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Review

Electrospun Nanofibers and Electrochemical Techniques for the Detection of Heavy Metal Ions

by
Angela Malara
1,2,*,
Antonio Fotia
3,
Emilia Paone
1,2 and
Giulia Serrano
2,4
1
Department of Civil, Energy, Environment and Material Engineering, Mediterranea University of Reggio Calabria, Via Graziella Loc Feo di Vito, 89124 Reggio Calabria, Italy
2
Consorzio Interuniversitario per la Scienza e la Tecnologia dei Materiali (INSTM), 50121 Firenze, Italy
3
Department of Information Engineering, Infrastructures and Sustainable Energy, Mediterranea University of Reggio Calabria, Via Graziella Loc Feo di Vito, 89124 Reggio Calabria, Italy
4
Department of Industrial Engineering—DIEF, University of Florence, Via di S. Marta 3, 50139 Firenze, Italy
*
Author to whom correspondence should be addressed.
Materials 2021, 14(11), 3000; https://doi.org/10.3390/ma14113000
Submission received: 5 May 2021 / Revised: 27 May 2021 / Accepted: 29 May 2021 / Published: 1 June 2021
(This article belongs to the Special Issue Synthesis and Characterization of Nanomaterials for Electrochemical Applications)
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Abstract

:
Contamination by heavy metals is currently one of the most environmental concerns especially due to the toxicity, pervasiveness, and persistence of these substances. As they are not biodegradable, heavy metals are harmful not only for water, air, and soil but also for human health, even in very low traces. There is therefore a pressing need to develop an efficient, economic, and rapid analysis method to be applied in a wide range of conditions and able to detect very low contaminants concentrations. Currently, the most novel solution in this field is represented by the combination of electrospun nanofibers and highly sensitive electrochemical techniques. It has been proved that nanofibers, due to their outstanding properties, perfectly fit as sensing material when trace concentrations of heavy metals were investigated by anodic stripping voltammetry, envisaged as the most sensitive electrochemical technique for this kind of measurements. This work aims to provide an overview of the latest trends in the detection of contaminants by the simultaneous use of electrospun fibers and anodic stripping voltammetry. Indeed, a clear and comprehensive vision of the current status of this research may drive future improvements and new challenges.

1. Introduction

Electrospinning (ES) is a versatile technique applied to produce nano- and microfibers. It makes use of an electrical force to extrude conductive polymeric solutions in fibers with nanoscale diameters. With the help of a suitable polymeric vector, it is possible to produce one-dimensional (1D) nanostructures of organic, inorganic, and hybrid composite materials [1], with different morphologies and architectures, such as dense, hollow, core–shell, and fiber assemblies [2].
The fields of application of electrospun nanostructures are numerous and wide, considering the high versatility of this kind of material. Manifold examples can be found in the environmental sector, such as in water treatment from contaminants [3], in the catalysis field, as improved catalysts [4], in biomedical applications, as medicament carriers [5], in sensor devices, as high reactive sensing materials [6,7], and in the sustainable exploitation of energy, as innovative adsorbents [8,9,10,11]. Moreover, the ES technique has been intensively employed for the design and fabrication of structured nanofibrous materials for energy conversion and storage devices, as well as dye-sensitized solar cells [12], fuel cells [13], lithium/sodium-ion batteries [14], supercapacitors [15], and electronic applications in general [16].
Numerous electrospun materials have been realized and tested for heavy metal ions (HMIs) detection, exploiting very different approaches. For example, nanofibrous membranes immobilized in a chemosensor/receptor system were applied for optical, electro, and mass detections of heavy metals [17], and in other cases, the spectral changes, measured by an optic spectrometer, gave information on the detection process over colorimetric fibrous membranes [18]. Besides, electrospun fibers were also used in HMIs determination by conventional electrochemical measurements in aqueous media, such as cyclic voltammetry [19,20], and solid samples, such as electrokinetic remediation [21]. Indeed, electrospun materials have been successfully used for the detection of HMIs in different environments, such as wastewaters [22], rivers, and soils [21,23], on account of not appropriate wastes disposals and, in general, other causes linked to human activities. As heavy metals are in most cases non-biodegradable, they accumulate in foods derived from land animals, fishes, and vegetables. In turn, they are uptaken by humans, causing serious diseases. In this light, it is of vital importance to detect such species at very low traces and their neutralization [24].
Electrospun nanofibers possess many favorable characteristics in this sense, such as high surface-to-volume ratio, porosity, tunability of nanofibers properties (chemical composition, morphology, and dimensions), and they can be easily functionalized to optimize material performances [25].
Several techniques, generally considered as standard methods, have been utilized to detect traces of HMIs on well-known large-scale instruments, such as atomic absorption spectroscopy, inductive coupled plasma-mass spectroscopy, ion chromatography, x-ray fluorescence spectroscopy, and others [26,27,28]. These techniques, however, suffer from many disadvantages, i.e., long time analyses, expensiveness, complicated instrumentation, need of highly specialized personnel, and inability to carry out the on-site measurement. On the other hand, electrochemical techniques have been widely used on account of several advantages over the above-cited ones, such as high sensing performances, very low limits of detection (LOD), simpleness, fastness, and cheapness, together with the ability to simultaneously detect different substances [29,30]. Particularly, among these electrochemical methods, stripping voltammetry is a good choice for HMIs detection because of its simplicity, easy instrumentation, high sensitivity, low LOD, short-time measurement, and, last but not least, portability [31].
In this mini-review, we summarized the most recent advancements in the development of fibers, fabricated by ES, for the detection of HMIs by the anodic stripping voltammetry (ASV). Indeed, the coupling of electrospun nanofibers, characterized by the above-described advantages with those of the detection ability of the selected electrochemical method, is at the present, and maybe also in the next future, the winning solution for the HMIs sensing. Therefore, a brief and comprehensive overview of the current status of this research, not yet reported to the best of our knowledge, could provide new strategies and potential opportunities for the HMIs sensing, aiming at avoiding serious health issues for human beings.
Is out of the scope of the present work to review the countless papers dealing with the HMIs detection by the traditional techniques cited above, and materials and components other than nanofibers fabricated by ES. This topic has been recently faced in, where, however, other detection methodologies, besides the selected electrochemical one, were reviewed [16,17,32,33,34].
In the following, some fundamental concepts on the ES design and heavy metal toxicity were first introduced. Then, ASV principles and main methodologies, namely linear sweep, differential pulse, and square wave were summarized. Finally, the most recent findings on the use of electrospun fibers for the detection of contaminants employing ASV were reviewed.

2. Electrospinning Design

ES is considered a very simple, scalable, and inexpensive technique able to produce nanofibrous structures. It is based on the application of an electric field to a polymer carrier solution, conveniently introduced into a glass syringe and pushed through the syringe needle towards a grounded collector while controlling its flow rate, as depicted in Figure 1. The increment of the intensity of the electric field causes the drop of polymer to elongate and form a conical shape, the so-called Taylor cone. When the applied electric field reaches a critical value, the repulsive electric forces overcome the surface tension of the drop, the polymer jet is ironed within the high electric field and due to the rapid evaporation of the solvent is finally deposited on the collector in the form of nanofibers.
Accurate control of working parameters is essential to tailor nanofibers’ characteristics, in terms of diameters and morphologies [35]. Those parameters can be mainly divided into three areas covering solution, process, and ambient factors. Polymer solution parameters have the most significant influence on the ES process and include molecular weight, concentration, viscosity, conductivity, and surface tension of the solution. Processing parameters are indeed considered to have a major influence on fibers formation and take into account the applied voltage, flow rate, diameter of the needle, and tip-collector distance. Ambient parameters, such as temperature and humidity, are known to determine a great influence on the entire process. A summarized description of working parameters is reported in Table 1. Although the precise control of those parameters allows properties tunability and can therefore result in very different kinds of nanofibers, the well-known outstanding features are common. High porosity, small pore size, remarkable high surface area-to-volume ratio, and low density are surely among the most important.
In the ES process, a wide choice of natural, synthetic, and hybrid polymers is possible. Indeed, with the help of a suitable polymer vector, nanofibers of organic, inorganic, and hybrid composite materials with desired physical, chemical, and mechanical properties are produced [8,36,37]. The functionalization with suitable additives or focused chemical/thermal treatments can further convey superior and specific features. Consequently, the field of applications of electrospun nanofibers is large and varied and it should be also highlighted that the ES process, aside from its ease and cheapness, is overall flexible for large-scale production.

3. Contamination and Toxicity of Heavy Metals

The term heavy metal is generally ascribed to any metallic element based on featuring parameters such as the atomic weight/number, density, chemical behavior, and toxicity. Even if heavy metals are natural components of the Earth’s crust [38,39,40], they can also be the result of numerous anthropogenic activities such as mine tailings, disposal of high metal wastes, leaded gasoline, animal manures, land application of fertilizers, sewage sludge, pesticides, wastewater irrigation, coal combustion residues, and spillage of petrochemicals, causing soil, water, and air contamination [41], Figure 2. Typical heavy metals are arsenic (As), cadmium (Cd), chromium (Cr), lead (Pb), mercury (Hg), thallium (Tl), copper (Cu), selenium (Se), and zinc (Zn). The major problems that affect these metals are mainly related to the impossibility to be degraded or destroyed.
As a result, the increasing consumption in technological and industrial sectors has led to a wide distribution of heavy metals in the environment promoting their bioaccumulation. As trace elements, some heavy metals, i.e., zinc, selenium, copper, just to cite a few, are necessary for human metabolism [42], but they can cause poisoning at high concentrations. Indeed, when long time exposure to these substances is considered, many human diseases can arise and ascribe to them [43,44,45,46]. Considering that heavy metals pollution affects all environmental compartments (soil, water, and air), there are various routes through which they present risks to humans, animals, plants, and ecosystems as a whole. Such ways include alteration of pH soil, absorption by plants, consumption of contaminated water, and direct ingestion through the food chain [47]. Therefore, the toxicity of heavy metals depends on several parameters such as the route, the dose, the time of exposure, but it also depends on specific individuals (age, gender, and health state). In Table 2 the main features of heavy metals are summarized.
With these premises, the detection and the quantitative determination of HMIs in environmental compartments are of paramount importance. Heavy metals have been included as the priority substances to be monitored, especially in water, by several international organization like the World Health Organization (WHO), the US Environmental Protection Agency (EPA), Centre for Disease Control (CDC), and European Union (EU) [48,49,50,51].

4. Electrochemical Techniques for the Detection of Heavy Metal Ions

The electrochemical techniques available for a different kind of analysis are numerous, as schematically depicted in Figure 3. The differences among them are mainly due to the LOD that can be achieved.
In HMIs detection, the need to have high sensitivity restricts the choice of the possible methods. In particular, stripping voltammetry is usually preferred.
Stripping voltammetry is a very sensitive analysis, highly indicated for the detection of trace metals in the ppb range. It is generally classified in anodic stripping voltammetry, cathodic stripping voltammetry, and adsorptive stripping voltammetry. Despite this, the anodic type is the most widely used.
ASV is regarded as a powerful electroanalytical technique and it is considered versatile and low cost [52]. Its main characteristic resides in the preconcentration of the analyte at the electrode followed by a potential sweep (voltammetry methods) to dissolve preconcentrated species of interest, making their quantification possible even at a low detection limit.
More than 20 elements, even simultaneously, can be detected with this method, reduced to the metallic state, and reoxidized. It consists of the formation of an amalgam due to the deposition of metal ions into a mercury-based electrode by the application of a sufficient potential to initiate reduction. In this configuration, while the applied potential is held constant the solution is stirred or otherwise, the electrode rotated for an established time. Finally, by scanning the applied potential in the opposite direction to the initial one, the amalgamated metals are stripped out of the mercury, that is to say oxidized. The peak currents obtained are proportional to the concentration of each metal in the solution and representative of the metal itself. The solubility of the analyte in mercury may influence the sensitivity. It is usually higher for metals that have higher solubilities, while in case of poor solubilities responses at the trace concentrations are not adequate. Mercury-free solid electrodes can also be used when it is necessary to detect elements that do not form amalgam or do not oxidize in combination with mercury.
Despite that this method is characterized by high sensitivity, there are even more possible actions to increase it. Indeed, according to the potential sweep, thus the waveforms produced, it is possible to identify linear sweep anodic stripping voltammetry (LSASV), differential pulse anodic stripping voltammetry (DPSAV), and square wave anodic stripping voltammetry (SWASV).

4.1. Linear Sweep Anodic Stripping Voltammetry

In the LSASV, the voltage profile involves a linear scan in time, as depicted in Figure 4a. The current signal, corresponding to the potential at which the species begins to be oxidized or reduced, produces well-defined and selective stripping peaks, due to a lower interference among species. A wide range of metal ion concentrations can be detected with this method. In many cases, LSASV has been envisaged as a good alternative to another long and expensive method for lead detection [53,54] and for Zn, Pb, Cu, and Hg in trace quantity both alone and mixed all together [55]. The determination of Cr(VI) with the lowest limit of detection was instead reported by Aliyu et al. [56].

4.2. Differential Pulse Anodic Stripping Voltammetry

The improvement of detection limits is possible in ASV when using potential waveforms other than the linear sweep. DPASV uses a staircase potential waveform superimposed on the linear waveform of linear sweep voltammetry, as shown in Figure 4b.
The differential pulse method is much more sensitive compared to the linear one. It provides a sharp peak for each species being analyzed and, as a consequence, the measure of the height or the area of these peaks results to be more precise, as its relation to the concentration is improved. Indeed, a small peak in the differential pulse mode, due to low concentrations, is much simpler to measure than only a small change in the height of the current, as depicted in Figure 5.
Moreover, it is much easier to distinguish two species with similar potential, considering that it only requires a difference of about 0.05 V contrary to LSASV where a difference of about 0.2 V is necessary.
Multiple heavy metals, in very low concentrations, have been successfully detected by this method, as extensively reported in the literature, where the advantages of the technique were clearly exploited [57,58,59].

4.3. Square Wave Anodic Stripping Voltammetry

If the potential waveform is a symmetrical square wave superimposed on a staircase potential, then SWASV is considered, Figure 4c. It is an extension of the square wave voltammetry, since it works the same, except for the preconcentration step, typical of all the stripping analysis. During each square wave cycle, the current is sampled twice, respectively at the end of the forward and reverse pulse. The difference in current between the two points is plotted versus the applied potential.
Being currents very high, LOD can achieve sensitivity in the parts-per-trillion range, especially when more than one metal ion in the sample is present.
Indeed, due to the high sensitivity and selectivity, it is generally preferred in the detection of heavy metals [60,61].

5. Recent Nanofibers for HMIs Sensors

In the last years, novel electrospun nanofibrous membranes acting as electrochemical sensors for HMIs detection have been manufactured. Very different types of electrospun nanofibrous membranes were considered, such as pure or doped, hybrid, and composite, demonstrated themselves as highly recommended materials in this sensing field, especially when their performances were compared with the same material synthesized with a different method.
The removal of heavy metals compounds from contaminated air, soil, and water using electrospun fibers is mainly due to the interactions between the active sites on the surface of fibers and HMIs, originated by electrostatic interactions and both physical and chemical affinity. Briefly, the functional sites of which fibers can be endowed, through the different functionalization or doped methods, promote the activation of anchor points for HMIs. Moreover, the high surface area to volume ratio of fibers conveys a broader dispersion of active sites, that along with the porous structure of fibrous membranes, assess the heavy metal removal capability of the electrospun [63].
Therefore, it has experimented that the integration of nanomaterials as electrodes can improve the sensitivity and reproducibility of electrochemical methods in the detection of HMIs [64].
When ASV is used, the preconcentration of the analyte at the electrode surface, by both static and dynamic adsorption, is first involved and then followed by a potential sweep that, through the oxidation/reduction process, determines the detection mechanism.
In this way, considering the advantageous combination of electrochemical techniques and nanofibrous materials (Figure 6), smaller electrochemical signal detectors, such as smart and field-portable devices, can be easily developed to replace classical bulky electrochemical workstations [31].
Limited examples of this combined system can be found in the literature. In particular, when polymeric nanofibers are considered, polyaniline conductive polymer was evidenced among the most used sources. Indeed, it played a dual role in both increasing the surface area, due to the monodimensional structure, and assuring at the same time a high conductivity due to the well-known electronic properties. Promphet et al. [65] reported electrospun nanoporous fibers fabricated by mixing graphene, polyaniline, and polystyrene and deposited onto carbon electrodes. The system was tested under SWASV for the simultaneous determination of Pb2+ and Cd2+ ions in the presence of Bi3+ ions. The observed increase in the electrochemical sensitivity of modified electrodes (observed in comparison to unmodified ones) was ascribed to an increase of the specific electrode surface area because of the presence of nanofibers. As usual, the ES process parameters (type of solvent, tip to collector distance, and electric field between syringe and collector) played a pivotal role in determining the fibers morphology and electrochemical sensitivity. The electrode system showed high reproducibility and was successfully applied in real river water samples, demonstrating to be a useful tool for the environmental monitoring of these ions with a detection limit for Pb2+ and Cd2+ down to 3.3 and 4.43 μg/L, respectively. Huang et al. [66] used one-dimensional phytic acid doped polyaniline nanofibers as a modifier for glassy carbon electrodes for simultaneous detection of Cd2+ and Pb2+ using DPASV. The reported detection limits were 0.02 and 0.05 µg/L for Cd2+ and Pb2+, respectively. The fabrication and evaluation of a glassy carbon electrode modified with self-doped polyaniline nanofibers/mesoporous carbon nitride and bismuth for simultaneous determination of trace Cd2+ and Pb2+ by SWASV were reported by Zhang et al. [67]. Under the optimum conditions, the fabricated electrode exhibited LOD of 0.7 nM for Cd2+ and 0.2 nM for Pb2+.
Both individual and simultaneous detection of Pb2+ and Cd2+ were afterward investigated on polyaniline nanotubes/electrospun polystyrene surface [68]. Morphological and electrochemical properties of the PANI nanotubes were demonstrated to depend on the size of the polystyrene fibers. Good sensitivity and reproducibility were demonstrated by SWASV. The LOD was found to be 9.65 × 10−11 mol/L and 2.67 × 10−10 mol/L for the individual detection of Pb2+and Cd2+ ions, respectively. Simultaneous detection of Zn2+, Cd2+, and Pb2+ using graphene–polyaniline nanocomposite electrode was investigated by SWASV in the presence of Bi3+. Metal ion concentration with detection limits of 1.0 μg/L for Zn2+ and 0.1 μg/L for both Cd2+ and Pb2+. The modified electrode allowed selective determination of the target metals in the presence of common metal interferences including Mn2+, Cu2+, Fe3+, Fe2+, Co3+, and Ni2+ [69]. Field monitoring of HMIs pollution for the detection of Hg2+ was demonstrated by Naourei et al. [70]. A novel conductive nanofibrillar structure made of a copolymer, poly(aniline-co-o-aminophenol) decorated with gold nanoparticles allowed mercury ions quantification by ASV with a very LOD of 0.23 nM. The sensor resulted efficient in Hg2+ detection in river water and in fish samples.
Along with electrospun polyaniline, another commonly reported system was based on carbon nanofibers, considered a system with remarkable surface area. Li 2010 et al. [71] constructed a bismuth-film modified graphite nanofibers–Nafion glassy carbon electrode for the simultaneous determination of trace Cd2+ and Pb2+. The electrochemical properties of the modified electrode, studied under optimal conditions, showed the LOD equal to 0.09 μg/L for Cd2+ and 0.02 μg/L for Pb2+ with a 10 min preconcentration by DPASV. High reproducibility and selectivity, in both real, such as river water, and human blood samples were demonstrated. The same metals, generally reported as representative metals, were also used by Zhao et al. [72] to test through the same electrochemical technique the performance of a carbon-based fibers/Nafion modified electrode, resulting in a LOD equal to 0.9 × 10−9 M and 1.5 × 10−9 M, for Pb2+ and Cd2+, respectively. A Nafion-modified glassy carbon electrode, combining bis(indolyl)methane with the unique properties of mesoporous carbon nanofiber, was fabricated for anodic stripping analysis of Hg2+ with a satisfactory result in HMIs coexistence (Hg2+, Cd2+, Pb2+, and Cu2+). This electrochemical sensor significantly improved selectivity and sensitivity towards Hg2+ determination with a detection limit of 0.3 nM [73]. Glutathione peptide was successfully immobilized onto a nanomaterial substrate electrode based on the carbon nanofiber. The repeatability, reproducibility, and analytical performance were compared to a classical screen-printed carbon electrode modified with glutathione. It was demonstrated that the enhanced surface area attributed to carbon nanofibers substrate gave higher results to Pb2+ and Cd2+ determination [74]. A facile, green, highly sensitive, and simultaneous method for the detection of trace HMIs was demonstrated by Zhang et al. [75]. Well-dispersed gold nanoparticles, grown on carbon nanofibers synthesized via the ES technique and exhibited a high surface-specific area and high porosity. When used as the working electrode for the simultaneous determination of HMIs such as Cd2+, Pb2+, and Cu2+ through the SWASV method, those properties resulted in being beneficial for the penetration of heavy metal ion solutions and increased the surface contact area of the electrode. Simultaneous detection of Cd2+, Pb2+, and Cu2+ with a low concentration of 0.1 mM, was attributed to the exposed well-dispersed gold nanoparticles and the high electron transport capability of carbon nanofibers. Vertically aligned carbon nanofibers were evaluated for the detection of Pb2+ by ASV by Robinson et al. [76]. The achieved detection limit reported was 1.73 nM. A nanocomposite of polypyrrole and carbon nanofibers modified carbon paste electrode was reported for the determination of traces of lead ions in real samples of water. The SWASV was used to investigate the analytical performances of the designed electrode. Under the optimum experimental conditions, good linearity between the stripping peak currents and the concentration of Pb2+ was obtained with a detection limit estimated around 0.05 μg/L [77]. Another research provides a convenient and efficient way to construct new sensors for simultaneous trace detection of HMIs. Bimetallic platinum-gold alloy nanoparticles were constructed with electrospun carbon nanofibers for simultaneous detection of trace Cd2+, Pb2+, and Cu2+ by SWASV with a sensitivity of 0.10 mM. The excellent sensitivity and low detection limit for HMIs detection were ascribed to the high conductivity of CNFs, fast response of platinum-gold alloy nanoparticles, and high specific surface area of the hybrid structure [78]. Porous carbon nanofibers co-doped with nitrogen and sulfur were used to modify a glassy carbon electrode. Compared to a bare glassy carbon electrode, the one modified shows improved sensitivity for Cd2+ in DPASV [79]. A novel elaborated electrochemical sensor based on a nanocomposite of ionic liquid 1-ethyl-3-methylimidazolium bis(trifluoromethylsulfonyl) imide, carbon nanofibers, and bismuth particles modified carbon paste was studied. The sensor exhibited excellent electroanalytical performances for the determination of Pb2+ and Cd2+ with LOD for Pb2+ and Cd2+ equal to 0.12 and 0.25 μg/L, respectively. A wide linear response range and low LOD with high sensitivity, selectivity, and reproducibility were obtained [80]. A three-dimensional carbon nanofiber network formed by the ES of a mixed solution of montmorillonite and polyacrylonitrile showed high stability, selectivity, and a low detection limit (0.4 μg/L) for Cu2+ as measured using DPASV [81]. A trace amount of As3+ detection was instead reported by using a sensing platform made by polyaniline nanosheet array on electrospun iron-containing carbon nanofibers substrate followed by self-deposition of gold nanoparticles. High sensitivity with a detection limit of 0.5 ppb was registered by SWASV [82].
Few other works reported on other kinds of pure, hybrid, and composite nanofibers for multiple HMIs detection. Reduced graphene oxide/polyvinyl butyral nanofibers on glassy carbon electrodes were used for fabricating an electrochemical sensor for Cu2+ detection by DPASV. The as-fabricated sensor showed good analytical performance with a low detection limit of 4.1 nM [83]. Zinc oxide nanofibers with high surface area, fabricated by ES, have demonstrated optimum sensitivity for Cd2+ and the simultaneous analysis with Cu2+, Pb2+, Cu2+, and Hg2+ is feasible in water samples. The strong affinity between zinc oxide and Cd2+ was exploited by SWASV and the reported LOD was equal to 1.8·10−9mol/L [84]. A zinc oxide nanofibers/L-cysteine nanocomposite was used as electrodes for the electrochemical sensing of Pb2+ ions. The high porosity of nanofibers combined with Lewis acid-base interaction of L-cysteine made it a great material for Pb2+ detection in a real sample. SWASV displayed excellent sensitivity, selectivity, and stability with a LOD of 0.397 μg/L [85]. To test Cu2+ ions contaminations in real environmental samples, an amino-rich organosilica-nanofiber-modified gold electrode was obtained upon ES. The 3-dimensional porous fiber promoted Cu2+ ions accumulation inside the structure. By using SWASV, a very sensitive response to Cu2+ ions was obtained, with a wide linear range, high stability, and low detection limit down to 2.6 pM [86].
Finally, it is noteworthy to highlight that, as inferred by the analyzed literature, the pivotal role in the sensing mechanism of HMIs by ASV was strictly dependent on the material features. Despite a very broad diameters distribution, ranging from 40–60 nm [66] to 2.44 μm [65] was evidenced for the reported cases, on account of different electrospun fibers (such as pure, hybrid, doped, and functionalized), the high surface area to volume ratio of fibers and membranes porosity were always ensured for each system.

6. Concluding Remarks

The application of ASV for the determination of HMIs using electrospun nanofibers is undoubtedly a well-assessed field of research. Heavy metals pollution is a pressing issue since it involves water, air, and soil contamination and consequently, it also results harmful to humankind. When high selectivity and very low traces of contaminants are studied, the combination materials/methods showed a great impact. ASV was evaluated in its main potential configurations, linear sweep, differential pulse, and square wave, whereas manifold electrospun structures, pure, doped, composite, and hybrid were considered. Indeed, the outstanding properties of electrospun fibers, in terms of their tunability by proper doping and functionalization, but also their high surface area to volume ratio and porosity, were opportunely revised for the specific application in the ASV of heavy metals.
However, the design and development of focused strategies for the effective detection of HMIs is still a big issue and needs further improvements. Through this contribution, an overview of the current trends in the detection of HMIs by ASV and electrospun nanofibers was provided. The review aims to drive future challenges in the enhancements of fibrous materials for both the detection and remediation of heavy metals in a sustainable perspective of a circular economy.

Author Contributions

Conceptualization, A.M. and E.P.; methodology, A.M. and A.F.; formal analysis, A.M. and G.S.; investigation, A.M. and E.P.; data curation, A.M., A.F., E.P. and G.S.; writing—original draft preparation, A.M; writing—review and editing, A.M., A.F., E.P. and G.S.; supervision, A.M. All authors have read and agreed to the published version of the manuscript.

Funding

This research was funded by Regione Toscana, POR-FESR 2014-2020, call FAR-FAS, of the project SENSOR.

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Data Availability Statement

Not applicable.

Conflicts of Interest

The authors declare no conflict of interest.

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Materials 14 03000 g001 550
Figure 1. Schematic representation of the electrospinning set-up.
Figure 1. Schematic representation of the electrospinning set-up.
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Materials 14 03000 g002 550
Figure 2. Schematic representation of heavy metals contamination in water, air, and soil environment.
Figure 2. Schematic representation of heavy metals contamination in water, air, and soil environment.
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Materials 14 03000 g003 550
Figure 3. Electrochemical techniques.
Figure 3. Electrochemical techniques.
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Materials 14 03000 g004 550
Figure 4. Profile of the potential versus time in (a) linear sweep, (b) differential pulse, and (c) square wave anodic stripping voltammetry (adapted from [62]).
Figure 4. Profile of the potential versus time in (a) linear sweep, (b) differential pulse, and (c) square wave anodic stripping voltammetry (adapted from [62]).
Materials 14 03000 g004
Materials 14 03000 g005 550
Figure 5. Profile of the current versus the potential for the linear sweep and differential pulse voltammograms in the presence of two contaminants.
Figure 5. Profile of the current versus the potential for the linear sweep and differential pulse voltammograms in the presence of two contaminants.
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Materials 14 03000 g006 550
Figure 6. Representative sketch of the analyzed combined system.
Figure 6. Representative sketch of the analyzed combined system.
Materials 14 03000 g006
Table
Table 1. Main electrospinning working parameters.
Table 1. Main electrospinning working parameters.
Electrospinning Working Parameters
SolutionProcessAmbient
Molecular weight Concentration
Viscosity
Conductivity
Surface tension		Applied voltage
Flow rate
Diameter of the needle
Tip-collector distance		Temperature
Humidity
Table
Table 2. Sources of heavy metals and toxicity on human health.
Table 2. Sources of heavy metals and toxicity on human health.
Heavy MetalsSourcesToxic Impact on Human HealthPermissible Limits [49,50]
Asdrinking-water and food; industrial processes; tobaccopigmentation changes, skin lesions, hyperkeratosis10 μg/L
Cdcorrosion of galvanized pipes, erosion of natural deposits, discharge from metal refineries, runoff from waste batteries and paintsrenal tubular dysfunction, osteoporosis, acute pneumonitis, cancer3 μg/L
Crcoal and oil combustion; electroplating; leather tanning; industrial processes, tobaccocontact dermatitis, hemolysis, renal diseases, allergic reaction, cancer50 μg/L
Pbdrinking-water and food; lead-containing pipes; children’s toys; cosmeticsmicrocytic anemia; nephropathy; immune system diseases; reproductive system diseases; developmental system disease10 μg/L
Hgaccidents, environmental pollution, dental care, preventive medical practices, industrial and agricultural operations, fish consumptioncalcium homeostasis; neurological diseases, corrosive to skin, corrosive to eyes, cancer, corrosive to the gastrointestinal tract6 μg/L
Tldrinking-water and food; air-borne contamination (fly ash)gaseous emission of cement factories, coal-burning power plants, metal sewers0.5 µg/L
Senatural deposits releases from copper smeltingendocrine function, hepatotoxicity, and gastrointestinal disturbances40 μg/L
Cuindustrial discharges, copper salts, plumbing materialbrain and kidney damage, chronic anemia, stomach and intestine irritation2 mg/L
Zndischarges of smelter slags and wastes, mine tailings, coal and bottom fly ash, fertilizersdizziness, fatigue5 mg/L
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Malara, A.; Fotia, A.; Paone, E.; Serrano, G. Electrospun Nanofibers and Electrochemical Techniques for the Detection of Heavy Metal Ions. Materials 2021, 14, 3000. https://doi.org/10.3390/ma14113000

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Malara A, Fotia A, Paone E, Serrano G. Electrospun Nanofibers and Electrochemical Techniques for the Detection of Heavy Metal Ions. Materials. 2021; 14(11):3000. https://doi.org/10.3390/ma14113000

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Malara, Angela, Antonio Fotia, Emilia Paone, and Giulia Serrano. 2021. "Electrospun Nanofibers and Electrochemical Techniques for the Detection of Heavy Metal Ions" Materials 14, no. 11: 3000. https://doi.org/10.3390/ma14113000

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