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Review

Screen-Printed Voltammetric Sensors—Tools for Environmental Water Monitoring of Painkillers

by
Katarzyna Tyszczuk-Rotko
*,
Jędrzej Kozak
and
Bożena Czech
Faculty of Chemistry, Institute of Chemical Sciences, Maria Curie-Skłodowska University in Lublin, 20-031 Lublin, Poland
*
Author to whom correspondence should be addressed.
Sensors 2022, 22(7), 2437; https://doi.org/10.3390/s22072437
Submission received: 14 January 2022 / Revised: 18 March 2022 / Accepted: 20 March 2022 / Published: 22 March 2022
(This article belongs to the Special Issue Screen-Printed Electrochemical Sensors and Their Applications)

Abstract

:
The dynamic production and usage of pharmaceuticals, mainly painkillers, indicates the growing problem of environmental contamination. Therefore, the monitoring of pharmaceutical concentrations in environmental samples, mostly aquatic, is necessary. This article focuses on applying screen-printed voltammetric sensors for the voltammetric determination of painkillers residues, including non-steroidal anti-inflammatory drugs, paracetamol, and tramadol in environmental water samples. The main advantages of these electrodes are simplicity, reliability, portability, small instrumental setups comprising the three electrodes, and modest cost. Moreover, the electroconductivity, catalytic activity, and surface area can be easily improved by modifying the electrode surface with carbon nanomaterials, polymer films, or electrochemical activation.

1. Introduction

Increased production and consumption of over-the-counter drugs such as painkillers, e.g., diclofenac, ibuprofen, naproxen, ketoprofen, or acetaminophen, are connected with their increased excretion and presence in wastewater from homes and hospitals [1,2,3,4,5,6,7,8]. There are different sources for the contamination of surface and underground waters with drug residue, including the pharmaceutical industry, farming and veterinary, healthcare centers, and households (incorrect waste management in case of expired drugs). Some residues of the pharmaceutical substances, together with sewage, enter wastewater treatment plans (WWTP), which unfortunately are not adjusted to degrade those highly specific compounds [9,10]. Interestingly, about 2000 active pharmaceutical ingredients are administered worldwide [11]. The greatest input of pharmaceuticals into the environment have, however, treated wastewater [12,13,14,15]. It was established that 30–90% of oral doses are excreted as active substances (Table 1) [16]. Conventional WWTP are not designed to remove pharmaceuticals; therefore, the removal rates vary (Table 1). The fate of pharmaceuticals in WWTP and the environment is affected by the pharmaceutical properties, including their persistence and connected half-life. Solubility, transformation products, bioaccumulation potential, and, first of all mobility, affect their toxicity [16].
Insufficient removal from wastewater influents was a main background for the application of various wastewater treatment methods: filtration [17], adsorption [18,19,20,21], Advanced Oxidation Processes [22,23,24,25], UV [26,27], ozonation [28,29,30,31], H2O2 [32,33], photocatalysis [34,35,36,37,38,39,40], Fenton and photo-Fenton process [41,42,43], electro-catalysis [44,45], electro-Fenton [46] etc.
Although the reported concentrations of pharmaceuticals in the environmental matrices are generally low—usually less than 1 μg L−1, but their huge usage and abundance in the environment make the authorities worried about the long-term impact on animals and humans (Table 1) [47]. Although there are no requirements to detect and limit the concentration of pharmaceuticals in wastewater and water, some of them have been identified as a priority for further study, including paracetamol and diclofenac [48].
Despite the large differences in the removal rates, it is known that sorption, adsorption, sedimentation, and biotransformation in WWTP occurred [49,50,51,52,53,54]. Hydrophobic or electrostatic interactions are responsible for the sorption of drugs [55]. However, highly hydrophilic acidic drugs such as acetylsalicylic acid, ibuprofen, ketoprofen, naproxen, and diclofenac (pKa 4.2–4.9) are not sorbed and remain in the water [50]. The other negative effect can arise from the presence of metabolized (mainly its hydroxy and carboxy derivatives) drugs as they can form conjugates with similar or even increased toxicity in comparison to the parent drug [6]. It was established that the presence of drugs in the water revealed significant oxidative stress and caused histological changes in Cyprinus Carpio tissues [56] or disrupted microalgal growth.
The presence of those substances in surface waters has a toxic action on fish and other water organisms and can cause an increase in the incidence of some diseases, e.g., cancer (female sex hormones). The presence of antibiotics in water is connected with the observed increase in drug resistance of various microorganisms, even pathogenic ones. Constant exposure to pharmaceuticals in drinking water has endangered the most sensitive groups such as infants, the elderly, or patients with kidney, liver failure, or cancer. Due to the presence of estrogens in the water, feminization of male individuals and an increase in the incidence of breast and testicular cancer are noted [57,58,59]. Some of the pharmaceuticals present in water (i.e., anticancer drugs) can penetrate the blood-placenta barrier revealing teratogenic and embryotoxic effects endangering pregnant women in particular [60,61].
Induction of oxidative stress is connected with the production of reactive oxygen species (ROS) (such as hydroxyl radicals (OH), superoxide radicals (O2•−), and hydrogen peroxide (H2O2) responsible for peroxidation of membranes’ polyunsaturated fatty acids and proteins [62]. In the studies considering the 98 pharmaceuticals detected in different water matrices (treated wastewater, surface water, and groundwater), it was established that 11 out of 49 pharmaceuticals were found to exert human health risk from ingesting contaminated surface water of India [63]. The growing problem of contamination of the water environment forces the use of various methods of removing pollutants and constant monitoring.
Residual pharmaceuticals in water samples are determined with laboratory methods, such as fluid/gas chromatography coupled with mass spectrometry. Unfortunately, these methods are expensive (cost of devices + cost of analysis) and frequently, among others, relate to the very low concentration of analytes in water samples (at ng L−1 or pg L−1 levels) and the costly and time-consuming initial sample preparation stage [64,65,66,67,68]. Compared to that, the voltammetric techniques are characterized by their low cost, simplicity of the analytic process, and the possibility to accumulate the analyte onto the surface of the working electrode before the appropriate electrode process, which eliminates the need to apply additional concentrating techniques (e.g., the extraction to solid phase) [69].
Table 1. The concentrations and removal rates of painkillers in the environmental matrices.
Table 1. The concentrations and removal rates of painkillers in the environmental matrices.
DrugExcretion and MetabolitesWWTP Removal Rate
(%)
Wastewater
Influent
(ng/L)
Wastewater
Effluent
(ng/L)
Surface Water
(ng/L)
diclofenac5–10% unchanged, metabolites: glucuronide, sulfate conjugates [49]9–60 [50]
57.9 [47]
up to 302 [50]
191,000 [47]
1300–3300 [51]
Up to 5450 [50]
10,000 [52]
80,000 [47]
up to 490 [50]
1200 [48]
1410 [53]
ibuprofen1% unchanged
Metabolites: (+)-2-40-(2-Hydroxy-2-methylpropyl)-phenylpropionic acid (25%) and (+)-2-40-(2- carboxypropyl)-phenylpropionic acid (37%), conjugated ibuprofen (14%) [49]
78–100 [50]
94.8 [47]
5533 [50]
344,000 [47]
711 [50]
18,000 [47]
400 [50]
126 [53]
naproxen<1 unchanged, metabolites: 6-o-Desmethyl naproxen (o1%), conjugates (66–92%) [49]50–98 [50]611,000 [50]33,900 [50]
10,000 [52]
297 [53]
390 [48]
400 [50]
ketoprofenMetabolites: Glucuronide conjugates [49]15–100 [50]5700 [50]
1000–10,000 [54]
1620 [50]120 [48]
329 [50]
paracetamol80% as conjugates, metabolites: Sulphate conjugate (30%), paracetamol cysteinate, mercapturate (5%) [49]91–99 [50]292,000 [50]
1000–10,000 [54]
1480 [50]
100,000 [52]
10,000 [48]
66 [50]
acetylsalicylic acidMetabolites: Salicylic acid (10%), salicyluric acid (75%), salicylic phenolic (10%) and acyl (5%) glucuronides, gentisic acid (o1%) [49]0 [50]1000–10,000 [54]1510 [50]<50 [50]
In the 1990s, screen printing technology for the preparation of electrochemical sensors was introduced. The screen-printed electrodes (SPEs) became objects of numerous research efforts aimed at investigating their practical application. The low manufacturing costs, appropriate repeatability levels, and electrochemical properties, all make them an attractive analytical tool [70,71,72,73,74,75,76,77].
The manufacture of screen-printed electrodes is the process of designing appropriate ink (print) composition and then pressing it through the appropriate template (screen) onto the carrier surface (most often ceramic or polymer). Both the ink composition and the area of the working electrode can be modified, e.g., with nanoparticles/metal films, polymer, or enzyme, depending on the application-specific requirements [70,71,72,73,74,75,76,77]. The entire electrode system (reference, counter, and working electrodes) is printed on the same substrate surface (Figure 1).
The key feature of the screen-printed electrodes, among other electrochemical sensors, is their miniaturization, enabling them to apply in portable/field devices. The application of the screen-printed electrodes in the carrying out measurements in situ enable minimalization or even elimination of errors, reduces the test time, and consequently, costs usually connected with sampling, transport, and storage of representative samples [78]. This justifies the thesis saying that there is a significant need to develop field devices for monitoring waters that will allow us to evaluate water quality at the sampling location in an easy and fast manner. Recent years saw the growing interest in the development of such devices. The use of portable devices is one of the development trends in environmental analytics [79].
A lot of papers describe the application of electrochemical sensors for the determination of residues of pharmaceuticals and screen-printed sensors [74,75,80]. Most electrochemical methods allow for the quantitative determination of these compounds in pharmaceutical preparations, biological samples, and beverages. However, the literature has available articles on the development of electrochemical sensors to determine pharmaceuticals, including painkillers in water samples. This article focuses on a summary of achievements in the field of screen-printed voltammetric sensors application in environmental water monitoring of painkillers.

2. Application of Screen-Printed Voltammetric Sensors for the Painkillers Determination in the Environmental Water Samples

Non-steroidal anti-inflammatory drugs (NSAIDs) are an important class of drugs because they are widely used to treat muscle pain and inflammatory rheumatic diseases, and this is an increasing trend. This fact, combined with improper disposal and ineffectiveness of wastewater treatment, leads to the ubiquitous presence of these drugs in the environment [81]. Diclofenac (DF), ibuprofen (IB), acetylsalicylic acid (AS), naproxen (NP) and ketoprofen (KP) belong to the NSAIDs (Figure 2A–E). Diclofenac exhibits activities characteristic of this group of drugs, i.e., anti-inflammatory, antipyretic, analgesic, and inhibiting platelet aggregation [82,83]. It is used to relieve symptoms of many illnesses, including non-articular rheumatism, osteoarthritis, sports injuries, and rheumatoid arthritis. In the proposed daily dose (50–150 mg), DF is completely tolerated [84]. Although no problems are caused when an appropriate amount of DF is used, its excessive or continuous use may cause symptoms such as epigastric discomfort, gastric ulcer, hematuria; meantime, the accumulated mass of toxic substances can cause kidney and liver dysfunctions [85]. Furthermore, the ubiquity of DF in the environment impairs fish health and water quality due to its poor degradation [86]. Ibuprofen ( (2–4 isobutyphenyl) propionic acid is commonly prescribed to treat chronic and acute pain and many rheumatic and musculoskeletal disorders. IB is also used to reduce fever [87]. Its action is due to the inhibition of cyclo-oxygenases, which are involved in the synthesis of prostaglandins involved in producing pain, inflammation, and fever [88]. Acetylsalicylic acid (aspirin) is an anti-inflammatory, antipyretic, and analgesic drug. Thanks to its effectiveness, it has a place in treating antithrombotic coronary heart disease, prevention of colon cancer, fever, headaches, and Alzheimer’s disease [89,90]. Naproxen (2-(6-methoxy-2-naphthyl)propionic acid) is an antipyretic and anti-inflammatory compound applied in the treatment of nonrheumatic inflammation, migraine, and gout [91]. Association therapy with paracetamol and naproxen has also been reported to benefit patients with pain related to rheumatoid arthritis. The naproxen drug should be given with precaution to elderly patients and patients with hemophilia, gastrointestinal bleeding, and platelet coagulation dysfunction. [92]. Ketoprofen is an arylpropionic acid derivative with anti-inflammatory, antipyretic, and analgesic properties [93]. It relieves pain associated with rheumatic and nonrheumatic inflammatory disorders, vascular headaches, and dysmenorrhea [94]. It is well absorbed after oral and rectal administration, and it can be administered by injection and transdermally. KP is metabolized in the liver and mainly excreted in urine [93].
Paracetamol (N-acetyl-p-aminophenol, Figure 2F), also known as acetaminophen or Tylenol, is extensively used to relieve moderate pain and reduce fever globally [95]. It has no anti-inflammatory effect. PA is the main ingredient in many cold and flu medications [82]. The antipyretic effect of this drug is related to the inhibition of prostaglandin synthesis in the central nervous system [83]. An overdose of PA may result in the accumulation of toxic metabolites that can cause acute and sometimes fatal nephro- and hepatotoxicity [82]. As a widely used pharmaceutical, PA is present in the environment, its concentration found in environmental water samples ranges from 1 to 10 nM.
Tramadol, (1R,2R)-2-[(dimethylamino)methyl]-1-(3-methoxyphenyl)cyclohexanol, TR, Figure 2G, is an l-opioid recipient agonist that acts on analgesic centrally is applied initially for treating modest to severe pain [96]. TR is a commonly misused drug that can lead to addiction or even death, although it has a preferable safety profile than other opioid analgesic drugs such as morphine or hydrocodone [97]. The typical dosage requirement for oral consumption of TR ranges between 50 and 100 mg per 4 to 6 h. The maximal dose of the drug will be 400 mg every day. Overdosing of TR can cause nausea, respiratory depression, vomiting, coma, dizziness, and tachycardia.
In the literature are few articles describing the use of screen-printed sensors in the monitoring of painkillers residues (DF, PA, IB, and TR) in environmental waters samples [82,83,98,99,100,101,102,103,104]. These sensors have also found application in the determination of painkillers in pharmaceutical preparations and biological samples, e.g., urine and serum [84,85,86,87,96,97,105,106,107,108,109,110,111,112,113]. There are no studies on voltammetric procedures to determine acetylsalicylic acid and naproxen in water samples in the literature. However, there are single procedures for determining AS [89,90,114] and NP [92,115] on screen-printed electrodes in pharmaceuticals and/or human physiological fluids. There are no attempts to use screen-printed sensors to analyze ketoprofen in any type of sample.

2.1. SPEs Modified with Carbon Nanomaterials

Carbon nanomaterials are very attractive for the mass production of SPEs and represent a significant opportunity to increase the analytical sensitivity of these devices, enabling new sensing applications [116,117]. These materials are characterized by excellent electrical conductivity, low electrical resistance, large surface area, and good physical and chemical stability [118]. In addition, the possibility of functionalization of their surface leads to an increase in analytical efficiency, including sensitivity and selectivity [119]. Carbon nanomaterials used as SPEs modifiers include mainly carbon black (CB), graphene-related materials, carbon nanofibers (CNFs), various forms of carbon nanotubes—single-, double-, and multiwalled (SWCNTs, DWCNTs, and MWCNTs), carbon nanohorns (CNHs), as well as carbon nano-onions (CNOs) [117,120,121,122,123].
In the literature, few articles describe the use of screen-printed sensors modified with carbon materials to monitor painkillers residues in environmental water samples [83,98,99,101,102]. The comparison of these assay procedures is presented in Table 2. The lowest detection limit of paracetamol for the accumulation time of 90 s (LOD, 0.54 nM) was obtained using a screen-printed carbon/carbon nanofibers sensor (SPCE/CNFs) [98]. Sasal et al. [98] described the application of a commercially available SPCE/CNFs sensor and differential pulse adsorptive stripping voltammetry (DPAdSV) for the direct determination of the low (real) concentration of PA in environmental water samples. This was done by monitoring the oxidation current of PA after adsorption of molecules onto the SPCE/CNFs surface at the potential of −0.95 V. According to the literature data, a PA oxidation mechanism at the SPCE/CNFs is associated with the formation of N-acetyl-p-quinoneimine (NAPQI) [99]. The adsorption of PA onto the electrode surface was confirmed by electrochemical impedance spectroscopy (EIS), cyclic voltammetry (CV), and theoretical studies. Moreover, the authors found that the SPCE/CNFs sensor presented better performance than the screen-printed sensors with carbon or carbon/multiwalled carbon nanotubes working electrodes. It was related to the developed active surface of the SPCE/CNFs, which mediates PA adsorption. Under optimized conditions, the DPAdSV measurements were performed in 0.1 M H2SO4 containing 0.01 µM EDTA to minimize the influence effect of interfering metal ions. The developed analytical procedure using SPCE/CNFs was applied to the direct determination of PA (in the range of 5–200 nM) in water samples collected from two Polish rivers and sea with the recovery values between 96.2 to 104.6%.
In [102], Sasal et al. proposed a DPAdSV voltammetric procedure at the commercially available screen-printed carbon sensor modified with carboxyl functionalized multiwalled carbon nanotubes (SPCE/MWCNTs-COOH) for the trace analysis of diclofenac (DF) (Figure 3). The authors stated that DF is irreversibly oxidized, and the oxidation process of DF is not purely diffusion-or adsorption-controlled at the SPCE/MWCNTs-COOH. Moreover, the number of electrons involved in the DF oxidation process equals 2. These results are consistent with the literature data, which proposed that DF is oxidized to 5-hydrohydiclofenac by losses of 2e and 2H+ [124,125]. The SPCE/MWCNTs-COOH provided a higher sensitivity and wider linear range than the SPCE (0.019 vs. 0.040 µA/nM and 0.5–200.0 vs. 1.0–200 nM, respectively). It is connected with the fact that the application of MWCNTs-COOH improved the electron transfer process and the active surface area of the electrode. The proposed DPAdSV procedure is characterized by simplicity, sensitivity, and time-saving. For the first time, the electrochemical sensor was applied to determine the real concentration of DF (0.42 ± 0.080 nmol L−1) in the river water samples without the sample pre-treatment step.
In voltammetric measurements, even a low concentration of surface-active substances can block the active surface of the electrode. Therefore, UV irradiation or microwave heating of the samples are suggested for the elimination of this type of interference. There are also other simple ways to minimize interferences from the organic matrix of samples, e.g., the application of potential pulses for accumulation. In that approach, the potential of cathode pulses was chosen in a way that made it represent the maximum adsorption of the determined element and the potential of anode pulses to desorb the interfering surfactants [126]. This method of eliminating interference from surfactants was described by Sasal et al. in [83]. The authors proposed using the DPAdSV technique, a commercially available SPCE/MWCNTs-COOH sensor, and pulsed potential accumulation for individual and simultaneous determination of paracetamol and diclofenac. The scheme of the individual steps of the optimized voltammetric procedure is presented in Figure 4. Moreover, the authors found that the application of carboxyl functionalized multiwalled carbon nanotubes and pulsed potential accumulation contributes to improving PA and DF peaks currents. The amplification of the PA and DF signals is related to a greater number of active centers at the SPCE/MWCNTs-COOH than at the SPCE. Based on the cyclic voltammetric examination, it was found that the PA and DF are irreversibly oxidized at the SPCE/MWCNTs-COOH, and these processes are not purely diffusion or adsorption controlled. The DPAdSV procedure with SPCE/MWCNTs-COOH shows the low LODs of 1.4 nM for PA and 0.03 nM for DF. The DPAdSV procedure at the SPCE/MWCNTs-COOH was successfully applied for the simultaneous analysis of PA and DF in spiked river water samples with recovery values between 96.5% and 104.8%. Moreover, the voltammetric procedure proposed by Sasal et al. allowed for the direct determination of PA (24.3 ± 0.5 nM) and DF (3.7 ± 0.7 nM) in the wastewater samples purified in a sewage treatment plant.
Serrano et al. [99] compared the analytical performances of the commercially available screen-printed carbon electrode (SPCE), multiwalled carbon nanotubes modified screen-printed carbon electrode (SPCNTE), screen-printed carbon electrode modified with carbon nanofibers (SPCNFE), and screen-printed graphene electrode (SPGPHE) for the individual and simultaneous determination of ibuprofen, paracetamol, and caffeine. The authors suggest that the SPCNFE was the most suitable carbon-based electrode for the voltammetric determination of the selected analytes in water at trace levels. Moreover, the applicability of SPCNFE for the analysis of environmental water samples was demonstrated by the simultaneous determination of PA, IB, and CF in spiked tap water samples. The good recoveries (103.1, 99.5, and 97.6% for PA, IB, and CF, respectively) and reproducibility (RSD of 8.93, 0.96, and 8.63% for PA, IB, and CF, respectively) were obtained. In hospital wastewater samples, only PA (7.74 µM) was determined. The IB and CF were not detected since the studied hospital wastewater sample did not contain IB, and the concentration of CF was below the LOD obtained for the SPCNFE.
In paper [101], Deroco et al. described the use of carbon black as a modifying nanomaterial of SPEs. The application of CB film onto the SPE surface contributed to the improvement of electrocatalytic activity for the [Fe(CN)6]3−/4− redox probe, and paracetamol and levofloxacin (LVF) signals. The authors stated that PA and LVF oxidation processes were fully controlled by diffusion, and these processes involved an equal number of electrons and protons. The developed sensor was successfully used to analyze PA (6.0, 10.0, and 70.0 µM) and LVF (2.0, 9.0, and 60.0 µM) in spiked river water samples with recovery values between 98.3 and 106.0%.
Table 2. Summary of voltammetric procedures to determine painkillers residues at the screen-printed electrodes modified with carbon materials in environmental water samples.
Table 2. Summary of voltammetric procedures to determine painkillers residues at the screen-printed electrodes modified with carbon materials in environmental water samples.
ElectrodeAnalyteMethodLinear Range [µM]LOD [µM]ApplicationRef.
SPCE/CNFsPADPAdSV0.002–0.05
0.1–2.0
0.00054river water,
sea water
[98]
SPCE/MWCNTs-COOHDFDPAdSV0.0001–0.010.000028river water[102]
SPCE/MWCNTs-COOHPA
DF
DPAdSV
(PPA)
0.005–5.0
0.0001–0.02
0.0014
0.000030
wastewater,
river water
[83]
SPCEPADPV13.20–377.07.17tap water,
hospital wastewater
[99]
SPCNTE2.64–33.700.66
SPCNFE1.98–33.700.66
SPGPHE3.31–23.200.66
SPCEIB18.40–489.605.33
SPCNTE9.21–155.102.91
SPCNFE19.40–114.405.82
SPGPHE30.50–86.309.21
SPCECF24.70–480.07.21
SPCNTE20.60–480.06.18
SPCNFE61.80–330.02.06
SPGPHE15.50–44.804.63
CB/SPCEPA
LVF
SWV0.80–30.0
0.90–70.0
2.60
0.42
river water[101]
PA–paracetamol; DF–diclofenac; IB–ibuprofen; CF–caffeine; LVF–levofloxacin; DPAdSV–differential-pulse adsorptive stripping voltammetry; PPA–pulsed potential accumulation; DPV–differential-pulse voltammetry; SWV–square-wave voltammetry; SPCE–screen-printed carbon electrode; SPCE/MWCNTs-COOH–carboxyl functionalized multiwalled carbon nanotubes modified screen-printed carbon electrode; SPCNTE–screen-printed carbon electrode modified with carbon nanotubes; SPCE/CNFs (SPCNFE)–screen-printed carbon electrode modified with carbon nanofibers; SPGPHE–screen-printed graphene electrode; CB/SPCE–screen-printed carbon electrode modified with carbon black.

2.2. SPEs Electrochemically Pretreated

SPEs consist of working electrodes made of conductive inks based on platinum, gold, silver, or carbon, the latter being the most used material because it is universal and cheap. Conductive inks from screen-printed carbon electrodes (SPCEs) contain carbon with organic solvents, binding pastes (e.g., polyester resin, ethylcellulose, or epoxy-based polymeric binder), and some additives that provide functional properties. The presence of these additional non-conductive materials can lead to a slowdown in the kinetics of heterogeneous electrochemical reactions. Therefore, much attention has been paid to developing surface treatment methods to improve the electrochemical properties of the SPCEs. The main purpose of the SPCEs pre-treatment was to remove organic ink components or contaminants and increase surface roughness or functionality [127,128,129]. Several methods of pre-treatment of SPEs can be found in the literature, such as heat treatment [127], oxygen plasma treatment [128], chemical treatment [129], polishing [130,131], and electrochemical treatment [132,133,134]. Electrochemical treatments allow the in situ easy activation of SPCEs. They usually hold the electrode at a constant potential for a short time or potential cycling to extreme anodic and/or cathodic potentials [127,135]. Table 3 shows summary of voltammetric procedures for painkillers residues determination at the electrochemically pretreated screen-printed electrodes electrochemically.
In paper [82], Kozak et al. proposed an electrochemically activated (25 voltammetric cycles from 1.0 to −0.7 V at a scan rate of 10 mV s−1 in a solution containing 0.1 M acetate buffer of pH = 4.0 ± 0.1 and 10 mM H2O2) screen-printed carbon electrode modified with sodium dodecyl sulfate (aSPCE/SDS) for the simultaneous determination of paracetamol, diclofenac, and tramadol. At the moment, there is the first paper describing the voltammetric procedure of tramadol determination with the use of screen-printed electrodes in environmental water samples [82]. The electrochemical activation contributes to the removal of the organic ink constituents or contaminants introduced into the printing stage, which consequently changes the morphology of the electrode surface and reduces the charge transfer resistance. Furthermore, the modification of the electrode surface with SDS contributes to the TR signal amplification and minimizes the influence of surfactants (Triton X-100 and CTAB). The author proved the adsorption of PA and DF onto the SPCE/SDS surface by analyzing differential capacity curves and stated that TR existing in the cationic form reaches the electrode surface by diffusion and is electrostatically attractive for the surface covered by SDS anions. The aSPCE/SDS showed a good linear response in the concentration ranges of 0.05–2.0 µM for PA, 0.001–0.2 µM for DF, and 0.01–0.2 and 0.2–2.0 µM for TR. The limits of detection obtained during the simultaneous determination of PA, DF, and TR are 0.015 µM, 0.00021 µM, and 0.0017 µM, respectively. The DPAdSV procedure with the aSPCE/SDS was successfully applied for the determination of PA, DF, and TR in river water and serum samples (the recovery values between 97.0 and 102.0%) as well as pharmaceuticals (the relative errors between determined and label values are in the ranges of 0 and 2.1%).
In paper [100], Raymounds-Pereira et al. proposed electrochemically pretreated (2 voltammetric cycles from −2.5 to 2.5 V at a scan rate of 100 mV s−1 in 0.5 M sulfuric acid solution) screen-printed carbon electrode (SPCE) for the determination of hydroquinone (HQ), paracetamol and estradiol (E2) in tap water. The authors concluded that pre-treatment did not affect the morphology of the electrode surface and did not introduce functional groups to the surface but removed non-conducting residues from the printing ink. This consequently contributed to the improvement of the sensor’s conductivity (the charge-transfer resistance decreased from 30 to 5 kΩ due to the pre-treatment) and sensitivity of the voltammetric procedure. The ability to determine PA, HQ, and E2 was verified by taking voltammetric measurements with tap water samples spiked with analytes in the concentration range of 1–7 µM). The results were compared to those obtained by high-performance liquid chromatography (HPLC). Using the Student’s test the author found that the voltammetric procedures yielded the same results as the standard method HPLC.
Amin et al. [104] show the application of electrochemically pretreated screen-printed graphite electrode (SPGE) to the electrochemical oxidation and detection of ibuprofen (IB). An SPGE surface was pretreated (conditioned) by applying a fixed potential of 1.6 V for 3 min vs. Ag pseudo reference electrode. Using pretreated SPGE, detection limits were improved 12.5 times to instrumental detection limits, thereby, LOD of 6.30 µM was achieved.

2.3. SPEs Modified with Polymers

Polymers are widely used modifiers for electrodes and SPEs. The most frequently used polymers for this purpose are conductive polymers that combine conventional properties of polymers with the electronic properties of metals and/or semiconductors. Mainly polyacetylene, polyaniline, polypyrrole, or polythiophene are used here [136,137]. In addition, it was found that the use of a conductive polymer to modify the electrode surface increases the electrical conductivity, high chemical stability, good magnetic properties, high electron affinity, optical properties, and low ionization potential [138]. Another group of polymers that can be used to modify the surface of the electrodes are ion-exchange polymers, one example of which is the well-known Nafion–perfluorinated sulfonated cation-exchanger [138]. Today, molecularly imprinted polymers (MIPs) in combination with electrochemical sensors are of great interest. MIP modified electrodes have proven the usefulness of both small and large biomolecules, such as proteins or DNA [139,140]. MIPs are typically prepared by forming a three-dimensional polymer network around a molecular template via a cross-linking step. Removal of this matrix creates binding cavities that retain the shape, size, and orientation of the target molecule, leading to a high selectivity in the recognition process [141,142]. MIPs offer some clear advantages, including very good stability with a high surface area over a wide range of experimental conditions and solvents, becoming powerful alternatives to biorecognition elements such as antibodies. Because of their high selectivity, simple synthesis methods, high stability, low cost, and good engineering capability, MIPs receive great attention as recognition elements in various fields, especially in electrochemical sensing [143,144]. The polymer layer on the surface of the electrodes can be applied in several ways. Most often it is done by dropping a polymer solution [145] or electropolymerization [137,146,147]. Other methods described in the literature are dispensing, inkjet printing, screen-printing, electrodeposition, electrospray, or pen-writing [138].
Seguro et al. [103] proposed a disposable voltammetric molecularly imprinted polymer screen-printed carbon sensor (MIP/SPCE) for the selective determination of diclofenac (Table 3). MIP preparation was achieved by cyclic voltammetry, using dopamine as a monomer in the presence of DF. The MIP/SPCE showed adequate selectivity (in comparison with other drug molecules), intra-day repeatability of 7.5%, inter-day repeatability of 11.5%, a linear range between 0.1 and 10 µM, and a limit of detection and quantification of 70 and 200 nM, respectively. Its applicability was demonstrated by the determination of DF in spiked water samples (river and tap water).

3. Conclusions

Monitoring the water environment for the presence and content of residues of pharmaceuticals, including painkillers a significant issue for contemporary analytical chemistry. This review demonstrates the applications of screen-printed sensors for the sensitive determination of environmental water pollutants (painkillers). Several examples described in this review paper show that the developed simple, sensitive, and selective voltammetric procedures with screen-printed sensors can be good tools for this purpose. The screen-printed electrodes modified with carbon nanomaterials, polymer film, or electrochemically activated showed advantageous electroconductivity, catalytic activity, and surface area. Moreover, the screen-printed sensors are potentially applicable not only in laboratory measurements but also in-field analysis. Due to their electrochemical properties, simplicity, disposability, short response time, and miniaturization, screen-printed sensors can find application in environmental water monitoring.
The screen-printed sensors area is expected to grow with new application domains. Future work will focus on improving the analytical parameters of screen-printed sensors to adjust them to the relative concentrations of the analytes in the environmental water samples, and on developing procedures and sensors for new substances AS, NP, KP) with analgesic properties. More attention should be given to expected interfering species and proven or possible strategies for mitigating their effects and improving selectivity. Moreover, sensor miniaturization, shortening the analysis time, reducing the volume of analyzed samples, and using reagents should be the aim of subsequent studies.

Author Contributions

Conceptualization, K.T.-R. and J.K.; investigation, K.T.-R., J.K. and B.C.; writing—original draft preparation, K.T.-R., J.K. and B.C.; writing—review and editing, K.T.-R., J.K. and B.C.; supervision, K.T.-R. All authors have read and agreed to the published version of the manuscript.

Funding

This research received no external funding.

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Data Availability Statement

The data presented in this study are available on request from the corresponding author.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. de Jesus Gaffney, V.; Mota-Filipe, H.; Pinto, R.A.; Thiemermann, C.; Loureiro, M.; Cardoso, V.V.; Benoliel, M.J.; Almeida, C.M. Chemical and biochemical characterization and in vivo safety evaluation of pharmaceuticals in drinking water. Environ. Toxicol. Chem. 2016, 35, 2674–2682. [Google Scholar] [CrossRef] [PubMed]
  2. Farré, M.I.; Pérez, S.; Kantiani, L.; Barceló, D. Fate and toxicity of emerging pollutants, their metabolites and transformation products in the aquatic environment. Trend. Anal. Chem. 2008, 27, 991–1007. [Google Scholar] [CrossRef]
  3. Szymonik, A.; Lach, J.; Malińska, K. Fate and removal of pharmaceuticals and illegal drugs present in drinking water and wastewater. Ecol. Chem. Eng. S 2017, 24, 65–85. [Google Scholar] [CrossRef] [Green Version]
  4. Khan, A.H.; Khan, N.A.; Ahmed, S.; Dhingra, A.; Singh, C.P.; Khan, S.U.; Mohammadi, A.A.; Changani, F.; Yousefi, M.; Alam, S.; et al. Application of Advanced Oxidation Processes Followed by Different Treatment Technologies for Hospital Wastewater Treatment. J. Clean Prod. 2020, 269, 122411. [Google Scholar] [CrossRef]
  5. Kosma, C.I.; Lambropoulou, D.A.; Albanis, T.A. Occurrence and Removal of PPCPs in Municipal and Hospital Wastewaters in Greece. J. Hazard. Mater. 2010, 179, 804–817. [Google Scholar] [CrossRef]
  6. Angeles, L.F.; Mullen, R.A.; Huang, I.J.; Wilson, C.; Khunjar, W.; Sirotkin, H.I.; McElroy, A.E.; Aga, D.S. Assessing Pharmaceutical Removal and Reduction in Toxicity Provided by Advanced Wastewater Treatment Systems. Environ. Sci. Water Res. Technol. 2020, 6, 62–77. [Google Scholar] [CrossRef]
  7. Brillas, E. A Critical Review on Ibuprofen Removal from Synthetic Waters, Natural Waters, and Real Wastewaters by Advanced Oxidation Processes. Chemosphere 2022, 286, 131849. [Google Scholar] [CrossRef]
  8. Larsson, D.G.J.; de Pedro, C.; Paxeus, N. Effluent from Drug Manufactures Contains Extremely High Levels of Pharmaceuticals. J. Hazard. Mater. 2007, 148, 751–755. [Google Scholar] [CrossRef]
  9. Boroń, M.; Pawlas, K. Pharmaceuticals in aquatic environment–literature review. Probl. Hig. Epidemiol. 2015, 96, 357. [Google Scholar]
  10. de Morais, J.L.; Zamora, P.P. Use of Advanced Oxidation Processes to Improve the Biodegradability of Mature Landfill Leachates. J. Hazard. Mater. 2005, 123, 181–186. [Google Scholar] [CrossRef]
  11. Burns, E.E.; Carter, L.J.; Snape, J.; Thomas-Oates, J.; Boxall, A.B.A. Application of Prioritization Approaches to Optimize Environmental Monitoring and Testing of Pharmaceuticals. J. Toxicol. Environ. Health B 2018, 21, 115–141. [Google Scholar] [CrossRef]
  12. Carballa, M.; Omil, F.; Ternes, T.; Lema, J.M. Fate of Pharmaceutical and Personal Care Products (PPCPs) during Anaerobic Digestion of Sewage Sludge. Water Res. 2007, 41, 2139–2150. [Google Scholar] [CrossRef] [PubMed]
  13. Evgenidou, E.N.; Konstantinou, I.K.; Lambropoulou, D.A. Occurrence and Removal of Transformation Products of PPCPs and Illicit Drugs in Wastewaters: A Review. Sci. Total Environ. 2015, 505, 905–926. [Google Scholar] [CrossRef] [PubMed]
  14. Hu, X.; Xie, H.; Zhuang, L.; Zhang, J.; Hu, Z.; Liang, S.; Feng, K. A Review on the Role of Plant in Pharmaceuticals and Personal Care Products (PPCPs) Removal in Constructed Wetlands. Sci. Total Environ. 2021, 780, 146637. [Google Scholar] [CrossRef] [PubMed]
  15. Fan, X.; Gao, J.; Li, W.; Huang, J.; Yu, G. Determination of 27 Pharmaceuticals and Personal Care Products (PPCPs) in Water: The Benefit of Isotope Dilution. Front. Environ. Sci. Eng. 2020, 14, 8. [Google Scholar] [CrossRef]
  16. OECD. Pharmaceutical Residues in Freshwater: Hazards and Policy Responses. In OECD Studies on Water; OECD: Paris, France, 2019; ISBN 978-92-64-77633-3. [Google Scholar]
  17. Pompei, C.M.E.; Campos, L.C.; da Silva, B.F.; Fogo, J.C.; Vieira, E.M. Occurrence of PPCPs in a Brazilian Water Reservoir and Their Removal Efficiency by Ecological Filtration. Chemosphere 2019, 226, 210–219. [Google Scholar] [CrossRef]
  18. Adeola, A.O.; de Lange, J.; Forbes, P.B.C. Adsorption of Antiretroviral Drugs, Efavirenz and Nevirapine from Aqueous Solution by Graphene Wool: Kinetic, Equilibrium, Thermodynamic and Computational Studies. Appl. Surf. Sci. Adv. 2021, 6, 100157. [Google Scholar] [CrossRef]
  19. Babas, H.; Kaichouh, G.; Khachani, M.; Karbane, M.E.; Chakir, A.; Guenbour, A.; Bellaouchou, A.; Warad, I.; Zarrouk, A. Equilibrium and Kinetic Studies for Removal of Antiviral Sofosbuvir from Aqueous Solution by Adsorption on Expanded Perlite: Experimental, Modelling and Optimization. Surf. Interfaces 2021, 23, 100962. [Google Scholar] [CrossRef]
  20. Bhadra, B.N.; Jhung, S.H. Adsorptive Removal of Wide Range of Pharmaceuticals and Personal Care Products from Water Using Bio-MOF-1 Derived Porous Carbon. Micropor. Mesopor. Mater. 2018, 270, 102–108. [Google Scholar] [CrossRef]
  21. Karunanayake, A.G.; Todd, O.A.; Crowley, M.L.; Ricchetti, L.B.; Pittman, C.U.; Anderson, R.; Mlsna, T.E. Rapid Removal of Salicylic Acid, 4-Nitroaniline, Benzoic Acid and Phthalic Acid from Wastewater Using Magnetized Fast Pyrolysis Biochar from Waste Douglas Fir. Chem. Eng. Sci. 2017, 319, 75–88. [Google Scholar] [CrossRef]
  22. Jafarinejad, S. Cost-Effective Catalytic Materials for AOP Treatment Units. In Applications of Advanced Oxidation Processes (AOPs) in Drinking Water Treatment; Gil, A., Galeano, L.A., Vicente, M.Á., Eds.; Springer International Publishing: Cham, Switzerland, 2017; Volume 67, pp. 309–343. ISBN 978-3-319-76881-6. [Google Scholar]
  23. Michael, I.; Frontistis, Z.; Fatta-Kassinos, D. Removal of Pharmaceuticals from Environmentally Relevant Matrices by Advanced Oxidation Processes (AOPs). In Comprehensive Analytical Chemistry; Elsevier: Amsterdam, The Netherlands, 2013; Volume 62, pp. 345–407. ISBN 978-0-444-62657-8. [Google Scholar]
  24. Nie, C.; Shao, N.; Wang, B.; Yuan, D.; Sui, X.; Wu, H. Fully Solar-Driven Thermo- and Electrochemistry for Advanced Oxidation Processes (STEP-AOPs) of 2-Nitrophenol Wastewater. Chemosphere 2016, 154, 604–612. [Google Scholar] [CrossRef] [PubMed]
  25. Krishnan, R.Y.; Manikandan, S.; Subbaiya, R.; Biruntha, M.; Govarthanan, M.; Karmegam, N. Removal of Emerging Micropollutants Originating from Pharmaceuticals and Personal Care Products (PPCPs) in Water and Wastewater by Advanced Oxidation Processes: A Review. Environ. Technol. Innov. 2021, 23, 101757. [Google Scholar] [CrossRef]
  26. Chevremont, A.-C.; Boudenne, J.-L.; Coulomb, B.; Farnet, A.-M. Fate of Carbamazepine and Anthracene in Soils Watered with UV-LED Treated Wastewaters. Water Res. 2013, 47, 6574–6584. [Google Scholar] [CrossRef] [PubMed]
  27. Pai, C.-W.; Wang, G.-S. Treatment of PPCPs and Disinfection By-Product Formation in Drinking Water through Advanced Oxidation Processes: Comparison of UV, UV/Chlorine, and UV/H2O2. Chemosphere 2022, 287, 132171. [Google Scholar] [CrossRef]
  28. Ahmad, N.A.; Yuzir, M.A.; Yong, E.L.; Abdullah, N.; Salim, M.R. Removal of Bisphenol A (BPA) in Surface Water by Ozone Oxidation Process. Appl. Mech. Mater. 2015, 735, 210–214. [Google Scholar] [CrossRef]
  29. Beltrán, F.J.; Pocostales, P.; Alvarez, P.; Oropesa, A. Diclofenac Removal from Water with Ozone and Activated Carbon. J. Hazard. Mater. 2009, 163, 768–776. [Google Scholar] [CrossRef]
  30. Hamdi El Najjar, N.; Touffet, A.; Deborde, M.; Journel, R.; Karpel Vel Leitner, N. Kinetics of Paracetamol Oxidation by Ozone and Hydroxyl Radicals, Formation of Transformation Products and Toxicity. Sep. Purif. Technol. 2014, 136, 137–143. [Google Scholar] [CrossRef]
  31. Lee, C.O.; Howe, K.J.; Thomson, B.M. Ozone and Biofiltration as an Alternative to Reverse Osmosis for Removing PPCPs and Micropollutants from Treated Wastewater. Water Res. 2012, 46, 1005–1014. [Google Scholar] [CrossRef]
  32. Andreozzi, R.; Caprio, V.; Marotta, R.; Vogna, D. Paracetamol Oxidation from Aqueous Solutions by Means of Ozonation and H2O2/UV System. Water Res. 2003, 37, 993–1004. [Google Scholar] [CrossRef]
  33. Sharma, J.; Mishra, I.M.; Kumar, V. Mechanistic Study of Photo-Oxidation of Bisphenol-A (BPA) with Hydrogen Peroxide (H2O2) and Sodium Persulfate (SPS). J. Environ. Manag. 2016, 166, 12–22. [Google Scholar] [CrossRef]
  34. Abramović, B.; Kler, S.; Šojić, D.; Laušević, M.; Radović, T.; Vione, D. Photocatalytic Degradation of Metoprolol Tartrate in Suspensions of Two TiO2-Based Photocatalysts with Different Surface Area. Identification of Intermediates and Proposal of Degradation Pathways. J. Hazard. Mater. 2011, 198, 123–132. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  35. Bahnemann, D. Photocatalytic Water Treatment: Solar Energy Applications. J. Sol. Energy 2004, 77, 445–459. [Google Scholar] [CrossRef]
  36. Guo, W.; Zhao, S.; Li, G.; Li, J.; Chen, F.; Chen, R. Chlorine-Enhanced Photocatalytic Degradation of PPCPs over Bi2MoO6/(BiO)2CO3 Heterostructures. J. Environ. Chem. Eng. 2021, 9, 106597. [Google Scholar] [CrossRef]
  37. Kumar, R.; Akbarinejad, A.; Jasemizad, T.; Fucina, R.; Travas-Sejdic, J.; Padhye, L.P. The Removal of Metformin and Other Selected PPCPs from Water by Poly(3,4-Ethylenedioxythiophene) Photocatalyst. Sci. Total Environ. 2021, 751, 142302. [Google Scholar] [CrossRef] [PubMed]
  38. Yang, H.; Wang, W.; Wu, X.; Siddique, M.S.; Su, Z.; Liu, M.; Yu, W. Reducing ROS Generation and Accelerating the Photocatalytic Degradation Rate of PPCPs at Neutral PH by Doping Fe-N-C to g-C3N4. Appl. Catal B Environ. 2022, 301, 120790. [Google Scholar] [CrossRef]
  39. Zhang, Q.; Chen, P.; Tan, C.; Chen, T.; Zhuo, M.; Xie, Z.; Wang, F.; Liu, H.; Cai, Z.; Liu, G.; et al. A Photocatalytic Degradation Strategy of PPCPs by a Heptazine-Based CN Organic Polymer (OCN) under Visible Light. Environ. Sci. Nano 2018, 5, 2325–2336. [Google Scholar] [CrossRef]
  40. Asif, A.H.; Wang, S.; Sun, H. Hematite-Based Nanomaterials for Photocatalytic Degradation of Pharmaceuticals and Personal Care Products (PPCPs): A Short Review. Curr. Opin. Green Sustain. Chem. 2021, 28, 100447. [Google Scholar] [CrossRef]
  41. Qian, H.; Yu, G.; Hou, Q.; Nie, Y.; Bai, C.; Bai, X.; Wang, H.; Ju, M. Ingenious Control of Adsorbed Oxygen Species to Construct Dual Reaction Centers ZnO@FePc Photo-Fenton Catalyst with High-Speed Electron Transmission Channel for PPCPs Degradation. Appl. Catal B Environ. 2021, 291, 120064. [Google Scholar] [CrossRef]
  42. Wu, J.; Wang, B.; Cagnetta, G.; Huang, J.; Wang, Y.; Deng, S.; Yu, G. Nanoscale Zero Valent Iron-Activated Persulfate Coupled with Fenton Oxidation Process for Typical Pharmaceuticals and Personal Care Products Degradation. Sep. Purif. Technol. 2020, 239, 116534. [Google Scholar] [CrossRef]
  43. Savun-Hekimoğlu, B.; Ince, N.H. Decomposition of PPCPs by Ultrasound-Assisted Advanced Fenton Reaction: A Case Study with Salicylic Acid. Ultrason. Sonochem. 2017, 39, 243–249. [Google Scholar] [CrossRef]
  44. Guo, M.; Feng, Y.; Li, X.; Yan, G.; Wang, X.; Li, X.; Zhang, S.; Yu, Y. Enhanced Degradation of Pharmaceuticals and Personal Care Products (PPCPs) by Three-Dimensional Electrocatalysis Coupled Biological Aerated Filter. J. Environ. Chem. Eng. 2021, 9, 106035. [Google Scholar] [CrossRef]
  45. Wang, W.; Lu, Y.; Luo, H.; Liu, G.; Zhang, R.; Jin, S. A Microbial Electro-Fenton Cell for Removing Carbamazepine in Wastewater with Electricity Output. Water Res. 2018, 139, 58–65. [Google Scholar] [CrossRef] [PubMed]
  46. Yang, H.; Zhou, M.; Yang, W.; Ren, G.; Ma, L. Rolling-Made Gas Diffusion Electrode with Carbon Nanotube for Electro-Fenton Degradation of Acetylsalicylic Acid. Chemosphere 2018, 206, 439–446. [Google Scholar] [CrossRef] [PubMed]
  47. Rashid, S.S.; Liu, Y.-Q. Comparison of Life Cycle Toxicity Assessment Methods for Municipal Wastewater Treatment with the Inclusion of Direct Emissions of Metals, PPCPs and EDCs. Sci. Total Environ. 2021, 756, 143849. [Google Scholar] [CrossRef]
  48. Boxall, A.B.A. The Environmental Side Effects of Medication: How Are Human and Veterinary Medicines in Soils and Water Bodies Affecting Human and Environmental Health? EMBO Rep. 2004, 5, 1110–1116. [Google Scholar] [CrossRef] [Green Version]
  49. Kasprzyk-Hordern, B.; Dinsdale, R.M.; Guwy, A.J. The Occurrence of Pharmaceuticals, Personal Care Products, Endocrine Disruptors and Illicit Drugs in Surface Water in South Wales, UK. Water Res. 2008, 42, 3498–3518. [Google Scholar] [CrossRef]
  50. Ziylan, A.; Ince, N.H. The Occurrence and Fate of Anti-Inflammatory and Analgesic Pharmaceuticals in Sewage and Fresh Water: Treatability by Conventional and Non-Conventional Processes. J. Hazard. Mater. 2011, 187, 24–36. [Google Scholar] [CrossRef]
  51. Stülten, D.; Zühlke, S.; Lamshöft, M.; Spiteller, M. Occurrence of Diclofenac and Selected Metabolites in Sewage Effluents. Sci. Total Environ. 2008, 405, 310–316. [Google Scholar] [CrossRef]
  52. Wu, D.; Sui, Q.; Yu, X.; Zhao, W.; Li, Q.; Fatta-Kassinos, D.; Lyu, S. Identification of Indicator PPCPs in Landfill Leachates and Livestock Wastewaters Using Multi-Residue Analysis of 70 PPCPs: Analytical Method Development and Application in Yangtze River Delta, China. Sci. Total Environ. 2021, 753, 141653. [Google Scholar] [CrossRef]
  53. Al-Baldawi, I.A.; Mohammed, A.A.; Mutar, Z.H.; Abdullah, S.R.S.; Jasim, S.S.; Almansoory, A.F.; Ismail, N. ’Izzati Application of Phytotechnology in Alleviating Pharmaceuticals and Personal Care Products (PPCPs) in Wastewater: Source, Impacts, Treatment, Mechanisms, Fate, and SWOT Analysis. J. Clean. Prod. 2021, 319, 128584. [Google Scholar] [CrossRef]
  54. Bayati, M.; Ho, T.L.; Vu, D.C.; Wang, F.; Rogers, E.; Cuvellier, C.; Huebotter, S.; Inniss, E.C.; Udawatta, R.; Jose, S.; et al. Assessing the Efficiency of Constructed Wetlands in Removing PPCPs from Treated Wastewater and Mitigating the Ecotoxicological Impacts. Int. J. Hyg. Environ. Health 2021, 231, 113664. [Google Scholar] [CrossRef] [PubMed]
  55. Liu, F.; Zhao, J.; Wang, S.; Du, P.; Xing, B. Effects of Solution Chemistry on Adsorption of Selected Pharmaceuticals and Personal Care Products (PPCPs) by Graphenes and Carbon Nanotubes. Environ. Sci. Technol. 2014, 48, 13197–13206. [Google Scholar] [CrossRef] [PubMed]
  56. Stepanova, S.; Praskova, E.; Chromcova, L.; Plhalova, L.; Prokes, M.; Blahova, J.; Svobodova, Z. The Effects of Diclofenac on Early Life Stages of Common Carp (Cyprinus Carpio). Environ. Toxicol. Pharmacol. 2013, 35, 454–460. [Google Scholar] [CrossRef] [PubMed]
  57. Webb, S.; Ternes, T.; Gibert, M.; Olejniczak, K. Indirect human exposure to pharmaceuticals via drinking water. Toxicol. Lett. 2003, 142, 157–167. [Google Scholar] [CrossRef]
  58. Maggioni, S.; Balaguer, P.; Chiozzotto, C.; Benfenati, E. Screening of endocrine-disrupting phenols, herbicides, steroid estrogens, and estrogenicity in drinking water from the waterworks of 35 Italian cities and from PET-bottled mineral water. Environ. Sci. Pollut. Res. 2013, 20, 1649–1660. [Google Scholar] [CrossRef] [PubMed]
  59. Brody, J.G.; Aschengrau, A.; McKelvey, W.; Swartz, C.H.; Kennedy, T.; Ruthann, A.R. Breast cancer risk and drinking water contaminated by wastewater: A case control study. Environ. Health 2006, 5, 28. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  60. Aschengrau, A.; Weinberg, J.M.; Janulewicz, P.A.; Romano, M.E.; Gallagher, L.G.; Winter, M.R.; Martin, B.R.; Vieira, V.M.; Webster, T.F.; White, R.F.; et al. Affinity for risky behaviors following prenatal and early childhood exposure to tetrachloroethylene (PCE)-contaminated drinking water: A retrospective cohort study. Environ. Health 2011, 10, 102. [Google Scholar] [CrossRef] [Green Version]
  61. Zwiener, C. Occurrence and analysis of pharmaceuticals and their transformation products in drinking water treatment. Anal. Bioanal. Chem. 2007, 387, 1159–1162. [Google Scholar] [CrossRef]
  62. Hena, S.; Gutierrez, L.; Croué, J.-P. Removal of Pharmaceutical and Personal Care Products (PPCPs) from Wastewater Using Microalgae: A Review. J. Hazard. Mater. 2021, 403, 124041. [Google Scholar] [CrossRef]
  63. Sengar, A.; Vijayanandan, A. Human health and ecological risk assessment of 98 pharmaceuticals and personal care products (ppcps) detected in indian surface and wastewaters. Sci. Total Environ. 2022, 807, 150677. [Google Scholar] [CrossRef]
  64. Kasprzyk-Hordern, B.; Dąbrowska, A.; Vieno, N.; Kronberg, L.; Nawrocki, J. Occurrence of acidic pharmaceuticals in the Warta River in Poland. Chem. Anal. 2007, 52, 289–303. [Google Scholar]
  65. Caban, M.; Lis, E.; Kumirska, J.; Stepnowski, P. Determination of pharmaceutical residues in drinking water in Poland using a new SPE-GC-MS(SIM) method based on Speedisk extraction disks and DIMETRIS derivatization. Sci. Total Environ. 2015, 538, 402–411. [Google Scholar] [CrossRef] [PubMed]
  66. Mirasole, C.; Di Carro, M.; Tanwar, S.; Magi, E. Liquid chromatography–tandem mass spectrometry and passive sampling: Powerful tools for the determination of emerging pollutants in water for human consumption. J. Mass Spectrom. 2016, 51, 814–820. [Google Scholar] [CrossRef] [PubMed]
  67. Ma, R.; Wang, B.; Lu, S.; Zhang, Y.; Yin, L.; Huang, J.; Deng, S.; Wang, Y.; Yu, G. Characterization of pharmaceutically active compounds in Dongting Lake, China: Occurrence, chiral profiling and environmental risk. Sci. Total Environ. 2016, 268, 557–558. [Google Scholar] [CrossRef]
  68. Paíga, P.; Santos, L.H.M.L.M.; Delerue-Matos, C. Development of a multi-residue method for the determination of human and veterinary pharmaceuticals and some of their metabolites in aqueous environmental matrices by SPE-UHPLC-MS/MS. J. Pharm. Biomed. 2017, 135, 75–86. [Google Scholar] [CrossRef] [Green Version]
  69. Wang, J. Stripping Analysis, Principles, Instrumentation and Applications; VCH Publishers: Hoboken, NJ, USA, 1985. [Google Scholar]
  70. Couto, R.A.S.; Lima, J.L.F.C.; Quinaz, M.B. Recent developments, characteristics and potential applications of screen-printed electrodes in pharmaceutical and biological analysis. Talanta 2016, 146, 801–814. [Google Scholar] [CrossRef]
  71. Barton, J.; García, M.B.; Santos, D.H.; Fanjul-Bolado, P.; Ribotti, A.; McCaul, M.; Diamond, D.; Magni, P. Screen-printed electrodes for environmental monitoring of heavy metal ions: A review. Microchim. Acta 2016, 183, 503–517. [Google Scholar] [CrossRef]
  72. Niu, X.; Lan, M.; Zhao, H.; Chen, C.; Li, Y.; Zhu, X. Review: Electrochemical Stripping Analysis of Trace Heavy Metals Using Screen-Printed Electrodes. Anal. Lett. 2013, 46, 2479–2502. [Google Scholar] [CrossRef]
  73. Trojanowicz, M. Impact of nanotechnology on design of advanced screen-printed electrodes for different analytical applications. Trends Anal. Chem. 2016, 84, 22–47. [Google Scholar] [CrossRef]
  74. Arduini, F.; Micheli, L.; Moscone, D.; Palleschi, G.; Piermarini, S.; Ricci, F.; Volpe, G. Electrochemical biosensors based on nanomodified screen-printed electrodes: Recent applications in clinical analysis. Trends Anal. Chem. 2016, 79, 114–126. [Google Scholar] [CrossRef] [Green Version]
  75. Hughes, G.; Westmacott, K.; Honeychurch, K.C.; Crew, A.; Pemberton, R.M.; Hart, J.P. Recent advances in the fabrication and application of screen-printed electrochemical (bio) sensors based on carbon materials for biomedical, agri-food and environmental analyses. Biosensors 2016, 6, 50. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  76. Cinti, S.; Arduini, F. Graphene-based screen-printed electrochemical (bio)sensors and their applications: Efforts and criticisms. Biosens. Bioelectron. 2017, 89, 107122. [Google Scholar] [CrossRef] [PubMed]
  77. Tyszczuk-Rotko, K.; Szwagierek, A. Green Electrochemical Sensor for Caffeine Determination in Environmental Water Samples: The Bismuth Film Screen-Printed Carbon Electrode. J. ElectroChem. Soc. 2017, 164, B342. [Google Scholar] [CrossRef]
  78. Hayat, A.; Marty, J.L. Disposable Screen Printed Electrochemical Sensors: Tools for Environmental Monitoring. Sensors 2014, 14, 10432–10453. [Google Scholar] [CrossRef] [Green Version]
  79. Namieśnik, J. Modern Trends in Monitoring and Analysis of Environmental Pollutants. Pol. J. Environ. Stud. 2001, 10, 127–140. [Google Scholar]
  80. Feier, B.; Florea, A.; Cristea, C.; Sandulescu, R. Electrochemical detection and removal of pharmaceuticals in waste waters. Curr. Opin. Electrochem. 2018, 11, 1–11. [Google Scholar] [CrossRef]
  81. Torrinha, Á.; Martins, M.; Tavares, M.; Delerue-Matos, C.; Morais, S. Carbon paper as a promising sensing material: Characterization and electroanalysis of ketoprofen in wastewater and fish. Talanta 2021, 226, 122111. [Google Scholar] [CrossRef]
  82. Kozak, J.; Tyszczuk-Rotko, K.; Wójciak, M.; Sowa, I. Electrochemically Activated Screen-Printed Carbon Sensor Modified with Anionic Surfactant (aSPCE/SDS) for Simultaneous Determination of Paracetamol, Diclofenac and Tramadol. Materials 2021, 14, 3581. [Google Scholar] [CrossRef]
  83. Sasal, A.; Tyszczuk-Rotko, K.; Wójciak, M.; Sowa, I.; Kuryło, M. Simultaneous analysis of paracetamol and diclofenac using MWCNTs-COOH modified screen-printed carbon electrode and pulsed potential accumulation. Materials 2020, 13, 3091. [Google Scholar] [CrossRef]
  84. Jahani, P.M.; Mohammadi, S.Z.; Khodabakhshzadeh, A.; Cha, J.W.; Asl, M.S.; Jang, H.W.; Shokouhimehr, M.; Zhang, K.; Van Le, Q.; Peng, W. Simultaneous voltammetric detection of morphine and diclofenac using graphene nanoribbon modified screen-printed electrode. Int. J. Electrochem. Sci. 2020, 15, 9037–9048. [Google Scholar] [CrossRef]
  85. Zhang, C.; Cao, Z.; Zhang, G.; Yan, Y.; Yang, X.; Chang, J.; Song, Y.; Jia, Y.; Pan, P.; Mi, W.; et al. An electrochemical sensor based on plasma-treated zinc oxide nanoflowers for the simultaneous detection of dopamine and diclofenac sodium. Microchem. J. 2020, 158, 105237. [Google Scholar] [CrossRef]
  86. Kimuama, K.; Rodthongkumb, N.; Ngamrojanavanichc, N.; Chailapakuld, O.; Ruecha, N. Single step preparation of platinum nanoflowers/reduced graphene oxide electrode as a novel platform for diclofenac sensor. Microchem. J. 2020, 155, 104744. [Google Scholar] [CrossRef]
  87. Tyszczuk-Rotko, K.; Kozak, J.; Węzińska, A. Electrochemically activated screen-printed carbon electrode for determination of ibuprofen. Appl. Sci. 2021, 11, 9908. [Google Scholar] [CrossRef]
  88. Bushra, R.; Aslam, N. An overview of clinical pharmacology of ibuprofen. Oman Med. J. 2010, 25, 155–161. [Google Scholar] [CrossRef] [PubMed]
  89. Diouf, A.; Moufid, M.; Bouyahya, D.; Österlund, L.; El Bari, N.; Bouchikhi, B. An electrochemical sensor based on chitosan capped with gold nanoparticles combined with a voltammetric electronic tongue for quantitative aspirin detection in human physiological fluids and tablets. Mater. Sci. Eng. 2020, 110, 110665. [Google Scholar] [CrossRef] [PubMed]
  90. Kruanetr, S.; Prabhu, R.; Pollard, P.; Fernandez, C. Pharmaceutical electrochemistry: The electrochemical detection of aspirin utilising screen printed Graphene electrodes as sensors platforms. Surf. Eng. Appl. Electrochem. 2015, 51, 283–289. [Google Scholar] [CrossRef] [Green Version]
  91. Stefano, J.S.; Montes, R.H.O.; Richter, E.M.; Munoz, R.A.A. Flow-injection analysis with multiple-pulse amperometry for simultaneous determination of paracetamol and naproxen using a homemade flow cell for screen-printed electrodes. J. Braz. Chem. Soc. 2014, 25, 484–491. [Google Scholar] [CrossRef]
  92. Kondori, T.; Tajik, S.; Akbarzadeh, T.N.; Beitollahi, H.; Graiff, C.; Jang, H.W.; Shokouhimehr, M. Synthesis and characterization of bipyridine cobalt(II) complex modified graphite screen printed electrode: An electrochemical sensor for simultaneous detection of acetaminophen and naproxen. RSC Adv. 2021, 11, 3049–3057. [Google Scholar] [CrossRef]
  93. Kuczyńska, J.; Nieradko-Iwanicka, B. The effect of ketoprofen lysine salt on mucosa of rat stomach after ethyl alcohol intoxication. Biomed. Pharmacother. 2021, 141, 111938. [Google Scholar] [CrossRef]
  94. Molina-Garcia, L.; Santos, J.L.M.; Ruiz-Medina, A.; Llorent-Martinez, E.J. Determination of ketoprofen based on its quenching effect in the fluorescence of quantum dots. J. Food Drug Anal. 2013, 21, 426–431. [Google Scholar] [CrossRef] [Green Version]
  95. Cao, F.; Dong, Q.; Li, C.; Chen, J.; Ma, X.; Huang, Y.; Song, D.; Ji, C.; Lei, Y. Electrochemical sensor for detecting pain reliever/fever reducer drug acetaminophen based on electrospun CeBiOx nanofibers modified screen-printed electrode. Sens. Actuators B 2018, 256, 143–150. [Google Scholar] [CrossRef]
  96. Jahani, P.M.; Mohammadi, S.Z.; Khodabakhshzadeh, A.; Asl, M.S.; Jang, H.W.; Shokouhimehr, M.; Zhang, K.; Van Le, Q.; Peng, W. Simultaneous voltammetric detection of acetaminophen and tramadol using molybdenum tungsten disulfide-modified graphite screen-printed electrode. Int. J. Electrochem. Sci. 2020, 15, 9024–9036. [Google Scholar] [CrossRef]
  97. Sima, V.; Cristea, C.; Bodoki, E.; Duţu, G.; Săndulescu, R. Screen-printed electrodes modified with HRP-zirconium alkoxide film for the development of a biosensor for acetaminophen detection. Cent. Eur. J. Chem. 2010, 8, 1034–1040. [Google Scholar]
  98. Sasal, A.; Tyszczuk-Rotko, K.; Chojecki, M.; Korona, T.; Nosal-Wiercińska, A. Direct determination of paracetamol in environmental samples using screen-printed carbon/carbon nanofibers sensor—Experimental and theoretical studies. Electroanalysis 2020, 32, 1618–1628. [Google Scholar] [CrossRef]
  99. Serrano, N.; Castilla, O.; Ariño, C.; Diaz-Cruz, M.S.; Diaz-Cruz, J.M. Commercial screen-printed electrodes based on carbon nanomaterials for a fast and cost-effective voltammetric determination of paracetamol, ibuprofen and caffeine in water samples. Sensors 2019, 19, 4039. [Google Scholar] [CrossRef] [Green Version]
  100. Raymundo-Pereira, P.A.; Gomes, N.O.; Machado, S.A.S.; Oliveira, O.N., Jr. Simultaneous, ultrasensitive detection of hydroquinone, paracetamol and estradiol for quality control of tap water with a simple electrochemical method. J. Electroanal. Chem. 2019, 848, 113319. [Google Scholar] [CrossRef]
  101. Deroco, P.B.; Fatibello-Filho, O.; Arduini, F.; Moscone, D. Effect of different carbon blacks on the simultaneous electroanalysis of drugs as water contaminants based on screen-printed sensors. Electroanalysis 2019, 31, 2145–2154. [Google Scholar] [CrossRef]
  102. Sasal, A.; Tyszczuk-Rotko, K.; Wójciak, M.; Sowa, I. First electrochemical sensor (screen-printed carbon electrode modified with carboxyl functionalized multiwalled carbon nanotubes) for ultratrace determination of diclofenac. Materials 2020, 13, 781. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  103. Seguro, I.; Pacheco, J.G.; Delerue-Matos, C. Low cost, easy to prepare and disposable electrochemical molecularly imprinted sensor for diclofenac detection. Sensors 2021, 21, 1975. [Google Scholar] [CrossRef] [PubMed]
  104. Amin, S.; Soomro, M.T.; Memon, N.; Solangi, A.R.; Uddin, S.; Qureshi, T.; Behzad, A.R. Disposable screen printed graphite electrode for the direct determination of ibuprofen in surface water. Environ. Nanotechnol. Monit. Manag. 2014, 1–2, 8–13. [Google Scholar]
  105. Saciloto, T.R.; Cervini, P.; Cavalheiro, É.T.G. Simultaneous voltammetric determination of acetaminophen and caffeine at a graphite and polyurethane screen-printed composite electrode. J. Braz. Chem. Soc. 2013, 24, 1461–1468. [Google Scholar] [CrossRef]
  106. Gilmartin, M.A.T.; Hart, J.P. Rapid detection of paracetamol using a disposable, surface-modified screen-printed carbon electrode. Analyst 1994, 119, 2431–2437. [Google Scholar] [CrossRef]
  107. Ma, L.-L.; He, Y.; Qin, D.; Chang, A.; Huang, A.; Xie, X.-J.; Zhang, Y. Fabrication, characterization and performance evaluation of screen-printed carbon electrodes: Determination of acetaminophen in Tylenol. Chinese. J. Anal. Chem. 2021, 49, 21187–21196. [Google Scholar] [CrossRef]
  108. Khairy, M.; Banks, C.E. A screen-printed electrochemical sensing platform surface modified with nanostructured ytterbium oxide nanoplates facilitating the electroanalytical sensing of the analgesic drugs acetaminophen and tramadol. Microchim. Acta 2020, 187, 126. [Google Scholar] [CrossRef]
  109. Zhang, Y.; Jiang, X.; Zhang, J.; Zhang, H.; Li, Y. Simultaneous voltammetric determination of acetaminophen and isoniazid using MXene modified screen-printed electrode. Biosens. Bioelectron. 2019, 130, 315–321. [Google Scholar] [CrossRef]
  110. Wei, Z.; Guo, S.; Cheng, L.; Li, T.; Zhang, Y.; Yang, H. Simultaneous determination of acetaminophen and tyrosine using screen-printed electrochemical sensor based on MWCNTs-doped poly(glycine)/poly(acrylic acid) conducting polymers. Int. J. Electrochem. Sci. 2019, 14, 6748–6758. [Google Scholar] [CrossRef]
  111. De Carvalhoa, R.C.; Bettsa, A.J.; Cassidya, J.F. Diclofenac determination using CeO2 nanoparticle modified screen-printed electrodes—A study of background correction. Microchem. J. 2020, 158, 105258. [Google Scholar] [CrossRef]
  112. Baezzat, M.R.; Tavakkoli, N.; Zamani, H. Construction of a new electrochemical sensor based on MoS2 nanosheets modifiedgraphite screen printed electrode for simultaneous determination of diclofenac and morphine. Anal. Bioanal. Chem. Res. 2022, 9, 153–162. [Google Scholar]
  113. Apetrei, I.M.; Bejinaru, A.A.; Boev, M.; Apetrei, C.; Buzia, O.D. Determination of ibuprofen based on screen-printed electrodes modified with carbon nanofibers. Farmacia 2017, 65, 790–795. [Google Scholar]
  114. Zhao, C.; Lin, J. Electrochemically reduced graphene oxide modified screen-printed electrodes for sensitive determination of acetylsalicylic acid. Int. J. Electrochem. Sci. 2017, 12, 10177–10186. [Google Scholar] [CrossRef]
  115. Baj-Rossi, C.; Jost, T.R.; Cavallini, A.; Grassi, F.; De Micheli, G.; Carrara, S. Continuous monitoring of Naproxen by a cytochrome P450-based electrochemical sensor. Biosens. Bioelectron. 2014, 53, 283–287. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  116. Yaghoubian, H.; Tajik, S.; Beitollahi, H.; Sarhadi, H.; Sheikhshoaie, I. Fe2MoO4 magnetic nanocomposite modified screenprinted graphite electrode as a voltammetric sensor for simultaneous determination of nalbuphine and diclofenac. J. Mater. Sci. Mater. Electron. 2021, 32, 17311–17323. [Google Scholar] [CrossRef]
  117. Cumba, L.R.; Camisasca, A.; Giordani, S.; Foster, R.J. Electrochemical properties of screen-printed carbon nano-onion electrodes. Molecules 2020, 25, 3884. [Google Scholar] [CrossRef] [PubMed]
  118. Kozak, J.; Tyszczuk-Rotko, K.; Sadok, I.; Sztanke, K.; Sztanke, M. Application of a screen-printed sensor modified with carbon nanofibers for the voltammetric analysis of an anticancer disubstited fused triazinone. Int. J. Mol. Sci. 2022, 23, 2429. [Google Scholar] [CrossRef] [PubMed]
  119. Ibáñez-Redín, G.; Furuta, R.H.M.; Wilson, D.; Shimizu, F.M.; Shimizu, F.M.; Materon, E.M.; Arantes, L.M.R.B.; Melendez, M.E.; Carvalho, A.L.; Reis, R.M.; et al. Screen-printed interdigitated electrodes modified with nanostructured carbon nano-onion films for detecting the cancer biomarker CA19-9. Mater. Sci. Eng. C 2019, 99, 1502–1508. [Google Scholar] [CrossRef]
  120. Kaewket, K.; Karuwan, C.; Sonsupap, S.; Maensiri, S.; Ngamchuea, K. Anti-fouling effects of carbon nanofiber in electrochemical sensing of phenolic compounds. J. Electrochem. Soc. 2021, 168, 067501. [Google Scholar] [CrossRef]
  121. Della Pelle, F.; Angelini, C.; Sergi, M.; Del Carlo, M.; Pepe, A.; Compagnone, D. Nano carbon black-based screen-printed sensor for carbofuran, isoprocarb, carbaryl and fenobucarb detection: Application to grain samples. Talanta 2018, 186, 389–396. [Google Scholar] [CrossRef]
  122. Bounegru, A.V.; Apetrei, C. Voltamperometric sensors and biosensors based on carbon nanomaterials used for detecting of caffeic acid-a review. Int. J. Mol. Sci. 2020, 21, 9275. [Google Scholar] [CrossRef]
  123. Sipa, K.; Brycht, M.; Leniart, A.; Skrzypek, S. The application of carbon nanomaterials as electrode surface modifiers for the voltammetric sensing of nitroxinil—A comparative studies. J. Electroanal. Chem. 2019, 848, 113294. [Google Scholar] [CrossRef]
  124. Goyal, R.N.; Chatterjee, S.; Agrawal, B. Electrochemical investigations of diclofenac at edge plane pyrolytic graphite electrode and its determination in human urine. Sens. Actuators B Chem. 2010, 145, 743–748. [Google Scholar] [CrossRef]
  125. Medsen, K.G.; Skonberg, C.; Jurva, U.; Cornett, C.; Hansen, S.H.; Johansen, T.N.; Olsen, J. Bioactivation of diclofenac in vitro and In Vivo: Correlation to electrochemical studies. Chem. Res. Toxicol. 2008, 21, 1107–1119. [Google Scholar] [CrossRef] [PubMed]
  126. Korolczuk, M. Application of pulsed potential accumulation for minimization of interferences from surfactants in voltammetric determination of traces of Cr(VI). Electroanalysis 2000, 12, 837–840. [Google Scholar] [CrossRef]
  127. González-Sánchez, M.I.; Gómez-Monedero, B.; Agrisuelas, J.; Iniesta, J.; Valero, E. Highly activated screen-printed carbon electrodes by electrochemical treatment with hydrogen peroxide. Electrochem. Commun. 2018, 91, 36–40. [Google Scholar] [CrossRef]
  128. Yuan, X.; Ma, L.; Zhang, J.; Zheng, Y. Simple pre-treatment by low-oxygen plasma activates screen-printed carbon electrode: Potential for mass production. Appl. Surf. Sci. 2021, 544, 148760. [Google Scholar] [CrossRef]
  129. Wei, H.; Sun, J.-J.; Xie, Y.; Lin, C.-G.; Wang, Y.-M.; Yin, W.-H.; Chen, G.-N. Enhanced electrochemical performance at screen-printed carbon electrodes by a new pretreating procedure. Anal. Chim. Acta 2007, 588, 297–303. [Google Scholar] [CrossRef] [PubMed]
  130. Lee, J.; Arrigan, D.W.M.; Silvester, D.S. Mechanical polishing as an improved surface treatment for platinum screen-printed electrodes. Sens. Bio-Sens. Res. 2016, 9, 38–44. [Google Scholar] [CrossRef] [Green Version]
  131. Cumba, L.R.; Foster, C.W.; Brownson, D.A.C.; Smith, J.P.; Iniesta, J.; Thakur, B.; do Carmo, D.R.; Banks, C.E. Can the mechanical activation (polishing) of screen-printed electrodes enhance their electroanalytical response? Analyst 2016, 141, 2791–2799. [Google Scholar] [CrossRef] [Green Version]
  132. Montiel, N.F.; Parrilla, M.; Beltran, V.; Nuyts, G.; Van Durme, F.; De Wael, K. The opportunity of 6-monoacetymorphine to selectively detect heroin at prenodized screen printed electrodes. Talanta 2021, 226, 122005. [Google Scholar] [CrossRef]
  133. De Oliveira Silva, R.; da Silva, E.A.; Fiorucci, A.R.; Ferreira, V.S. Electrochemically activated multiwalled carbon nanotubes modified screen-printed electrode for voltammetric determination of sulfentrazone. J. Electroanal. Chem. 2019, 835, 220–226. [Google Scholar] [CrossRef]
  134. Kozak, J.; Tyszczuk-Rotko, K.; Wójciak, M.; Sowa, I.; Rotko, M. First screen-printed sensor (electrochemically activated screen-printed boron-doped diamond electrode) for quantitative determination of rifampicin by adsorptive stripping voltammetry. Materials 2021, 14, 4231. [Google Scholar] [CrossRef]
  135. González-Sánchez, M.I.; Gómez-Monedero, B.; Agrisuelas, J.; Iniesta, J.; Valero, E. Electrochemical performance of activated screen-printed carbon electrodes for hydrogen peroxide and phenol derivatives sensing. J. Electroanal. Chem. 2019, 839, 75–82. [Google Scholar] [CrossRef] [Green Version]
  136. Cinto, S. Polymeric materials for printed-based electroanalytical (bio)applications. Chemosensors 2017, 5, 31. [Google Scholar] [CrossRef] [Green Version]
  137. Raj, M.; Gupta, P.; Goyal, R.N.; Shim, Y.-B. Graphene/conducting polimer nano-composite loaded screen printed carbon sensor for simultaneous determination of dopaminę and 5-hydroxytryptamine. Sens. Actuators B Chem. 2017, 239, 993–1002. [Google Scholar] [CrossRef]
  138. Valasii, L.; Tsimpliaras, D.; Katseli, V.; Economou, A.; Svancara, I.; Stoces, M.; Mikysek, T.; Prodromidis, M. Disposable nafion-modified screen-printed graphite electrodes for the rapid voltammetric assay of caffeine. Insights Anal. Electrochem. 2015, 1, 2470–9867. [Google Scholar] [CrossRef]
  139. Kumar, D.; Prasad, B.B. Multiwalled carbon nanotubes embedded molecularly imprinted polimer-modified screen printed carbon electrode for the quantitative analysis of C-reactive protein. Sens. Actuators B Chem. 2012, 171–172, 1141–1150. [Google Scholar] [CrossRef]
  140. Stoica, B.E.; Gavrila, A.-M.; Sarbu, A.; Iovu, H.; Brisset, H.; Miron, A.; Iordache, T.-V. Uncovering the behaviour of screen-printed carbon electrodes modified with polymers molecularly imprinted with lipopolysaccharide. Electrochem. Commun. 2021, 124, 106965. [Google Scholar] [CrossRef]
  141. Ekomo, V.M.; Branger, C.; Bikanga, R.; Florea, A.-M.; Istamboilie, G.; Calas-Blanchard, C.; Noguer, T.; Sarbu, A.; Brisset, H. Detection of Bisphenol A in aqueous medium by screen printed carbon electrodes incorporating electrochemical molecularly imprinted polymers. Biosens. Bioelectron. 2018, 112, 156–161. [Google Scholar] [CrossRef]
  142. Ayankojo, A.G.; Reut, J.; Opik, A.; Syritski, V. Sulfamethizole-imprinted polymer on screen-printed electrodes: Towards the design of a portable environmental sensor. Sens. Actuators B Chem. 2020, 320, 128600. [Google Scholar] [CrossRef]
  143. Rebelo, P.; Pacheco, J.G.; Cordeiro, M.N.D.S.; Melo, A.; Delerue-Matos, C. Azithromycin electrochemical detection using a molecularly imprinted polymer prepared on a disposable screen-printed electrode. Anal. Methods 2020, 12, 1486–1494. [Google Scholar] [CrossRef]
  144. Motaharian, A.; Hosseini, M.R.M.; Naseri, K. Determination of psychotropic drug chlorpromazine using screen printed carbon electrodes modified with novel MIP-MWCNTs nano-composite prepared by suspension polymerization method. Sens. Actuators B Chem. 2019, 288, 356–362. [Google Scholar] [CrossRef]
  145. Antiochia, R.; Gorton, L. A new osmium-polymer modified screen-printed graphene electrodefor fructose detection. Sens. Actuators B Chem. 2014, 195, 287–293. [Google Scholar] [CrossRef]
  146. Chakkarapani, L.D.; Brandl, M. Carbon screen-printed electrode coated with poly(toluidine blue) as an electrochemical sensor for the detection of tyramine. Eng. Proc. 2020, 2, 51–56. [Google Scholar]
  147. Faradilla, P.; Setiyanto, H.; Mannurung, R.V.; Saraswaty, V. Electrochemical sensor based on screen printed carbon electrode–zinc oxide nano particles/molecularly imprinted-polymer (SPCE–ZnONPs/MIP) for detection of sodium dodecyl sulfate (SDS). RSC Adv. 2022, 12, 743–752. [Google Scholar] [CrossRef]
Figure 1. Optical microscopic image of screen-printed carbon electrode (SPCE, Metrohm DropSens, Oviedo, Spain).
Figure 1. Optical microscopic image of screen-printed carbon electrode (SPCE, Metrohm DropSens, Oviedo, Spain).
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Figure 2. The structural formulas of diclofenac (A), ibuprofen (B), acetylsalicylic acid (C), naproxen (D), ketoprofen (E), paracetamol (F) and tramadol (G).
Figure 2. The structural formulas of diclofenac (A), ibuprofen (B), acetylsalicylic acid (C), naproxen (D), ketoprofen (E), paracetamol (F) and tramadol (G).
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Figure 3. SEM images and DPAdSV curves recorded at the SPCE and SPCE/MWCNTs-COOH. DPAdSV curves recorded at the surface of the SPCE/MWCNTs-COOH in solution containing increasing concentrations of DF: 0.1, 0.2, 0.5, 1.0, 2.0, 5.0 and 10.0 nmol L−1, and calibration graph of DF [102].
Figure 3. SEM images and DPAdSV curves recorded at the SPCE and SPCE/MWCNTs-COOH. DPAdSV curves recorded at the surface of the SPCE/MWCNTs-COOH in solution containing increasing concentrations of DF: 0.1, 0.2, 0.5, 1.0, 2.0, 5.0 and 10.0 nmol L−1, and calibration graph of DF [102].
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Figure 4. Scheme of voltammetric measurements of PA and DF at the SPCE/MWCNTs-COOH [83].
Figure 4. Scheme of voltammetric measurements of PA and DF at the SPCE/MWCNTs-COOH [83].
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Table 3. Summary of voltammetric procedures for painkillers residues determination at the electrochemically pretreated screen-printed electrodes or modified with polymer film in environmental water samples.
Table 3. Summary of voltammetric procedures for painkillers residues determination at the electrochemically pretreated screen-printed electrodes or modified with polymer film in environmental water samples.
ElectrodeAnalyteMethodLinear Range [µM]LOD [µM]ApplicationRef.
aSPCE/SDSDF
PA
TR
DPAdSV0.001–0.2
0.05–20.0
0.01–0.2
0.2–2.0
0.00021
0.015
river water[82]
electrochemically pretreated SPCEPA
HQ
E2
DPV0.5–10.0
0.5–10.0
0.5–10.0
0.22
0.19
0.89
tap water[100]
electrochemically pretreated SPGEIBSWV0.80–30.06.30river water, wastewater[104]
MIP/SPCEDFDPV0.1–100.07river water,
tap water
[103]
PA–paracetamol; DF–diclofenac; HQ–hydroquinone; E2–estradiol; IB–ibuprofen; DPAdSV–differential-pulse adsorptive stripping voltammetry; DPV–differential-pulse voltammetry; SWV–square-wave voltammetry; aSPCE/SDS–activated screen-printed carbon electrode modified with sodium dodecyl sulfate; electrochemically pretreated SPCE–electrochemically pretreated screen-printed carbon electrode; electrochemically pretreated SPGE–electrochemically pretreated screen-printed graphite electrode; MIP/SPCE–screen-printed carbon electrode modified with molecularly imprinted polymer.
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Tyszczuk-Rotko, K.; Kozak, J.; Czech, B. Screen-Printed Voltammetric Sensors—Tools for Environmental Water Monitoring of Painkillers. Sensors 2022, 22, 2437. https://doi.org/10.3390/s22072437

AMA Style

Tyszczuk-Rotko K, Kozak J, Czech B. Screen-Printed Voltammetric Sensors—Tools for Environmental Water Monitoring of Painkillers. Sensors. 2022; 22(7):2437. https://doi.org/10.3390/s22072437

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Tyszczuk-Rotko, Katarzyna, Jędrzej Kozak, and Bożena Czech. 2022. "Screen-Printed Voltammetric Sensors—Tools for Environmental Water Monitoring of Painkillers" Sensors 22, no. 7: 2437. https://doi.org/10.3390/s22072437

APA Style

Tyszczuk-Rotko, K., Kozak, J., & Czech, B. (2022). Screen-Printed Voltammetric Sensors—Tools for Environmental Water Monitoring of Painkillers. Sensors, 22(7), 2437. https://doi.org/10.3390/s22072437

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