phosphorothionate (DMTP)

Diethyl phosphorothionate (DETP)

Dimethyl phosphorodithionate (DMDTP)

Diethyl phosphorodithionate (DEDTP)

Any organophosphorus insecticide

containing these phosphates or thiophosphates
Table 11: Occurrence of Pesticide-related, Phenolic Residues in Human Urine^

Residue^ Percent

positive

Arithmetical

mean (ppb)

Maximum

value (ppb)

Pentachlorophenol 84.8 6.3 193.0

3,5,6-TC-2-P 16.1 <5.0 31 .7

2,4,5-TCP ' 1.7 <5.0 32.4

£-Nitrophenol 1 .7 <10.0 113.0

Si 1 vex 0.2 <5.0 3.2

2,4-D 0 - trace

2,4,5-T 0 - trace

Dicamba 0 - -

^Based on the analysis of 416--418 samples collected from the general

population via the Health and Nutritional Examination Survey II,

National Center for Health Statistics.

*^Limits of detection range from 5 to 30 ppb (5 to 30 ug/L)

.

Table 12: Occurrence of Dialkyl Phosphate Residues in Human Urine^

Dial kyl. phosphate

residue^

Percent

positive

Arithmetical

mean (ppb)

Maximum

value (ppb)

Dimethyl phosphate (DMP) 11.5 <20 80

Diethyl phosphate (DEP) 7.9 <20 420

Dimethyl phosphothionate 6.5 <20 360

(DMTP)

Diethyl phosphothionate 10.8 <20 900

(DETP)

Dimethyl phosphodi thionate 0 — trace

(DEDTP)

Diethyl phosphodithionate 0.2 <20 20

^Based on the analysis of 418 samples collected from the general population

via the Health and Nutritional Examination Survey II, National Center for

Health Statistics

.

^Limit of detection for all residues = 20 ppb (20 yg/L)

27
D. Pharmacology and Metabolism of Silvex, Dicamba, and Related Pesticides

The fate of Silvex [2-(2,4,5-trichlorophenoxy)propanoic acid] was studied in seven men and one woman following oral administration of 1 mg/kg, and

no adverse effects were observed (285). Recovery of Silvex and its conjugates

in the urine through 168 h ranged from 66.6 to 95.1 percent of the dose administered, with a mean value and relative standard deviation of 80.3 ±10.5 percent.

In humans, Silvex is readily absorbed after ingestion, and is subsequently

readily excreted, predominantly via the urine (285).

The fate of 2,4,5-T following oral administration to humans has been reported

(286); similar pharmacokinetic studies using ^'^C-ring-label ed 2,4,5-T were conducted with other animals (287-291).

The pharmacokinetic data obtained with ^'^C-ring-label ed Silvex indicated

that a statistical projection of experimental results on large doses of Silvex

to attempt to predict the hazard of exposure to small doses is most certainly

not justified, because the capability to excrete Silvex in the urine becomes

saturated. Urinary excretion of Silvex is saturated at the 50 mg/kg dose level

(292).

The metabolic fate of ^‘^C-ring-label ed Dicamba (3,6-dichloro-2-methoxybenzoic acid) in animals has been reported (293). Following oral administration,

the ^‘^C-labeled Dicamba was readily absorbed, but only partially metabolized.

Within six hours after the final dose of Dicamba, ^^^89 percent had been excreted

in the urine. The major metabolite was 3,6-dichloro-2-hydroxybenzoic acid

(DCHBA). Minor metabolites identified in the urine were 2 ,5-dichl orophenol and

the D-gl ucuronide conjugate of DCHBA. The fate of Dicamba has been studied in

various components of the environment, including soils (294,295), plants (296-

298), animals (293,299,300), and aquatic environment (293b).

Oral administration of 2,4-D, 2,4,5-T, or PCP to rats did not cause

abnormal accumulation of porphyrin ( e.g . , porphyrobilinogen) in the urine (301,

302), liver, or kidney (302), as observed for pentachloro- (303) or hexachlorobenzene (301). Similarly, 2 ,4,5-trichlorophenol (301 ,304), a metabolite of

2,4,5-T (305), did not effect any increase in total porphyrins in urine.

E. Trace Analyses of Pesticides: 2,4-D, 2,4,5-T, Silvex, Dicamba , and Others (General Overview)

For reliable assessment of human exposure to pesticides, and other toxic

pollutants, analytical methods having a high degree of accuracy are required.

In recent years, techniques have been developed to measure external exposure to

pesticides in the urine; thin-layer chromatography, electron capture detectors

for EC-GC, and, in some cases, gas chromatography—mass spectrometry are employed

as confirmatory, analytical techniques.

Sample preparation is a very important factor for accurate analytical,

trace analysis (281); the sample must be representative of the batch of material

from which it was taken. Losses caused by absorption onto container surfaces,

evaporation, thermal decomposition, or exposure to light can often be great

enough to invalidate the results (306).

28
Solvent extraction is seldom specific for the analyte, and traces of

impurities are often introduced from the solvent itself (281). There have been some recent improvements in the methodology of isolation and concentration; the use of organophilic resins, e.g. , Amberlite XAD-2 and Tenax is noteworthy (306-

308). The procedure for removing pesticides from urine with XAD-2 resin is

rapid, requires no complex clean-up, and appears satisfactory for the extraction,

and analysis (as methyl esters) of 2,4-D (and related herbicides) at the 0.1-ppm

level in urine (269,309,310). Because 2,4,5-T, Silvex, and Dicamba are structurally quite similar to 2,4-D, and as they are largely unmetabolized in urine,

the same technique can be used for their extraction and analysis.

There is a wide choice of pesticide-residue derivatives (311-313) and

chemical derivatization methods (313,314) for chromatography, but only those

capable of working efficiently on the microscale are acceptable. In view of the

increased sensitivity of GC with electron-capture detection, (pentafluorophenyl )-

methyl derivatives of acid herbicides have gained in importance, and have been

applied in various fields (315-319).

Recently, DeBeer ^ al_. (320) and Van Peteghem and Heyndrickx (312,322)

reported a highly sensitive GC method, with mass-fragmentographic detection, for

the quantitative determination of traces of 2,4-D in urine, using the . trideuterated-methyl ester of 2,4-D as the internal standard. For the herbicides

studied, e.g. , 2,4-D and 2,4-DP [2-(2,4-dichlorophenoxy)propanoic acid], calibration curves in the nanogram range were established.

One of the main problems in pesticide-residue analysis is confirmation of

the identity of the residue in the sample. This is essential and particularly

difficult when no background information about the sample is available. Mass

spectrometry and GC-MS are often the only techniques having a sensitivity

sufficient for trace-analytical study. Modern, rapid-scanning, mass spectrometry,

with on-line, computerized, data acquisition and processing, facilitates the

collection of several thousand spectra during GC-MS analysis. These data can be

further processed (mass-resolved chromatography), or be presented as a chromatographic profile, by using a particular ion or any selection of ions in the

spectrum of complex mixtures (mass chromatography).

Modern methodology for organic trace-analysis provides many new techniques

using spectrophotometry, paper- and thin-layer chromatography, and gas-liquid

chromatography, combined with microcoulometric , flame-ionization, or electroncapture detection. Typical extracts submitted for analysis may require further

purification in order to ensure that the compound of interest is free from

substances that could cause chemical interference with its quantitative estimation. General-purpose detectors are invaluable in dealing with mixtures of

unknown, volatile compounds, and the flame-ionization detector (FID) for GC has

been extensively used in trace pesticide and food analyses. It is now possible

to detect low-picogram quantities of 2, 6-dimethyl phenol with a FID (281).

The new improvements in GC methodology include the use of fused-silica

columns (323,324), new capillary-column injector-design (325,326), the use of

specific detectors (photoionization and ultrasonic), and IR-UV spectroscopic

detectors, and also the use of mixed stationary phases.

29
The recently introduced negative-ion, chemical ionization [NICI), mass spectrometry (327-329) for quantitative estimation of electron-capturing

compounds ( e.g . , toxic polychlorinated organics and pesticides (30,31 ,62,64,

330,331) offers unsurpassed sensitivity, and considerable selectivity. A

recent application of negative-ion, atmospheric-pressure ionization (NIAPI), mass spectrometry for trace analysis offers a sensitive technique for determination

of pesticides ( e.g ., 2,4,5-T) in blood and urine. The method gives quantitative

data that differ to within only a few percent of the mean, for samples in the

50--100-pg range (332). The most selective detector is the thermal -energy

analyzer (TEA) (333).

Modern methodology for trace analysis also includes liquid chromatography

(LC) with UV detectors; (the technique is, however, much less sensitive than

FID used in GC (334) liquid chromatography--mass spectrometry (LC-MS) (335);

the use of a microbore column (336); also, chromatography with a mass spectrometer as the detector (selected ion-monitoring) (337); chemical ionization (338,

339); metastable-ion, mass spectrometry (340), e.g. , mass-analyzed, ion,

kinetic-energy spectrometry (341), and immunological assays (342,343) as an alternative to mass spectrometry.

F. Additional Recent Results on Analysis of Pesticides

A multiresidue procedure for the determination, and confirmation, of a variety of acidic herbicide residues in human urine has recently been described

by Draper (344). 2,4-D, 2,4,5-T, Silvex, Dicamba, POP, and others were determined

simultaneously with a high degree of quantitative accuracy, precision, and

sensitivity. Samples were hydrolyzed with mineral acid in order to liberate the

residues from conjugates. Acids were isolated from the urine hydrolyzate by

acid--base partitioning, and derivatized with ethereal diazomethane. Pesticides

were determined quantitatively by EC-GC, and structures were confirmed by

computer-controlled GC-MS. Recoveries were 80—104 percent for fortifications

at 0.1 mg/L, and detection limits for herbicides in urine were 0.05--0.1 mg/L by

EC-GC, and 0.1— 0.5 mg/L by GC-MS. Methylation of urinary extracts was found

superior (344) to (pentafl uorophenyl )methylation (318). Derivatization with

(pentafl uorophenyl )methyl bromide (PFB) was unacceptable for several reasons: it

enhanced the electron-capture response of urinary acid herbicides, and the

specific detection of PFB analogs by mass spectrometry was limited by the

similarity of their electron-impact, mass spectra. Exposure of forest workers

to 2,4-D was carefully monitored; human exposure-levels in these tests were

below that which might endanger health (23.7--57 ug/kg of body weight) (345.),,

The lowest detectable concentration of 2,4-D and 2,4,5-T in human urine was '(346)

0.05 mg/mL. Mass-fragmentographic determination of 2,4-D in human urine, using

deuterated, internal standards, has been discussed (320). Separation and

identification of 2,4-D (347) and other chlorinated pesticides (348) in urine

by thin-layer chromatography have been described. The authoritative, recent

book by Lawrence (348a) deals with the application of HPLC to the analysis of

pesticides, e.g. , fungicides, herbicides, plant growth regulators, and rodenticides.

30
i VII. PHTHALATE ESTERS (PLASTICIZERS) IN HUMAN URINE

A. General

Esters of phthalic acid are widely used as industrial solvents and plasticizers in the manufacture of a variety of plastic formulations. The use and

production of phthalic ester plasticizers, e.g. , bis (2-ethyl hexyl ) phthalate

(DEHP), bi s (2-ethyl hexyl ) adipate (DEHA) and diethyl (DEP) or di butyl (DBP)-

phthalate have been steadily increasing over the past two decades. The total

annual production has reached nearly 5 x 10® kg and continues to increase

(349-353). The plasticizer industry predicts future yearly increases of 6

percent in plasticizer production in the 1980's (354).

The most widely used plastic in medical devices is poly(vinyl chloride)

(PVC). To make the rigid PVC more flexible, plasticizers are added. These

plasticizers may contribute up to 40 percent by weight of the finished product

(355,356). DEHP is the plasticizer most commonly used in medical devices.

The main use of diethyl phthalate (DEP) as a plasticizer is in the production of cellulose acetate films, which may contain up to 20 percent of the

finished product. In addition, it is used extensively as a denaturant for

cosmetic alcohol and in hair-spray preparations (357).

The plasticizer DEHP has achieved increased interest; together with other

phthalate esters, it constitutes a new class of environmental pollutants (349,

357,358). Over one-fourth of the total production of plasticizers in 1972 was accounted for by DEHP. In addition to animal and human urine (350,351), DEHP

has been found in commercial solvents (359), the organic matter of soil (360),

water (361), marine water (349), ocean sediment (349,353), fish (362), fatty

foods taken from plastic packages (363), automobile atmospheres (364), milk

(365), rice meal, herbs, instant coffee, and cocoa (366), and human blood

(367-370). Phthalate ester plasticizers were found to be extracted by blood

from plastic tubing and from the plastic bags used for blood storage (368);

the plasticizers were found in patients who had received extensive blood transfusions (368,371 ). Plasticizers were also found in human plasma (372),

platelet concentrations (373), and human tissue (374,375). There are reports

that phthalates are formed during the thermal oxidation of cooking oils (376),

and there is even some evidence that indicates that they occur naturally as a result of biosynthesis (377,378). A recent report (349) indicates a high

level of phthalate esters in the water near the Gulf of Mexico (->^100 ng/L), but

a relatively low level in fish samples ('^^5 ng/g). This can be interpreted as the possible consequence of metabolism and excretion by the fish, and warrants

monitoring for phthalate metabolites, as well as for the parent compounds.

The leaching of phthalates from hemodialysis equipment was demonstrated,

and its implication in the production of hepatitis in blood-transfusion patients

has been considered (356,379-381).

31
B . Toxicity of Phthalate Esters

Autian (356) reviewed the toxicology of the phthalate plasticizers in

animals and in cell culture. Phthalate esters have been reported to have a low

order of toxicity (356,382-390) and a weak teratogenic effect (391-393) in

experimental animals. However, Guess £t al_. (394) emphasized the subtle toxic

effects of phthalate ester plasticizers. Recent results (395) suggest that the

effects of phthalate esters ( e .g . , DEP) arise from the toxicity of their

metabol i tes

.

Diethyl phthalate (DEP) has been shown to be toxic to cells in culture

systems, and to be teratogenic in the chick embryo (396) and rat (391), and,

when it is added (5 percent) to the diets of male rats, it causes an increase

in the liver weight (357). Further studies are required in this area of subtle

toxic effects, possilDly associated with accumulation and metabolism of phthalate

esters (389).

a . Toxicity of DEHP

The extensive use of polyvinyl -stored blood and blood-products during the

past decade has failed to reveal any definitive adverse effects in humans of

such storage. The results presented by Rubin and Schiffer (355) and Wallin

et £I_. (387) indicate rapid clearance of DEHP from blood, and extensive urinary

excretion within 24 hours; this may be seen from Table 13.

Table 13: Urinary Excretion of DEHP (355)

24-hr DEHP excretion

(mg DEHP equivalents)

Patient #

Total DEHP

received (mg)

Pretransfusion

Posttransfusion

Max. excreted

(%)

3 62.2 9.0^ 55.9^ 90

4 67.8 13.8 40.0 60^’^

12-hour collection immediately prior to transfusion: 1250 ml of urine.

°Not a complete 24-hour collection, but does contain all of the urine excreted

during the first 8 hours, and most of the urine excreted during the subsequent

16 hours: 1650 ml of urine.

^The urinary data indicate that a major portion of the DEHP administered is

excreted within 24 hours, although determination of the exact quantitative

portion is complicated by the pretransfusion excretion of significant amounts

of DEHP-related material.

*^The assay procedure used for the urine samples does not distinguish between

unchanged DEHP and phthalic acid-containing metabolites.

32
Thus, the results (355,397) do not support any concern that the transfusion

of blood stored in polyCvinyl chloride) blood-bags leads to deposition of the

plasticizer, DEHP, in the tissues of man. However, these facts should not

diminish the concern for any possible adverse biological effects of acute or chronic exposure to this compound, particularly when one considers that patients

in a wide array of debilitated states receive transfusions of blood and blood

products. The authors (355) advocated the development of alternative plastic

formulations that do not result in appreciable migration of any chemical con- stituents. DEHP has been shown to be detrimental to the reproduction of marine

organisms at parts per billion (,ppb) levels in water (398). Studies recently

reported by the National Toxicology Program identified DEHP and bi s( 2-ethyl hexyl

)

adipate (DEHA), as hepatocarci nogens in mice (399).

C. Metabolism of Phthalate Esters

a. General

The leaching of DEHP by blood but not by simple salt solutions (368), from

plastic transfusion bags (369) and medical -grade hemodialysis tubings (400) has

been demonstrated. Lewis ^

(401 ) (401 ) reported that 6.1 mg of DEHP was leached into blood in 1 hr in patients undergoing hemodialysis therapy. Later,

Chen et (402) found that the 24-hr urinary DEHP concentrations of postdialysis urines range from 0.9 to 2.6 percent of the total 6.1 mg of DEHP that

migrated from the hemodialysis system. The low concentrations of DEHP excreted

in the urine suggest that DEHP leached into patients during hemodialysis treatments could be taken up by tissues or be metabolized. (Compare Table 13.) The

detection limit of DEHP in urine is C402) 15 ng/mL. Lewis ^

(401) also

reported that most of the DEHP present in serum at the completion of hemodialysis

will disappear in 5 to 7 hours. The foregoing data thus amplify existing knowledge concerning the metabolic disposition of DEHP, and reinforce the current

opinion that the use of this material does not pose an imminent threat to human

heal th

.

b. Metabolism of DEHP

Shaffer et (382) reported for the first time on metabolic studies of

DEHP in man and rabbits as early as 1945. However, knowledge concerning the

metabolic aspects of DEHP remained scanty until detailed metabolic studies were

made in 1972.

Papers on the metabolism of DEHP published since 1972 by many workers (368,

403-410) describe in detail the elimination, distribution, urinary metabolites,

and hydrolysis of DEHP, in many cases (403-405,411) with respect to experimental

animals. Five urinary metabolites of DEHP, including mono (2-ethyl hexyl ) phthalate

(MEHP) and phthalic acid were confirmed (403,406); another report demonstrated

the presence of seven (397), and more-recent findings (412) even nine, metabolites of DEHP. As shown by A1 bro ^

£l_. (406) and by Daniel and Bratt (403),

DEHP following oral administration is rapidly hydrolyzed to the half-ester,

MEHP, by pancreatic lipase; the principal metabolites being identified as the

acid, alcohol, and ketone resulting from the sequential w- and (w-l )-oxidation

of MEHP. The alcohols can be further oxidized to the corresponding carboxylic

acid or ketone and the keto-acid may subsequently be subject to B-oxidation.

33
Human leukemia patients were recently reported (404,405) to excrete 80

percent of their DEHP metabolites in urine as D-gl ucuronide conjugates; in the

24-hr urine of these patients, MEHP was a significant metabolite (20 percent);

alcoholic metabolites amounted to >60 percent and diacids constituted only

'^'9 percent of the total

.

Elimination, distribution, and metabolism of DEPH in animals were also

studied by the tracer technique, using [^‘Cjcarbonyl DEHP (387,403,410). Of the

dose, ''^O percent was excreted in the urine in 5 to 7 days following intravenous

or oral administration; the [^‘*C]DEHP was preferentially localized in the liver

for a short time (387,403,406). The transformation of DEHP into certain

metabolites in aquatic organisms has been reported (413-415).

c. Metabolism of related phthalate esters

The urinary metabolites following oral administration of dimethyl (416),

dibutyl (416,417), or dioctyl (416) phthalates have been reported. When administered into the stomach, most of the diethyl phthalate (DEP) and dibutyl phthalate

CDBP) was metabolized to monoester and phthalic acid, and these were rapidly

excreted in the urine (395). Exposure of rats to DBP aerosols (concentration

50 mg/m^, 6 hours daily for 6 months) has also been examined (392); the results

suggest that the adverse effects of phthalate esters arise from their accumulation in the brain. The in vivo metabolism of dialkyl phthalates has been

studied extensively (356.357.406,410).

D. Determination of Plasticizers in Human Urine

The methods applied for the determination of phthalate esters in human and

animal urine involve an array of techniques, including GC, LC, GC-MS, and com- puterized mass spectrometry. Recent analytical methodology and techniques have

been comprehensively reviewed by Risby ^al_. (418) (GC), Majors ^al_. (419)

(LC), and Burl ingame ^ al . (420) (GC-MS and GC-MS-on-1 ine computer techniques).

a . GC methods

The original GC method of Piechocki ejt (372) for the determination of

DEHP in human plasma (limit of detection, 50 ng of DEHP) has been widely applied

for the analysis of phthalates in urine. In a typical procedure (421), DEHP

and all phthalic acid-containing metabolic intermediates of DEHP in the urine were hydrolyzed to phthalic acid by the method of Shaffer ^ (422) as previously described (374). Following methylation with diazomethane, the

phthalic acid content was determined by GC (of the dimethyl phthalate formed) in

a 6 ft column of 3 percent SE-30 using a flame-ionization detector. Hexadecane

(Cie) was used as the internal standard for quantitation. Other GC methods

(355,402), or a combination of GC, t.l.c., and spectroscopy techniques (406)

for analysis of phthalates in urine have been described. Recently, Peterson

and Freeman (353) have reported a highly sensitive and selective GC-MS analytical

scheme (423) for the analysis of phthalate esters ( e.g . , DEHP) found in dated

sediment cores of the Chesapeake Bay. The GC-MS method (395,405,406,416) thus

proved to be efficient for the quantitative analysis of phthalate esters and

their metabolites in urine.

34 I'
b. LC methods

Recently, Draviam ^

(424) developed a method for the separation and

quantitation of plasticizers ( e.g . , DEHP) and their metabolites from human urine

using liquid chromatography (LC) . Urine was diluted with an equal volume of

water, and extracted at pH 2 with diethyl ether. The extract was dried, the

solvent vacuum-stripped, and the residue dissolved in methanol for injection

into the chromatograph. A reversed-phase column containing 10-um particles

was used for the analysis. Ionic suppression, 0.5 percent acetic acid in water,

at pH 3 was used to resolve the acidic components. A step gradient of

acetonitrile--water (containing acetic acid) was used to elute the polar metabolites

as well as the nonpolar plasticizers. Mass spectrometry was used to identify

the compounds in the LC fractions. From the LC fractions of the urine extract

phthalic acid, MEHP, DEHP, and normal urinary constituents ( e.g . , hippuric and

benzoic acid derivatives) were identified. The detection limits (at a wavelength of 245 nm) for a reference mixture of phthalic acid and phthalate esters

are listed in (424) Table 14.

Table 14: Detection Limits for Phthalate Esters^

Compound Detection limits (yg/mL)

Phthalic acid 2.7

Monomethyl phthalate 1.5

Monobutyryl phthalate 3.3

Monobutyl phthalate 1 .6

Mono (2-ethyl hexyl ) phthalate 2.1

Butyl benzoyl phthalate 2.0

Bi s (2-ethyl hexyl ) phthalate (DEHP) 1.4

^LC, UV detector at 245 nm.

c. Recent LC-MS methods

Recently, Harvan ^

(412) discussed, and compared, the electron impact

(El), methane-positive chemical ionization (MPCI), oxygen-negative chemical

ionization (ONCI), and collision-induced dissociation, mass-analyzed, ion

kinetic energy (CID-MIKE) spectra (208,414,425,426) of the nine metabolites of

DEHP isolated from rat urine. The metabolites were methylated with diazomethane,

and fractions were purified by LC on a Porasil A-60 column using a tetrahydrofuran—hexane gradient (prefractionation is necessary).

35
The DI mass spectra of all metabolites of DEHP are very similar, so that

little specific structural information is afforded by this technique. The MPCI

and ONCI techniques give similar information, in that the mass of the side-chain

can be deduced in each case from the respective mass spectrum. However, the

data are complementary in the sense that information gained by the observation

of the loss of a fragment in one case is usually available by formation of that

ion in the other; this is exemplified by the formation of the side-chain ion in

the ONCI spectra. Thus, either method of ionization can be used as a check on the other. This is further illustrated by the ion--molecul e reaction-product

ions observed in the case of the hydroxyl metabolites. The presence of the

hydroxyl group is indicated by the [MH-H 2 O] ions observed in the MPCI spectra,

and is supported by the [M + O 2 ]" ions found in the ONCI experiment.

The CID--MIKE spectra demonstrated the potential of this technique as a versatile and specific detection-system. Although the El, MPCI, and ONCI mass spectra of the two isomeric tri -esters [ e.g . , 1, 2-dial kyl esters of 3-alkyl-ophthalic acid, metabolites of DEHP) (406) were similar, their MIKE spectra were

different. This enables the use of single reaction monitoring, e.g

.

, the

monitoring of a particular fragment-ion generated from a specific parent-ion and

application of this information for determination of the structure. The MIKE

spectra were thus used to assign the structure for four new, including three

hydroxylated , metabolites of DEHP (412). The other methods used for analysis

involve the radio-assay of ^‘^C-labeled DEHP (and metabolites) in urine, followed

separation by t.l.c. (387,389,427).

Acknowl edgment

The author thanks Dr. Robert Purcell, the National In-stitutes of Health,

for the valuable information on handling of urine samples. The author also

thanks the Environmental Protection Agency for the financial support of this

project (Interagency Agreement No. ADI 3-F-1-467-0)

.

36
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Washington, D.C., 1978, Chapter 4.

426. E. Soletero-Riqau, T. L. Kruger and R. G. Cooks, Anal. Chem., 49, 435

0977).

427. B. G. Lake, P. G. Brantom, S. D. Gangolli, K. R. Butterworth, and

P. Grasso, Toxicology , 341-356 (1976).

60
NBS»114A (REV. 2«eo) U.S. DEPT. OF COMM.

BIBLIOGRAPHIC DATA

1 .

SHEET (See instructions)

PUBLICATION OR

REPORT NO.

NBSIR 83-2690

2. Performing Organ. Report NoJ 3. Publication Date

June 1983

4. TITLE AND SUBTITLE

Priority Toxic Pollutants in Human Urine: Their Occurrence and Analysis

5. AUTHOR(S)

A. J. Fatiadi

6. PERFORMING ORGANIZATION (If joint or other than NBS, see instructions) 7. Contract/Grant No. national bureau of standards

DEPARTMENT OF COMMERCE 8. Type of Report & Period Covered

WASHINGTON, O.C. 20234

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

NBS/Environmental Monitoring Systems Laboratory, U.S. Environmental Protection

Agency, Las Vegas, NV 89114

10. SUPPLEMENTARY NOTES

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

II. ABSTRACT (A lOO-yvord or less factual summary of most significant information, if document includes a significant

bibliography or iiterature survey, mention it here)

This survey reviews and discusses the occurrence of priority pesticides and

industrial chemicals in human urine. An overview of some recent analytical

methodology for determination of selected toxic pollutants and their metabolites

as they are found in human urine is also presented. The review includes 427

references.

12. KEY WORDS (Six to twelve entries; aiphabetical order; capitalize oniy proper names; and separote key words by semicolons)

chemicals; exposure; human; industrial; methodology; pollutants; survey; toxic;

urine.

13. AVAILABILITY

nn Unlimited

14. NO. OF

PRINTED PAGES

1 1 For Official Distribution. Do Not Release to NTIS

1 1 Order From Superintendent of Documents, U.S. Government Printing Office, Washington, D.C.

20402.

63

15. Price

1 XI Order From National Technical Information Service (NTIS), Springfield, VA. 22161

$10.00

I

I

‘IRl
1iII