Skip to main content
Download PDF
Download ePub

Association between bisphenol A exposure and body mass index in Chinese school children: a cross-sectional study

Environmental Health volume 11, Article number: 79 (2012) Cite this article

Abstract

Background

There is increasing evidence suggesting that Bisphenol A (BPA), one of the highest volume chemicals produced worldwide, can interfere with the body’s natural weight control mechanisms to promote obesity. However, epidemiological studies for this are limited, especially for children.

Methods

A cross-sectional study was conducted to investigate the association between BPA exposure and body mass index (BMI) in school children. Three primary and three middle schools were randomly selected from 26 primary and 30 middle candidate schools in Changning District of Shanghai City in China. According to the BMI-based criteria by age and sex for screening of overweight or obese children, we randomly chose 20 obese, 10 overweight, and 30 normal weight children aged 8-15 years of age from each selected school. First morning urine was collected and total urine BPA concentrations were determined by ultra-performance liquid chromatography tandem mass spectrometry. Multiple linear regression analysis was conducted to examine the association of urine BPA concentrations and daily intake estimates with BMI.

Results

BPA was detected in 84.9% of urine samples with a geometric mean of 0.45 ng/mL. The daily intake estimates ranged from 0.03 μg/day to 1.96 μg/day with a geometric mean of 0.37 μg/day. The average urine BPA concentrations and daily intake estimates were similar for boys and girls, but significantly higher in older children than younger ones, and showed an increasing trend with BMI. Multiple linear regression analyses showed that urine BPA concentrations were significantly associated with increasing BMI values in all subjects after adjustment for age and sex and the results were similar before and after corrected by urine specific gravity. When stratified by age or sex, the associations remained significant in females and in those 8-11 years of age before corrected by specific gravity. Similar results were shown for the association between BMI and daily intake estimates.

Conclusions

There is a possibility that BPA exposure increases BMI in school children. Given the cross-sectional nature of this study, longitudinal studies are warranted to confirm BPA exposure as a contributor to increased BMI in children.

Peer Review reports

Background

Bisohenol A (BPA) is one of the highest volume chemicals produced worldwide, with over six billion pounds produced each year [1]. It was mainly used for the production of epoxy resins and polycarbonate plastics. Epoxy resins are commonly used as food-contact surface lacquer coatings and polycarbonate plastics are used in compact disk manufacturing, household appliances, food packaging and plastic bottles among others [2]. Because unbound monomers remain after BPA polymerization, BPA molecules can be leached from those products into environment and food. The widespread occurrence of BPA in environment and food has been well documented [3]. The main route of human exposure to BPA is through food intake and BPA has been detected in human urine, blood, milk and tissues, indicating that human exposure to BPA is extensive [4]. Moreover, lab researches have found that BPA is a typical endocrine disrupting chemical (EDC) [5], and human exposure to BPA has been reported to be associated with various adverse effects, such as metabolic and reproductive diseases [6].

There is increasing evidence suggesting that some endocrine disrupting chemicals can act as obesogens and interfere with body’s natural weight control mechanisms by disrupting adipose tissue biology, endocrine hormone systems, or central hypothalamic-pituitary-adrenal axis [7, 8]. However, most of the studies about the association of BPA, one of focused EDCs, with obesity are lab researches [9, 10]. For example, Huc et al observed that lipid accumulation in HepG2 cells was induced by BPA at 10-4-10-12 M level [11]. Sargis et al. reported that BPA significantly stimulated glucocorticoid receptor (GR) to promote adipogenesis without significant activation of the peroxisome proliferator-activated receptor-γ in the 3 T3-L1 Cell Line at an incubation concentration of 100 nM [12]. Gestational or perinatal exposure of mice to 2.4-500 μg/kg body weight -day of BPA resulted in increased body weight of offspring [13–15].

To our knowledge, there have been only three published epidemiological studies primarily designed for the association between BPA exposure and obesity [16–18]. Two of them were conducted in adults, one in children and adolescents, and all of them used a cross-sectional design. Children and adolescents are in rapid growth and are more susceptible to external disturbance compared with adults. Additionally, it has been reported that children are extensively exposed to BPA and exposure levels are even higher compared with adults [19, 20]. In this study we examined the association between BPA exposure and body mass index (BMI) in Chinese school children.

Methods

Study population

There were a total of 26 primary schools with 17,570 students and 30 middle schools with 21,059 students in Changning District in Shanghai City of China. For the current study, three primary schools (a total of 518, 448, and 573 students, respectively) and three middle schools (467, 541, and 374 students, respectively) were randomly selected. From each selected school, 20 obese, 10 overweight, and 30 normal weight students aged 8-15 years were randomly chosen in the basis of the most recent yearly regular physical examination conducted in October, 2011, and available information included weight, height, age, sex, and ethnicity of students. The students with liver, kidney, or endocrine diseases were excluded. A total of 360 students were selected and they were all Han people. The study was approved by the Ethical Review Board of Fudan University School of Public Health. Either participants or guardians provided a written informed consent for study participation.

Anthropometric measurement

Body weight (kg) and height (cm) were measured using the same type of apparatus and followed the standard procedures recommended by Cameron [21]. Subjects were required to wear light clothes and stand straight and barefoot when being measured. All instruments were properly calibrated. Each technician was required to pass a training course for the anthropometric measurement. BMI is a reasonable measure of fatness in children and adolescents [22] and calculated as weight in kilograms divided by height in meters squared. Normal weight, overweight, and obese individuals were identified according to the BMI-based criteria by age and sex proposed by the Working Group on Obesity in China (WGOC) (see Additional file 1: Table S1 for the BMI cut-off values) [23].

Measurement of urine BPA

First morning urine was collected by participants themselves. In order to minimize the contamination of BPA during urine sampling and storing, the participants were told to avoid a contact of urine with plastic products in the process of urine collection, and urine samples were collected in glass centrifuge tubes, which was rinsed by acetone and baked at 350°C for 2 hours. The collected urine samples were transported to lab as soon as possible and stored in dark at -20°C until analysis. All the urine samples were collected between January 3 and 6, 2012, about 3 months after the latest physical examination.

The analysis of total urine BPA (free and conjugated) was carried out by solid-phase extraction coupled with ultra-performance liquid chromatography isotope dilution tandem mass spectrometry, as described previously [24, 25]. All urine analyses were carried out in a random order for three BMI groups (normal weight, overweight, and obesity), which was blinded to analytical technicians. To reduce a potential systematic drift of analytical method over time, all the analyses of urine samples were completed in March 2012. The analytical method was included in the Supplement.

Statistical analyses

For measurements below the limit of detection (LOD, 0.07 ng/mL, see Additional file 1), a default value of LOD divided by the square root of 2 was assigned, which produces reasonably nonbiased means and standard deviations [26]. Daily intake estimates were calculated in the basis of urine BPA concentrations using a modified method proposed by Lakind and Naiman [27], with the reference values recommended by the International Commission on Radiological Protection (ICRP) [28]. The average value (600 ml/day) of the ICRP urine outputs (500 ml/day for children 5 years of age and 700 ml/day for those 10 years of age) was used for the 6-11 year age group. For the 12-19 year age group, the ICRP urine output of 15 years of age (1200 ml/day) was used. The calculation formula is DI = C × V/1000, where DI is the daily intake estimate (μg/day), C is the urinary BPA concentration (ng/mL), and V is urinary output (mL/day).

For descriptive statistics, arithmetic mean and standard deviation for weight, height, and BMI for all subjects or by sex, age (8-9, 10-11, 12-13, and 14-15 years of age), and BMI (normal weight, overweight, and obesity) were calculated. For urinary BPA concentrations and daily intake estimates, we also calculated geometric mean (GM) and its 95% confidence interval (CI), median, and range. The 95% CI of GM was a natural exponential transform of that of arithmetic mean of naturally log-transformed urine BPA concentrations. A natural log-transformation was used to normalize the BPA data. Analysis of variance was used to examine the associations of BPA with age, sex, and BMI.

Due to the glucuronidation of BPA in the liver and its elimination by active tubular secretion, creatinine adjustment may not be appropriate for urine BPA concentration [29, 30]. Additionally, BMI could predict the urine creatinine concentration, and therefore, the associations between urine BPA and BMI may be altered by creatinine adjustment [31]. Instead, we used specific gravity (SG) to correct for urinary dilution as recommended by Mahalingaiah et al. [30]. SG was measured using a handheld refractometer (Atago PAL 10-S; Tokyo, Japan). The correction formula was Pc = P × [(1.024–1)/(SG–1)], where Pc is the SG-corrected BPA concentration (ng/mL), P is the experimental BPA concentration (ng/mL), and SG is the specific gravity of urine sample [32].

Since the distribution of BMI values was slightly right skewed, a natural log-transformation was used to improve the normal distribution of BMI values. And then multiple linear regression analyses were performed to study the associations of naturally log-transformed urinary BPA concentrations or daily intake estimates with BMI values. We first included all the subjects in regression models and then conducted age- and sex-stratified analysis before and after taking into account for covariates. Urine BPA concentrations and daily intake estimates were examined before (adjusted model 1) and after (adjusted model 2) SG correction.

Analyses of variance for mean differences in BMI and their 95% CIs between quartile 2, 3 or 4 and quartile 1 (reference) of urine BPA concentration were carried out in all subjects or stratified by age and sex taking either age in year or sex into consideration. Data analyses were performed using SPSS (version 17; SPSS, Inc., Chicago, IL, USA); p < 0.05 was considered significant, and all statistical tests were two-sided.

Results

Of 360 eligible subjects, 53 did not provide urine samples and 48 provided urine samples but not first morning urine. A total of 259 subjects were included in this study, and among them, 124 had normal weight, 53 were overweight, and 82 were obese (Table 1). The mean and standard deviation of weight, height, and BMI in all subjects or by age or sex were listed in Table 1.

Table 1 Mean and standard deviation of weight, height, and body mass index (BMI) among study participants
Full size table

As shown in Table 2, BPA was detected in 84.9% of urine samples with a GM of 0.45 ng/mL and a median of 0.60 ng/mL. The daily intake estimates ranged from 0.03 μg/day to 1.96 μg/day with a GM of 0.37 μg/day. The average levels of the urine BPA concentrations and the daily intake estimates were similar in boys and girls but were significantly higher in older children than younger ones. Urine BPA concentration and daily intake estimates increased with BMI after adjustment for sex and age. A pair comparison showed that average urine BPA concentrations and daily intake estimates were significantly higher in the obesity group compared with the normal weight group. The adjusted mean difference was 0.658 (95% CI: 0.195, 1.120, p = 0.006) for naturally log-transformed urine BPA and was 0.642 (95% CI: 0.161, 1.122, p = 0.009) for naturally log-transformed daily intake estimate. However, there were no significant difference between the overweight group and the normal weight group or between the obesity group and the overweight group.

Table 2 Urine bisphenol A (BPA) concentrations (ng/mL) and daily intake estimates (μg/day) among study participants
Full size table

Table 3 showed that urine BPA concentration was significantly associated with increasing BMI as a continuous variable in all subjects after adjustment for age and sex. The results were similar before and after urine BPA concentrations were corrected by SG. There were sex- and age- related variations in the association. Adjusted model 1 shows that before corrected by SG, the association between urine BPA concentration and BMI was significant in females and in the 8-11 year age group. However, the association was not significant after corrected by SG although the association in the 8-11 age group narrowly missed statistical significance (p = 0.081) (adjusted model 2). The regression coefficient (β) represented the change of naturally log-transformed BMI value per one unit of naturally log-transformed urine BPA concentration. The results of BPA intake estimate associated with BMI were similar to those of urine BPA associated with BMI (see Additional file 1: Table S2).

Table 3 Multiple linear regression analyses for the associations between urine bisphenol A (BPA) concentration (ng/mL) and body mass index (BMI, Kg/m 2 ) among study participants
Full size table

Figure 1 shows the adjusted mean differences in BMI for urine BPA concentration quartiles 2, 3, and 4 compared with quartile 1. Average BMI tended to be higher in the BPA quartile 2, 3 and 4 groups compared with the quartile 1 group.

Figure 1
figure 1

Analysis of variance for mean differences of body mass index (BMI) between quartiles 2, 3 or 4 of urine BPA concentrations corrected by specific gravity with quartile 1 in all subjects or stratified by age (8-11 and 12-15 year age groups) or sex after adjustment for age in year and sex. Error bars indicated 95% confidence interval.

Full size image

Discussion

Only few epidemiological studies have been conducted to determine the association between BPA exposure and obesity, and provided inconsistent results. Two cross-sectional studies found no significant associations: one used data from the InCHINTI Study, a prospective population-based study of Italian adults 20-74 years of age [33], and another used data from the National Health and Nutrition Examination Survey (NHANES) 2003-2004 of adults 18-74 years of age [34]. Other three cross-sectional studies found a significant positive association between BPA exposure and obesity based on combined data from the NHANES 2003-2004 and the NHANES 2005-2006 [16], data from children and adolescents who participated in the NHANES 2003-2008 [17], and data from Chinese adults 40 years of age or older [18]. The discrepancy between the studies conducted by Lang et al. [34] and Carwile et al. [16] might reflect a different statistical power to detect a moderate association. In contrast to the studies described above, our study’s participants were school children, and the analysis of BPA was performed in a short time span (one month), in the same laboratory, and by the same analytical team, which minimized potential measurement biases.

The levels (0.45 ng/m L of GM) and detection frequency (84.9%) of BPA in this study were below those from most previous studies of children and adolescents (Table 4). The detection frequency of BPA in these studies ranged from 92.9% to 98.6% with an exception of 79% in a study of Egypt girls [35], and the levels varied between 0.84 ng/m L and 3.7 ng/m L of GM. Based on individual body weights, we calculated BPA daily intake estimates, which ranged from 0.19 ng/kg-day to 277.30 ng/kg-day with a GM of 8.22 ng/kg-day (detail data available upon request). The GM of daily intake estimates in this study was also lower than those from most previous studies (Table 4), and much lower than the tolerable daily intake of 50 μg/kg-day recommended by the European Food Safety Authority (EFSA) in 2007 [36]. The GM of daily intake estimates in the previous studies ranged from 54.0 ng/kg-day to 71.0 ng/kg-day (Table 4).

Table 4 Urine bisphenol A (BPA) concentrations (ng/mL) and daily intake estimates (ng/kg-day) from previous studies
Full size table

In the present study, multiple linear regression analysis showed that high urine BPA and daily intake estimate were significantly associated with an increase in BMI value in all subjects. Specific gravity correction weakened the association, especially after stratified by age or sex. It was reported that overweight and obese subjects might have less urine output [39], which might lead to a higher urine BPA concentration, and similarly a higher urine SG. In this respect, urine SG correction was appropriate. However, there is also a possibility that urine solute excretion increases urine SG in overweight or obese subjects [40], and urine SG correction might result in an underestimation of true urine BPA concentrations in overweight or obese subjects and therefore weaken the association with BMI. Small sample size could be another important reason for non-significant association when stratified by sex and age.

Animal and cell studies have demonstrated that BPA can promote adipogenesis by diverse mechanisms [7, 8]. Among them, BPA interactions with specialized nuclear receptors (such as steroid hormone receptors or thyroid hormone receptors) may serve as a primary mechanism for promoting adipogenesis [41].

BPA has been reported to result in a variety of dysfunctions by binding to estrogen receptors (ERs) [6]. Soriano et al. found that BPA behaved as a strong estrogen via nuclear ERβ by using pancreatic β-cell from ERβ-/- mice at 1 nM of BPA exposure level [42]. BPA also stimulated calcium influx and prolactin secretion in rat pituitary tumor cells by membrane estrogen receptor α at as low as pM level [43]. Three human cell lines (Ishikawa, HeLa and HepG2) were used to evaluate the estrogenic promoter activity of BPA on estrogen receptors α and β, and BPA were found to act as cell type specific agonists or antagonists at different concentration levels ranging from 1 nM to 1000 nM [44]. Moreover, a role for sex steroid hormones in regulating adipocyte hypertrophy and hyperplasia was confirmed by knockout models of sex steroid pathway components [7].

Thyroid function is critical to the maintenance of basal metabolism, and BPA may influences thyroid hormone. A large cross-sectional study from Denmark found that thyroid function,was associated with BMI [45]. Fox et al. found that thyroid function within the reference range, as assessed by serum thyroid stimulating hormone concentration, is associated with body weight in both sexes using data from Framingham Offspring Study [46]. Moreover, Moriyama et al. observed that BPA could inhibit the binding of T3 to the rat hepatic thyroid hormone receptors with an inhibition constant (Ki) of 200 μM and suppress the transcriptional activities mediated by endogenous thyroid hormone receptors at as low as 100 nM [47].

In our studies, we observed that there are some age- or sex-specific differences in the associations between urine BPA and BMI. Previous epidemiological studies also reported age- or sex-specific differences in the association between urine BPA and obesity or between urine phthalate metabolites and BMI [16, 48]. Different sex hormone profiles between sex and age subgroups might explain the differences observed. Puberty usually begins between 10 and 13 years of age, and serum levels of endogenous sex hormones in puberty significantly rise, especially estradiol in girls and testosterone in boys. There also exist distinct differences in sex hormones between prepubertal boys and girls. Klein et al. reported that prepubertal girls had a 8-fold higher estrogen level than prepubertal boys [49]. The differences may lead to different susceptibility of participants to sex hormone perturbation caused by BPA.

Although plausible physiological mechanisms for BPA as an obesogen are present, there are some important gaps between our study and lab researches for meaningful interpretations. In this study, the GM of daily intake estimates was 8.22 ng/kg-day, but it was approximately 290-60,000 times lower than the pre or perinatal exposure dose (2.4-500 μg/kg-day) tested in mice lab studies reported previously [13–15]. Moreover, based on a human test about BPA metabolism and kinetics [29], the average concentration level of free serum BPA in study participants was estimated at pM level using the average BPA exposure level (8.22 ng/kg-day) in this study. This estimated serum BPA level was comparable to the least effect concentration inducing lipid accumulation in the HepG2 cell [11], but about 50,000 times lower than that promoting adipogenesis in 3 T3-L1 cell [12]. The reasons for the discrepancy of detected effect level are not clear, and the impacting factors may include cross-species, different exposure window during life course, different exposure route and/or duration to BPA for animal studies and different cell types or effect endpoints tested for cell experiments.

There were some study limitations that should be considered when interpreting the results. First, the cross-sectional nature of the association of BPA and obesity could not rule out the possibility of reverse causation. BPA exposure could be a proxy for other variables related to obesity, such as caloric intake, diet composition, daily indoor time, parental education, and family income level [17]. Of them, caloric intake or diet composition is of concern. Because food is thought as the main exposure route for BPA in human population, it is possible that increased overall calaric intake or different diet composition among obese individuals might increase the risk of BPA exposure, compared to normal weight ones.

Second, due to the short half-life (less than 6 h) of BPA in human body [29], the one spot urine analysis is not an ideal measure for long-term exposure given that obesity was most likely associated with long-term low-dose exposure. Mahalingaiah et al. reported that spot urine samples showed a moderate sensitivity for predicting an individual’s tertile categorization. Misclassification due to this spot urine might result in an attenuated estimate of the strength of association between BPA exposure and BMI [30]. The first morning urine used in the current study improved this circumstance by adding more comparability between individuals than pure spot urine as most previous studies did. However, due to its rapid metabolism in human body, BPA exposure estimates from first morning urine may just represent the exposure at the prior meal (dinner), not daily or average exposure level. Given the food indigestion as the main exposure route to BPA, the use of first morning urine may result in an elevated BPA exposure estimate [50, 51].

Third, exposure to BPA might also be an indicator of exposure to multiple environmental chemicals such as phthalates and organotins. Some studies have reported that urine phthalate metabolites were significantly associated with BMI [52]. Urine concentrations of other environmental chemicals, especially phthalate metabolites and organotins, may be needed to be investigated to clarify their roles in the association between BPA exposure and BMI.

Conclusions

In this study, we found that urine BPA concentration and daily BPA intake estimate were positively associated with BMI in Chinese school children. Due to being much lower than the recommended tolerable daily intake of 50 μg/kg-day proposed by EFSA, the effective dose estimated from the current cross-sectional data required a further risk reassessment of BPA exposure. Given the cross-sectional nature of this study, longitudinal studies are warranted to confirm BPA exposure as a contributor to increased BMI.

Abbreviations

BPA:

Bisphenol A

BMI:

Body mass index

EDCs:

Endocrine disrupting chemicals

GR:

Glucocorticoid receptor

WGOC:

Working group on obesity in China

LOD:

Limit of detection

ICRP:

International commission on radiological protection

CI:

Confidence interval

GM:

Geometric mean

SG:

Specific gravity

EFSA:

European food safety authority

ERs:

Estrogen receptors

NHANES:

National health and nutrition examination survey

ER:

Estrogen receptor.

References

  1. Diamanti-Kandarakis E, Bourguignon J, Giudice LC, Hauser R, Prins GS, Soto AM, Zoeller RT, Gore AC: Endocrine-disrupting chemicals: an endocrine society scientific statement. Endocr Rev. 2009, 30: 293-342. 10.1210/er.2009-0002.

    Article  CAS  Google Scholar 

  2. Fromme H, Kuchler T, Otto T, Pilz K, Muller J, Wenzel A: Occurrence of phthalates and bisphenol A and F in the environment. Water Res. 2002, 36: 1429-1438. 10.1016/S0043-1354(01)00367-0.

    Article  CAS  Google Scholar 

  3. Kang J, Kondo F, Katayama Y: Human exposure to bisphenol A. Toxicology. 2006, 226: 79-89. 10.1016/j.tox.2006.06.009.

    Article  CAS  Google Scholar 

  4. Vandenberg LN, Hauser R, Marcus M, Olea N, Welshons WV: Human exposure to bisphenol A (BPA). Reprod Toxicol. 2007, 24: 139-177. 10.1016/j.reprotox.2007.07.010.

    Article  CAS  Google Scholar 

  5. Maffini MV, Rubin BS, Sonnenschein C, Soto AM: Endocrine disruptors and reproductive health: the case of bisphenol-A. Mol Cell Endocrinol. 2006, 254–255: 179-186.

    Article  Google Scholar 

  6. Rubin BS: Bisphenol A: an endocrine disruptor with widespread exposure and multiple effects. J Steroid Biochem. 2011, 127: 27-34. 10.1016/j.jsbmb.2011.05.002.

    Article  CAS  Google Scholar 

  7. Gruen F, Blumberg B: Endocrine disrupters as obesogens. Mol Cell Endocrinol. 2009, 304: 19-29. 10.1016/j.mce.2009.02.018.

    Article  CAS  Google Scholar 

  8. Thayer KA, Heindel JJ, Bucher JR, Gallo MA: Role of environmental chemicals in diabetes and obesity: a national toxicology program workshop review. Environ Health Persp. 2012, 120: 779-789. 10.1289/ehp.1104597.

    Article  CAS  Google Scholar 

  9. Tang-Peronard JL, Andersen HR, Jensen TK, Heitmann BL: Endocrine-disrupting chemicals and obesity development in humans: a review. Obes Rev. 2011, 12: 622-636. 10.1111/j.1467-789X.2011.00871.x.

    Article  CAS  Google Scholar 

  10. Vom Saal FS, Nagel SC, Coe BL, Angle BM, Taylor JA: The estrogenic endocrine disrupting chemical bisphenol A (BPA) and obesity. Mol Cell Endocrinol. 2012, 354: 74-84. 10.1016/j.mce.2012.01.001.

    Article  CAS  Google Scholar 

  11. Huc L, Lemarie A, Gueraud F, Helies-Toussaint C: Low concentrations of bisphenol A induce lipid accumulation mediated by the production of reactive oxygen species in the mitochondria of HepG2 cells. Toxicol in Vitro. 2012, 26: 709-717. 10.1016/j.tiv.2012.03.017.

    Article  CAS  Google Scholar 

  12. Sargis RM, Johnson DN, Choudhury RA, Brady MJ: Environmental endocrine disruptors promote adipogenesis in the 3 t3-l1 cell line through glucocorticoid receptor activation. Obesity. 2010, 18: 1283-1288. 10.1038/oby.2009.419.

    Article  CAS  Google Scholar 

  13. Rubin BS, Murray MK, Damassa DA, King JC, Soto AM: Perinatal exposure to low doses of bisphenol A affects body weight, patterns of estrous cyclicity, and plasma LH levels. Environ Health Perspect. 2001, 109: 675-680. 10.1289/ehp.01109675.

    Article  CAS  Google Scholar 

  14. Nikaido Y, Yoshizawa K, Danbara N, Tsujita-Kyutoku M, Yuri T, Uehara N, Tsubura A: Effects of maternal xenoestrogen exposure on development of the reproductive tract and mammary gland in female CD-1 mouse offspring. Reprod Toxicol. 2004, 18: 803-811. 10.1016/j.reprotox.2004.05.002.

    Article  CAS  Google Scholar 

  15. Howdeshell KL, Hotchkiss AK, Thayer KA, Vandenbergh JG, Vom SF: Exposure to bisphenol A advances puberty. Nature. 1999, 401: 763-764. 10.1038/44517.

    Article  CAS  Google Scholar 

  16. Carwile JL, Michels KB: Urinary bisphenol A and obesity: NHANES 2003-2006. Environ Res. 2011, 111: 825-830. 10.1016/j.envres.2011.05.014.

    Article  CAS  Google Scholar 

  17. Trasande L, Attina TM, Blustein J: Association between urinary bisphenol A concentration and obesity prevalence in children and adolescents. JAMA. 2012, 308: 1113-1121. 10.1001/2012.jama.11461.

    Article  CAS  Google Scholar 

  18. Wang T, Li M, Chen B, Xu M, Xu Y, Huang Y, Lu J, Chen Y, Wang W, Li X, Liu Y, Bi Y, Lai S, Ning G: Urinary Bisphenol A (BPA) concentration associates with obesity and insulin resistance. J Clin Endocrino Metab. 2012, 97: E223-E227. 10.1210/jc.2011-1989.

    Article  CAS  Google Scholar 

  19. Calafat AM, Ye X, Wong L, Reidy JA, Needham LL: Exposure of the US population to bisphenol A and 4-tertiary-octylphenol: 2003-2004. Environ Health Persp. 2008, 116: 39-44.

    Article  CAS  Google Scholar 

  20. Bushnik T, Haines D, Levallois P, Levesque J, Van Oostdam J, Viau C: Lead and bisphenol A concentrations in the Canadian population. Health Rep. 2010, 21: 7-18.

    Google Scholar 

  21. Cameron N: The methods of axiological anthropometry. Human Growth. Edited by: Falkner F, Tanner JM. 1978, London: Plenum Press, 2

    Google Scholar 

  22. Pietrobelli A, Faith MS, Allison DB, Gallagher D, Chiumello G, Heymsfield SB: Body mass index as a measure of adiposity among children and adolescents: a validation study. J Pediatr. 1998, 132: 204-210. 10.1016/S0022-3476(98)70433-0.

    Article  CAS  Google Scholar 

  23. Ji CY: Report on childhood obesity in China (1) - Body mass index reference for screening overweight and obesity in Chinese school-age children. Biomed Environ Sci. 2005, 18: 390-400.

    Google Scholar 

  24. Zhang Z, Alomirah H, Cho H, Li Y, Liao C, Tu BM, Mohd MA, Nakata H, Ren N, Kannan K: Urinary Bisphenol a concentrations and their implications for human exposure in several Asian countries. Environ Sci Technol. 2011, 45: 7044-7050. 10.1021/es200976k.

    Article  CAS  Google Scholar 

  25. Liao C, Kannan K: Determination of free and conjugated forms of bisphenol a in human urine and serum by liquid chromatography-tandem mass spectrometry. Environ Sci Technol. 2012, 46: 5003-5009. 10.1021/es300115a.

    Article  CAS  Google Scholar 

  26. Hornung RW, Reed LD: Estimation of average concentration in the presence of nondetectable values. Appl Occup Environ Hyg. 1990, 5: 46-51. 10.1080/1047322X.1990.10389587.

    Article  CAS  Google Scholar 

  27. Lakind JS, Naiman DQ: Bisphenol A (BPA) daily intakes in the United States: estimates from the 2003-2004 NHANES urinary BPA data. J Expo Sci Environ Epidemiol. 2008, 18: 608-615. 10.1038/jes.2008.20.

    Article  CAS  Google Scholar 

  28. Valentin J: Basic anatomical and physiological data for use in radiological protection: reference values: ICRP Publication 89. Ann ICRP. 2002, 32: 1-277.

    Article  Google Scholar 

  29. Volkel W, Colnot T, Csanady GA, Filser JG, Dekant W: Metabolism and kinetics of bisphenol a in humans at low doses following oral administration. Chem Res Toxicol. 2002, 15: 1281-1287. 10.1021/tx025548t.

    Article  Google Scholar 

  30. Mahalingaiah S, Meeker JD, Pearson KR, Calafat AM, Ye X, Petrozza J, Hauser R: Temporal variability and predictors of urinary bisphenol a concentrations in men and women. Environ Health Persp. 2008, 116: 173-178.

    Article  CAS  Google Scholar 

  31. Barr DB, Wilder LC, Caudill SP, Gonzalez AJ, Needham LL, Pirkle JL: Urinary creatinine concentrations in the US population: implications for urinary biologic monitoring measurements. Environ Health Persp. 2005, 113: 192-200.

    Article  CAS  Google Scholar 

  32. Boeniger MF, Lowry LK, Rosenberg J: Interpretation of urine results used to assess chemical-exposure with emphasis on creatinine adjustments- a review. Am Ind Hyg Assoc J. 1993, 54: 615-627. 10.1080/15298669391355134.

    Article  CAS  Google Scholar 

  33. Galloway T, Cipelli R, Guralnik J, Ferrucci L, Bandinelli S, Corsi AM, Money C, McCormack P, Melzer D: Daily Bisphenol a excretion and associations with sex hormone concentrations: results from the InCHIANTI adult population study. Environ Health Persp. 2010, 118: 1603-1608. 10.1289/ehp.1002367.

    Article  CAS  Google Scholar 

  34. Lang IA, Galloway TS, Scarlett A, Henley WE, Depledge M, Wallace RB, Melzer D: Association of urinary bisphenol A concentration with medical disorders and laboratory abnormalities in adults. Jama-J Am Med Assoc. 2008, 300: 1303-1310. 10.1001/jama.300.11.1303.

    Article  CAS  Google Scholar 

  35. Nahar MS, Soliman AS, Colacino JA, Calafat AM, Battige K, Hablas A, Seifeldin IA, Dolinoy DC, Rozek LS: Urinary bisphenol A concentrations in girls from rural and urban Egypt: a pilot study. Environ Health. 2012, 11: 20-10.1186/1476-069X-11-20.

    Article  CAS  Google Scholar 

  36. Lakind JS, Naiman DQ: Daily intake of bisphenol A and potential sources of exposure: 2005-2006 National Health and Nutrition Examination Survey. J Expo Sci Environ Epidemiol. 2011, 21: 272-279. 10.1038/jes.2010.9.

    Article  CAS  Google Scholar 

  37. Becker K, Goeen T, Seiwert M, Conrad A, Pick-Fuss H, Mueller J, Wittassek M, Schulz C, Kolossa-Gehring M: GerES IV: Phthalate metabolites and bisphenol A in urine of German children. Int J Hyg Envir Heal. 2009, 212: 685-692. 10.1016/j.ijheh.2009.08.002.

    Article  CAS  Google Scholar 

  38. Casas L, Fernandez MF, Llop S, Guxens M, Ballester F, Olea N, Basterrechea Irurzun M, Santa Marina Rodriguez L, Riano I, Tardon A, Vrijheid M, Calafat AM, Sunyer J: Urinary concentrations of phthalates and phenols in a population of Spanish pregnant women and children. Environ Int. 2011, 37: 858-866. 10.1016/j.envint.2011.02.012.

    Article  CAS  Google Scholar 

  39. Eijsvogels TM, Veltmeijer MT, Schreuder TH, Poelkens F, Thijssen DH, Hopman MT: The impact of obesity on physiological responses during prolonged exercise. Int J Obes (Lond). 2011, 35: 1404-1412. 10.1038/ijo.2010.277.

    Article  CAS  Google Scholar 

  40. Powell CR, Stoller ML, Schwartz BF, Kane C, Gentle DL, Bruce JE, Leslie SW: Impact of body weight on urinary electrolytes in urinary stone formers. Urology. 2000, 55: 825-830. 10.1016/S0090-4295(99)00617-2.

    Article  CAS  Google Scholar 

  41. Casals-Casas C, Desvergne B: Endocrine disruptors: from endocrine to metabolic disruption. In: Annu Rev Physiol. 2011, 73: 135-162. 10.1146/annurev-physiol-012110-142200.

    CAS  Google Scholar 

  42. Soriano S, Alonso-Magdalena P, García-Arévalo M, Novials A, Muhammed SJ, Salehi A, Gustafsson J, Quesada I, Nadal A: Rapid insulinotropic action of low doses of Bisphenol-A on mouse and human islets of langerhans: role of estrogen receptor β. PLoS One. 2012, 7: e31109-10.1371/journal.pone.0031109.

    Article  CAS  Google Scholar 

  43. Wozniak AL, Bulayeva NN, Watson CS: Xenoestrogens at picomolar to nanomolar concentrations trigger membrane estrogen receptor-alpha-mediated Ca2+ fluxes and prolactin release in GH3/B6 pituitary tumor cells. Environ Health Perspect. 2005, 113: 431-439. 10.1289/ehp.7505.

    Article  CAS  Google Scholar 

  44. Li Y, Burns KA, Arao Y, Luh CJ, Korach KS: Differential estrogenic actions of endocrine-disrupting chemicals Bisphenol A, Bisphenol AF and Zearalenone through estrogen receptor α and β in Vitro. Environ Health Perspect. 2012, 120: 1029-1035. 10.1289/ehp.1104689.

    Article  CAS  Google Scholar 

  45. Knudsen N, Laurberg P, Rasmussen LB, Bulow I, Perrild H, Ovesen L, Jorgensen T: Small differences in thyroid function may be important for body mass index and the occurrence of obesity in the population. J Clin Endocrinol Metab. 2005, 90: 4019-4024. 10.1210/jc.2004-2225.

    Article  CAS  Google Scholar 

  46. Fox CS, Pencina MJ, D'Agostino RB, Murabito JM, Seely EW, Pearce EN, Vasan RS: Relations of thyroid function to body weight: cross-sectional and longitudinal observations in a community-based sample. Arch Intern Med. 2008, 168: 587-592. 10.1001/archinte.168.6.587.

    Article  Google Scholar 

  47. Moriyama K, Tagami T, Akamizu T, Usui T, Saijo M, Kanamoto N, Hataya Y, Shimatsu A, Kuzuya H, Nakao K: Thyroid hormone action is disrupted by bisphenol A as an antagonist. J Clin Endocrinol Metab. 2002, 87: 5185-5190. 10.1210/jc.2002-020209.

    Article  CAS  Google Scholar 

  48. Hatch EE, Nelson JW, Qureshi MM, Weinberg J, Moore LL, Singer M, Webster TF: Association of urinary phthalate metabolite concentrations with body mass index and waist circumference: a cross-sectional study of NHANES data, 1999-2002. Environ Health. 2008, 7: 27-10.1186/1476-069X-7-27.

    Article  Google Scholar 

  49. Klein KO, Baron J, Colli MJ, McDonnell DP, Cutler GJ: Estrogen levels in childhood determined by an ultrasensitive recombinant cell bioassay. J Clin Invest. 1994, 94: 2475-2480. 10.1172/JCI117616.

    Article  CAS  Google Scholar 

  50. Teeguarden JG, Calafat AM, Ye X, Doerge DR, Churchwell MI, Gunawan R, Graham MK: Twenty-four hour human urine and serum profiles of bisphenol a during high-dietary exposure. Toxicol Sci. 2011, 123: 48-57. 10.1093/toxsci/kfr160.

    Article  CAS  Google Scholar 

  51. Ye X, Wong LY, Bishop AM, Calafat AM: Variability of urinary concentrations of bisphenol A in spot samples, first morning voids, and 24-hour collections. Environ Health Perspect. 2011, 119: 983-988. 10.1289/ehp.1002701.

    Article  CAS  Google Scholar 

  52. Hatch EE, Nelson JW, Stahlhut RW, Webster TF: Association of endocrine disruptors and obesity: perspectives from epidemiological studies. Int J Androl. 2010, 33: 324-331. 10.1111/j.1365-2605.2009.01035.x.

    Article  CAS  Google Scholar 

Download references

Acknowledgements

This project was supported by Key Laboratory of Public Health Safety of Ministry of Education, School of Public Health, Fudan University, China. It also was funded by Project 985 innovation platform for superiority subject, Ministry of Education, China.

Author information

Authors and Affiliations

  1. Key Laboratory of Public Health Safety of Ministry of Education, School of Public Health, Fudan University, Shanghai, 200032, China

    He-xing Wang, Ying Zhou & Qing-wu Jiang

  2. Centers for Disease Control and Prevention of Changning district, Shanghai, 200051, China

    Chuan-xi Tang & Jin-gui Wu

  3. Department of Epidemiology and Community Medicine, Faculty of Medicine, University of Ottawa, Ottawa, Ontario, Canada

    Yue Chen

Authors
  1. He-xing Wang
    View author publications

    You can also search for this author in PubMed Google Scholar

  2. Ying Zhou
    View author publications

    You can also search for this author in PubMed Google Scholar

  3. Chuan-xi Tang
    View author publications

    You can also search for this author in PubMed Google Scholar

  4. Jin-gui Wu
    View author publications

    You can also search for this author in PubMed Google Scholar

  5. Yue Chen
    View author publications

    You can also search for this author in PubMed Google Scholar

  6. Qing-wu Jiang
    View author publications

    You can also search for this author in PubMed Google Scholar

Corresponding author

Correspondence to Ying Zhou.

Additional information

Competing interests

All the authors declared that they had no competing interests.

Authors’ contributions

HXW and YZ had full access to all of the data in the study and take responsibility for the integrity of the data and the accuracy of the data analysis; YZ, YC, and QWJ developed the study concept and design; CXT, JGW, HXW, and YZ performed the collection of anthropometric data and urine samples; HXW, YZ, YC, and QWJ conducted the analysis and interpretation of data; CXT, JGW, HXW, YZ, and YC wrote the majority of the manuscript; YC and QWJ had critical revision of the manuscript for important intellectual content; HXW, YZ, and YC conducted the statistical analysis; YZ, JGW, and QWJ supplied administrative, technical, or material support; YC and QWJ supervised the study. All authors read and approved the final manuscript.

Electronic supplementary material

12940_2012_609_MOESM1_ESM.doc

Additional file 1:Table S1. BMI-based criteria by age and sex for screening of overweight and obese school children proposed by Working Group on Obesity in China (WGOC) in 2005. Table S2 Multiple linear regression analyses for the associations between daily intake estimates (μg/day) and body mass index (BMI, Kg/m2) among study participants. (DOC 86 KB)

Authors’ original submitted files for images

Below are the links to the authors’ original submitted files for images.

Authors’ original file for figure 1

Rights and permissions

Open Access This article is published under license to BioMed Central Ltd. This is an Open Access article is distributed under the terms of the Creative Commons Attribution License ( https://creativecommons.org/licenses/by/2.0 ), which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.

Reprints and Permissions

About this article

Cite this article

Wang, Hx., Zhou, Y., Tang, Cx. et al. Association between bisphenol A exposure and body mass index in Chinese school children: a cross-sectional study. Environ Health 11, 79 (2012). https://doi.org/10.1186/1476-069X-11-79

Download citation

  • Received:

  • Accepted:

  • Published:

  • DOI: https://doi.org/10.1186/1476-069X-11-79

Keywords

  • Bisphenol A
  • Urine
  • Body mass index
  • Obesity
  • School children

Environmental Health

ISSN: 1476-069X