Electrochemical Impedance Spectroscopy Detection of Endocrine Disruptors

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This entry is adapted from the peer-reviewed paper 10.3390/s20226443

Endocrine disruptors (EDs) are contaminants that may mimic or interfere with the body’s hormones, hampering the normal functions of the endocrine system in humans and animals. These substances, either natural or man-made, are involved in development, breeding, and immunity, causing a wide range of diseases and disorders. The traditional detection methods such as enzyme linked immunosorbent assay (ELISA) and chromatography are still the golden techniques for EDs detection due to their high sensitivity, robustness, and accuracy. Nevertheless, they have the disadvantage of being expensive and time-consuming, requiring bulky equipment or skilled personnel. On the other hand, early stage detection of EDs on-the-field requires portable devices fulfilling the Affordable, Sensitive, Specific, User-friendly, Rapid and Robust, Equipment free, Deliverable to end users (ASSURED) norms. Electrochemical impedance spectroscopy (EIS)-based sensors can be easily implemented in fully automated, sample-to-answer devices by integrating electrodes in microfluidic chips.

endocrine biosensor impedance MIP immunosensor aptasensor

1. Introduction

Endocrine disruptors (EDs) are environmental contaminants that disrupt the normal functioning of the endocrine system in mollusk, crustacea, fish, reptiles, birds, and mammals. For humans, these compounds may cause cancerous tumors ^[1]^[2]^[3] and infertility ^[4]. Natural EDs originate in living organisms and can be either hormones (testosterone, estrogen, or progesterone) or mycotoxins such as zearalenone. Synthetic EDs can be found in plastic additives, industrial reagents, and waste. Some of the most common synthetic EDs are precursors in the production of rubber, pesticides and plastic additives such as atrazine, alkylphenols, bisphenol A (BPA) ^[5], parabens, perfluoroalkyl acids ^[6], phthalates and polychlorinated biphenyls (PCBs) ^[7]. A list of relevant EDs is given in Table 1.

A variety of analytical methods have been used for the detection of EDs, including liquid chromatography coupled with mass spectrometry (LC-MS) ^[8], gas chromatography coupled with mass spectrometry (GS-MS) ^[9], high-performance liquid chromatography (HPLC) coupled with fluorescence detection ^[10] or with mass spectrometry ^[11]^[12]. These methods usually require laborious and time-consuming steps for sample pre-concentration, and high amounts of reagents. By comparison, electrochemical sensors and biosensors offer advantages such as low cost, portability, and do not require complex pretreatment steps. Moreover, biosensors can be used for selective, fast, and direct detection of analytes in real samples.

Table 1. List of relevant EDs compounds.

Analyte	IUPAC Name	Molecular Weight (g/mol)	Source	Ref.
17β-estradiol (E2)	(8R,9S,13S,14S,17S)-13-Methyl-6,7,8,9,11,12,14,15,16,17-decahydrocyclopenta[a]phenanthrene-3,17-diol	272.388	endogenous hormone, medication	^[13]
Acetamiprid (AAP)	N-[(6-chloro-3-pyridyl)methyl]-N′-cyano-N-methyl-acetamidine	222.678	insecticide	^[14]
Atrazine (ATZ)	6-chloro-N2-ethyl-N4-(propan-2-yl)-1,3,5-triazine-2,4-diamine	215.69	herbicide for grassy weeds in crops	^[15]
Pentabromodiphenyl ether (BDE-47)	2,2′,4,4′-Tetrabromodiphenyl ether	485.79	flame retardant	^[16]
Bisphenol A (BPA)	4,4′-(propane-2,2-diyl)diphenol	228.291	precursor to polycarbonates, plastic and epoxy resins	^[17]
Carbendazim (CBZ)	methyl 1H-benzimidazol-2-ylcarbamate	191.187	fungicide	^[18]
Cortisol	11β,17α,21-Trihydroxypregn-4-ene-3,20-dione	362.46	endogenous hormone, medication	^[19]
Dibutyl phthalate (DBP)	Dibutyl benzene-1,2-dicarboxylate	278.348	plasticizer	^[20]
Dichloro-diphenyl-trichloroethane (DDT)	1-chloro-4-[2,2,2-trichloro-1-(4-chlorophenyl)ethyl]benzene	354.48	pesticide	^[21]
Di(2-ethylhexyl) phthalate (DEHP)	Bis(2-ethylhexyl) benzene-1,2-dicarboxylate	390.564	plasticizer	^[22]
Microcystin-LR (MC-LR)	(5R,8S,11R,12S,15S,18S,19S,22R)-15-[3-(diaminomethylideneamino)propyl]-18-[(1E,3E,5S,6S)-6-Methoxy-3,5-dimethyl-7-phenylhepta-1,3-dienyl]-1,5,12,19-tetramethyl-2-methylidene-8-(2-methylpropyl)-3,6,9,13,16,20,25-heptaoxo-1,4,7,10,14,17,21-heptazacyclopentacosane-11,22-dicarboxylic acid	995.189	cyanobacteria toxin	^[23]
Norfluoxetine (NorFLX)	(S)-3-Phenyl-3-[4-(trifluoromethyl)phenoxy]propan-1-amine	295.305	antidepressant	^[24]
3,3’,4,4’-tetrachlorobiphenyl (PCB-77)	3,3′,4,4′-tetrachloro-1,1′-biphenyl	291.99	flame retardants, plasticizers, dielectric and heat transfer fluids	^[25]
Testosterone	(8R,9S,10R,13S,14S,17S)-17-Hydroxy-10,13-dimethyl-1,2,6,7,8,9,11,12,14,15,16,17-dodecahydrocyclopenta[a]phenanthren-3-one	288.431	endogenous hormone, anabolic steroid	^[26]
Tributyltin hydride	tributylstannane	291.06	precursor in organic synthesis	^[27]
Zearalenone (ZEN)	(3S,11E)-14,16-Dihydroxy-3-methyl-3,4,5,6,9,10-hexahydro-1H-2-benzoxacyclotetradecine-1,7(8H)-dione	318.369	mycotoxin	^[28]

Electrochemical impedance spectroscopy (EIS) is a sensitive technique which can be used to monitor biomolecular events occurring at the electrode surface. These events include affinity interactions involving peptides, receptors, nucleic acids, whole cells, and antibodies.

2. Basic Elements of EIS-Based Sensors

2.1. Principle of EIS Detection

Electrochemical impedance spectroscopy (EIS) is an electrochemical technique that measures the impedance properties of an electrochemical system using a large range of frequencies. Here, the electrochemical process is described by an electrical circuit consisting of resistance, capacitors, and constant phase elements combined in parallel or in series.

The most widely used model for describing processes at the electrochemical interface is the Randles equivalent circuit ^[29], consisting of electrolyte resistance (R_s), charge-transfer resistance (R_ct) at the electrode/electrolyte interface, double-layer capacitance (C_dl), mass transfer resistance (R_mt) and Warburg impedance (W). The R_s parameter is determined by the conductivity of the solution and the distance between the electrodes. The double layer capacitance depends on the electrode area, nature, and electrolyte’s ionic strength. R_ct and W represent the Faradaic impedance. R_ct depends on the charge transfer kinetics and can be thought of as the ratio of overpotential to current in the absence of mass transfer limitation. The linear segment registered at low frequencies is attributed to the Warburg diffusion element, the impedance being controlled by the diffusion process in this region.

Equivalent circuit models can serve to describe the electrochemical, chemical, and physical processes occurring at the electrode surface, since each circuit component can be assigned to a physical process in the electrochemical cell. Electrochemical reactions involve electrolyte resistance, adsorption of electroactive species, charge transfer at the electrode surface, and mass transfer from the bulk solution to the working electrode surface. Each electrochemical process is represented by an electrical circuit that consists of capacitors, resistance and constant phase elements that are connected in parallel or in series.

EIS has been proven to be a useful tool for the analysis of interfacial or bulk electrical properties of the electrode, which can be used to quantitatively determine electrochemical processes ^[30]. EIS enables label-free detection with high signal-to noise ratio amenable to on-site analysis.

2.2. Types of Impedance Sensors

Impedance sensors can be classified according to the relation between the charge transfer process and the parameters measured into Faradaic or capacitive sensors.

(A) Faradaic impedance sensors use electrodes with conductive surfaces; the measurements require redox-active molecules in solution, such as hexacyanoferrate(II)/(III) anions or hexaammineruthenium (II)/(III) cations ^[31]. Charge transfer resistance (R_ct) is the main parameter that characterizes the electrochemical process at the sensor’s surface. The surface-binding of non-conductive molecules blocks the electron transfer (ET), causing an increase in R_ct. Conversely, the binding of conductive molecules or molecules able to catalyze redox reactions leads to the decrease in R_ct.

(B) Non-Faradaic (Capacitive) sensors are systems where the sensing surface is covered by an insulating layer. The double-layer capacitance (C_dl) is the main parameter that characterizes the reactions occurring at the electrolyte/electrode interface ^[32]. The binding of the molecules to the surface usually decreases the value of C_dl.

2.3. Electrochemical Impedance Spectroscopy for Biosensing Applications

EIS also presents the possibility of carrying out label-free experiments, unlike other electrochemical techniques, such as amperometry and voltammetry ^[30]. The EIS sensors are often based on various modified surfaces that increase the amount of bioreceptor on the surface, and consequently the performance of the biosensor.

A biosensor is an analytical device in which a biological component, called a bioreceptor, is integrated or in direct contact with a physicochemical detector that turns the biological signal into a measurable analytical signal ^[33]. Biosensors offer a simple, rapid and cost-effective alternative for the detection of harmful compounds ^[34]. The bioreceptor is the component that interacts in a specific manner with the analyte, and can be an enzyme, antibody, nucleic acid, organelle, cell, or an organic tissue. The selectivity of the biosensor is determined by the affinity features of the biological receptor. The signal generated by the interaction between the analyte of interest and the biological recognition element is then transformed by a transducer to an optical or electrical readout. The EIS technique has been used to monitor specific interactions occurring at the electrode surface between a receptor and the specific target analyte; the impedance is used to quantitatively assess the analyte. The advantages of EIS biosensors are their sensitivity, simplicity, and possibility to achieve real-time detection. The use of EIS also has several disadvantages such as being sensitive to the surrounding environment, often requiring a Faraday cage to reduce noise, bulky experimental setups and the need for theoretical simulation for data analysis ^[35].

3. EIS Sensors for EDs Detection

Recently reported EIS sensors and biosensors for EDs detection have used various metal oxides ^[36], metal organic frameworks (MOFs) ^[37] and molecularly-imprinted polymers (MIPs) ^[38], either as supporting layers, or recognition elements.

3.1. Molecular-Imprinted Polymer Sensors

MIPs are artificial recognition elements used in the development of sensors due to their high selectivity, chemical and thermal stability, and easy customization compared to receptors from biological sources. MIPs are created by polymerizing a functional monomer in the presence of the analyte template ^[39]. After the removal of the template, cavities with specific shapes are formed, allowing a highly selective interaction with the target analyte ^[40]. MIPs bind to the target molecules, leading to variations in physical parameters at the sensor surface, such as mass, absorbance, or electron transfer (ET) rate. In the case of electrochemical sensors, the specific interaction often hampers the electron transfer between the electrode and the redox probe in the solution, which can be quantified through EIS measurements. MIPs have been designed for the extraction of various EDs, such as 17β-estradiol ^[38] or bisphenol A (BPA) ^[41] from contaminated environments. In MIP-based EIS sensors, the ED molecules fill the MIP cavities, hindering ET and thus increasing the R_ct value. MIPs are usually immobilized on the sensor surface and interact with the analyte in solution.

3.2. Metal Composite-Based Sensors

Metal composites represent a combination of two metals or a combination between a metal and another type of material, such as a polymer. Metal–polymer composites have a large surface area and enhanced electrical conductivity due to their mesoporous structures. Metal–organic frameworks (MOFs) are a class of compounds consisting of metal ions or clusters coordinated to organic ligands to form one-, two-, or three-dimensional structures. Due to their customizable structure and functionality, high porosity and large internal surface area, MOFs have great potential in electrochemical sensing applications ^[42]. However, there are few notable works reporting MOF-based sensors for EDs s detection with moderate performance, most of them not being tested on real samples.

3.3. Graphene, Carbon-Nanotubes and Cyclodextrins Based Sensors

Graphene is an allotrope of carbon with 2D layers of sp²-hybridized carbon. It is used for sensor modification due to its high electric conductivity and large surface area, which is amenable to functionalization with biomolecules. Single carbon nanotubes (SWCNT) and multiwalled carbon nanotubes (MWCNT) were used to modify the electrochemical transducers, due to their high electron transfer rate, surface area, minimization of the surface fouling and stability ^[43].

A simple approach for detecting polychlorinated biphenyls such as PCB-77 was developed by Wei et al. ^[44], where pyrenecyclodextrin (PyCD) was immobilized a SWCNT-modified GCE. The presence of the pyrenyl group on the CD favored the attachment on the surface of the carbon nanotubes trough π–π stacking. The PCB-77 molecules formed complexes with the immobilized PyCD that hindered ET between the ferro/ferricyanide anions and the sensor surface.

Recently, Hsine et al. ^[45] combined the use of a porphyrin derivative with that of thermally reduced graphene oxide (TRGO), which also can be attached using π–π interactions. BPA molecules were absorbed on the surface of the nanocomposite, increasing the membrane resistance, which was quantified with EIS.

4. EIS Biosensors for the Detection of EDs

4.1. Immunosensors

Immunoassays are based on the specific interaction between an antigen and the corresponding antibody (Ab), which can be transduced into a measurable physical signal ^[46]. Immunosensors can be prepared using monoclonal, polyclonal or recombinant Abs. Immunosensors have been used for the detection of EDs, such as DES, estradiol, phthalates and bisphenol A ^[47]. The bonds between antibodies and antigens are relatively weak and can be dissociated by changing the properties of the environments, i.e., pH and ionic strength. Singh et al. developed a simple label-free immunosensor for 17β-estradiol ^[48]. Silver wire electrodes were modified with an 11-mercaptoundecanoic acid self-assembled monolayer (SAM) and the 1-ethyl-3-(3-dimethylaminopropyl)carbodiimide (EDC)-N-hydroxy succinimide (NHS) chemistry was used to covalently bind the 17β-estradiol monoclonal antibodies. In this case, the parameter measured was the capacitance.

Chen et al. used a tyramine-modified rutile TiO₂ mesocrystals (Tyr-RMC) to label a ZEN mimic peptide ^[49]. The peptide@Tyr-RMC conjugate binds an antibody-modified GCE in competition with free ZEN. Although the peptide-based sensor was designed for an assay based on dual-signal readout competitive enzyme-linked immunosorbent assay (C-ELISA), the ZEN could also be detected by EIS, with the signal gradually decreasing while the concentration increases.

4.2. Aptamer-Based Biosensors

Aptamers are oligonucleotides that bind to a specific target. Because of their in vitro selection and production, the relatively new technology of aptamers has emerged as an alternative to antibodies, as they are obtained through chemical synthesis, with high reproducibility, and their production is not dependent on living organisms. They can be easily regenerated, have a much longer shelf life, and can be stored at ambient temperature.

Kang et al. ^[50] developed a microfluidic aptasensor for the detection of BPA using an anodized aluminum oxide-based capacitive sensor. A gold electrode surface was immobilized on top of the Anodized aluminum oxide (AOO) surface and this allowed the immobilization of a thiol-modified BPA aptamer. The capacitance of the system decreased due to the conformational change of immobilized aptamer at the binding to the BPA molecules. The sensing surface was encased in a microfluidic channel and this allowed a real-time capacitance measurement during the binding of BPA to the immobilized aptamer. A capacitive aptamer microelectrode array has also been used for the detection of BPA, with aptamers immobilized on an array made of interdigitated aluminum microelectrodes ^[51]. The method combines AC electro-kinetics (ACEK) effects and capacitance measurement. The main advantages of the detection system are the low cost of the disposable microelectrodes, fast response time (20 s), and the limit of detection reported for BPA is 2.8 fg/mL.

4.3. Estrogen Receptor-Based Biosensors

Human-estrogen receptor alpha (ER-α) is a protein that belongs to the nuclear receptor group and can bind xenoestrogens such as 17β-estradiol. Due to its specificity and ability to be engineered, ER-α was used as bio-recognition element for the development of ED detection methods ^[52].

Im et al. ^[53] developed an EIS biosensor for 17β-estradiol based on the biding of estrogen to the surface-immobilized estrogen. The surface modification of the Au electrode involved the use of 3-mercaptopropionic acid (3-MPA), which binds to the Au surface via thiol groups and the ECD-NHS chemistry for the covalent binding of the estrogen receptor-alpha (ER-α) to the carboxyl groups of 3-MPA. The hormone has been detected at a concentration of 10⁻⁶ M. The biosensor was developed further by the same group ^[54] by using BSA to block the remaining binding sites. The dynamic range was within 1 × 10⁻¹³–1 × 10⁻⁹ M with a LOD of 1 × 10⁻¹³ M.

4.4. Enzyme-Based Biosensors

Other biorecognition elements, such as enzymes, were used to develop the ED biosensors. In the case of phenolic compounds, these biosensors are often based on the enzymatic oxidation by enzymes such as tyrosinase ^[55] or laccase ^[56]. Metal composites have been used to modify the working electrodes and to provide a large surface area for enzyme immobilization and improved surface charge transfer.

Recently, a laccase biosensor for BPA detection was developed using a conjugate containing reduced graphene oxide and ferrous-ferric oxide nanoparticles (rGO-Fe₃O₄ NPs) ^[57]. Chit95 (chitosan with a degree of deacetylation of 95%) was used for laccase immobilization. The modified biosensor was used for both amperometric and impedimetric detection. Laccase (source: Trametes versicolor) catalyzes the oxidation reaction of p-diphenols. The biosensor provided a linear range of 0.025–20 μM and a LOD of 65 nM using EIS detection.

4.5. Peptide-Based Biosensors

Peptides are oligomers and polymers that can be customized with highly controlled preparation methods, due to the variety of natural and synthetic amino acids available for synthesis. Peptides have been employed in biosensing due to their specificity, better chemical and conformational stability compared to antibodies ^[58], low cost and facile synthesis and modification protocols that allow customization for a wide variety of applications ^[59].

Gutés et al. ^[60] reported a novel peptide-based biosensor for the detection of decabromodiphenyl ether (DBDE). The supporting electrode was prepared by growing graphene on a copper foil, decorating with AuNPs and spin-coating with poly(methylmetacrylate) (PMMA). The composite materials were transferred on a GCE. The DBDE binding peptide sequence, WHWNAWNWSSQQ, was immobilized by incubation of the AuNP-functionalized graphene electrode. The peptide-AuNP-graphene modified electrode was used for the EIS determination of polybrominated diphenyl ethers (PBDEs) and provided a response to molecules with similar structure and the biosensor showed little interference from similar compounds such as diphenyl ether.

4.6. Microbial Biosensors

Microbial biosensors use microorganisms as a sensitive biological element. Their main advantage is the fact that, unlike molecule-based biosensors, they provide information on toxicity or bioavailability ^[61]. The microbes are usually genetically engineered by modifying their structure to serve as bio-receptors for the target molecule ^[62].

Furst et al. have developed an electrochemical sandwich assay that measures the total estrogenic activity of a sample ^[63]. E. coli cells were engineered to display the estrogen receptor α (ER-α) capture agent, while a synthesized antibody mimic protein was immobilized on a gold electrode via cysteine gold chemistry. The ED molecules first bind the receptor proteins anchored onto the surface, then E. coli cells from solution attach to the receptor-bound ED, thus causing the increase in EIS signal. The system was used for the detection of estrogenic activity in solutions containing 17β-estradiol, 4-nonylphenol, genistein and DES. The calculated LOD for 17β-estradiol was 500 pM. The method did not detect individual compounds but allowed for the estimation of the total estrogenic activity.

References

Soto, A.M.; Sonnenschein, C. Environmental causes of cancer: Endocrine disruptors as carcinogens. Nat. Rev. Endocrinol. 2010, 6, 363–370.
Bedia, C.; Dalmau, N.; Jaumot, J.; Tauler, R. Phenotypic malignant changes and untargeted lipidomic analysis of long-term exposed prostate cancer cells to endocrine disruptors. Environ. Res. 2015, 140, 18–31.
Troisi, R.; Hatch, E.E.; Palmer, J.R.; Titus, L.; Sampson, J.N.; Xu, X.; Hoover, R.N. Estrogen Metabolism in Postmenopausal Women Exposed In Utero to Diethylstilbestrol. Cancer Epidemiol. Biomark. Prev. 2018, 27, 1208–1213.
Giulivo, M.; Lopez de Alda, M.; Capri, E.; Barcelo, D. Human exposure to endocrine disrupting compounds: Their role in reproductive systems, metabolic syndrome and breast cancer. A review. Environ. Res. 2016, 151, 251–264.
Ohore, O.E.; Zhang, S. Endocrine disrupting effects of bisphenol A exposure and recent advances on its removal by water treatment systems. A review. Sci. Afr. 2019, 5, e00135.
White, S.S.; Fenton, S.E.; Hines, E.P. Endocrine disrupting properties of perfluorooctanoic acid. J. Steroid Biochem. Mol. Biol. 2011, 127, 16–26.
Metzler, M.; Pfeiffer, E. Chemistry of Natural and Anthropogenic Endocrine Active Compounds. In Endocrine Disruptors—Part I; Metzler, M., Ed.; Springer: Berlin/Heidelberg, Germany, 2001; pp. 63–80.
Benigni, P.; Thompson, C.J.; Ridgeway, M.E.; Park, M.A.; Fernandez-Lima, F. Targeted High-Resolution Ion Mobility Separation Coupled to Ultrahigh-Resolution Mass Spectrometry of Endocrine Disruptors in Complex Mixtures. Anal. Chem. 2015, 87, 4321–4325.
Pintado-Herrera, M.G.; González-Mazo, E.; Lara-Martín, P.A. In-cell clean-up pressurized liquid extraction and gas chromatography–tandem mass spectrometry determination of hydrophobic persistent and emerging organic pollutants in coastal sediments. J. Chromatogr. A 2016, 1429, 107–118.
Pérez, R.L.; Escandar, G.M. Multivariate calibration-assisted high-performance liquid chromatography with dual UV and fluorimetric detection for the analysis of natural and synthetic sex hormones in environmental waters and sediments. Environ. Pollut. 2016, 209, 114–122.
Barreca, S.; Busetto, M.; Colzani, L.; Clerici, L.; Daverio, D.; Dellavedova, P.; Balzamo, S.; Calabretta, E.; Ubaldi, V. Determination of estrogenic endocrine disruptors in water at sub-ng L−1 levels in compliance with Decision 2015/495/EU using offline-online solid phase extraction concentration coupled with high performance liquid chromatography-tandem mass spectrometry. Microchem. J. 2019, 147, 1186–1191.
Myridakis, A.; Balaska, E.; Gkaitatzi, C.; Kouvarakis, A.; Stephanou, E.G. Determination and separation of bisphenol A, phthalate metabolites and structural isomers of parabens in human urine with conventional high-pressure liquid chromatography combined with electrospray ionisation tandem mass spectrometry. Anal. Bioanal. Chem. 2015, 407, 2509–2518.
Stanczyk, F.Z.; Archer, D.F.; Bhavnani, B.R. Ethinyl estradiol and 17β-estradiol in combined oral contraceptives: Pharmacokinetics, pharmacodynamics and risk assessment. Contraception 2013, 87, 706–727.
Kong, D.; Zhang, J.; Hou, X.; Zhang, S.; Tan, J.; Chen, Y.; Yang, W.; Zeng, J.; Han, Y.; Liu, X.; et al. Acetamiprid inhibits testosterone synthesis by affecting the mitochondrial function and cytoplasmic adenosine triphosphate production in rat Leydig cells†. Biol. Reprod. 2016, 96, 254–265.
Silveyra, G.R.; Canosa, I.S.; Zanitti, M.; Rodríguez, E.M.; Medesani, D.A. Interference of an atrazine commercial formulation with the endocrine control of ovarian growth exerted by the eyestalks. Environ. Sci. Pollut. Res. 2020, 27, 965–973.
Sheikh, I.A. Endocrine-disrupting potential of polybrominated diphenyl ethers (PBDEs) on androgen receptor signaling: A structural insight. Struct. Chem. 2020.
Loffredo, L.F.; Coden, M.E.; Berdnikovs, S. Endocrine Disruptor Bisphenol A (BPA) Triggers Systemic Para-Inflammation and is Sufficient to Induce Airway Allergic Sensitization in Mice. Nutrients 2020, 12, 343.
Yan, S.; Wang, M.; Zha, J.; Zhu, L.; Li, W.; Luo, Q.; Sun, J.; Wang, Z. Environmentally Relevant Concentrations of Carbamazepine Caused Endocrine-Disrupting Effects on Nontarget Organisms, Chinese Rare Minnows (Gobiocypris rarus). Environ. Sci. Technol. 2018, 52, 886–894.
Oray, M.; Abu Samra, K.; Ebrahimiadib, N.; Meese, H.; Foster, C.S. Long-term side effects of glucocorticoids. Expert Opin. Drug. Saf. 2016, 15, 457–465.
Xie, F.; Chen, X.; Weng, S.; Xia, T.; Sun, X.; Luo, T.; Li, P. Effects of two environmental endocrine disruptors di-n-butyl phthalate (DBP) and mono-n-butyl phthalate (MBP) on human sperm functions in vitro. Reprod. Toxicol. 2019, 83, 1–7.
Soto, A.M.; Sonnenschein, C. Endocrine disruptors: DDT, endocrine disruption and breast cancer. Nat. Rev. Endocrinol. 2015, 11, 507–508.
Rowdhwal, S.S.S.; Chen, J. Toxic Effects of Di-2-ethylhexyl Phthalate: An Overview. BioMed Res. Int. 2018, 2018, 1750368.
Mallia, V.; Ivanova, L.; Eriksen, G.S.; Harper, E.; Connolly, L.; Uhlig, S. Investigation of In Vitro Endocrine Activities of Microcystis and Planktothrix Cyanobacterial Strains. Toxins 2020, 12, 228.
Hudon Thibeault, A.-A.; Laurent, L.; Vo Duy, S.; Sauvé, S.; Caron, P.; Guillemette, C.; Sanderson, J.T.; Vaillancourt, C. Fluoxetine and its active metabolite norfluoxetine disrupt estrogen synthesis in a co-culture model of the feto-placental unit. Mol. Cell. Endocrinol. 2017, 442, 32–39.
Bell, M.R. Endocrine-disrupting actions of PCBs on brain development and social and reproductive behaviors. Curr. Opin. Pharmacol. 2014, 19, 134–144.
Lo, E.M.; Rodriguez, K.M.; Pastuszak, A.W.; Khera, M. Alternatives to Testosterone Therapy: A Review. Sex. Med. Rev. 2018, 6, 106–113.
Mitra, S.; Srivastava, A.; Khandelwal, S. Long term impact of the endocrine disruptor tributyltin on male fertility following a single acute exposure. Environ. Toxicol. 2017, 32, 2295–2304.
Kowalska, K.; Habrowska-Górczyńska, D.E.; Piastowska-Ciesielska, A.W. Zearalenone as an endocrine disruptor in humans. Environ. Toxicol. Pharmacol. 2016, 48, 141–149.
Lasia, A. Definition of Impedance and Impedance of Electrical Circuits. In Electrochemical Impedance Spectroscopy and Its Applications; Lasia, A., Ed.; Springer: New York, NY, USA, 2014; pp. 7–66.
Bahadır, E.B.; Sezgintürk, M.K. A review on impedimetric biosensors. Artif. Cells Nanomed. Biotechnol. 2016, 44, 248–262.
Schrattenecker, J.D.; Heer, R.; Melnik, E.; Maier, T.; Fafilek, G.; Hainberger, R. Hexaammineruthenium (II)/(III) as alternative redox-probe to Hexacyanoferrat (II)/(III) for stable impedimetric biosensing with gold electrodes. Biosens. Bioelectron. 2019, 127, 25–30.
Ertürk, G.; Mattiasson, B. Capacitive Biosensors and Molecularly Imprinted Electrodes. Sensors 2017, 17, 390.
Thévenot, D.R.; Toth, K.; Durst, R.A.; Wilson, G.S. Electrochemical biosensors: Recommended definitions and classification. Biosens. Bioelectron. 2001, 16, 121–131.
Jaffrezic-Renault, N.; Kou, J.; Tan, D.; Guo, Z. New trends in the electrochemical detection of endocrine disruptors in complex media. Anal. Bioanal. Chem. 2020, 412, 5913–5923.
Luka, G.; Ahmadi, A.; Najjaran, H.; Alocilja, E.; DeRosa, M.; Wolthers, K.; Malki, A.; Aziz, H.; Althani, A.; Hoorfar, M. Microfluidics Integrated Biosensors: A Leading Technology towards Lab-on-a-Chip and Sensing Applications. Sensors 2015, 15, 30011–30031.
Khanna, M.; Roy, S.; Kumar, R.; Wadhwa, S.; Mathur, A.; Dubey, A.K. MnO2 Based Bisphenol-A Electrochemical Sensor Using Micro-Fluidic Platform. IEEE Sens. J. 2018, 18, 2206–2210.
Cheng, Y.H.; Barpaga, D.; Soltis, J.A.; Shutthanandan, V.; Kargupta, R.; Han, K.S.; McGrail, B.P.; Motkuri, R.K.; Basuray, S.; Chatterjee, S. Metal–Organic Framework-Based Microfluidic Impedance Sensor Platform for Ultrasensitive Detection of Perfluorooctanesulfonate. ACS Appl. Mater. Interfaces 2020, 12, 10503–10514.
Le Noir, M.; Lepeuple, A.-S.; Guieysse, B.; Mattiasson, B. Selective removal of 17β-estradiol at trace concentration using a molecularly imprinted polymer. Water Res. 2007, 41, 2825–2831.
Crapnell, R.D.; Hudson, A.; Foster, C.W.; Eersels, K.; Grinsven, B.V.; Cleij, T.J.; Banks, C.E.; Peeters, M. Recent Advances in Electrosynthesized Molecularly Imprinted Polymer Sensing Platforms for Bioanalyte Detection. Sensors 2019, 19, 1204.
Saylan, Y.; Akgönüllü, S.; Yavuz, H.; Ünal, S.; Denizli, A. Molecularly Imprinted Polymer Based Sensors for Medical Applications. Sensors 2019, 19, 1279.
Wu, X.; Wang, X.; Lu, W.; Wang, X.; Li, J.; You, H.; Xiong, H.; Chen, L. Water-compatible temperature and magnetic dual-responsive molecularly imprinted polymers for recognition and extraction of bisphenol A. J. Chromatogr. A 2016, 1435, 30–38.
Kumar, P.; Deep, A.; Kim, K.-H. Metal organic frameworks for sensing applications. Trends Anal. Chem. 2015, 73, 39–53.
Sireesha, M.; Jagadeesh Babu, V.; Kranthi Kiran, A.S.; Ramakrishna, S. A review on carbon nanotubes in biosensor devices and their applications in medicine. Nanocomposites 2018, 4, 36–57.
Wei, Y.; Kong, L.-T.; Yang, R.; Wang, L.; Liu, J.-H.; Huang, X.-J. Electrochemical impedance determination of polychlorinated biphenyl using a pyrenecyclodextrin-decorated single-walled carbon nanotube hybrid. Chem. Comm. 2011, 47, 5340–5342.
Hsine, Z.; Bizid, S.; Zahou, I.; Ben Haj Hassen, L.; Nasri, H.; Mlika, R. A highly sensitive impedimetric sensor based on iron (III) porphyrin and thermally reduced graphene oxide for detection of Bisphenol A. Synth. Met. 2018, 244, 27–35.
Duffy, G.F.; Moore, E.J. Electrochemical Immunosensors for Food Analysis: A Review of Recent Developments. Anal. Lett. 2017, 50, 1–32.
Li, X.; Huang, Y.; Chen, M.; Tong, Y.; Zhang, C. A label-free electrochemical bisphenol A immunosensor based on chlorogenic acid as a redox probe. Anal. Methods 2017, 9, 2183–2188.
Singh, A.C.; Bacher, G.; Bhand, S. A label free immunosensor for ultrasensitive detection of 17β-Estradiol in water. Electrochim. Acta 2017, 232, 30–37.
Chen, Y.; Zhang, S.; Hong, Z.; Lin, Y.; Dai, H. A mimotope peptide-based dual-signal readout competitive enzyme-linked immunoassay for non-toxic detection of zearalenone. J. Mater. Chem. B 2019, 7, 6972–6980.
Kang, B.; Kim, J.H.; Kim, S.; Yoo, K.-H. Aptamer-modified anodized aluminum oxide-based capacitive sensor for the detection of bisphenol A. Appl. Phys. Lett. 2011, 98, 073703.
Cui, H.; Wu, J.; Eda, S.; Chen, J.; Chen, W.; Zheng, L. Rapid capacitive detection of femtomolar levels of bisphenol A using an aptamer-modified disposable microelectrode array. Microchim. Acta 2015, 182, 2361–2367.
La Spina, R.; Ferrero, V.E.V.; Aiello, V.; Pedotti, M.; Varani, L.; Lettieri, T.; Calzolai, L.; Haasnoot, W.; Colpo, P. Label-Free Biosensor Detection of Endocrine Disrupting Compounds Using Engineered Estrogen Receptors. Biosensors 2017, 8, 1.
Im, J.-E.; Han, J.-A.; Kim, B.K.; Han, J.H.; Park, T.S.; Hwang, S.; In Cho, S.; Lee, W.-Y.; Kim, Y.-R. Electrochemical detection of estrogen hormone by immobilized estrogen receptor on Au electrode. Surf. Coat. Technol. 2010, 205, S275–S278.
Kim, B.K.; Li, J.; Im, J.-E.; Ahn, K.-S.; Park, T.S.; Cho, S.I.; Kim, Y.-R.; Lee, W.-Y. Impedometric estrogen biosensor based on estrogen receptor alpha-immobilized gold electrode. J. Electroanal. Chem. 2012, 671, 106–111.
Ba, S.; Vinoth Kumar, V. Recent developments in the use of tyrosinase and laccase in environmental applications. Crit. Rev. Biotechnol. 2017, 37, 819–832.
Asadgol, Z.; Forootanfar, H.; Rezaei, S.; Mahvi, A.H.; Faramarzi, M.A. Removal of phenol and bisphenol-A catalyzed by laccase in aqueous solution. J. Environ. Health Sci. Eng. 2014, 12, 93.
Fernandes, P.M.V.; Campiña, J.M.; Silva, A.F. A layered nanocomposite of laccase, chitosan, and Fe3O4 nanoparticles-reduced graphene oxide for the nanomolar electrochemical detection of bisphenol A. Microchim. Acta 2020, 187, 262.
Liu, Q.; Wang, J.; Boyd, B.J. Peptide-based biosensors. Talanta 2015, 136, 114–127.
Pavan, S.; Berti, F. Short peptides as biosensor transducers. Anal. Bioanal. Chem. 2012, 402, 3055–3070.
Gutés, A.; Lee, B.-Y.; Carraro, C.; Mickelson, W.; Lee, S.-W.; Mabouduan, R. Impedimetric graphene-based biosensors for the detection of polybrominated diphenyl ethers. Nanoscale 2013, 5, 6048–6052.
Melamed, S.; Elad, T.; Belkin, S. Microbial sensor cell arrays. Curr. Opin. Biotechnol. 2012, 23, 2–8.
Gawrys, M.D.; Hartman, I.; Landweber, L.F.; Wood, D.W. Use of engineered Escherichia coli cells to detect estrogenicity in everyday consumer products. J. Chem. Technol. Biot. 2009, 84, 1834–1840.
Furst, A.L.; Hoepker, A.C.; Francis, M.B. Quantifying Hormone Disruptors with an Engineered Bacterial Biosensor. ACS Cent. Sci. 2017, 3, 110–116.

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