Levels of Seven Urinary Phthalate Metabolites in a Human Reference Population.

Using a novel and highly selective technique, we measured monoester metabolites of seven commonly used phthalates in urine samples from a reference population of 289 adult humans. This analytical approach allowed us to directly measure the individual phthalate metabolites responsible for the animal reproductive and developmental toxicity while avoiding contamination from the ubiquitous parent compounds. The monoesters with the highest urinary levels found were monoethyl phthalate (95th percentile, 3,750 ppb, 2,610 [micro]g/g creatinine), monobutyl phthalate (95th percentile, 294 ppb, 162 [micro]g/g creatinine), and monobenzyl phthalate (95th percentile, 137 ppb, 92 [micro]g/g creatinine), reflecting exposure to diethyl phthalate, dibutyl phthalate, and benzyl butyl phthalate. Women of reproductive age (20-40 years) were found to have significantly higher levels of monobutyl phthalate, a reproductive and developmental toxicant in rodents, than other age/gender groups (p [is less than] 0.005). Current scientific and regulatory attention on phthalates has focused almost exclusively on health risks from exposure to only two phthalates, di-(2-ethylhexyl) phthalate and di-isononyl phthalate. Our findings strongly suggest that health-risk assessments for phthalate exposure in humans should include diethyl, dibutyl, and benzyl butyl phthalates.

Key words: exposure, glucuronidase, human, metabolism, phthalates, urine. Environ Health Perspect 108:979-982 (2000). [Online 1 September 2000]

http://ehpnet1.niehs.nih.gov/docs/2000/108p972-982blount/abstract.html

Dialkyl or alkyl aryl esters of 1,2-benzenedi-carboxylic acid, commonly called phthalates, are ubiquitous industrial chemicals with a wide range of chemical and toxicologic characteristics. Phthalates are used primarily as plasticizers in flexible polyvinyl chloride (PVC) products such as blood bags and children's toys. Nonpolymeric uses of phthalates as fixatives, detergents, lubricating oils, and solvents lead to their inclusion in numerous and diverse products such as cosmetics and wood finishes. The widespread use of phthalates results in multiple human exposure routes (oral, dermal, inhalation, and intravenous). Phthalates are lipophilic compounds that appear not to bioaccumulate (1). Phthalates are rapidly metabolized to their respective monoesters and further oxidative products, which are glucuronidated and excreted through the urine and feces (1-4).

Animal toxicology of several phthalates has been studied. Di-(2-ethylhexyl) phthalate (DEHP) is a rodent liver carcinogen through a mechanism thought to involve peroxisome proliferation (5); however, carcinogenicity by this mechanism is unlikely to be relevant to humans (6,7). Several phthalates, DEHP, dibutyl phthalate (DBP), and benzyl butyl phthalate (BzBP), are teratogenic in animals (8-10). DBP is also toxic to the testes, possibly through its metabolite, monobutyl phthalate (MBP) (11,12); other phthalate metabolites, monobenzyl phthalate (MBzP) and mono-2-ethylhexyl phthalate (MEHP), are Sertoli cell toxicants and teratogens in animals (13,14). Furthermore, administration of DBP and DEHP to pregnant rats interferes with normal fetal development in male offspring (15). Regarding reproductive and developmental effects, phthalates vary in potency, with DEHP being the most potent and DBP and BzBP roughly an order of magnitude less potent (8-15).

Based on the varied toxicities of phthalates, internal dose measurements of specific phthalates and their monoester metabolites (16) are important for exposure assessment, and ultimately for accurate human risk assessment. Previous methods for assessing human exposure to phthalates have been subject to laboratory and sample-collection contamination problems from these environmentally ubiquitous compounds (17-20). For this reason, previous measurements of internal phthalate dose have focused on highly exposed people (21,22). As the primary urinary metabolite, phthalate monoesters are useful biomarkers of specific phthalate exposure.

We report the urinary phthalate monoester levels for a human reference population using a new, highly selective technique (23). This analytical approach allows us to directly measure the individual phthalate metabolites responsible for the reproductive and developmental toxicity of phthalates in animals while avoiding contamination from the ubiquitous parent compound. The metabolites measured are monoethyl phthalate (MEP), MBP, MBzP, mono-n-octyl phthalate, MEHP, and mono-3-methyl-5-dimethylhexyl phthalate (monoisononyl, MINP). Commercially used di-isononyl phthalate (DINP) is a technical mixture containing a number of different isomers; therefore, several metabolite isomers are expected. We chose the monoester metabolite of one representative isomer for DINP. Measurement of this single isomer may underestimate exposure to DINP. Current efforts are focused on quantification of additional metabolites of DINP.

Subjects

The urine samples for this study were originally collected from adults during 1988-1994 as part of the Third National Health and Nutrition Examination Survey (NHANES III). Randomly selected urine samples from 289 subjects were analyzed for phthalate monoesters. Urine samples were collected at different times throughout the day and were not first-morning voids. This sampling of the NHANES III population was not designed to be representative of the U.S. population but rather to serve as a reference range for a demographically described group. The population studied comprised noninstitutionalized adults aged 20-60 years (mean [+ or -] SD 37.4 [+ or -] 10.6 years). The gender distribution (56% female) was similar across age groups. Racial distribution was weighted toward minority groups (Caucasian 39%, African American 30%, Mexican American 23%, and other 8%).

Methods

The method used has been described previously (23). All samples were spiked with 13[C.sub.4]-labeled phthalate monoesters and 4-methylumbelliferone glucuronide. The samples were then treated with a [Beta]-glucuronidase to release the phthalate monoesters from its conjugated form. Deconjugated urine samples were extracted twice with Oasis HLB SPE (Waters Corp., Milford, MA) as described (23) and resuspended in mobile phase. Chromatographic separation by HPLC was followed with tandem mass spectrometry on a triple quadrupole instrument (Finnigan TSQ 7000; Finnigan MAT, San Jose, CA) using atmospheric pressure chemical ionization. Retention times as well as parent-fragment ion combinations have been described previously (23). Levels of 4-methylumbelliferone were monitored as quality control for the deconjugation step. Urinary creatinine was measured with an ASTRA analyzer (Beckman, Brea, CA) based on a Jaffe rate reaction, in which creatinine reacts with picrate in an alkaline solution to form a red creatinine-picrate complex (24). Results are reported as micrograms phthalate monoester per gram of urinary creatinine. Creatinine adjustment is used to correct for variations in urine volume. Method blanks, quality control samples (spiked human urine), and standards were analyzed along with unknown human urine samples.

This method has been refined to monitor and eliminate monoester contamination by excluding the use of phthalate-containing plastics, prescreening reagents, and labware, and routinely monitoring method and instrument blanks. Phthalate diesters are often components of flexible PVC plastics. Therefore, products containing this polymer were not used. Although the polypropylene and glass components used were unlikely to contain significant amounts of phthalates, we prescreened representative vials, pipette tips, glassware, and sampling cups for phthalate monoester contamination. As an additional precaution, method blanks were analyzed in parallel with unknown samples. Insignificant phthalate monoester levels were found in blanks (typically [is less than] 0.5% of the mean level found in human samples). A blank containing [is greater than] 5 ppb of any analyte resulted in rejection of all analytical results acquired on that day and an effort to identify the source of the contamination.

One source of contamination that had to be eliminated was diester lipase activity in the glucuronidase enzyme preparation (23). We enzyme-treated artificial urine samples (25) with and without spiked phthalate diesters to determine if the presence of phthalate diesters would cause an artifactual increase in phthalate monoester levels. When samples spiked with phthalate diesters were incubated with [Beta]-glucuronidase/sulfatase (Helix pomatia, H-1), significant amounts of the corresponding phthalate monoesters were formed (MEP, MBP, MBzP, and MEHP). These enzymes, H. pomatia [Beta]-glucuronidase/sulfatase (from two vendors), were contaminated with an enzymatic activity that hydrolyzed phthalate diesters to generate phthalate monoesters; nonspecific lipases with this activity are common (26). Given the abundance of phthalate diesters in the environment (including the laboratory), the use of the H. pomatia [Beta]-glucuronidase/sulfatase should be avoided for analysis of phthalate monoesters. Escherichia coli [Beta]-glucuronidase (K12; Roche Biomedical, Indianapolis, IN) has excellent glucuronidase activity and no measurable lipase activity on phthalate diesters. Although this enzyme lacks sulfatase activity, no phthalate conjugates other than glucuronides have been detected in human urine (27). For previously published phthalate monoester measurements, H. pomatia [Beta]-glucuronidase/sulfatase was used; therefore artifactually high results may be present (3,22).

Results and Discussion

Our study provides an assessment of human exposure to phthalates. Phthalate monoester levels in human urine vary widely (Table 1); urinary creatinine adjustment reduces this variation somewhat (Table 2). In this reference population, the phthalate monoesters with the highest urinary levels found are MEP (16,200 ppb, 6,790 [micro]g/g creatinine), MBP (4,670 ppb, 2,760 [micro]g/g creatinine), and MBzP (1,020 ppb, 540 [micro]g/g creatinine), which reflect exposure to diethyl phthalate (DEP), DBP, and BzBP. DEP and DBP are used extensively in products with volatile components such as perfumes, nail polishes, and hair sprays, possibly leading to inhalation and efficient absorption through the lungs. Dermal absorption also occurs at a significant rate for phthalates with short side chains such as DEP, DBP, and BzBP (28).

Table 1. Total urinary phthalate monoester concentrations (nanograms monoester per milliliter urine).

                             Percentile

Phthalate        Min     5th    25th    50th

Ethyl          < LOD    26.1     119     305
Benzyl           1.4     4.2    11.0    21.2
Butyl            2.2     6.9    19.4    41.0
Cyclohexyl     < LOD   < LOD   < LOD   < LOD
2-Ethylhexyl   < LOD   < LOD     1.4     2.7
Isononyl       < LOD   < LOD   < LOD   < LOD
Octyl          < LOD   < LOD   < LOD   < LOD

                Percentile
                                        Geometric
Phthalate       75th    95th      Max     mean

Ethyl          1,110   3,750   16,200      345
Benzyl          42.2     137    1,020     22.6
Butyl           82.3     294    4,670     41.5
Cyclohexyl     < LOD     8.6     13.7      0.3
2-Ethylhexyl     7.0    21.5     66.6      3.5
Isononyl       < LOD     7.3     79.7      1.5
Octyl          < LOD     2.3     30.5      0.6

Abbreviations: LOD, limit of detection; Max, maximum; Min, minimum. LODs for phthalates (ng/mL) are as follows: MEP, 1.0; MBP, 0.6; MBzP, 0.8; monocyclohexyl phthalate, 0.7; MEHP, 1.2; MNP, 0.8; and mono-n-octyl phthalate, 0.9.

Table 2. Total urinary phthalate monoester concentrations (micrograms monoester per gram urinary creatinine).

                             Percentile

Phthalate        Min     5th    25th    50th

Ethyl          < LOD    30.2     133     280
Benzyl           2.1     5.0    10.8    19.5
Butyl            1.6     9.3    19.4    33.4
Cyclohexyl     < LOD   < LOD   < LOD   < LOD
2-Ethylhexyl   < LOD   < LOD     1.3     2.7
Isononyl       < LOD   < LOD   < LOD   < LOD
Octyl          < LOD   < LOD   < LOD   < LOD

                 Percentile
                                       Geometric
Phthalate       75th    95th     Max     mean

Ethyl            704   2,610   6,790      345
Benzyl          36.9    91.9     544     20.2
Butyl           60.1     162   2,760     36.9
Cyclohexyl       0.4     1.0    10.3      0.3
2-Ethylhexyl     5.2    15.2     192      3.0
Isononyl       < LOD     6.8    90.3      1.3
Octyl          < LOD     2.1    27.0      0.5

Abbreviations: LOD, limit of detection; Max, maximum; Min, minimum.

The highest levels of MEHP in this study (67 ppb, 192 [micro]g/g creatinine) agree with levels found previously in urine from occupationally exposed subjects (22). The median MEHP levels for this general reference population were 70-fold lower than the highest values. In urine, the more lipophilic phthalate monoesters, such as MEHP and MINP, were generally found at lower levels than other monoesters. The relatively low median MEHP and MINP levels suggest either low exposures to DEHP and DINP, storage in adipose tissue, or metabolism and excretion through another pathway. Limited data suggest that DEHP is partially excreted in the feces (1); because of similar lipophilicity, DINP may also be excreted fecally. Further complicating assessment, DINP consists of a mixture of phthalate isomers that yield a large number of monoester metabolites. Only one of these metabolites, mono-3-methyl-5-dimethylhexyl phthalate, was measured in urine and was assumed to be representative of the presence of other DINP metabolites. In any event, these data on monoesters indicate that the internal dose of MEP, MBP, and MBzP is probably much higher than that of MINP and MEHP.

Glucuronidation has been hypothesized to mitigate phthalate monoester toxicity in rodents (29). To assess the degree of phthalate monoester conjugation, we analyzed a subset of 73 samples with and without [Beta]-glucuronidase treatment. Low urinary levels of monoester before deglucuronidation suggest that MBP and MBzP were present predominately as the glucuronide form. However, a small portion (5%) of the reference population had substantially higher percentages of unconjugated MBP than the rest of the population (67% above the next lowest value). These differences in MBP glucuronidation could be caused by enzymatic saturation due to a large recent dose of parent diester phthalate. Arguing against simple saturation, urinary MBP levels did not correlate with the ratio of MBP/MBP-glucuronide. Although based on limited data, this observation underscores the potential variability in the human metabolism of phthalate monoesters and thereby variable monoester exposure and toxicity.

For analytes found in [is greater than] 75% of subjects (MEHP, MEP, MBzP, and MBP), we examined log-transformed creatinine-adjusted levels by analysis of variance models to assess effects from selected demographic factors: age (four groups), sex, race (four groups), socioeconomic status (two groups), urban/rural residence, and education (two groups). All comparison cells described contain [is greater than] 50 people. Significant differences in creatinine-adjusted values between groups were not caused by differences in urinary creatinine levels. Because of the large number of statistical tests performed on our data, the effects of demographic factors on urinary phthalate levels should be considered for generating hypotheses only.

After adjustment for the effects of other factors, creatinine-adjusted MEP levels increased on average by 1.7% (p [is less than] 0.02) for every yearly increase in age; conversely, creatinine-adjusted MBzP levels decreased by 1% (p [is less than] 0.04) for the same increase in age. Subjects who had completed [is less than or equal to] 12 years of formal education had higher levels of MBzP (22 [micro]g/g creatinine) than subjects with more formal education (16 [micro]g/g creatinine; p [is less than] 0.01). Further statistical testing indicated that MBP levels in non-Hispanic whites also differed between the two education groups ([is less than or equal to] 12 years: 53 [micro]g/g creatinine; [is greater than] 12 years: 28 [micro]g/g creatinine; p [is less than] 0.001), whereas MBP levels in non-Hispanic blacks and Hispanics were comparable regardless of education (33 [micro]g/g creatinine). Further statistical testing also showed that rural females had significantly higher urinary levels of MBzP (26 [micro]g/g creatinine) than rural males (14 [micro]g/g creatinine; p [is less than] 0.001), urban females (19 [micro]g/g creatinine; p [is less than] 0.02), and urban males (18 [micro]g/g creatinine; p [is less than] 0.02).

Of concern, women of childbearing age (20-40 years) had significantly higher urinary levels of MBP (46.9 [micro]g/g creatinine) than other sex/age groups (31.4 [micro]g/g creatinine; p = 0.003). Furthermore, six of the eight highest MBP levels were found in these women. Creatinine adjustment did not account for this effect. Nine of the highest 10 noncreatinine-adjusted values were found in women of reproductive age. Ten subjects had urinary MBP [is greater than] 300 [micro]g/g creatinine, including three women of reproductive age with levels [is greater than] 2,000 [micro]g/g creatinine (Figure 1). A similar analysis for urinary MBzP did not indicate a difference, but a more detailed look at the rural women with high levels of MBzP suggests that rural women of childbearing age have higher levels (31.6 [micro]g/g creatinine) than older (41-60 years) rural women (21.1 [micro]g/g creatinine). The small study size and nonrepresentative nature of this sample population limits the applicability of these statistical associations. However, these findings do indicate the possibility of significant demographic variations in exposure and/or metabolism.

[Figure 1 ILLUSTRATION OMITTED]

From a public health perspective, these data provide evidence that phthalate exposure is both higher and more common than previously suspected. Exposure data for phthalates is critically important for human risk assessment, especially among potentially susceptible populations. Although DEHP and DINP are produced in the largest quantities, these reference range data indicate a substantial internal human dose of DBP, DEP, and BzBP. MBP and MBzP are of particular concern because of their developmental and reproductive toxicity in animals (12-15). Therefore, assessments of health risk from exposures to phthalates should include exposures to DBP, DEP, and BzBP.

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Benjamin C. Blount,(1) Manori J. Silva,(1) Samuel P. Caudill,(1) Larry L. Needham,(1) Jim L. Pirkle,(1) Eric J. Sampson,(1) George W. Lucier,(2) Richard J. Jackson,(1) and John W. Brock(1)

(1) National Center for Environmental Health, Centers for Disease Control and Prevention, Atlanta, Georgia, USA; (2) National Toxicology Program, National Institute of Environmental Health Sciences, Research Triangle Park, North Carolina, USA

Address correspondence to J.W. Brock, National Center for Environmental Health, Centers for Disease Control and Prevention, 4770 Buford Highway MS F-17, Atlanta, GA 30341 USA. Telephone: [phone]. Fax: [phone]. E-mail: [e-mail]

We thank E. Milgram, C. Hodge, N. Malek, and J. Reidy for assistance with methods development and implementation; E. Gunter for providing urinary creatinine analysis; and the National Center for Health Statistics for assistance with demographic information.

This work was partially funded by the National Toxicology Program and the National Institute of Environmental Health Sciences.

Received 26 May 2000; 19 July 2000.