Environmental and Human Health Risks of Estrogenic Compounds: A Critical Review of Sustainable Management Practices

Abstract

The concentrations of estrogens and xenoestrogens in the environment are rising rapidly, posing significant and multifaceted risks to human health and ecosystems. It is imperative for governments to develop policies that leverage sustainable technologies to mitigate the presence of pharmaceutical estrogenic compounds in the environment. This review examines the global environmental and human health risks associated with indigenous estrogens and synthetic pharmaceutical xenoestrogens, while critically evaluating sustainable approaches to their management. A total of 28 studies, published between December 2013 and 18 January 2024, and sourced from PubMed and Scopus, were systematically reviewed. Most of these studies focused on estrogenic compounds in aquatic environments where they contribute to reproductive and developmental abnormalities in fish and may enter the human food chain, primarily through fish consumption. Sustainable methods for removing or neutralizing estrogenic compounds include adsorption, filtration, and enzymatic degradation. Additionally, technologies such as activated sludge processes and high-rate algal ponds demonstrate promise for large-scale applications; however, further research and standardized operational guidelines are needed to optimize their efficiency and sustainability. This review has concluded that ECs can have severe consequences on the environment, most notably, impairment of reproductive functions in fish and humans, underscoring the urgent need for governments to implement drug take-back programs, establish evidence-based guidelines for wastewater and pharmaceutical waste treatment, and set enforceable thresholds for estrogenic compounds in surface and drinking water. Existing regulations such as the UK’s Regulation on the registration, evaluation, authorization, and restriction of chemicals and the United States’ National Primary Drinking Water Regulations can be modified to include ECs as dangerous chemicals to aid in maintaining safe EC levels”. Such measures are critical for reducing the environmental concentrations of pharmaceutical estrogenic compounds and safeguarding both public health and ecological integrity.

1. Introduction

Estrogen is a steroid hormone involved in regulating various bodily functions, including those of the neuroendocrine, vascular, skeletal, immune, central nervous system, and reproductive systems [1,2]. The three main naturally occurring estrogens in the human body are estrone (E1), estradiol (E2), and estriol (E3). E1 and E2 are produced in the ovaries and adrenal glands, while E3, a metabolite of E1 and E2, is primarily produced by the placenta during pregnancy [3,4]. E1 is the primary form of estrogen after menopause, while E2 is predominant before menopause. Estrogens are also produced in the male body from androgens such as testosterone [5]. What is unique about steroids in comparison to other cell-signaling molecules is their ability to permeate the cell membrane and enter the nucleus to alter gene expression [6]. However, naturally occurring estrogens are not the only compounds that can be estrogenic. Molecules that are foreign to the body and have a similar enough structure to bind to estrogen receptors are considered xenoestrogens [7].

Estrogenic compounds (ECs) are molecules that interact with estrogen receptors on cell membranes or in the nuclei to induce biological responses [8]. This may include indigenous estrogens produced in the human body, phytoestrogens from plants, mycotoxins from fungi, and xenoestrogens, which are synthetic molecules that mimic estrogen [9]. Xenoestrogens have a wide range of industrial applications such as in plastics production, preservatives, and personal care products [10]. Common categories of synthetic xenoestrogens include bisphenols, parabens, and phthalates [10]. Xenoestrogens are also produced for therapeutic purposes. For example, Ethinyl estradiol (EE2) is a very common xenoestrogen found in hormonal birth control and hormone replacement therapy that is 200 times more potent than E2 [11].

Estrogenic compounds can be easily released into the natural environment and may have unintended negative consequences [12]. Estrogens that are naturally produced in the body can be released through excrement and urine, particularly by pregnant animals [13]. The largest source of naturally occurring estrogen is livestock in the agricultural industry [13]. Their excrement is distributed in the environment as fertilizer and contaminates the waterways through runoff [14]. Estrogenic compounds can also be released through landfills and general plastic pollution, which can leach chemicals such as bisphenol A (BPA) [15].

Once these estrogens enter the environment, their half-life can range from 12 h to 180 days, depending on the presence of UV light, microorganisms, oxygen, and other environmental factors [16]. During aerobic microorganism degradation in aerated soil, the half-lives of E1, E2, and E3 were 2.8–4.9, 0.8–1.1, and 0.7–1.7 days, respectively. In river water, however, E1, E2, and EE2 were 2–3, 2–3, and 4–6 days, respectively [13,17]. Generally, EE2 is the most resilient steroidal estrogen to decompose, and it is the most biologically active. Various microbes can metabolize estrogen, but they can also convert one form of estrogen into another. For example, nitrifying bacteria can convert E1 into E3 and Sphingobacterium sp. can convert EE2 to E1. This transformation between different types of estrogen may also vary depending on other compounds present in the system such as methanogenic, sulfate, iron, and nitrate-reducing agents [13].

The majority of EC management processes focus on aquatic environments, primarily wastewater treatment plants. Wastewater treatment plants have different methods of processing water due to a lack of standardized regulations regarding wastewater treatment and various factors such as cost, wastewater composition, and environmental impacts [18]. Generally, treatment involves a four-step process: preliminary debris removal followed by primary, secondary, and tertiary treatment [19]. Primary treatment removes solids, oils, and fats by settling, sedimentation, and filtration [19]. Secondary treatment removes remaining suspended solids and microbes through methods such as aerobic treatment, anaerobic treatment, bioreactors, activated sludge, and biological filters [19]. Lastly, tertiary treatment is the advanced removal of chemical contaminants such as detergents and toxic compounds through chemical precipitation, neutralization, adsorption, disinfection, and ion exchange [20]. Advanced treatments like nanofiltration (NF), membrane bioreactors (MBRs), reverse osmosis (RO) ultrafiltration (UF), and advanced oxidation processes (AOPs) are efficient in removing estrogens [20]. However, these processes often come with high costs and are not ubiquitous [21].

If ECs are improperly managed, they can be released into the environment where they can severely impact a wide range of human bodily systems and disrupt ecosystems. In the human body specifically, exposure to estrogenic compounds can increase the risk of certain cancers such as breast, skin, liver, and testicular cancers [22]. They may also cause other conditions such as diabetes, autism spectrum disorder, prostate hyperplasia, reproductive abnormalities, and thyroid disease [23,24]. Estrogen is also important in neurological development, especially during fetal and perinatal life, where it is involved in brain development and controlling sexual behavior such as gender identity [25]. In animals, ECs can contaminate the ecosystems and disrupt the sex ratios of vulnerable animal populations through the feminization of males [26]. Their effects have been documented in both wild and domestic animals with significant interruptions in aquatic biomass, impaired vision in cats, infertility in sheep, and morphological abnormalities in cows [13].

Estrogens and xenoestrogens are becoming increasingly concerning as their concentrations rapidly increase in the environment [13]. The impacts that estrogenic compounds can have on human health and the environment are vast and complex as they can easily spread between water, soil, and air [26]. It is more critical than ever for governments to create policies and industries to utilize sustainable technologies to treat or reduce the amount of pharmaceutical estrogenic compounds in the environment, which to date remain opaque. Current reviews on this topic focus broadly on the effects of ECs on the environment and health [13,21]. However, there is a gap in the literature focusing on pharmaceutical estrogens specifically, the sustainability of estrogen management, and the role that federal and regional government can play in regulating pharmaceutical estrogen management. This review, therefore, aims to investigate the global environmental and human health risks of indigenous estrogens and synthetic pharmaceutical xenoestrogens in the environment and to critically appraise the sustainable methods of processing them.

2. Materials and Methods

The methodology in this review follows the Preferred Reporting Items for Systematic reviews and Meta-Analyses (PRISMA) guidelines (Figure 1 and Supplementary Materials).

Table 1. PECO table used to formulate the research question.

Population	Individuals who live in areas with high levels of estrogenic compounds in the environment
Exposure	Exposure to native estrogens and pharmaceutical xenoestrogens through water, food, and/or soil
Comparative	Individuals who experience little to no exposure to environmental estrogens
Outcome	Increased risk of breast, skin, liver, and testicular cancer; diabetes; autism spectrum disorder; prostate hyperplasia; reproductive abnormalities; and thyroid disease

is a Population Exposure Control Outcome (PECO) table used to formulate the research question and search terms. Our population is people who live near areas that contain high levels of estrogenic compounds (Table 1). The exposure is pharmaceutical xenoestrogens and native estrogens. The control group would include individuals who experience little to no exposure to estrogenic compounds from the environment. Lastly, the outcome is the adverse health effects associated with increased estrogen exposure (Table 1).

2.1. Eligibility Criteria

This review examined published primary research discussing the impact of estrogens and ECs from pharmaceutical sources on humans and our environment (food, soil, air, or water) as well as the management practices of these pharmaceutical ECs.

2.2. Search Strategy

Articles published from December 2013 to 18 January 2024 were searched using PubMed and Scopus databases with the following keywords and Boolean operators: (healthcare OR drug OR medical OR pharmaceutical) AND (estrogen OR oestrogen OR estrogenic OR oestrogenic) AND (environment OR food OR soil OR water OR air) AND (waste management OR waste processing OR environment management). After the initial search, the terms pollution and contamination were included, but significant differences were not found.

All articles written in English were selected. Search results were exported to Zotero (https://www.zotero.org/ accessed on 20 November 2024) citation manager, where results were de-duplicated. The titles and abstracts of the studies were analyzed to ensure relevance to the topic.

Papers were sorted into “yes”, “no”, and “maybe” categories. Papers in the “maybe” category were read in full to determine whether they were appropriate. The majority of excluded papers were removed due to irrelevance as many did not directly discuss pharmaceutical estrogenic compounds or natural estrogens. Relevance was determined using the PECO Table (Table 1). The included papers were then studied in full.

2.3. Quality Appraisal

Selected articles were assessed using the Mixed Methods Appraisal tool [27]. The questions that were used in this tool were dependent on the type of research method used in the paper (

Table 2. Risk of bias checklist formatted off of the Mixed Methods Appraisal Tool Version 2018.

Authors	Title	Are There Clear Research Questions?	Do the Collected Data Address the Research Questions?	Are the Research Methods Appropriate for Answering the Research Question?	Are the Findings Adequately Derived from Data or Observations?	Are the Interpretations of the Results Sufficiently Substantiated by Data or Observations?	Did the Researchers Address/Minimize Possible Sources of Bias (How)?	Total Score
Meyer et al. [28]	Environmental Xenoestrogens Super-Activate a Variant Murine ER Beta in Cholangiocytes.	Y	Y	Y	Y	Y	Y	6
Wakim et al. [29]	Unveiling the presence of endocrine disrupting chemicals in northern French soils: Land cover variability and implications.	Y	Y	Y	Y	Y	Y	6
Sanseverino et al. [30]	Holistic approach to chemical and microbiological quality of aquatic ecosystems impacted by wastewater effluent discharges	Y	Y	Y	Y	Y	Y	6
Dai et al. [31]	Human health risk assessment of selected pharmaceuticals in the five major river basins, China	Y	Y	Y	Y	Y	Y	6
Liu et al. [32]	Identification, contribution, and estrogenic activity of potential EDCs in a river receiving concentrated livestock effluent in Southern Taiwan	Y	Y	Y	Y	Y	N	5
Arya et al. [33]	Pharmaceutical chemicals, steroids and xenoestrogens in water, sediments and fish from the tidal freshwater Potomac River (Virginia, USA)	Y	Y	Y	Y	Y	Y	6
Xu et al. [34]	The occurrence and ecological risks of endocrine disrupting chemicals in sewage effluents from three different sewage treatment plants, and in natural seawater from a marine reserve of Hong Kong	Y	Y	Y	Y	Y	Y	6
Comber et al. [35]	Active pharmaceutical ingredients entering the aquatic environment from wastewater treatment works: A cause for concern?	Y	Y	Y	Y	Y	Y	6
Hom-Diaz et al. [36]	Microalgae cultivation on wastewater digestate: β-estradiol and 17α-ethynylestradiol degradation and transformation products identification.	Y	Y	Y	Y	Y	N/A	5
Xu et al. [37]	Optimizing Adsorption of 17α-Ethinylestradiol from Water by Magnetic MXene Using Response Surface Methodology and Adsorption Kinetics, Isotherm, and Thermodynamics Studies.	Y	Y	Y	Y	Y	N	5
Matamoros et al. [38]	Capability of microalgae-based wastewater treatment systems to remove emerging organic contaminants: a pilot-scale study.	Y	Y	Y	Y	Y	N	5
Deng et al. [39]	Competitive Degradation of Steroid Estrogens by Potassium Permanganate Combined with Ultrasound.	Y	Y	Y	Y	Y	Y	6
Petrie et al. [40]	Assessing potential modifications to the activated sludge process to improve simultaneous removal of a diverse range of micropollutants.	Y	Y	Y	Y	Y	Y	6
Mills et al. [41]	Removal of ecotoxicity of 17α-ethinylestradiol using TAML/peroxide water treatment.	Y	Y	Y	Y	Y	N	5
Ma et al. [42]	Simultaneous Degradation of Estrone, 17β-Estradiol and 17α-Ethinyl Estradiol in an Aqueous UV/H2O2 System.	Y	Y	Y	Y	Y	N	5
Yang et al. [43]	Removal of antibiotics and estrogens by nanofiltration and reverse osmosis membranes	Y	Y	Y	Y	Y	Y	6
Zhao et al. [44]	Biotransformation of Current-Use Progestin Dienogest and Drospirenone in Laboratory-Scale Activated Sludge Systems Forms High-Yield Products with Altered Endocrine Activity	Y	Y	Y	Y	Y	Y	6
Mainetti et al. [45]	Broad diversity of bacteria degrading 17ß-estradiol-3-sulfate isolated from river sediment and biofilm at a wastewater treatment plant discharge	Y	Y	Y	Y	Y	N	5
Islam et al. [46]	Secondary treatment phase of tertiary wastewater treatment works significantly reduces estrogenic load	Y	Y	Y	Y	Y	Y	6
Alves et al. [47]	Biosorption of organic micropollutants onto lignocellulosic-based material	Y	Y	Y	Y	Y	N	5
Spina et al. [48]	Ecofriendly laccases treatment to challenge micropollutants issue in municipal wastewaters	Y	Y	Y	Y	Y	Y	6
Castillo Meza et al. [49]	Detection and removal of biologically active organic micropollutants from hospital wastewater	Y	Y	Y	Y	Y	N	5
Valitalo et al. [50]	Effect-based assessment of toxicity removal during wastewater treatment	Y	Y	Y	Y	Y	Y	6
King et al. [51]	Concentrations of levonorgestrel and ethinylestradiol in wastewater effluents: Is the progestin also cause for concern?	Y	Y	Y	Y	Y	Y	6
Matrtins et al. [52]	Biogenic platinum and palladium nanoparticles as new catalysts for the removal of pharmaceutical compounds	Y	Y	Y	Y	Y	N	5
Ribeiro et al. [53]	Environmental friendly method for urban wastewater monitoring of micropollutants defined in the Directive 2013/39/EU and Decision 2015/495/EU	Y	Y	Y	Y	Y	N	5
Wildhaber et al. [54]	Novel test procedure to evaluate the treatability of wastewater with ozone	Y	Y	Y	Y	Y	N	5
Osachoff et al. [55]	Evaluating the treatment of a synthetic wastewater containing a pharmaceutical and personal care product chemical cocktail: Compound removal efficiency and effects on juvenile rainbow trout	Y	Y	Y	Y	Y	N	5

). These acted as guidelines to critically appraise the studies.

2.4. Risk of Bias

The risk of bias for each of the studies included in this paper was assessed with a list of 6 questions derived from the Mixed Methods Appraisal Tool Version 2018, a set of questions that are used to evaluate the quality of empirical research. Questions were answered with “yes” or “no” answers. Each “yes” answer is worth 1 point and each “no” answer is worth 0 points. Points were summed to create a score that was used to compare each study’s validity (Table 2).

3. Results

3.1. Search Results

There were 219 articles from the initial filtered search. After reviewing the papers for relevance, 191 studies were removed, leaving 28 papers (see Figure 1). The majority of excluded papers were removed due to irrelevance. These studies were then assessed for risk of bias and none were removed in this process.

3.2. Study Characteristics

The studies included in this review came from 13 countries and used many different study designs to analyze pharmaceutical xenoestrogens and naturally occurring estrogens in water and soil.

Table 3. This table displays the specific papers that fall into various categories of study characteristics.

Country investigated	United Kingdom [28,35,40,41], France [29], Italy [30,47], China [31,34,37,39,42,43], Taiwan [32], the United States [33,44,49], Spain [36,38], Switzerland [45,54], Australia [46,51], Brazil [47], Finland [50], Portugal [52,53], and Canada [54]
Study design	Laboratory experimental studies [34,36,37,38,39,40,41,42,43,44,47,48,52,53,54,55], field studies [28,29,30,32,33,34,45,46,48,49,50,51,53], and secondary analyses [31,35]
Environment studied	Soil [28,29,45], water [30,31,32,34,35,36,37,38,39,40,41,42,43,44,46,47,48,49,50,51,52,53,54,55], both [33]
Sampling method	24 h composite water samples [48,49,50,54], cross-sectional sampling [28,29,36,44,45,48,49,50,51], longitudinal sampling [30,32,33,34,35,38,40,46,53,54]
Estrogen studied	E1 [29,31,32,33,34,35,39,40,42,43,46,53,55], E2 [29,31,32,33,35,36,39,40,42,43,46,47,52,53], and EE2 [29,31,32,33,35,36,37,39,40,41,42,43,46,47,51,53,55]

provides an outline of the characteristics of each study. Studies were published between 2014 to 2023 and were carried out in the United Kingdom, France, Italy, China, Taiwan, the United States, Spain, Switzerland, Australia, Brazil, Finland, Portugal, and Canada (Table 3). The different study designs included laboratory experimental studies, field studies, and secondary analyses (Table 3). Three of the studies investigated estrogenic compounds in soil while 24 were in water, and one discussed both (Table 3). Four studies utilized 24 h composite samples when studying estrogens and xenoestrogens in water. Nine studies utilized cross-sectional sampling, while 10 studies sampled longitudinally. Details about sampling including sample size and duration of sampling are included in

Table 4. This table shows the characteristics of each study including their main objectives, study design or data source, and general findings.

Author, Year	Title	Aim of Study	Location	Research Design and Examined Compounds	Organism Evaluated	Sampling Method	Outcomes
Meyer et al., 2016 [28]	Environmental Xenoestrogens Super-Activate a Variant Murine ER Beta in Cholangiocytes.	Investigating xenoestrogen presence in landfills	Northeast England	Field Study Unspecified	Mouse cell line and human breast cancer cell line	- Shallow soil samples within 200 m of active landfills in peri-urban areas	- 6 landfill sample sites contained oestrogenic chemicals - These oestrogens behaved as irreversible agonists of a murine ERβ variant in a pancreatohepatobiliary cell context - Acute exposure of mice to a pooled oestrogenic environmental sample resulted in activation of the ERβgene involved in cholestatic and primary biliary cholangitis
Wakim et al., 2024 [29]	Unveiling the presence of endocrine disrupting chemicals in northern French soils: Land cover variability and implications.	Analyzing endocrine disrupting chemicals in soil	Northern France	Field Study Estrone, estradiol, estriol, alpha-ethinylestradiol, bisphenol A	-	- 240 soil samples from 30 sites with diverse landscapes and use patterns	- High concentration of 29.391 ng/g of 17β-estradiol and 47.16 ng/g of 17α-ethinylestradiol in soils - E2 and E3 had the lowest detection frequency, being detected in 17% of sites - Concentration of the EDCs is higher in forest lands compared to agricultural lands (p < 0.0001), highly influenced by the high concentrations of αEE2 and E3 in forest and semi-natural lands - Urban and grassland sites had concentrations closer to the median for EDCs - Hormones excreted by humans and animals have a half-life of 1–10 days in soil and degrade rapidly under high temperature and aerobic conditions - EE2 is more resistant to degradation in the environment, and therefore may pose a more significant environmental risk - Reasons for high levels of estrogens may include runoff from agricultural practices and sewage sludge
Sanseverino et al., 2022 [30]	Holistic approach to chemical and microbiological quality of aquatic ecosystems impacted by wastewater effluent discharges	Analysis of contaminants that are leached into aquatic environments from wastewater treatment plant effluent	North Italy	Field Study Unspecified estrogenic compounds	-	- Samples from the influent, after biological treatment and chemical treatment, effluent, and 5 km outside of the wastewater treatment plants (WWTPs) across 4 months	- Estrogenicity was detected in influent, effluent, and 5 km downstream the treatment plant indicating that this WWTP was not effective in removing estrogen from the water
Dai et al., 2021 [31]	Human health risk assessment of selected pharmaceuticals in the five major river basins, China	Evaluate the human health risks from pharmaceutical exposure through drinking water and fish consumption	China (Yangtze, Haihe, Pearl, Songliao, and Yellow River Basins)	Meta-analysis 17β-Ethinyl estradiol (EE2), 17βestradiol (E2), estriol (E3), estrone(E1)	Human	- Meta-analysis of water data	- Intake of pharmaceuticals from drinking water was significantly lower than from eating fish - Estrogen had one of the highest risk quotients of all pharmaceuticals tested among all age groups - Highest risk for estrogenic compounds was found in the Haihe River Basin and Songliao River Basin among children
Liu et al., 2018 [32]	Identification, contribution, and estrogenic activity of potential EDCs in a river receiving concentrated livestock effluent in Southern Taiwan	Measure endocrine-disrupting chemicals in the Wuluo River	Southern Taiwan (Wuluo River)	Field Study Bisphenol A, 4-nonylphenol, t-nonylphenol, octylphenol, nonylphenol mono-ethoxylate, nonylphenol di-ethoxylate, estrone, 17 β-estradiol, estriol, 17ß-ethinylestradiol, diethylstilbestrol, methyl paraben, ethyl paraben, propyl paraben, butyl paraben	-	- 12 water sampling sites receiving household or animal wastewaters or located at intersections of the Wuluo river across 4 seasons - 1 site dried up and was replaced with another similar location	- In the fall, highest detected concentration: 147.63 ng/L for BPA - In the winter, highest detected concentration: 661.26 ng/L for nonylphenol mono-ethoxylate - In the summer, highest concentration: 1384.6 ng/L for BPA- E1, benzophenone, nonylphenol di-ethoxylate, and benzophenone-3 were detected in over 90% of samples - Largest contributors to estrogenic activity in the water were E1 and E2
Arya et al., 2017 [33]	Pharmaceutical chemicals, steroids and xenoestrogens in water, sediments and fish from the tidal freshwater Potomac River (Virginia, USA)	Analyzing pharmaceutical chemicals and steroids in water, sediments, and fish species near wastewater treatment plants	Virginia, USA (Potomac River)	Field Study Equilin, b-Estradiol, Estriol, Estrone, 17b-Ethinylestradiol, Mestranol, 19-Norethindrone, Atrazine, BPA, Diethylstilbestrol, 4-Nonylphenol, 4-tert-Octylphenol, Triclosan, Vinclozolin	White perch (Morone americana) and banded killifish (Fundulus diaphanus)	- 4 zones where 38 surface water samples, 38 sediment samples, and fish were collected	Water - Highest concentration observed (in descending order) for 17a-ethinylestradiol, norethindrone, mestranol and trimethoprim, with mean peak concentrations ranging from 450 (17a-ethinylestradiol in lower Hunting Cr.) to 99 ng/L (testosterone in upper Hunting Cr.) - WWTPs may not be the main source of estrogens in the river as upstream concentrations made significant contributions to estrogen concentrations Sediment - Highest concentrations were for 17a-ethinylestradiol and 19-norethindrone (253 to 44 ng/g dwt) - WWTP emissions were not associated with estrogenic compounds found in sediment Fish - 19 pharmaceutical chemicals, steroids, and xenoestrogens were found in banded killifish and 16 in white perch - Moderate bioaccumulation was observed - Highest pharmaceutical estrogen concentrations were for estrone (killifish only)
Xu et al., 2014 [34]	The occurrence and ecological risks of endocrine disrupting chemicals in sewage effluents from three different sewage treatment plants, and in natural seawater from a marine reserve of Hong Kong	Analyze common endocrine disruptors in sewage effluents, and assess the ecological risks	Hong Kong	Field Study, Randomized Controlled Trial (Laboratory Experimental Study) 4-nonylphenol, Triclosan, Bisphenol A, 4-tert- octylphenol, Estrone	- O. melastigma	- Influents, effluents, and receiving waters were sampled during both wet and dry season for each STP	- About 3500 g of 4-nonylphenol and 1300 g of BPA would be discharged into the marine environment from the three sewage treatment plants every year - In Shek O effluents the mean concentrations of 4-nonylphenol (3595.03 ng/L) and E1 (24.14 ng/L) were much higher than their corresponding predicted no effect concentration (PNEC) at 330 ng/L and 3 ng/L, indicating poor removal strategies - At Stanley and SWIMS, nonylphenol and BPA removal was much more efficient, indicating that biological treatment of sewage was effective at removing NP and BPA - The use of activated sludge processes was found to be more effective than biological filters - Effluent concentrations of NP and BPA were higher during dry season, but NP and BPA concentrations in the receiving waters were higher during wet season (likely due to high rates of runoff) - EC removal rates and temperature are positively correlated - The diluted effluents and natural seawaters from the marine reserve acted as endocrine disruptors to medaka fish
Comber et al., 2017 [35]	Active pharmaceutical ingredients entering the aquatic environment from wastewater treatment works: A cause for concern?	Assess pharmaceutical removal from wastewater and potential risks to the natural environment	UK	Secondary Research Study E1, E2, EE2	-	- Data from the Chemical Investigation Program, with a total of 70 water treatment sites	- On average, E1, E2, and EE2 were removed with 58–98, 89–96, and 53–71% efficiency, respectively - Removal of E1, E2, and E3 primarily occurred during primary treatment of wastewater - EE2 was found to be of high concern for inefficient removal and high environmental risk
Hom-Diaz et al., 2015 [36]	Microalgae cultivation on wastewater digestate: β-estradiol and 17α-ethinylestradiol degradation and transformation products identification.	Assess microorganism removal of E2 and EE2 from water	Spain	Laboratory Experimental Study E2, EE2, tris(2-butoxyethyl)phosphate, BPA	Selenastrum capricornutum and Chlamydomonas reinhardtii	- Anaerobic sludge samples from an urban WWTP	- E2 and EE2 enhanced algal growth - Overall, the presence of anaerobic digester concentrate (ADC) allowed for high rates of degradation as it increased algal growth - S. capricornutum removed between 88% and 100% of E2 and 60 and 95% of EE2 was removed after 7 days - C. reinhardtii completely removed E2 and EE2, but in the presence of ADC, EE2 removal decreased to 76%
Xu et al., 2021 [37]	Optimizing Adsorption of 17α-Ethinylestradiol from Water by Magnetic MXene Using Response Surface Methodology and Adsorption Kinetics, Isotherm, and Thermodynamics Studies.	Investigate magnetic MXene to adsorb EE2 from water	China	Laboratory Experimental Study EE2	-	- Studied ECs in water	- Fe3O4@Ti3C2 had a higher adsorption capacity than entrapped activated carbon in alginate biopolymer, multi-walled carbon nanotubes, 4K anthracite, and biochar (3.83 mg/g at pH 6.4) - The predicted optimal conditions were an exposure of 6.7 h at pH 6.4 with an initial EE2 and adsorbent concentration of 0.9 8mg/L and 88.9 mg/L, respectively -This resulted in an observed adsorption efficiency of 95.34%
Matamoros et al., 2015 [38]	Capability of microalgae-based wastewater treatment systems to remove emerging organic contaminants: a pilot-scale study.	Evaluate effect of hydraulic retention time, temperature, and sunlight on removing organic contaminants by high-rate algal ponds	Spain	Laboratory Experimental Study Oxybenzone, Methylparaben, Tris(2-chloroethyl) phosphate, Triphenyl phosphate, Bisphenol A	-	- Water samples were collected from the influent and effluent	- Summer % removal efficiency (4 days, 8 days): oxybenzone (97,99), methylparaben (59,75), tris(2-chloroethyl) phosphate (39,63), triphenyl phosphate (82,89), bisphenol A (72,85) - Winter % removal efficiency (4 days, 8 days): oxybenzone (75,88), methylparaben (12,25), tris(2-chloroethyl) phosphate (15,21), triphenyl phosphate (24,68), bisphenol A (66,78) - Significant differences in biodegradation and sorption was not seen due to hydraulic retention time (HRT) during the warm season, but significant differences were observed in the cold season - HRT of 4 days can remove most EOCs in both warm and cold seasons. - Higher temperature (26 vs. 11 °C) and higher solar radiation (282 vs. 74 W/m2) may increase removal of EOCs
Deng et al., 2015 [39]	Competitive Degradation of Steroid Estrogens by Potassium Permanganate Combined with Ultrasound.	Assess competitive elimination of estrogens in KMnO4/ultrasound treatment processes	China	Laboratory Experimental Study E1, E2, EE2	-	- Studied ECs in water	- After 120 min of contact with 2 mg/L of KMnO4, E1, E2, and EE2 had removal rates of 37.0, 34.4, and 34.0%, respectively - When KMnO4 was increased to 6mg/L, removal increased to 71.6% (E2), 70.5% (EE2), and 67.8% (E1) - After one ultrasound irradiation, removal efficiencies were 37.1% (E1), 31.1% (E2), and 29.7% (EE2) after 120 min of contact - removal rates were better in dual-combinations rather than in a tri-estrogen system - removal rates were higher in natural water than in pure water, possibly due to the presence of dissolved organic matter, cations, and anions
Petrie et al., 2014 [40]	Assessing potential modifications to the activated sludge process to improve simultaneous removal of a diverse range of micropollutants.	Evaluate the influence of solids and hydraulic retention times on removal of micropollutants in sludge processes	UK	Laboratory Experimental Study E1, E2, EE2, Nonylphenol, 4- nonylphenol- monoethoxylate, 4- nonylphenol- diethoxylate, NP3- 12EO	-	- 10 L water samples were collected over a 2-year period	- E1 removal of 19% (3 days solid retention time [SRT], 8 h hydraulic retention time [HRT]) to 93% (10 days SRT, 8 h HRT and 27 days SRT, 24 h HRT) - E2 removal of 63% (3 days SRT, 8 h HRT) to 95% (27 days SRT, 24 h HRT) - E3 removal of 92% (3 days SRT, 8 h HRT) to 98% (127 days SRT, 16 h and 24 h HRT) - EE2 removal of 29% (10 days SRT, 8 h HRT) to 65% (27 days SRT, 24 h HRT) - E1-3S removal of 64% (27 days SRT, 8 h HRT) to 85% (10 days SRT, 8 h HRT)
Mills et al., 2015 [41]	Removal of ecotoxicity of 17α-ethinylestradiol using TAML/peroxide water treatment.	Assess removal of EE2 from aqueous solutions using peroxidase enzyme replicas	UK	Laboratory Experimental Study EE2	-	- Studied ECs in water	- Degradation of 10 ppm of EE2 with 80 nM TAML analogue 2 and 11.46 ppm H2O2 at pH 7.5 was completed within 25 min - Intermediates from EE2 degradation had estrogenic activity, but at potencies of 35–57% of EE2 - Estrogenicity was completely eliminated and all EE2 was degraded in all treatments except in the most mild condition using 80 nM TAML analogue 1 and 0.16 ppm H2O2 in unbuffered water - At pH 10, 100 nM of TAML analogue 1, and 60 mM H2O2, 10 μM of EE2 was completely degraded within 60 min - Treatment lowered, but did not eliminate, estrogenic activity in continuous flow-through tanks without having any significant effects on fish mortality or functioning
Ma et al., 2015 [42]	Simultaneous Degradation of Estrone, 17β-Estradiol and 17α-Ethinyl Estradiol in an Aqueous UV/H2O2 System.	Assess simultaneous degradation rates of combined estrogenic compounds under H2O2 and UV treatment	China	Laboratory Experimental Study E1, E2, EE2	-	- Studied ECs in water	- In the presence of only UVC for 50 min, E1, E2, and EE2 were degraded at 97.0, 32.0, and 28.2%, respectively - After exposure to UV and 5 mg/L H2O2 for 50 min, E1, E2, and EE2 removal increased to 97.0, 49.2, and 51.7%, respectively - When H2O2 concentration was increased to 15 mg/L, conversion increased to 99.7, 76.4, and 77.6%, respectively - Removal efficiency of each estrogen decreases when solutions contain combinations of estrogens with E2 and EE2 being most effected - E1 can be effectively removed by UV/H2O2 within 50 min while E2 and EE2 require 120 min
Yang et al., 2023 [43]	Removal of antibiotics and estrogens by nanofiltration and reverse osmosis membranes	Evaluate effectiveness of commercial nanofiltration and reverse osmosis membranes at removing antibiotics and estrogens	China	Laboratory Experimental Study E1, E2, EE2, EE2, BPA, Dienestrol (DIE)	-	- Studied ECs in water	- After 3 h of filtration, estrogen levels in feedwater decreased by 6–22% and stayed relatively constant during hours 3–8 - DIE had high rates of self-degradation, leading to 12% of concentration reduction - The 3 nanofiltration membranes (DL, NF270, and NF90) had an adsorption capacity of 0–1.8, 0.2–2.7, and 1.0–4.0 μg/cm2, respectively, while the reverse osmosis membrane (XLE) had a capacity of 0–2.1 μg/cm2 - Removal efficiency of estrogens by NF90 and XLE remained over 92% despite changes in pH - Filtration by NF270 was 25–40% at pH 4.0–6.0 and 78–85% at pH 11.0 - DL had lower levels of filtration at 6–75% - NF90 and XLE were the most effective for removing estrogens
Zhao et al., 2021 [44]	Biotransformation of Current-Use Progestin Dienogest and Drospirenone in Laboratory-Scale Activated Sludge Systems Forms High-Yield Products with Altered Endocrine Activity	Characterize structure and bioactivity of transformation products of DIE and DRO during activated sludge treatments	Washington, USA	Laboratory Experimental Study Dienogest (DIE) transformation products, Drospirenone (DRO) transformation products	-	- Wastewater was sampled from the aeration tank of a WWTP	- Though DIE and DRO are not estrogenic, their products after treatment are - 13 likely transformation products (TPs) were found for DRO - 22 likely TPs were found for DIE - Biotransformation half-lives for DIE and DRO were 16–30 h and under 0.5 h, respectively - TP309 and TP311, from DIE, exhibited estrogenicity at a level similar to estrone - TP309 is 4 times more antiestagenic and 2 times more antigonadotropic than DIE - TP309 may have a molar yield of up to 55% and can be stable for over 30 h
Mainetti et al., 2021 [45]	Broad diversity of bacteria degrading 17ß-estradiol-3-sulfate isolated from river sediment and biofilm at a wastewater treatment plant discharge	Investigate degradation of E2-3S in rivers receiving water from WWTPs, assess river microorganisms responsible for E2-3S degradation	Switzerland (river Murg)	Field Study 17b-estradiol-3- sulfate (E2-3S)	Pseudomonas mendocina Pseudogemmobacter bohemicus Empedobacter brevis Acinetobacter oryzae Microbacterium esteraromaticum Acinetobacter towneri Delftia acidovorans Pseudomonas japonica Alcaligenes faecalis Bacillus subtilis Sphingopyxis ummariensis Bordetella trematum Rhodococcus defuvii Sphingobacterium alimentarium Comamonas aquatica Pseudomonas hunanensis Kaistia adipata Comamonas testosteroni	- 3 soil samples were collected from 3 sites, respectively	- Enriched organisms can completely deconjugate E2-3S, making it active and ecologically harmful - 26 different microbes were identified, 11 of which were from upstream on the WWTP, 7 from the outflow biofilm, and 8 from downstream of the WWTP
Islam et al., 2021 [46]	Secondary treatment phase of tertiary wastewater treatment works significantly reduces estrogenic load	Evaluate wastewater treatment strategies in removing estrogenic compounds and their marine and estuarine receiving waters	Hunter region along the New South Wales south-east coast of Australia	Field Study E1, E2, E3, EE2, BPA, 4-t-octyl phenol (4-t-OP), 4- nonylphenol (4-NP)	-	- 1 L samples collected at each point of treatment and in surrounding environment	Tanilba Bay WWTP - 4-t-OP had significantly higher concentrations in influent (158 ng/L) than in other sampling points - 4-NP had higher concentrations in influent (28.57 ng/L) than receiving waters (12.15 ng/L), but not significant differences between sampling points - E1, E2, E3, and 4-t-OP were removed with the highest efficiency (89.72, 99.62, 99.98, and 95.28%, respectively) - EE2, BPA, and 4-NP were removed at 77.49, 44.85, and 39.21%, respectively Belmont WWTW - E1, E2, and E3 had higher concentrations in influent than any other sampling point, while EE2 remained consistent throughout treatment (though effluent concentrations were lower than influent) - E1, E2, E3, BPA, and 4-t-OP concentrations were decreased by 89.75–99.97% - EE2 and 4-NP removal was observed at 75.67 and 77.96%, respectively - E1, E2, BPA, and NP level were 2–3 times higher at Belmont than Tanilba Bay - Hazard index was higher for Tanilba Bay (0.0218 compared to Belmont’s 0.0097) - Predicted estrogenic activity from Tanilba Bay and Belmont receiving water was fairly low - Secondary treatment largely removed estrogenic compounds
Alves et al., 2020 [47]	Biosorption of organic micropollutants onto lignocellulosic-based material	Assess adsorption of hormones onto Pinus elliottii bark biosorbents	Brazil	Laboratory Experimental Study 17b-estradiol, 17a- ethinylestradiol	Pinus elliottii bark	- Studied ECs in water	- Pinus elliotti bark biosorbent was more efficient at higher temperatures and had an equal or greater removal capacity for all hormones than granulated activated charcoal - Adsorption of 17a-ethinylestradiol was entropic and non-spontaneous, but adsorption of 17b-estradiol was entropic and spontaneous
Spina et al., 2019 [48]	Ecofriendly laccases treatment to challenge micropollutants issue in municipal wastewaters	Evaluate enzymatic treatments to remove micropollutants from wastewater	Italy	Laboratory Experimental Study and Field Study 4-t-butylphenol, Diethyl phthalate, 2-hydroxybiphenyl, Alachlor, 4-n- octylphenol, Oxybenzone, 4-n- nonylphenol, Bisphenol A	L. sativum R. subcapitata	- 2 L 24 h composite water samples from a municipal WWTP after primary sedimentation and after treatment	- Laccases should be used at the end of wastewater treatment for higher efficiency - After laccase treatment, chemical oxygen demand was reduced by 26.9% in the wastewater sample taken after primary sedimentation (W1) (negligible the final effluent (W2) due to low initial estrogen concentrations) - Laccase treatment caused W1 micropollutant concentrations to decrease up to 70% for 9 chemicals - Laccase treatment decreased micropollutants by up to 93% in W2, but low residual concentrations led to lower rates of removal for some chemicals such as 4-t-butylphenol - L. sativum assays indicated that ecotoxicity of W1 was reduced while no changes were observed for W2 - R. subcapitata assays showed that W1 toxicity did not change, but W2 no longer inhibited algal growth - Average reduction in estrogenic activity was 93.7% for W1 and 92.0% for W2
Castillo Meza et al., 2019 [49]	Detection and removal of biologically active organic micropollutants from hospital wastewater	Assess hospital wastewater and efficiency of its treatment	Pennsylvania, USA	Field Study Hexestrol	-	- 10 L 24 h composite water samples from a medical center at 2 sewer vaults	- MnOx-coated coir fibers removed over 90% of 29 out of 52 compounds and only 6 compounds were removed under 50% - Hexestrol was removed by 54% after 24 h with MnOx-coated coir fibers - Compounds that are reactive with estrogen receptor b were removed below detection rates
Valitalo et al., 2017 [50]	Effect-based assessment of toxicity removal during wastewater treatment	Assess toxicity of influent and effluent from municipal WWTPs	Finland	Field Study Unspecified combination	-	- 24 h composite samples of 6–43 L from influent and effluent of 7 municipal WWTPs	- All influent and effluent samples had estrogenic activity - Estrogenicity was reduced in effluent to between 0.61 and 3.1 ng E2 eq./L compared to the initial 0.45–32 ng E2 eq./L - Estrogenic activity was reduced by 78 to 97% in most treatment plants, but WWTP 3 and 7 did not remove estrogenic activity at all. These plants initially had low estrogenicity. - Zebrafish embryos were very sensitive to the toxic effects of all wastewater effluent samples with 20–43% mortality
King et al., 2015 [51]	Concentrations of levonorgestrel and ethinylestradiol in wastewater effluents: Is the progestin also cause for concern?	Evaluate levonorgestrel in wastewaters, EE2 and levonorgestrel in treated sewage and receiving waters	Australia	Secondary Research Study Field Study, Levonorgestrel, Ethinylestradiol	-	- 1 L water samples from upstream of the WWTP, treated effluent, at the discharge point, and 2 points downstream	- In 2010, the estimated total EE2 and levonorgestrel in treated wastewater was 0.1–0.5 and 0.2–0.6 ng/person, respectively - Provisional no-effect concentration of levonorgestrel is 0.096 ng/L - Treated effluent had the highest concentrations of EE2 out of all sampling sites at 1.5–2.0 ng/L - Levonorgestrel concentrations were all below the limit of detection
Matrtins et al., 2016 [52]	Biogenic platinum and palladium nanoparticles as new catalysts for the removal of pharmaceutical compounds	Investigate biogenic palladium and biogenic to remove pharmaceuticals from water	Portugal	Laboratory Experimental Study 17b-estradiol	D. vulgaris	- Studied ECs in water	- The Bio-Pt and Bio-Pd adsorbed about 11% of 17b-estradiol in the absence of H2 - In the presence of H2, Bio-Pt removed 94% of 17b-estradiol while only 35% was removed by Bio-Pd - After treatment, estrogenic activity decreased by 71% (Bio-Pt) - D. vulgaris was not effective in removing 17b-estradiol
Ribeiro et al., 2015 [53]	Environmental friendly method for urban wastewater monitoring of micropollutants defined in the Directive 2013/39/EU and Decision 2015/495/EU	Assess UV in municipal wastewater treatment	Portugal	Laboratory Experimental Study and Field Study 17b-estradiol estrone, 17a- ethinylestradiol	-	- 2.5 L water samples of effluent after conventional secondary treatment and after UV tertiary treatment	- EE2 and E2 demonstrated poor fragmentation in mass spectrometry and only selected reaction monitoring could be conducted - EE2 was found in 2 samples between 584 and 776 ng/L while E1 and E2 had very low concentrations after secondary treatment, indicating EE2 was poorly removed by UV treatment
Wildhaber et al., 2015 [54]	Novel test procedure to evaluate the treatability of wastewater with ozone	Feasibility assessment of ozonation as a wastewater treatment	Switzerland	Laboratory Experimental Study Unspecified combination	-	- 5 days composite effluent samples from 7 municipal WWTPs	- A high concentration of unknown ozone-reactive compounds was identified in the wastewater - Ozonation with 1.5gO3/gDOC led to bromate concentrations up to 408 µg/L, but after dilution into receiving waters, concentrations should be below drinking water guidelines - 3/7 of wastewater effluents had high estrogenic activity, and after ozonation, estrogenic activity was below quantification level for all tested wastewaters
Osachoff et al., 2014 [55]	Evaluating the treatment of a synthetic wastewater containing a pharmaceutical and personal care product chemical cocktail: Compound removal efficiency and effects on juvenile rainbow trout	Evaluate activated sludge reactors in reducing pharmaceuticals and personal care products, determine ecological effects	Canada	Laboratory Experimental Study Di(2-ethylhexyl) phthalate (DEHP), Estrone, Ethinyl estradiol, 4- nonylphenol, Tonalide, Triclosan, Triclocarban	Rainbow trout (Oncorhynchus mykiss)	- Studied ECs in water	- After activated sludge treatment, DEHP, E1, and EE2 were removed at concentrations under 75% and NP, TCC, TCS, and TON were removed over 90% - Influent cocktail and methanol treatments (IC/IM) resulted in immediate mortality of the fish due to dissolved oxygen levels of under 3 mg/L - At 50% dilution of IM and IC, no fish mortality occurred - When effluent methanol and cocktail treatments (EM/EC) were tested, there were 87 and 7% fish mortalities, respectively - Plasma VTG protein levels much higher in fish from IC than EC treatment groups, indicating changes in estrogenicity, but not proportionally to estrogenic compound concentration reductions - Reductions in gene and protein expression between effluent and influent groups was not observed

. A range of estrogenic compounds were included in these studies with E1, E2, and EE2 being the most widely discussed with 13, 14, and 17 studies directly referencing them, respectively (Table 3). An in-depth description of each of the studies, including aims and outcomes can be found in Table 4.

3.3. Risk of Bias

Table 2 includes the risk of bias checklist that was used to assess each of the studies. 15 of the studies received a score of 6 (100%) while 13 studies received a score of 5 (83.3%) (Table 2). On average, the included studies had a risk of bias score of 5.54 (Table 2).

4. Discussion

4.1. Evaluation of Available Literature

In this paper, 28 papers were reviewed. Each study had a relatively low risk of bias, with points only being deducted for addressing and minimizing bias. Many of the studies that did not receive a “yes” in this category did not discuss the limitations of the study or possible sources of bias (Table 2). This does not indicate that the study is inherently biased or invalid, but the lack of transparency on the topic requires readers to be more discerning when assessing the research. All researchers declared the sources of funding and/or any conflicts of interest. The range of topics discussed in the literature was extensive with an emphasis on the variety of wastewater treatment methods to remove E1, E2, E3, and EE2.

As many studies investigated ECs in aqueous environments, this left a gap in the material regarding ECs in soil and air. Only 4 studies in this review discuss the presence of ECs in soil and none include ECs found in the air [28,29,33,45]. Though there is little to no research on pharmaceutical ECs in the air, there is evidence that particulate matter can have estrogenic properties and the management of these compounds, and their health risks must be further investigated [56]. Also, although there was extensive research conducted on aquatic ECs and how to remove them from contaminated waters, discussion about management practices to reduce the introduction of pharmaceutical ECs into water systems and the general environment outside of a wastewater treatment plant was lacking.

In five studies, wastewater treatment plants were compared for efficacy in removing estrogenic compounds by measuring the estrogenicity of water or the concentrations of specific xenoestrogens along different steps of the treatment process. This research method is particularly useful in assessing what methods are the most effective and can help shape regulations and recommendations to create standardized wastewater treatment systems. However, these studies were only conducted in Europe, Asia, and Australia. This may be due to a variety of factors including funding availability, research infrastructure, and political stability. The contaminants found in the wastewater and each country’s environment and capacity to invest in different removal methods vary significantly, requiring further investigation.

4.2. Characterizing Estrogenic Compounds in the Environment

The estrogens and xenoestrogens included in these studies were E1, E2, E3, EE2, BPA, 4-nonylphenol, t-nonylphenol, 4-tert-octylphenol, nonylphenol mono-ethoxylate, nonylphenol di-ethoxylate, 4-t-butylphenol, diethylstilbestrol, diethyl phthalate, di(2-ethylhexyl)phthalate, 2-hydroxybiphenyl, alachlor, methyl paraben, ethyl paraben, propyl paraben, butyl paraben, tris(2-butoxyethyl)phosphate, tris(2-chloroethyl) phosphate, triphenyl phosphate, equilin, mestranol, dienestrol, hexestrol, levonorgestrel, 17b-estradiol-3-sulfate, 19-norethindrone, tonalide, triclosan, triclocarban, vinclozolin, oxybenzone, 4-nonylphenol-monoethoxylate, 4-nonylphenol-diethoxylate, and dienogest and drospirenone transformation products.

Due to the wide range of ECs and their potential to transform into different compounds with varying levels of ecological impact, several studies measured estrogenicity using biological assays such as the chemical-activated luciferase expression (ERα-CALUX) assay, which measures estrogenic and anti-estrogenic activity using a reporter protein that glows when it comes in contact with estrogenic substances, rather than measuring specific compound concentrations [30,48,50,57]. Although biological assays are useful for understanding the presence of ECs on a larger scale, studies assessing individual ECs were able to characterize specific compounds that may pose a larger ecological risk. Many found that EE2 and BPA were harder to remove through traditional wastewater treatment processes and can have higher levels of estrogenicity [29,32,33,34,46,51,53]. Both forms of measuring EC presence in the environment are necessary to better understand their potential implications and design removal guidelines that more effectively address pollutants that are the most prevalent.

Creating these guidelines can be difficult due to the variety of ways that ECs can enter the environment, including leaching from landfills, runoff from agricultural practices, and sewage sludge [28,29]. Some of these ECs are free estrogens, like E1, E2, E3, and EE2, which are biologically active. There may also be conjugated estrogens that are generally non-toxic, but they can be naturally degraded into free estrogens, which have the potential for long-term harm. For example, 17β-estradiol-3-sulfate is a naturally produced compound that acts as an E3 storage pool and it can be deconjugated by bacteria found in river sediments, converting it to E3 [45]. The presence of conjugated estrogens was not widely discussed in studies evaluated here, but many did attempt to measure the presence of free estrogens.

EE2 was frequently detected, which is expected given its more stable structure, but the specific source was not identified. EE2 and E3 were measured at much higher concentrations in forest lands compared to urban, grassland, and agricultural areas in France [29]. However, the origins and fate of these compounds were not determined and are not widely discussed in other literature. Another study by Arya et al. in the United States analyzing water and sediment in a section of the Potomac River receiving wastewater effluent observed high concentrations of EE2, norethindrone, and mestranol in water and EE2 and 19-norethindrone in sediment [33]. Wastewater treatment plants contributed to these ECs, but these emissions were not associated with the compounds found in sediment indicating that there must be another source of ECs that remains unspecified but perhaps due to the large presence of ECs in waters upstream from the wastewater treatment plants [33]. It is crucial that studies such as these are repeated in other regions and settings as the duration in which ECs can persist and the concentrations in which they are released strongly depend on environmental conditions. For example, hormones excreted by humans and animals have a half-life in soil ranging from 1 to 10 days and may degrade at faster rates in higher temperatures, UV exposure and aerobic conditions [29,32].

4.3. Consequences of Pharmaceutical Estrogenic Compounds in the Environment

Exposure to ECs in nature can lead to several adverse effects observed in both humans and wildlife. These effects can be quite extensive as ECs travel from one system to another, such as leaching from soil to water [22]. Once ECs enter the water system, they can more easily spread and reach shallow groundwater [22]. The most common sources of these contaminating ECs are biosolids or sewage sludge, contaminated soil, sediments, surface waters, influent and effluent of wastewater treatment plants (WWTPs), and landfill leachate [22]. Despite ECs’ potential to interact with the environment in several different forms, literature available on this topic greatly centers around the effects of ECs in water.

In lakes, rivers, and reservoirs in China, Dai et al. found that the primary exposure pathway for aquatic estrogenic compounds to enter the human body was through fish consumption rather than drinking water [31]. However, exposure pathways can be much more complex including ingestion, absorption, and inhalation [56]. This identifies a large gap in the research conducted on ECs and room for future developments in our understanding of these compounds on the environment and health. Of the compounds studied, E1, E3, and EE2 had the highest health risks for people of all age categories, with the highest risk for children from 2 to 6 years of age [31]. These exposures may lead to an increased risk of reproductive impairments, dysfunctions, cancers, and diseases despite being present in low concentrations [31]. These findings are consistent with previous research as children often spend more time in the environment where they can be exposed to ECs and their skin and blood–brain barriers are more permeable, making them more sensitive to pollutants [58]. Of note, they also have a larger body surface area to volume compared to adults.

Meyer et al. studied the effects of xenoestrogens on the gallbladder and liver and found that they may have negative effects on the development and function of bile ducts, leading to the development of cholestatic and primary biliary cholangitis, a chronic autoimmune liver disease due to the presence of antibodies to mitochondrial proteins [28]. The research relating estrogens and liver disease is somewhat disputed. It is widely accepted that native estrogens have a protective role in chronic liver disease, particularly in premenopausal women [59]. However, some clinical studies have documented increased estrogen levels in those who suffer from chronic liver disease [59]. More research must be conducted to understand the differences in the way that natural and synthetic estrogens can impact liver and other organ functions.

The effects of ECs may also be observed in wildlife, most notably fish and amphibians. It is widely recognized that feminization of male fish can occur due to xenoestrogen exposure [51]. In female fish, however, pharmaceutical estrogens such as levonorgestrel, found in emergency contraceptive pills, have been associated with impaired oogenesis, oocyte maturation, and ovulation or the masculinization of female fish [60,61]. There have also been links between EC exposure and higher rates of mortality and decreased body length among fish embryos [34,50]. Osachoff et al. found that concentrations of plasma vitellogenin protein, an egg yolk precursor used as a marker for environmental estrogen contamination, were lower in fish that lived in activated sludge effluent compared to those in influent [55]. However, the changes in plasma vitellogenin protein and other estrogen-dependent proteins were not proportional to the decrease in estrogen levels in the treated water, indicating that the changes in estrogenicity were not enough to eliminate ecological risk [55]. Because estrogen receptors have been phylogenetically conserved among vertebrates, the harmful effects of these compounds can span across numerous organisms in the ecosystem [60]. This is especially true when considering the potential for bioaccumulation of pharmaceuticals as observed by Arya et al. and the risks of human consumption of fish that lived in estrogenically active waters [31,33].

4.4. Evaluation of Estrogen Management Methods

The efficiency of wastewater treatment plants in removing ECs was analyzed in 3 studies from Italy, Hong Kong, and Finland, and they found that estrogenic activity can be detected in wastewater effluent of receiving waters, indicating that the wastewater treatment plant was not effective in removing estrogen from the water [30,34,50]. However, other studies in Finland, Sweden, the United Kingdom, and Hong Kong did find that the wastewater treatment plants studied were effective in removing estrogens and xenoestrogens [34,35,46,54]. This demonstrates the need to create standardized regulations for wastewater management and develop technologies that are effective, cost-efficient, and environmentally sustainable.

The methods used to treat wastewater and the alternatives that are currently being developed will be examined in this section. The specific wastewater treatment processes to be discussed can be grouped into four categories: activated sludge [40,44,55], estrogen adsorption and filtration [37,43,47], algal and enzymatic degradation [36,38,41,48], and other methods [39,42,49,52,53].

4.4.1. Activated Sludge

Activated sludge is often inefficient at removing estrogens and xenoestrogens, such as E1 and EE2, and biotransformation of dienogest and drospirenone into estrogenic products has been documented (

Table 5. SWO/AT analysis of EC management methods.

Management Method	Activated Sludge	Adsorption and Filtration	Algal and Enzymatic Degradation	Other Methods
Strengths	Conventional treatment applied on a large scale Produces biogas, which can be used as renewable energy	High EC removal rates Sustainable options using renewable materials and low energy requirements	High EC removal rates Low energy requirement	Bio-Pt is low-cost, low-toxicity, and eco-friendly UVC + H2O2 achieve high EC removal rates
Weaknesses	Low EC removal rates Biotransformation of products may decrease effectiveness	Potentially costly at a large scale	Limited large-scale evidence for pharmaceutical ECs Enzyme efficacy may vary depending on the presence of chemicals and microbes	Low EC removal rates for MnOx UVC + H2O2 efficiency decreases when multiple ECs are present Byproducts of Bio-Pt treatment decrease effectiveness
Opportunities/Advantages	Renewable energy sources could make the process more sustainable Can be easily integrated into existing systems Potential for optimization by altering solid and hydraulic retention time	Development of new biosorbents can displace costly, nonrenewable traditional adsorbents	Promising applications in bioremediation	Can be combined with other treatments to increase effectiveness
Threats	High-energy consumption (largely dependent on nonrenewable sources) Potentially harmful bioproducts	Synthetic filters may have negative environmental impacts during production or disposal	Potentially harmful estrogenic intermediate Algal growth may be seasonally dependent	Potentially harmful byproducts (Bio-Pt)

) [40,44,55]. However, by optimizing conditions including solid and hydraulic retention time, efficiency can increase [40]. Activated sludge processes should also be modified to become more sustainable as the current methods typically require large amounts of energy, often from fossil fuels [62]. This may be achieved by utilizing renewable sources of energy and increasing the concentration of organic matter to improve the efficiency of energy recovery in the form of biogas [62].

4.4.2. Adsorption and Filtration

Adsorption and filtration mechanisms are reported to be a good option for sustainable and cost-effective wastewater treatment (Table 5) [63]. Magnetic MXene composite Fe₃O₄@Ti₃C₂, Pinus elliotti bark, nanofiltration, and reverse osmosis were all discussed in the studies in this review [37,43,47]. Fe₃O₄@Ti₃C₂ was very effective at adsorbing EE2 with an efficiency of 95.34% after 6.7 h of treatment [57]. Pinus elliotti bark is a natural biosorbent that has a similar or greater removal capacity for E2 and EE2 than granulated activated charcoal, which can be derived from nonrenewable resources and suffer from high production cost [47]. There were also high success rates for the removal of estrogens by NF90, a nanofiltration membrane, and XLE, a reverse osmosis membrane, which were both over 92% [43].

4.4.3. Algal and Enzymatic Degradation

High-rate algal ponds can be used to treat wastewaters and in constructed wetlands, and are an affordable, low-energy method to remove xenoestrogens, such as oxybenzone, methylparaben, tris(2-chloroethyl) phosphate, triphenyl phosphate, and BPA from industrial, municipal, and agricultural sources, but strong evidence supporting its effectiveness on pharmaceutical ECs and natural estrogens has yet to be gathered (Table 5) [38,64,65]. Hom-Diaz et al. studied S. capricornutum and C. reinhardtii and found that after 7 days, S. capricornutum removed 88–100% of E2 and 60–95% of EE2, while C. reinhardtii completely removed both E2 and EE2 except for EE2 in the presence of an anaerobic digester centrate, which decreased removal to 76% [36]. Though these findings are promising, further research is needed to understand the full implementation of high-rate algal ponds in large-scale systems.

Enzymatic degradation is promising, particularly for bioremediation, because it is an eco-friendly, economical, and effective way of eliminating harmful pollutants (Table 5) [66]. Biological laccase enzymes from Trametes pubescens MUT 2400 were used to treat municipal wastewater with an average reduction in estrogenic activity of 93.7% in a sample that treated wastewater collected after primary sedimentation (W1) and 92.0% in a sample that had already undergone secondary treatment [48]. Laccases should be used at the end of wastewater treatment for higher efficacy due to the loss of laccase activity in W1 samples due to the potential for enzymatic inhibition by chemicals and microbes present in wastewater. Tetra-amido macrocyclic ligand (TAML) activators are functional peroxidase enzyme replicas that have been paired with peroxide to degrade EE2. Mills et al. found that 10 ppm of EE2 can be degraded with 80 nM TAML analog 2 and 11.46 ppm H₂O₂ within 25 min. Estrogenic intermediates were produced through this process and had an estrogenicity of 35–57% of EE2.

4.4.4. Other Methods

Ma et al. utilized ultraviolet-C radiation (UVC) and hydrogen peroxide to degrade E1, E2, and EE2 and found that when UVC exposure was paired with 15 mg/L of hydrogen peroxide, removal efficiencies reached 99.7, 76.4, and 77.6%, respectively. However, when multiple estrogens are degraded at once, removal efficiency decreases (Table 5) [42]. In practice, Ribeiro et al. observed that wastewater effluent from a plant that uses UV treatment contained EE2 concentrations between 584 and 776 ng/L while E1 and E2 were measured at very low concentrations, indicating that EE2 was poorly removed by UV treatment [53].

Manganese oxide (MnOx) coated coir fibers have been used to treat hospital wastewaters before dilution into larger WWTPs through oxidation by the MnOx and sorption by the coir fibers [49]. Hexestrol, a pharmaceutical xenoestrogen used for hormone replacement therapy, was removed by 54% after 24 h, and by the end of MnOx treatment, the organic compounds that were reactive with Estrogen Receptor β were removed below detection rates [49]. Deng et al. conducted trials pairing potassium permanganate and ultrasound and found that in natural water, E1, E2, and EE2 were removed at 60.8, 60.8, and 56.5% efficiency, respectively [39].

Biogenic platinum (Bio-Pt) nanoparticles can be used as reductive catalysts to break down estrogens in environmental remediation projects [52]. When activated by hydrogen gas, Bio-Pt removed 94% of E2 after 24 h of treatment, ultimately reducing estrogenic activity by 71% after taking into account the toxicity of the byproducts from the reaction of 17β-estradiol with Bio-Pt [52]. Bio-Pt is reported to be a sustainable option for removing ECs because it is cost-effective, has low toxicity, and is eco-friendly [67]. However, it must be combined with another treatment modality, such as nanofiltration to reach ecologically safe levels of estrogenicity.

There are several approaches to removing ECs from water. Some effective and environmentally sustainable options are adsorption and filtration using pinus elliotti bark or nanofiltration and degradation with laccase enzymes or TAML activators. Activated sludge processes and high-rate algal ponds also have the potential for large-scale applications but require further investigation and standardized guidelines to reach maximum efficiency and sustainability.

4.5. Implementation of Management Practices

Reducing pharmaceutical ECs found in the environment begins with proper disposal of waste and unused medications. U.S. guidelines for the disposal of pharmaceutical estrogens and xenoestrogens were not found at the time of this study. In the EU, the Regulation on the registration, evaluation, authorization, and restriction of chemicals (REACH) attempts to minimize the effects of harmful substances on human health and the environment by requiring reports from EU member states and the European Economic Area (EEA) countries every 5 years and registering chemical substances, their risks, and their management methods to limit or ban dangerous compounds [68]. Though ECs have not specifically been regulated through REACH, a similar approach may be recommended for overseeing their production, management, and disposal. The Healthcare Environmental Resource Center and Practice Greenhealth recommends treating ECs as hazardous waste or incinerating them using a municipal or regulated medical waste incinerator and although the U.S. Food and Drug Administration does not discuss pharmaceutical ECs specifically, there are drug-take-back facilities, as in the UK, that can aid in the proper disposal of unused or expired medications [68,69]. These may be a good starting point for reducing the introduction of ECs into the environment, but clearer guidelines that specifically address pharmaceutical xenoestrogens and infrastructure for accessible drug-take-back programs are necessary in every country to eliminate the problem.

Regulations about acceptable EC levels entering the environment vary from country to country. In the United States, for example, estrogenic compounds are not included in the National Primary Drinking Water Regulations [70]. However, the only pharmaceutical or natural estrogen, EE2, is on the Contaminant Candidate List, meaning that it does not have any legal regulation in public water systems [71]. The European Union has taken steps to advise monitoring estrogens found in surface water by proposing maximum detection limits of 0.035 ng/L for EE2 and 0.4 ng/L for E1 and E2, as well as adding E2 to the drinking water watch list [72,73]. However, attaining these limits in practice has been difficult despite modern methods of water treatment [72]. The UK Environmental Agency also monitors E1, E2, and EE2 in surface waters to protect marine life with maximum thresholds of 3 ng/L, 1 ng/L, and 0.1 ng/L, respectively. Because there are many potential sources of environmental ECs and they can easily disperse and contaminate surrounding areas, it is important that all countries create regulations on acceptable levels for ECs in wastewater effluent without causing ecological harm, similar to the guidelines set by the UK. Because there are no international guidelines on pharmaceutical estrogen management, further research is required to inform policies specific to each country’s needs followed by stringent inspection policies of water for estrogenicity. To ensure such regulations are enforced, very precise and rapid methods to measure EC concentrations are required. Such methods using liquid chromatography–mass spectrometry have been validated for E1, E2, E3, and EE2 as they are some of the most prevalent and widely researched, but as novel EC research is conducted, the speed in which testing can be performed and the diversity of ECs measured should be improved upon [73].

4.6. Strengths and Limitations

The strengths of this review include synthesizing and comparing several wastewater treatment processes to remove ECs with an emphasis on sustainability and investigating national guidelines to create actionable recommendations to reduce EC concentrations in the environment. On the other hand, some limitations include a lack of data about EC management practices, particularly in air and soil. None of the studies included in the study were conducted in Africa, and only one was conducted in South America. This may be due to low- and middle-income countries in South America and Africa being mostly developing with limited resources diverting governmental priorities to issues other than environmental and human health. It is also possible that research published in languages other than English, and not reported here, could enrich the discussion in this review. Because management practices of ECs are dependent on environmental factors and regional differences, it is crucial that further research is conducted to identify methods of treating ECs found in other substrates and regional solutions informed by region-specific research.

5. Conclusions

This review highlights the need for comprehensive research and management strategies for pharmaceutical xenoestrogens and naturally occurring estrogens in the environment. These compounds have extensive effects on the health of animals and humans, including endocrinological, vascular, immunological, and neuronal functions, and so require efficient and sustainable management strategies, particularly in aquatic ecosystems. Using approaches such as adsorption, filtration, and enzymatic degradation can help reduce the presence of ECs in water, but further research is required to inform policies standardizing wastewater treatment, address the gap in removing ECs from soil and air, and refine large-scale water treatment technologies.