Mass Spectrometric and Rapid Electrochemical Detection and Reductive Dehalogenation of Triclosan

ISSN: 2380-2391

Journal of Environmental Analytical Chemistry

  • Research Article   
  • J Environ Anal Chem 2018, Vol 5(2): 235
  • DOI: 10.4172/2380-2391.1000235

Mass Spectrometric and Rapid Electrochemical Detection and Reductive Dehalogenation of Triclosan

Janine Rizos and Achim Habekost*
Department of Chemistry, University of Ludwigsburg, Ludwigsburg, Germany
*Corresponding Author: Achim Habekost, Department of Chemistry, University of Ludwigsburg, Ludwigsburg, Germany, Tel: 0049-7141-140-332, Email: [email protected]

Received Date: Mar 26, 2018 / Accepted Date: Apr 03, 2018 / Published Date: Apr 09, 2018

Abstract

Triclosan is a chlororganic substance used as a bactericide in numerous cosmetics. Intensive triclosan use results in the exposure into the environment; therefore, it is vital to analyze and detoxify triclosan-contaminated wastewater, sludge and soil.

This study investigates two analytical strategies. The first is a rapid and inexpensive electrochemical screening technique based on commercial Screen-Printed Electrodes (SPE), which delivers initial results suitable for field measurements and screening. The second is Gas Chromatography–Mass Spectrometry (GC-MS), which is more sophisticated, accurate and sensitive. This latter method can provide more reliable determination of triclosan, e.g., for suspicious samples. We tested the limits of triclosan detection for different electrochemical methods and compared these to mass spectrometry with and without derivatization of triclosan.

In addition to these analytical techniques, gas phase dehalogenation was used to dechlorinate triclosan. Reductive dechlorination of triclosan occurs efficiently at moderately elevated temperatures (350-550°C) with zero valent iron. In contrast to oxidative processes, reductive dehalogenation leads to harmless and completely dechlorinated products.

Keywords: Triclosan; Electrochemical and mass spectrometric detection; Reductive dechlorination

Abbreviations

GC-MS: Gas Chromatography–Mass Spectrometry; MS: Mass Spectrometry; SPE: Screen-Printed Electrodes; DPV: Differential Pulse Voltammetry; ECL: Electrogenerated Chemiluminescence; HPLC: High-Performance Liquid Chromatography; LOD: Limit of Detection.

Introduction

Triclosan (5-Chlor-2-(2,4-dichlorophenoxy)-phenol), (Figure 1) is a bactericide used in numerous everyday products (e.g., in cosmetics such as toothpaste, deodorants and soaps, and in various antiseptics). Triclosan can act as an endocrine disruptor and can cause allergic reaction. The maximum accepted concentration in cosmetics is 0.3% [1]. In low concentrations triclosan is bacteriostatic, while at higher concentrations triclosan is bactericidal [2-5]. The acceptable level for the presence of triclosan in drinking water reflects the No Observed Adverse Effect Level (NOAEL) and can reach several mg/L [6].

environmental-analytical-chemistry-Structure-Triclosan

Figure 1: Structure of Triclosan.

The use of triclosan is controversial because it is not clear whether it influences antibiotic and cross-resistance. The authors of a metaanalysis ordered by the European Commission concluded that it is currently not possible to properly estimate the risks of triclosan [1]. But the high levels of triclosan used mean that considerable amounts are released into the environment.

The SciFinder database contains more than 11,000 articles with the keyword “triclosan”. In the last few years, investigations have primarily focused on analytics, the fate of triclosan in wastewater, sludge and sediments and the extraction and (oxidative) degradation of triclosan [7-12]. In addition to MS and HPLC analysis [13], and to a lesser extent spectrophotometric analysis [14], electrochemical investigations are common because the electrochemical device is simple and the analysis (e.g., of wastewater or sewage sludge) can be done on-site. New electrode materials such as nanorods [15], carbon quantum dots [16], electrodes modified with TiO2 [17] are used, as well as SPE [18]. A review of the electrochemical methods is provided by Montaseri and Forbes [19].

Solid-phase extraction is widely used for sample extraction and analyte enrichment. Materials such as octadecyl bonded silica cartridge [20,21] and other extracting agents such as different copolymers are used, which exhibit both hydrophilic and hydrophobic characteristics [22,23]. Common elution reagents for these cartridge materials include methanol, ethyl acetate, and acetone [24].

Current methods of degradation of triclosan (e.g., in wastewater and sewage sludge) include biological degradations [25], oxidative degradation with Fenton reagent [26,27], photoelectrocatalytical methods with TiO2 [28,29], degradation in sunlight [30], sonoelectrochemical [31] and photocatalytic methods [32], oxidation with different oxidants [33,34], combinations of electrochemical methods and ozone [35,36] and solely electrochemical methods [37]. The kinetics and the mechanism of the (oxidative) degradation are investigated by Gao [38] and Suarez [39].

In this paper, our goal is to detect triclosan with very simple and commercial electrochemical equipment, for a first estimation of the triclosan concentration, and to compare the data with normal GC-MS. We also present a dehalogenation method which has already been successfully applied to the dehalogenation of PCBs and brominated diphenylethers [40,41].

Experimental Part

Chemicals and materials: Triclosan (Sigma 72779), iron powder (1-10 μm, Merck 1.03819), derivatizing agent: trimethylchlororsilane (Roth, Germany, 2338.1), dichloromethane (Roth, Germany, 8424.1), tris (2, 2’-bipyridyl)ruthenium (II) chloride (Sigma, 34967), DLproline (Sigma Aldrich, 171824.), buffer (pH 10) (Roth, Germany.

GC-MS: GC: Hewlett-Packard 6890 with HP 5 column, temperature profile: start temperature: 50°C, 2 min isotherm temperature ramp: 15°C/min; end temperature: 270°C, 2 min isotherm, MSD: Hewlett- Packard 5973, injection: 1 μL).

UVVIS: photometer (Perkin Elmer, Lambda XLS+).

Electrochemistry: Pt-grids for electrolysis (Hedinger, Germany), potentiostat (μstat 400, DropSens), SPE (DRP-220 Au-AT, Au as working electrode, Au as counter electrode, Ag as pseudoreference electrode, DropSens)

Amperometry: HPLC pump (Knauer HPLC pump 64), Rheodyn injection valve, 10 μL loop, electrochemical HPLC cell (DRP HPLCELL, DropSens).

Spectroelectrochemistry: Transmission / reflection cell (DRP REFLECELL, DropSens) with fiber optics (DR PROBE, DropSens), light source: HPLC detector 432 with a D2 lamp, Kontron), photomultiplier (Hamamatsu, R4220P with power supply: MH5781).

Electrogenerated chemiluminescence: ECLSTAT (potentiostat + ECL-cell (DropSens)).

Gas phase dehalogenation: Carbolite tubular furnace (HST 12-40, Carbolite Gero), Perfusor VI (B. Brand), 10 mL syringe.

Mass spectrometric characterization of triclosan

For gas chromatographic-mass spectrometric analyzation we used different triclosan concentrations in ethanol. Figure 2 shows a detail of the GC for triclosan concentrations between 1 mmol/L and 0.5 μmol/L (injection volume: 1 μL). Triclosan was identi ied via the NIST MSdatabase (quality>95%), with the mass spectrometer operating in fullscan mode.

environmental-analytical-chemistry-peak-triclosan

Figure 2a: GC-MS peak triclosan.

environmental-analytical-chemistry-MS-Triclosan

Figure 2b: EI-MS Triclosan.

environmental-analytical-chemistry-Selected-fragments

Figure 2c: Selected fragments.

As indicated in Figure 3, the Limit of Detection (LOD) is about 0.15 mg/L (=0.52 μmol/L=0.15 ng in 1 μL used). The main fragments are listed in Figure 2c.

environmental-analytical-chemistry-triclosan-peak

Figure 3: Intensity of the triclosan peak at different triclosan concentrations. Insert: detail.

The ion intensity shows linear concentration dependence from 1.5 ng up to 300 ng triclosan (R2=0.99).

Derivatization

Gibson [42] and Yu [23] investigated various acidic pharmaceuticals and a range of potential endocrine disrupting components via GC-MS. They derivatized the substances with different derivatization agents on the basis of methylchlorosilanes. Our goal is to determine whether there is any advantage in derivatizing triclosan. For our study, only one silanization agent was used, since triclosan contains only the phenolic OH group which forms a trimethylsilyl derivative. Therefore, we compared two triclosan solutions with and without the derivatization agent.

Solution A) contained 100 μmol triclosan+150 μmol trimethylchlorosilane+5 mL dichloromethane.

Solution B) was the same as solution A), but without trimethylchlorosilane.

Both solutions were heated up to about 50°C in a reflux condenser for five hours with subsequent evaporation of the solvent and the excess derivatization agent in a rotary evaporator. At least, we added 1 mL dichloromethane, respectively. Derivatization was nearly completed. Figure 4 shows the resulting gas chromatograms with and without derivatization.

environmental-analytical-chemistry-Triclosan-derivate

Figure 4: GC-MS of derivated triclosan: A: Triclosan-derivate, B: Triclosan, C: Impurity, D: Dichlorodibenzodioxin. Insert: Without derivatization reagent.

Unexpectedly, the gas chromatograms show that dichlorodibenzodioxin is formed with and without derivatization agent. We think that dichlorodibenzodioxin is formed at temperatures necessary for the derivatization process. Therefore, we cannot support derivatization. In addition, we found that derivatization does not lead to a lower LOD.

Electrochemical characterization via Differential Pulse Voltammetry (DPV), voltabsorptogram and amperometry

We tried several SPE and selected a gold electrode, because its sensitivity was highest and the surface is easy to clean (Figure 5). Triclosan can be electrochemically oxidized at his OH group beginning at 0.3 V. This oxidation is electrochemically irreversible, as indicated by the lack of reduction peak in the cyclic voltammogram (Figure 6). In addition, the oxidation product covers the used gold surface and the second cyclic voltammogram scan shows a significantly lower current. It is well known that the phenoxy radicals produced couple to form a passivating polymeric film on the electrode surface. This electrochemically generated film is strongly adherent and continuous over the electrode surface [42,43]. Therefore, the electrode must be cleaned after every measurement. This was done either by polishing the surface with fine aluminum oxide powder or through intense rinsing with ethanol. Thus, the deviation between the current of ten cyclic voltammograms is lower than ten percent.

environmental-analytical-chemistry-SEM-image

Figure 5: SEM image of the DRP 220AT electrode used. “AT” means the electrode was made with high temperature ink (Image kindly from DropSens).

environmental-analytical-chemistry-cyclic-voltammograms

Figure 6: Two successive cyclic voltammograms of triclosan (scan rate: 50 mV/s). Solid line: first scan, dotted line: second scan.

Dejmkowa [6] showed the pH dependence of the DP voltammograms of triclosan and found that the currents are maximal at pH=10-12. Therefore, we used buffered solutions of pH=10.

For detailed characterization of the oxidation product, we electrolyzed triclosan in a buffer solution (pH=10) with platinum grid electrodes for 5 min (3 V, 40 mA) and analyzed the product via UVVIS (Figure 7). The oxidation products show an absorption maximum around 320 nm. Johnson [44] investigated the electrochemical degradation of 4-chlorophenol in an aqueous medium using a platinum anode coated with a quaternary metal oxide film containing Ti, Ru, Sn, and Sb oxides. Liquid chromatography, including reverse phase and ion exchange chromatography, is coupled with electrospray mass spectrometry. The authors identified twenty-six intermediate products. We believe analogous reaction products result in the case of triclosan, but they were not identified.

environmental-analytical-chemistry-UVVIS-spectrum

Figure 7: UVVIS spectrum of the oxidation product of triclosan after 5 min electrolysis.

The electrochemical irreversibility of the oxidation of triclosan can also be demonstrated via spectroelectrochemical measurements: Cyclic voltammogram and absorbance of the triclosan solution at 330 nm are measured simultaneously. Figure 8 shows the spectroelectrochemical setup employed: Light from a spectrometer is passed with a fiber through the solution (60 μL volume). The reflected beam (reflection on the gold electrode) is guided through a different fiber into a photomultiplier.

environmental-analytical-chemistry-Spectroelectrochemical

Figure 8: Spectroelectrochemical cell with a fiber from the spectrometer (top). The light (330 nm) passes the solution and the reflected light (reflection on the Au surface) is collected via a different fiber and is guided into a photomultiplier. The SPE is inside the cell. Bottom: fiber for transmitted light, not used here.

Figure 9 shows both the cyclic voltammogram and the voltabsorptogram at 330 nm. At about 0.3 V the oxidation of triclosan occurs, and up to about 0.5 V the absorbance increases until the oxidation is completed. At reverse scan the absorbance remains high, indicating that an irreversible oxidation has taken place in this potential range. The derivative voltabsorptogram at 330 nm exhibits a complete correlation with the cyclic voltammogram because the two signals are related to the same process.

environmental-analytical-chemistry-Simultaneous-detection

Figure 9: Simultaneous detection of the cyclovoltammogram (solid line) and the voltabsorptogram at 330 nm (thick points) and derived voltabsorptogram d(absorbance)/d(voltage) (dotted line) of 1 mmol triclosan in an aqueous solution at pH=10 (scan rate 50 mV/s).

DPV is a sensitive electrochemical method. Figure 10 shows the results (parameter: EPuls: 50 mV, EStep: 5 mV, tPuls: 40 ms, scan rate: 30 mV/s). The LOD is about 10 times higher than the mass spectrometric method (=0.7 mg/L). The saturation at higher concentrations (not shown in Figure 10) is due to the restriction of the area of the SPE used (=0.125 cm2).

environmental-analytical-chemistry-DPV-current

Figure 10: DPV current as a function of triclosan concentration. The arrows indicate the deviation of three measurements.

Figure 11 demonstrates the sensitivity of the employed amperometry: The solution was injected into the aqueous solution via a Rheodyne valve in a loop (volume: 10 μL) and was pumped through an electrochemical HPLC cell with an SPE inside (pump rate: 1 mL/ min). The applied potential was 0.5 V.

environmental-analytical-chemistry-Amperometric-detection

Figure 11: Amperometric detection of triclosan at 0.5 V.

After each measurement the SPE was carefully polished with aluminum oxide powder. The LOD with AM is about 10 ng=1 mg/L (Figure 11). The saturation at about 200 ng triclosan is lower than for the (batch) DPV. With the (lowest) HPLC-pumping rate of 1 mL/min and an AM sampling rate of 0.1 s, the time constant is too high to resolve higher concentrations of triclosan (i.e., the effective electrode area is smaller than the real area).

Electrogenerated Chemiluminescence (ECL)

Since the 1960s, the ECL technique has become increasingly attractive in analytical chemistry [45-52]. ECL involves generating an excited state in the commonly used and extensively investigated tris(2, 2’-bipyridyl)ruthenium (II) ([Ru(bpy)3]2+) on an electrode surface. First, the [Ru(bpy)3]2+ is oxidized and then undergoes an electrontransfer reaction with a coreactant. During the latter process, an excited state is created that subsequently decays and light is emitted. ECL represents a “marriage of electrochemical and spectroscopic methods” [50]. The ECL system used is a combination of [Ru(bpy)3]2+ and proline (as coreactant), which produces one of the most intense ECL results [53]. In addition, this system has excellent water solubility and is less toxic than tripropylamine, one of the most common coreactants in ECL studies (Table 1). By adding triclosan, the ECL is quenched. This quenching can be used to quantitatively determine triclosan. Figure 12 shows the ECL quenching of triclosan at a concentration of 50 μmol/L (=14 mg/L). This is the lowest concentration of triclosan which quenches the ECL of Ru2+/proline, a value which is about twenty times higher than DPV. A further disadvantage of this method is the low reproducibility (see the error bar in Figure 12).

Method Limit of Detection (LOD) Estimation
MS 0.15 mg/L Expensive, low LOD, convenient method for simultaneous detection of a wide range of substances.
DPV 0.7 mg/L Easy to use, cleaning procedure is needed for electrodes.
AM 1 mg/L Easy to use, appropriate method in combination with HPLC.
ECL 14 mg/L Information about quenching the chemiluminescence of [Ru(bpy)3]2+, comparably low reproducibility.
Voltabsorptometry - Two-dimensional spectroscopy: information about electrochemical and optical properties.

Table 1: Summary of the methods used.

environmental-analytical-chemistry-Solid-line

Figure 12: Solid line: ECL of 50 μmol/L [Ru(bpy)3]2++50 μmol/L proline with error bar. Dotted line: ECL of 50 μmol/L [Ru(bpy)3]2+ +50 μmol/L proline+50 μmol/L triclosan.

Reductive dehalogenation of triclosan with zero-valent iron

The dechlorination procedure is described in detail by Aristov and Habekost [40,41]. Some fundamental aspects are explained here: The reactor is a V2A stainless steel tube 18 mm dia. and 700 mm long. About 20 g of iron powder are gently mixed with a 0.5 g tuft of glass wool in a rotary mixer until a low density homogeneous fluffy powder is obtained. This is poured into the tube to a length of about 200 mm. The reactor is heated with a hinged tube furnace. The operating mode of the reactor is conceived so as to allow injection of condensed phase reactants under controlled, prolonged, continuous flow conditions. In tests with toluene or propanol as the proton donor, triclosan and toluene or propanol are mixed in a separate vessel, in a mass ratio of 1:5, and then transferred to a 100 mL syringe. The syringe is depressed by a perfusor so that the liquid solution is injected into the reactor tube at a rate of about 1 mL per 10 s and vaporized inside.

A nitrogen gas stream (at about 10 mL / min flow rate) transports the gaseous reactants and dehalogenation products through the tube. Upon exiting the tube, the products are condensed in a cooled trap and then taken to an offline GC-MS for analysis (via micro-syringe extraction). Figure 13 shows a schematic of the apparatus.

environmental-analytical-chemistry-dechlorination-apparatus

Figure 13: Schematic of the dechlorination apparatus.

The duration of contact between the triclosan and the dehalogenating iron is between 15 s and 20 s, depending on the reactor temperature. This was determined by injecting the triclosan into the reactor at the front and end of the tube, directly into the ice-cooled trap. The difference in detection times is the transit time through the reactor. Detailed kinetics studies were not attempted. However, since the iron and the proton source are both present in excess, a (pseudo) first-order reaction is likely, with a half-life of less than 15 s.

The gas chromatographs show significant reduction of the signals corresponding to the triclosan at temperatures as low as 400°C. However, temperatures of about 550°C are required to achieve the intended goal of “complete” conversion: at these temperatures, a comparison of the peak heights shows that conversion rates of better than 99% are achieved (Figure 14).

environmental-analytical-chemistry-phase-dehalogenation

Figure 14: Gas phase dehalogenation at different temperatures: a) direct injection b) 300°C c) 400°C d) 500°C e) 550°C. The GCs were normalized on the maximal product concentration (no internal standard was used) x=not to be identified.

Figure 15 shows that the peaks between 9 and 15 min at 550°C were all checked against the NIST database for MS and correspond unequivocally to various condensation products of toluene and phenyl.

environmental-analytical-chemistry-phase-dehalogenation

Figure 15: Part of Figure 14 (550°C). The numbers correspond to Table 2. x=not to be identified.

As can be seen from Table 2, no chlorine organic substance, especially no chlorinated dibenzodioxine, were detected.

Peak Substance (quality>90%) Peak Substance (quality>90%)
1 Dibenzofuran 11 Phenylphenole
2 Diphenyl ether 12 Diphenylethene
3 Dibenzodioxin 13 Methylanthracene
4 Fluorene 14 Methylanthracene
5 Methylfluorene 15 Phenanthrene
6 Methylfluorene 16 ?
7 Methylfluorene 17 Naphthalene derivate
8 Anthracene 18 Pyrene
9 Anthracene 19 Pyrene
10 Fluorene derivate 20 Methylpyrene

Table 2: Assignment of the peaks from Figure 15.

Further work

A) Analytics: Does the Selected Ion Monitor (SIM) modus in mass spectrometry give a better LOD? Does a lower pumping rate influence saturation in amperometry?

B) Dehalogenation: In a previous work we were able to show that a mixture of iron and quicklime shows great promise for incorporation in soil and sediment remediation processes, but several questions remain. First, we observed that the empty steel tube by itself, with no iron powder inside, is also capable of complete conversion of the OCs, but at higher temperatures (above 600°C). Presumably, reducing the iron powder grain size (e.g., to nanometer scales) will allow efficient dehalogenation to proceed at even lower temperatures than necessary in the work presented here. Second, since water must be added to the triclosan/quicklime mixture to produce the calcium hydroxide proton donor, dehalogenation efficiency should be tested under conditions with an excess of water, to more closely simulate actual contaminated soil conditions. Third, replacing the nitrogen carrier gas with air should be tested. Especially, does any chlorinated dibenzodioxine result in the air-filled tube?

Results and Discussion

The total ion signal intensity of the triclosan peak at different concentrations is shown in Figure 3. The LOD (signal:noise=3:1) is about 0.15 mg/L (=0.52 μmol/L). Derivatization with trimethylchlorosilanes substitutes the phenolic group by forming a trimethylsilyl derivative. But derivatization does not lead to lower detection limit. Unexpectedly, dichlorodibenzodioxin is formed at higher temperatures.

Electrochemistry plays an important role in the analytics of triclosan. Commercial SPE are suitable for rapid and inexpensive electrochemical screening technique. The results especially with DPV and AM technique are suitable for field measurements and screening. Spectroelectrochemical measurements deliver additional information about the resulting electrochemical oxidation products. ECL can be used if the substance under investigation can influence the ECL of the [Ru(bpy)3]2+ used. But the LOD of the ECL method in case of triclosan is much higher than the LOD of DPV and AM. The plots of the dependence of the peak currents on the triclosan concentrations are linear between 0.7 mg/L and 200 mg/L for DPV and between 1 mg/L and 15 mg/L for AM.

Figure 14 shows gas chromatograms of triclosan at different reductive dehalogenation temperatures. One sees that 550°C is sufficient for dehalogenation to occur, as the triclosan disappears from the chromatogram and no chlorinated product are exciting in the tube, confirmed by the analysis of the products.

Conclusion

This paper has described three (spectro) electrochemical methods for identifying triclosan: DPV, AM and ECL. We have shown that these methods have different LODs, and the ECL signal has the disadvantage that reproducibility is poor. The Au electrode used has to be cleaned before every measurement because the oxidation product forms a passivating polymeric film on the electrode surface.

The electrochemical methods give a preliminary estimation of the triclosan concentrations. The advantages of the screen-printed electrodes used are their easy handling and their rapid feasibility. Mass spectrometry can provide more reliable determination of triclosan for suspicious samples.

Acknowledgements

Achim Habekost thanks the Vector foundation, the Fonds der Chemischen Industrie and the University of Ludwigsburg for financial support.

References

Citation: Rizos J, Habekost A (2018) Mass Spectrometric and Rapid Electrochemical Detection and Reductive Dehalogenation of Triclosan. J Environ Anal Chem 5: 235. Doi: 10.4172/2380-2391.1000235

Copyright: © 2018 Rizos J, et al. This is an open-access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricteduse, distribution, and reproduction in any medium, provided the original author and source are credited.

Select your language of interest to view the total content in your interested language

Post Your Comment Citation
Share This Article
Recommended Conferences
  • International Conference on Analytical Chemistry

    August 29-30, 2018 Toronto, Canada

  • Annual Congress on Chemistry

    September 12-13, 2018 Singapore City, Singapore

  • International Conference on EnvironmentalChemistry and Engineering

    September 20-22, 2018 Berlin, Germany

  • International Conference on Mass Spectrometryand Chromatography

    October 8-9, 2018 Dubai, UAE

Viewmore
Article Usage
  • Total views: 346
  • [From(publication date): 0-2018 - Aug 17, 2018]
  • Breakdown by view type
  • HTML page views: 314
  • PDF downloads: 32

Post your comment

captcha   Reload  Can't read the image? click here to refresh