Skip to main content

Advertisement

Download PDF

Urinary mycoestrogens and age and height at menarche in New Jersey girls

Environmental Health volume 18, Article number: 24 (2019) Cite this article

Abstract

Background

Despite evidence of the endocrine disrupting properties of zearalenone (ZEN) and alpha-zearalanol (zeranol, α-ZAL), they have been minimally studied in human populations. In previous cross-sectional analyses, we demonstrated that 9–10 years old girls with detectable urinary ZEN were of shorter stature and less likely to have reached the onset of breast development than girls with undetectable urinary ZEN. The aim of this study was to examine baseline concentrations of ZEN, (α-ZAL), and their phase-1 metabolites in relation to subsequent growth and timing of menarche using 10 years of longitudinal data.

Methods

Urine samples were collected from participants in the Jersey Girl Study at age 9–10 (n = 163). Unconjugated ZEN, (α-ZAL), and their metabolites were analyzed using high performance liquid chromatography and tandem mass spectrometry. Information on height, weight, and pubertal development was collected at a baseline visit with annual follow-up by mail thereafter. Cox regression was used to evaluate time to menarche in relation to baseline ZEN, (α-ZAL), and total mycoestrogen exposure. Z-scores for height and weight were used in mixed models to assess growth.

Results

Mycoestrogens were detectable in urine in 78.5% of the girls (median ZEN: 1.02 ng/ml, range 0–22.3). Girls with detectable urinary concentrations of (α-ZAL) and total mycoestrogens (sum of ZEN, (α-ZAL) and their metabolites) at baseline were significantly shorter at menarche than girls with levels below detection (p = 0.04). ZEN and total mycoestrogen concentrations were inversely associated with height- and weight-z-scores at menarche (adjusted β = − 0.18, 95% CI: -0.29, − 0.08, and adjusted β = − 0.10, 95% CI: -0.21, 0.01, respectively).

Conclusion

This study supports and extends our previous results suggesting that exposure to ZEN, (α-ZAL), and their metabolites is associated with slower growth and pubertal development in adolescent girls.

Peer Review reports

Introduction

Puberty is a critical developmental window during which there are rapid and significant changes in maturation and activation of multiple hormone axes [1, 2]. These changes make puberty a particularly susceptible time period for endocrine disruption. Exposures during this critical window can impact the physiology of female reproductive organs and the hypothalamic-pituitary-ovarian hormonal axis, including abnormal pubertal changes and ultimately, increased susceptibility to hormone-sensitive cancers including breast cancer [3].

Zearalenone (ZEN) is a mycotoxin produced by certain fungal species of the genus Fusarium, while alpha-zearalanol (zeranol, α-ZAL) is a synthetic derivative of ZEN as well as a product of ZEN metabolism. ZEN and α-ZAL are widely found in the food supply, where exposure may be deliberate (e.g. α-ZAL administered to livestock as a growth promoter) or inadvertent (e.g. fungal contamination of grain products by ZEN). Consequently, both ZEN and α-ZAL can be found through a range of food products including cereal, meat, milk, wine, beer, dried fruit and spices. Although these mycoestrogens have short half- lives (< 24 h) [4], continuous exposure through the diet presents a public health concern. In livestock, ZEN, α-ZAL, and their metabolites (i.e., α-zearalenol, β-zearalenol, zearalanol, β-zearalanol) are generally present due to the consumption of contaminated feed. These mycoestrogens have demonstrated endocrine disrupting effects in livestock and exposure can disrupt estrous cycling, resulting in decreased fertility [5, 6]. In fact, ZEN and zearanol are recognized as phytoestrogens, naturally occurring compounds that mimic the activity of estrogen, causing changes in hormone production and balance [7,8,9]. Despite widespread exposure to these compounds through diet [10,11,12], little is known about the effects of ZEN and α-ZAL exposures in human populations, particularly during critical windows of exposure such as puberty.

Several small studies, primarily in clinical populations, have measured ZEN exposure during the prepubertal period [13,14,15]. An Italian study (n = 63) examined 32 girls with central precocious puberty and 31 healthy controls [13]. Girls with detectable levels of ZEN (n = 6) and α-zearalenol were taller and proportionally heavier (p < 0.01) than girls with undetectable levels of these mycoestrogens. Asci et al. measured ZEN levels in girls living in the Mediterranean area of Turkey (n = 78) [14]. Girls were divided into three groups: girls with premature thelarche (PT), girls with idiopathic precocious puberty (IPP), and a control group. The authors reported that girls in the PT group had twice the levels of ZEN compared to the control group (p = 0.07). Similarly, girls in the IPP group had 2.8 times the levels of ZEN compared to the control group (p < 0.05). In the Jersey Girl study, a cross-sectional study of healthy 9–10 year old girls in the U.S., we previously reported that peripubertal girls with detectable ZEN in urine were of shorter stature (p < 0.0001) and less likely to have reached the onset of breast development than girls with undetectable ZEN (Prevalence ratio: 0.79, 95% confidence interval [95% CI]: 0.60, 1.04) [16]. We now extend these findings in the Jersey Girl Study cohort using follow-up data gathered for up to 10 years post-baseline. The aim of the current analysis is to examine baseline levels of ZEN, α-ZAL, and their phase-1 metabolites in relation to subsequent growth and onset of menarche. To our knowledge, this is the first longitudinal analysis of urinary mycoestrogens and pubertal outcomes in healthy girls.

Methods

Population

Study procedures for the Jersey Girl Study have been described in detail elsewhere [16]. In brief, 202 girls were recruited through pediatric practices, flyers, and word of mouth throughout the state of New Jersey between 2006 and 2014. Eligibility criteria included: female, age 9–10 years, English-speaking, in good health, no cognitive impairments, and living with biological mother. Parental consent and girl’s assent were obtained before data collection began. The study was approved by the Rutgers Health Sciences Institutional Review Board. Analyses in the current study included 163 girls with mycoestrogens measures.

Baseline questionnaire & visit

Interested mothers completed a brief questionnaire over the phone to determine study eligibility. Once mothers and daughters were consented to the study, they completed a clinic visit during which trained staff collected data on anthropometry and pubertal development. Girls brought in first morning void urine samples to their visit. A self-administered baseline questionnaire was completed by the girls’ mothers, with questions on demographic factors, environmental exposures, medical history, and prenatal and early childhood factors.

Follow-up questionnaires

Annual follow-up questionnaires were mailed to participants until the onset of menses. On each questionnaire, girls and/or mother reported girls’ current height, weight, and date at menarche (if applicable). The number of follow-up questionnaires completed ranged from 2 to 7 with most girls (83%) had 4–5 measurements within the follow-up period. This analysis includes follow-up data through December 2017. For 25 girls age at menarche was unknown, either because they have not reached menses yet (n = 9) or they have been lost to follow-up (n = 16).

Exposure data

Uunconjugated urinary ZEN, α-ZAL, and their metabolites were measured at baseline in urine samples from the first 163 participants enrolled in the study. Participants were instructed to collect a first morning void urine sample (using provided collection cups) and to bring it to the in-person baseline study visit. Samples were aliquoted and stored at − 70 °C, until analysis at the Chemical Analysis Facility Core of the Environmental and Occupational Health Sciences Institute (EOHSI) at Rutgers University. The analytical protocol has been previously described [16]). Briefly, free ZEN, α-ZAL and their metabolites were measured using High Performance Liquid Chromatography (HPLC) and tandem mass spectrometry (MS/MS) A Thermo Surveyor HPLC with a Hypersil C18 column were coupled to a Thermo LTQ linear ion trap mass spectrometer were used for the analysis. Commercial standards were used to define the calibration curve. The limit of detection (LOD) was 0.05 ng/ml. Concentrations of all analytes were corrected for urine dilution by specific gravity [17].

Our primary models considered ZEN and zearanol individually. Secondly, we summed all of the analytes [aglycones] (ZEN, zearanol, and their related metabolites, i.e., α-zearalenol, β-zearalenol, β-zearalanol, and zearalanol) into a composite measure (“total mycoestrogens”). We considered concentrations continuously and also categorized participants by status (ZEN, α-ZAL, and total mycoestrogen above LOD, versus below LOD). Values below LOD were assigned a value of the LOD divided by the squared root of two [18].

Statistical analysis

We examined univariate statistics (means, medians, percentages, interquartile ranges (IQR) for all variables of interest. We compared mycoestrogen concentrations in relation to participant characteristics using Kruskal-Wallis tests. Mycoestrogen concentrations were log transformed to approximate normality for all statistical models. Two sets of models were fit examining 1) age at menarche/time to menarche; and 2) height and weight at menarche. For the menarche outcome, time to menarche was calculated as the duration between the baseline visit and the date of menarche as reported on the annual follow-up questionnaires. Loss to follow-up girls and girls with no menarche yet were right censored. In our primary models, unadjusted and adjusted Cox regression models were used to estimate hazard ratios (HRs) and 95% CIs for time to menarche in relation to mycoestrogen concentrations at baseline. Secondarily, we examined early menarche, defined as onset of menses at or before 11.8 years of age (corresponding to the 25th percentile of the age at menarche distribution of all girls reporting age at menarche). To look at early menarche, we fit unadjusted and adjusted logistic regression to estimate odds ratios (ORs) and 95% CIs. Thirty-four girls met the early menarche definition and a total of 139 girls with complete menarche information were included in this analysis. For Cox and logistic regression models, exposure was dichotomized into detectable and undetectable mycoestrogen concentrations at baseline. Mixed effect linear models with an unstructured correlation matrix were used to assess average height- and weight-z-scores (continuous) in relation to mycoestrogen levels. These models included repeated measures for height- and weight-z-scores, consequently models calculate estimates using longitudinal height- and weight-z-scores for each girl.

The following potential confounders were considered in all multivariable models: girl’s age at recruitment, race, maternal education, family income, county of residence, mid-parental height, and body mass index (BMI) at menarche. Mid-parental height was calculated as [(mother’s height now + father’s height now) + 2.5]/2 [19]. In models examining menarcheal outcomes, we additionally considered BMI at menarche as a potential covariate. BMI was calculated as weight (kg) over height (m) squared (at the follow-up time where menarche was reported) and we used CDC sex- and age-specific tables to categorize subjects as: underweight (BMI <5th percentile), normal weight (BMI ≥5th - < 85th percentile), overweight (BMI ≥ 85th - ≤95th percentile), and obese (BMI > 95% percentile). Confounding factors were separately evaluated based on percentage change in regression coefficient estimates in each multivariable model (ZEN, α-ZAL, total mycoestrogens) compared to bivariate models, and only those variables changing the coefficient estimate > 10% were retained in final models.

Survival and logistic regression models examining menarcheal outcomes were adjusted for family income and BMI at menarche. Because BMI could potentially be in the causal pathway in time to menarche analyses, it may not be appropriate to adjust for it. Therefore, two adjusted Cox regression models are presented, 1) Model A adjusted for only family income, and 2) Model B adjusted for family income as well as BMI at menarche. Mixed effect linear models examining height- and weight- z-scores as main outcomes were adjusted for mid-parental height and family income. All statistical analyses used SAS 9.4 (SAS Institute, Cary, NC, USA). Statistical significance was based on alpha < 0.05.

Results

ZEN was detected in 55% of the samples, α-ZAL in 20% for and total mycoestrogens in 78%. [16]. Corrected arithmetic mean values and standard deviations were as follows: ZEN: 0.57 (0.07) ng/ml; α-ZAL: 0.21 (0.03) ng/ml; α-zearalenol: 0.13(0.02) ng/ml; β-zearalenol: 0.29 (0.03) ng/ml; β-zearalanol: 0.24 (0.04) ng/ml; zearalanone: 0.21 (0.03) ng/ml, total mycoestrogens: 0.89 (0.06) ng/ml. Table 1 shows medians and IQRs for ZEN, α-ZAL, and total mycoestrogens only for demographic variables relevant to the current study and new outcome variables. Girls with higher urinary concentrations of ZEN (p = 0.04), α-ZAL (p = 0.04), and total mycoestrogens (p = 0.07) were shorter at menarche than girls with lower concentrations. We compared characteristics of girls lost to follow-up with those with complete follow-up data. Girls lost to follow up were similar with respect to age at baseline, race, and baseline BMI than those with complete data. Mothers’ of girls with complete data were slightly more likely to have a graduate degree.

Table 1 Medians and interquartile ranges for unconjugated ZEN, zeranol and total mycoestrogens according to selected characteristic among the Jersey Girl Study participants included in these analyses (n = 163)
Full size table

Average age at menarche was 12.8 years and 34 girls met the early menarche definition. Although not statistically significant, results of unadjusted models suggested that girls with detectable urinary α-ZAL tended to have longer time to menarche compared to girls with undetectable levels (Table 2). In adjusted models, ZEN and total mycoestrogen results were largely null suggesting no effect by BMI. The results of our secondary logistic regression analyses examining early menarche were similar and indicated no relationship between baseline >LOD mycoestrogen concentrations and early menarche (not shown) and led to similar conclusions compared to our primary Cox regression analysis.

Table 2 Cox regression models for the association between mycoestrogen exposure (ng/ml) and time to menarche in the Jersey Girl Study
Full size table

Table 3 shows β and 95% CIs from mixed effect linear models. All mycoestrogen levels at baseline showed negative associations with average weight- and height-z-scores during the time between enrollment and menarche (unadjusted and adjusted models [for mid-parental height and family income]). α-ZAL levels were significantly associated with lower average height (adjusted β = − 0.23, 95%CI: -0.37,-0.08) and weight (adjusted β = − 0.18, 95%CI: -0.29,-0.08) at menarche z-scores in adjusted models. Similarly, total mycoestrogen levels were significantly associated with lower height (adjusted β = − 0.17, 95%CI: -0.33,-0.09) at menarche z-scores but not with weight at menarche z-scores. None of the examined associations were significant for ZEN concentrations considered individually.

Table 3 Mixed effect linear models for the association between mycoestrogen exposure (ng/ml) and height and weight z-scores at menarche in the Jersey Girl Study (n = 163)
Full size table

Discussion

This study is the first longitudinal study to evaluate ZEN exposure in relation to age at menarche and growth in healthy peri-pubertal girls. We observed that girls with detectable mycoestrogen levels were significantly shorter in stature at menarche than girls with mycoestrogen levels below the LOD. Girls with detectable α-ZAL concentrations were also less likely to have early menarche, but results were not statistically significant. The current study has expanded the findings from our previous report suggesting delayed pubertal development (i.e., thelarche) in girls with detectable mycoestrogen levels compared to girls with levels below the LOD [16].

Very few studies have measured mycoestrogen levels in relation to pubertal timing or growth [13,14,15,16]. Beyond our previous work in this population, a single study has evaluated body size [13] and no study has evaluated age at menarche. Our results contrast with those reported by Massart et al. suggesting that ZEN and α-zearalenol levels were positively associated with height and weight in girls. However, they measured mycotoxins in serum from girls (6–7 years old) participating in an idiopathic central precocious puberty case-control study. Additionally, they had a smaller sample size (n = 63) and only 6 girls had detectable levels of ZEN and α-ZAL. Finally, for those 6 girls with detectable serum ZEN levels, exposure (median ZEN: 0.12 ng/ml) was 10-fold lower than our measures in urine (median ZEN: 1.02 ng/ml). Thus given the differences in population, age at assessment, biospecimen type, and exposure levels, results of the two studies may not be readily comparable.

A larger literature has examined peri-pubertal growth and menarche in relation to other endocrine disruptors that act on sex steroid pathways. For example, in one study of adolescent girls, high intake of isoflavones, the predominant dietary phytoestrogens, was associated with older age at breast development [20]. Similarly in a diverse urban cohort, girls with higher levels of urinary phytoestrogens (i.e., daidzein, genistein, enterolactone) were less likely to have experienced Tanner Breast Stage 2+ than girls with low levels [21, 22]. Most recently, in the same cohort, Wolff et al. examined age at menarche in relation to urinary concentrations of phthalates and phenols, two classes of chemicals linked to altered estrogenic activity [23]. They showed that 2,5-Dichlorophenol was associated with early menarche (HR: 1.34; 95% CI: 1.06, 1.71) whereas enterolactone (HR: 0.82; 95% CI: 0.66, 1.03) and mono-3-carboxypropyl phthalate (HR: 0.73: 95% CI: 0.59, 0.91) were associated with later menarche. Finally, higher perfluorooctanoic acid (PFOA) and perfluorooctane sulfonate (PFOS) levels have been associated with delayed age of menarche [24]. Our results suggest that ZEN may have anti-estrogenic properties similar to those demonstrated in the phytoestrogen studies [20, 21, 23]. Like phytoestrogens, ZEN may inhibit the activity of key enzymes in the steroidogenic pathway including aromatase [25] and 17β-hydroxysteroid dehydrogenase [26], but more research is needed to fully understand these pathways.

Human exposure to ZEN is predominantly through food sources. ZEN can be found in the entire food chain through different products including cereal, milk, meat, dried fruit and spices. Although ZEN is not regulated in the U.S., the European Food Safety Authority (EFSA) established the tolerable daily intake for ZEN as 0.25 μg/kg body weight per day [12]. The European Commission also regulates limits for human consumption products (e.g., maize, cereals) and animal feed (e.g., maize, cereal, complementary feeding stuff). Our previous report suggested that beef and popcorn are the main sources of ZEN exposure in our study population [16], and meat (all types) was the primary source of ZEN exposure in local adult women [27], but additional work is needed to confirm these results and identify additional common sources of dietary exposure in humans.

ZEN metabolism plays a significant role in ZEN toxicity. ZEN follows two major biotransformation pathways: hydroxylation and conjugation [28]. Hydroxylation leads to α-zearalenol and β- zearalenol as well as α-ZAL, β-zearalanol, and zearalanone. Some of these hydroxylation metabolites tend to be more toxic than ZEN [29]. For example, in reporter gene assays examining estrogenic potency, ZEN was ~ 70 times less potent than α –zearalenol but twice as potent as β–zearalenol [29]. Conjugation results in ZEN glucuronide conjugates that are less toxic than ZEN. An in vitro study assessing ZEN biotransformation, reported that formation of ZEN glucuronides is a detoxification pathway that may attenuate estrogenic effects [30]. The proportion of ingested ZEN that goes through detoxification is not well understood and the relative contributions of the two biotransformation pathways may have different effects in human health. In the current study, ZEN urinary concentrations were higher than those of α-ZAL and other metabolites, suggesting that a portion of ZEN is excreted with no biotransformation. Other biomonitoring studies in adults have reported that some of the metabolites levels in urine are comparable or exceeded those of ZEN [31, 32]. We were not able to measure conjugated ZEN (or metabolites) which may explain the higher number of participant with undetectable levels of α-ZAL and other metabolites. Additionally, it may increase the potential for measurement error in our estimates. Exposure misclassification may be larger in the Cox regression results where exposure was categorized (<LOD, >LOD). It is difficult to speculate the effect of exposure misclassification in our results given the very limited toxicokinetics data on ZEN in humans. Furthermore, human biotransformation of these compounds may be influenced by sex, age, and diet adding to the variability of the biomarker. Additional biomarker(s) studies are needed to further investigate ZEN metabolism and toxicity.

It is well known that exposures during early life including childhood and puberty can influence cancer risk [1, 33]. For example, an estimated 10% reduction in breast cancer risk is expected for each two-year increase in age at menarche [34]. Growth metrics (including height and height velocity) during childhood have also been associated with cancer risk including breast, endometrial, testicular and prostate cancers [35,36,37,38]. Pubertal growth is mostly stimulated by estradiol and experimental studies have shown that estrogen may affect epiphyseal maturation, normal skeleton proportions, and bone mineralization [39,40,41]. Furthermore, there is some evidence that at low concentrations estrogens may accelerate linear growth whereas at high levels may stop linear growth [40]. ZEN is a structural estrogen analogue, able to mimic the activity of naturally occurring estrogens [9]. It has been hypothesized that ZEN can exert its estrogenic effect by affecting pituitary and gonadal function [9]. Experimental studies have shown that ZEN affects breast cancer development and progression through its estrogenicity [42,43,44]. In contrast with some of the experimental evidence, our results suggest that ZEN may also have anti-estrogenic properties. Differences in exposure levels (which are typically much higher in animal models than we observed in our study) and timing of exposure may also be important to consider. It is possible, for instance, that exposure to ZEN and/or its metabolites during critical developmental periods may suppress the production of 17β-hydroxysteroid dehydrogenase, ultimately resulting in anti-estrogenic properties.

Our study has several strengths and limitations of note. This is the first longitudinal study to evaluate the relationship between ZEN exposure and growth and pubertal outcomes in girls and we were able to retain 85% of participants through menarche. At the same time, like the other existing epidemiological studies of mycoestrogens, we had a relatively small sample size and exposure was based on a single urine sample collected at baseline. We were not able to measure conjugated metabolites which may lead to exposure misclassification and limit our ability to compare our results to other studies. While we had detailed anthropometrics at baseline, height and weight during the follow-up period was self-reported, which may have led to random error. However, this was reduced by the annual prospective data collection. Additionally, we had a homogenous population and differences in race and ethnicity could not be examined. This is important since some ethnic groups may be more vulnerable to mycotoxin exposures due to differences in dietary patterns [45], endogenous hormone concentrations [46, 47], and menarcheal timing [48]. In spite of these limitations, this study provides evidence that mycoestrogen exposure may impact girls’ growth and pubertal development. These results demonstrate a strong need for additional research to examine the impact of these chemicals on reproductive development at critical points in the life course.

Conclusion

Previous experimental evidence shows that mycoestrogens act as endocrine disruptors and their effect may depend on dose, hormonal environment, and critical windows of exposure. However, epidemiological studies examining important windows of exposure during childhood are lacking. Our study is the first one to examine mycoestrogens in relation to age at menarche. We demonstrated that girls with detectable mycoestrogen levels were significantly shorter in stature at menarche compared to girls with undetectable levels. Future studies in humans are extremely important given the evidence of widespread mycoestrogen exposure in human populations.

References

  1. 1.

    Biro FM, Deardorff J. Identifying opportunities for cancer prevention during preadolescence and adolescence: puberty as a window of susceptibility. J Adolesc Health. 2013;52(5 Suppl):S15–20.

  2. 2.

    Rudel RA, Fenton SE, Ackerman JM, Euling SY, Makris SL. Environmental exposures and mammary gland development: state of the science, public health implications, and research recommendations. Environ Health Perspect. 2011;119(8):1053–61.

  3. 3.

    Gore AC, Chappell VA, Fenton SE, Flaws JA, Nadal A, Prins GS, et al. EDC-2: the Endocrine Society's second scientific statement on endocrine-disrupting chemicals. Endocr Rev. 2015;36(6):E1–e150.

  4. 4.

    Nagel SC, vom Saal FS, Welshons WV. The effective free fraction of estradiol and xenoestrogens in human serum measured by whole cell uptake assays: physiology of delivery modifies estrogenic activity. Proc Soc Exp Biol Med. 1998;217(3):300–9.

  5. 5.

    Zhu CC, Hou YJ, Han J, Cui XS, Kim NH, Sun SC. Zearalenone exposure affects epigenetic modifications of mouse eggs. Mutagenesis. 2014;29(6):489–95.

  6. 6.

    Li Y, He X, Yang X, Huang K, Luo Y, Zhu L, et al. Zinc inhibits the reproductive toxicity of Zearalenone in immortalized murine ovarian granular KK-1 cells. Sci Rep. 2015;5:14277.

  7. 7.

    Dees C, Foster JS, Ahamed S, Wimalasena J. Dietary estrogens stimulate human breast cells to enter the cell cycle. Environ Health Perspect. 1997;105(Suppl 3):633–6.

  8. 8.

    Withanage GS, Murata H, Koyama T, Ishiwata I. Agonistic and antagonistic effects of zearalenone, an etrogenic mycotoxin, on SKN, HHUA, and HepG2 human cancer cell lines. Vet Hum Toxicol. 2001;43(1):6–10.

  9. 9.

    Kowalska K, Habrowska-Gorczynska DE, Piastowska-Ciesielska AW. Zearalenone as an endocrine disruptor in humans. Environ Toxicol Pharmacol. 2016;48:141–9.

  10. 10.

    EFSA. Scientific Opinion on the risks for public health related to the presence of zearalenone in food. EFSA J. 2011;9(6):2197.

  11. 11.

    Mally A, Solfrizzo M, Degen GH. Biomonitoring of the mycotoxin Zearalenone: current state-of-the art and application to human exposure assessment. Arch Toxicol. 2016;90(6):1281–92.

  12. 12.

    EFSA. Appropriateness to set a group health-based guidance value for zearalenone and its modified forms. EFSA J. 2016;4:4425.

  13. 13.

    Massart F, Meucci V, Saggese G, Soldani G. High growth rate of girls with precocious puberty exposed to estrogenic mycotoxins. J Pediatr. 2008;152(5):690–5 5.e1.

  14. 14.

    Asci A, Durmaz E, Erkekoglu P, Pasli D, Bircan I, Kocer-Gumusel B. Urinary zearalenone levels in girls with premature thelarche and idiopathic central precocious puberty. Minerva Pediatra. 2014;66:571–8.

  15. 15.

    Szuets P, Mesterhazy A, Falkay G, Bartok T. Early telarche symptoms in children and their relations to zearalenon contamination in foodstuffs. Cereal Res Commun. 1997;25(3):429–36.

  16. 16.

    Bandera EV, Chandran U, Buckley B, Lin Y, Isukapalli S, Marshall I, et al. Urinary mycoestrogens, body size and breast development in New Jersey girls. Sci Total Environ. 2011;409(24):5221–7.

  17. 17.

    Pearson MA, Lu C, Schmotzer BJ, Waller LA, Riederer AM. Evaluation of physiological measures for correcting variation in urinary output: implications for assessing environmental chemical exposure in children. J Expo Sci Environ Epidemiol. 2009;19(3):336–42.

  18. 18.

    Hornung R, Reed L. Estimation of average concentration in the presence of nondetectable values. App Occup Environ Hyg. 1990;5:46–51.

  19. 19.

    Kliegman R, Marcdante K, Jenson H, Behrman R. Essentials of pediatrics. 5th ed. Cambridge: Elsevier Saunders; 2006.

  20. 20.

    Cheng G, Remer T, Prinz-Langenohl R, Blaszkewicz M, Degen GH, Buyken AE. Relation of isoflavones and fiber intake in childhood to the timing of puberty. Am J Clin Nutr. 2010;92(3):556–64.

  21. 21.

    Wolff MS, Britton JA, Boguski L, Hochman S, Maloney N, Serra N, et al. Environmental exposures and puberty in inner-city girls. Environ Res. 2008;107(3):393–400.

  22. 22.

    Wolff MS, Teitelbaum SL, Pinney SM, Windham G, Liao L, Biro F, et al. Investigation of relationships between urinary biomarkers of phytoestrogens, phthalates, and phenols and pubertal stages in girls. Environ Health Perspect. 2010;118(7):1039–46.

  23. 23.

    Wolff MS, Pajak A, Pinney SM, Windham GC, Galvez M, Rybak M, et al. Associations of urinary phthalate and phenol biomarkers with menarche in a multiethnic cohort of young girls. Reprod Toxicol (Elmsford, NY). 2017;67:56–64.

  24. 24.

    Lopez-Espinosa MJ, Fletcher T, Armstrong B, Genser B, Dhatariya K, Mondal D, et al. Association of Perfluorooctanoic Acid (PFOA) and Perfluorooctane sulfonate (PFOS) with age of puberty among children living near a chemical plant. Environ Sci Technol. 2011;45(19):8160–6.

  25. 25.

    Adlercreutz H, Bannwart C, Wahala K, Makela T, Brunow G, Hase T, et al. Inhibition of human aromatase by mammalian lignans and isoflavonoid phytoestrogens. J Steroid Biochem Mol Biol. 1993;44(2):147–53.

  26. 26.

    Rice S, Mason HD, Whitehead SA. Phytoestrogens and their low dose combinations inhibit mRNA expression and activity of aromatase in human granulosa-luteal cells. J Steroid Biochem Mol Biol. 2006;101(4–5):216–25.

  27. 27.

    Mauro T, Hao L, Pop LC, Buckley B, Schneider SH, Bandera EV, et al. Circulating zearalenone and its metabolites differ in women due to body mass index and food intake. Food Chem Toxicol. 2018;116(Pt B):227–32.

  28. 28.

    Ediage EN, Di Mavungu JD, Song S, Wu A, Van Peteghem C, De Saeger S. A direct assessment of mycotoxin biomarkers in human urine samples by liquid chromatography tandem mass spectrometry. Anal Chim Acta. 2012;741:58–69.

  29. 29.

    Frizzell C, Ndossi D, Verhaegen S, Dahl E, Eriksen G, Sorlie M, et al. Endocrine disrupting effects of zearalenone, alpha- and beta-zearalenol at the level of nuclear receptor binding and steroidogenesis. Toxicol Lett. 2011;206(2):210–7.

  30. 30.

    Frizzell C, Uhlig S, Miles CO, Verhaegen S, Elliott CT, Eriksen GS, et al. Biotransformation of zearalenone and zearalenols to their major glucuronide metabolites reduces estrogenic activity. Toxicol In vitro. 2015;29(3):575–81.

  31. 31.

    Ali N, Degen GH. Urinary biomarkers of exposure to the mycoestrogen zearalenone and its modified forms in German adults. Arch Toxicol. 2018;92(8):2691–700.

  32. 32.

    Sarkanj B, Ezekiel CN, Turner PC, Abia WA, Rychlik M, Krska R, et al. Ultra-sensitive, stable isotope assisted quantification of multiple urinary mycotoxin exposure biomarkers. Anal Chim Acta. 2018;1019:84–92.

  33. 33.

    Clarke MA, Joshu CE. Early life exposures and adult Cancer risk. Epidemiol Rev. 2017;39(1):11–27.

  34. 34.

    Hsieh CC, Trichopoulos D, Katsouyanni K, Yuasa S. Age at menarche, age at menopause, height and obesity as risk factors for breast cancer: associations and interactions in an international case-control study. Int J Cancer. 1990;46(5):796–800.

  35. 35.

    Bandera EV, Chandran U, Zirpoli G, Ciupak G, Bovbjerg DH, Jandorf L, et al. Body size in early life and breast cancer risk in African American and European American women. Cancer Causes Control. 2013;24(12):2231–43.

  36. 36.

    Aarestrup J, Gamborg M, Ulrich LG, Sorensen TI, Baker JL. Childhood body mass index and height and risk of histologic subtypes of endometrial cancer. Int J Obes. 2016;40(7):1096–102.

  37. 37.

    Cook MB, Gamborg M, Aarestrup J, Sorensen TI, Baker JL. Childhood height and birth weight in relation to future prostate cancer risk: a cohort study based on the Copenhagen school health records register. Cancer Epidemiol Biomarkers Prev. 2013;22(12):2232–40.

  38. 38.

    Ahlgren M, Melbye M, Wohlfahrt J, Sorensen TI. Growth patterns and the risk of breast cancer in women. N Engl J Med. 2004;351(16):1619–26.

  39. 39.

    Smith EP, Boyd J, Frank GR, Takahashi H, Cohen RM, Specker B, et al. Estrogen resistance caused by a mutation in the estrogen-receptor gene in a man. N Engl J Med. 1994;331(16):1056–61.

  40. 40.

    Aksglaede L, Juul A, Leffers H, Skakkebaek NE, Andersson AM. The sensitivity of the child to sex steroids: possible impact of exogenous estrogens. Hum Reprod Update. 2006;12(4):341–9.

  41. 41.

    Veldhuis JD, Metzger DL, Martha PM Jr, Mauras N, Kerrigan JR, Keenan B, et al. Estrogen and testosterone, but not a nonaromatizable androgen, direct network integration of the hypothalamo-somatotrope (growth hormone)-insulin-like growth factor I axis in the human: evidence from pubertal pathophysiology and sex-steroid hormone replacement. J Clin Endocrinol Metab. 1997;82(10):3414–20.

  42. 42.

    Khosrokhavar R, Rahimifard N, Shoeibi S, Hamedani MP, Hosseini MJ. Effects of zearalenone and alpha-Zearalenol in comparison with Raloxifene on T47D cells. Toxicol Mech Methods. 2009;19(3):246–50.

  43. 43.

    Ahamed S, Foster JS, Bukovsky A, Diehl JA, Wimalasena J. Removal of Cdk inhibitors through both sequestration and downregulation in zearalenone-treated MCF-7 breast cancer cells. Mol Carcinog. 2002;34(1):45–58.

  44. 44.

    Zhong S, Liu S, Chen S, Lin H, Wang W, Qin X. Zeranol stimulates proliferation and aromatase activation in human breast preadipocytes. Mol Med Rep. 2016;14(1):1014–8.

  45. 45.

    Batis C, Hernandez-Barrera L, Barquera S, Rivera JA, Popkin BM. Food acculturation drives dietary differences among Mexicans, Mexican Americans, and non-Hispanic whites. J Nutr. 2011;141(10):1898–906.

  46. 46.

    Henderson BE, Bernstein L, Ross RK, Depue RH, Judd HL. The early in utero oestrogen and testosterone environment of blacks and whites: potential effects on male offspring. Br J Cancer. 1988;57(2):216–8.

  47. 47.

    Troisi R, Hoover RN, Thadhani R, Hsieh CC, Sluss P, Ballard-Barbash R, et al. Maternal, prenatal and perinatal characteristics and first trimester maternal serum hormone concentrations. Br J Cancer. 2008;99(7):1161–4.

  48. 48.

    Braithwaite D, Moore DH, Lustig RH, Epel ES, Ong KK, Rehkopf DH, et al. Socioeconomic status in relation to early menarche among black and white girls. Cancer Causes Control. 2009;20(5):713–20.

Download references

Acknowledgements

We thank all participants in the Jersey Girl Study for their time and collaboration in our research.

Funding

This project was supported by the National Institute of Environmental Health Sciences (P30 ES005022) and the Rutgers Cancer Institute of New Jersey, New Brunswick, NJ.

Availability of data and materials

The datasets generated and/or analyzed during the current study are not publicly available due to parts of the data still under analysis and unpublished but are available from the corresponding author on reasonable request.

Author information

Affiliations

  1. Rutgers Cancer Institute of New Jersey, 195 Little Albany St., New Brunswick, NJ, 08901, USA
    • Zorimar Rivera-Núñez
    • , Elizabeth A. Szamreta
    • , Bo Qin
    • , Yong Lin
    • , Helmut Zarbl
    •  & Elisa V. Bandera
  2. Environmental and Occupational Health Sciences Institute (EOHSI), Rutgers University, 170 Frelinghuysen Rd, Piscataway, NJ, 08854, USA
    • Emily S. Barrett
    • , Helmut Zarbl
    •  & Brian Buckley
  3. Rutgers School of Public Health, 683 Hoes Lane West, Piscataway, NJ, 08854, USA
    • Emily S. Barrett
    • , Elizabeth A. Szamreta
    • , Yong Lin
    • , Brian Buckley
    •  & Elisa V. Bandera
  4. Department of Nutritional Sciences, Rutgers University, 65 Dudley Rd, New Brunswick, NJ, 08901-8520, USA
    • Sue A. Shapses
Authors
  1. Zorimar Rivera-Núñez
    View author publications
    You can also search for this author in
  2. Emily S. Barrett
    View author publications
    You can also search for this author in
  3. Elizabeth A. Szamreta
    View author publications
    You can also search for this author in
  4. Sue A. Shapses
    View author publications
    You can also search for this author in
  5. Bo Qin
    View author publications
    You can also search for this author in
  6. Yong Lin
    View author publications
    You can also search for this author in
  7. Helmut Zarbl
    View author publications
    You can also search for this author in
  8. Brian Buckley
    View author publications
    You can also search for this author in
  9. Elisa V. Bandera
    View author publications
    You can also search for this author in

Contributions

ZRN conducted statistical analyses and wrote the manuscript draft. ESB critically review the manuscript and analyses, and contributed to the writing. EAS assisted in data collection and analysis. YL assisted in statistical analysis. SAS, BQ, HZ critically review the manuscript. BB critically reviewed the manuscript and wrote analytical protocol details. EVB designed the study and critically reviewed the analyses and manuscript. All authors read and approved the final manuscript.

Corresponding author

Correspondence to Zorimar Rivera-Núñez.

Ethics declarations

Ethics approval and consent to participate

Parental consent and girls’ assent were obtained before data collection. This study was approved by the Rutgers Health Sciences Institutional Review Board.

Consent for publication

Not applicable.

Competing interests

The authors declare that they have no competing interests.

Publisher’s Note

Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.

Rights and permissions

Open Access This article is distributed under the terms of the Creative Commons Attribution 4.0 International License (http://creativecommons.org/licenses/by/4.0/), which permits unrestricted use, distribution, and reproduction in any medium, provided you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons license, and indicate if changes were made. The Creative Commons Public Domain Dedication waiver (http://creativecommons.org/publicdomain/zero/1.0/) applies to the data made available in this article, unless otherwise stated.

Reprints and Permissions

About this article

Verify currency and authenticity via CrossMark

Cite this article

Rivera-Núñez, Z., Barrett, E.S., Szamreta, E.A. et al. Urinary mycoestrogens and age and height at menarche in New Jersey girls. Environ Health 18, 24 (2019). https://doi.org/10.1186/s12940-019-0464-8

Download citation

Keywords

  • Zearalenone
  • (α-ZAL)
  • Mycoestrogens
  • Puberty
  • Endocrine disruptors

Comments

By submitting a comment you agree to abide by our Terms and Community Guidelines. If you find something abusive or that does not comply with our terms or guidelines please flag it as inappropriate. Please note that comments may be removed without notice if they are flagged by another user or do not comply with our community guidelines.

Environmental Health

ISSN: 1476-069X