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Article

Catalytic Advanced Oxidation Processes for Sulfamethoxazole Degradation

by
Jéssica Martini
†,
Carla A. Orge
*,
Joaquim L. Faria
,
M. Fernando R. Pereira
and
O. Salomé G. P. Soares
*
Laboratory of Separation and Reaction Engineering–Laboratory of Catalysis and Materials (LSRE-LCM) Faculdade de Engenharia, Universidade do Porto, Rua Dr. Roberto Frias s/n, 4200-465 Porto, Portugal
*
Authors to whom correspondence should be addressed.
†
Current address: Centro de Tecnologia–Departamento de Engenharia Sanitária e Ambiental, Universidade Federal de Santa Maria, Avenida Roraima, n° 1000, 97105-900 Santa Maria, Brasil.
Appl. Sci. 2019, 9(13), 2652; https://doi.org/10.3390/app9132652
Submission received: 30 April 2019 / Revised: 24 June 2019 / Accepted: 25 June 2019 / Published: 29 June 2019
(This article belongs to the Section Chemical and Molecular Sciences)
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Versions Notes

Abstract

:
The degradation of sulfamethoxazole (SMX) by several advanced oxidation processes (AOPs) is carried out in the presence of different catalysts. The catalysts used consisted of carbon nanotubes (CNT), titanium dioxide (TiO2), a composite of carbon nanotubes and titanium dioxide (TiO2/CNT), and iron supported on carbon nanotubes (Fe/CNT). SMX removal was evaluated by catalytic ozonation, photocatalysis, catalytic oxidation with hydrogen peroxide, and combinations of these processes. The evolution of the SMX concentration during reaction time, the mineralization degree, the toxicity of the treated solution, and the formation of organic intermediates and ions were monitored. Ozonation catalyzed by Fe/CNT and CNT and photocatalytic ozonation in the presence of CNT presented the fastest degradation of SMX, whereas photocatalytic ozonation with CNT showed the best results in terms of organic matter removal (92% of total organic carbon (TOC) depletion). Total mineralization of the solution and almost complete reduction of toxicity was only achieved in the photocatalytic ozonation with H2O2 and Fe/CNT catalysts. The compound 3-amino-5-methylisoxazole was one of the first intermediates formed during SMX degradation. p-Benzoquinone was only formed in photocatalysis. Oxalic and oxamic acids were also detected and in most of the catalytic processes they appeared in small amounts. Ion concentrations increased with the reaction time.

1. Introduction

Advanced oxidation processes (AOPs) are based on the oxidation of organic pollutants by strong oxidizing species, notably hydroxyl radicals (HO●), which react rapidly and indiscriminately with several organic compounds. Their main objective is to mineralize the pollutants into carbon dioxide and water, or convert them into by-products, sometimes less harmful to human health and the aquatic environment [1]. These processes have been shown as an effective alternative to the removal of persistent compounds, such as hormones, drugs, and pesticides.
In the presence of catalysts, it is expected that the oxidation capacity of the processes will increase and, consequently, the degradation of the main pollutant and intermediates would be easily attained, leading to higher levels of mineralization. Catalytic reactions can be homogeneous or heterogeneous, wherein solution and catalyst are in the same phase, or in distinct phases, respectively.
Carbon-based catalysts are widely studied and presented good results in catalytic ozonation reactions [2,3,4,5,6,7]. There are different suggestions of reaction mechanisms for ozonation catalyzed by carbon materials. Some studies have suggested that carbon material acts as the initiator of O3 decomposition, producing H2O2 and, consequently OH● in solution [2,5,8,9]. On the other hand, some researchers suggested that O3 adsorption and reaction on the carbon surface led to the formation of free radicals which can react with organic species [3,5,10]. Furthermore, OH● present in solution and those on the surface of the material may contribute to the mineralization of the compounds [11]. The efficiency of the catalytic ozonation process depends on the chemical and textural properties of the catalyst, as well as on the temperature and pH of the solution. Usually, the higher surface area of the carbon material leads to better O3 decomposition [11]. Furthermore, delocalized π electrons on the carbon nanotube (CNT) surface are known to be active sites for the decomposition of O3 and radical formation [4]. On the other hand, acidic CNTs present lower catalytic activity, because the electron density is more moderate, resulting in fewer electrons on the surface to react with O3—despite exhibiting high content of oxygenated surface groups and delocalized π electrons [4]. The decomposition of O3 in water also strongly depends on the pH of the solution, because the pH increase enhances the decomposition of O3 and, also, the surface properties of the catalysts can be modified [12].
Photocatalytic reactions arise from the combination of photolysis with a catalyst, in this case, named as photo-catalyst. The photo-catalyst should be photoactive, capable of responding to visible and/or UV light, biologically and chemically inert, photo-stable, and non-toxic [13,14]. Photocatalysts are typically materials that have a band gap energy between the valence band (VB) and conduction band (BC). However, in some conditions, the electrons are promoted from VB to BC generating an electron-hole pair (e−/h+), thus presenting electrical conductivity, and can act as an electron donor or acceptor [15,16]. The most used photo-catalyst is TiO2 because it is not toxic, chemically stable, and inexpensive [15]. Composites with TiO2 and CNT are an interesting alternative in photocatalytic reactions since it is expected that the use of TiO2/CNT composites reduces the recombination of the pair e−/h+, because the excited electron of the conduction band of TiO2 can migrate to the CNT [17,18]. Another aspect is that the presence of Ti–O–C linkages increases light absorption, leading to an increase in the photocatalytic activity. Also, the presence of CNT contributes to a rise in the surface area of the composite, thereby increasing the available active centers when compared with pure TiO2 [19,20]. In spite of photocatalysis being mainly used in organic pollutant degradation, removal of heavy metals was also investigated [21]. The sequence of two solar photocatalytic processes (TiO2 photocatalysis in the presence of O2 followed by the presence of N2) was proven to be efficient in the removal of copper, iron, and zinc presented in real soil washing effluents. The results indicate that wastewaters can be successfully treated under a natural sunlight source, although it requires more time to reach significant pollutant removal efficiencies than simulated irradiation.
When photolysis, ozonation, and an appropriate catalyst are combined, the catalyst is photo-excited through radiation and O3 molecules can adsorb on the catalyst surface, resulting in the production of active oxygen radicals (O●). Another advantage is that the presence of O3 decreases the recombination of the pair e−/h+ [22].
Catalytic reactions involving hydrogen peroxide (H2O2) are mainly promoted by the addition of transition metals with high valence, such as Ti, V, Mo, W, and Re [23]. The formation of hydroxyl radicals by H2O2 can also be promoted by Fenton reaction or photo-Fenton, whose catalytic process is based on electron transfer between a cationic metal and H2O2. In this process, Fe2+ acts as a catalyst and combined with H2O2 under acid conditions produces reactive species, especially OH● radicals. Furthermore, the photo-Fenton process presents improved efficiency due to the formation of additional amounts of OH● radicals through photoreduction of the iron ions formed during the Fenton reaction, since the photoreduction leads to regeneration of these ions to complete the catalytic cycle [24]. This improvement was confirmed by Malato et al. during the degradation of three pesticides (imidacloprid, methomyl, and formetanate) under solar radiation [25]. The homogenous photo-Fenton process revealed to be more efficient than photocatalysis in the presence of TiO2 in terms of pollutant removal, mineralization degree, and toxicity reduction.
This work aims to study the degradation of sulfamethoxazole (SMX) by catalytic advanced oxidation processes. SMX is a synthetic antibiotic of the sulfonamides group commonly used to treat respiratory and urinary diseases caused by bacteria [26]. Additionally, SMX is also used in agriculture as herbicide and in preventive care in veterinary medicine [27]. This antibiotic is found in waterbodies in small concentrations, but its presence in the environment can cause extensive damage to aquatic organisms, especially the emergence of resistant bacteria [28,29]. There is no doubt about the occurrence of sulfamethoxazole (SMX) as a pollutant in several aquatic instances around Europe. According to Bila et al., SMX was detected in Germany in the range 300–1500 ng L−1 and 0.4 μg L−1 in wastewater treatment plants, 30–85 ng L−1 and 0.03 μg L−1 in surface waters, and 410 ng L−1 in underground waters [30]. Gaffney et al. reported the presence of SMX in drinking waters (approximately 22 ng L−1) in the Netherlands and USA [31]. In Portugal, the presence of SMX was also confirmed. According to the report performed by Madureira et al., SMX was detected in concentrations around 53.3 ng L−1 in the Douro river, 0.27 ng L−1 in drinking waters, and 8.0 ng L−1 at the sampling point in the Tagus river [32]. As SMX is a persistent contaminant, it is not easily degraded by conventional treatment processes, requiring the application of advanced techniques. Therefore, the following catalytic advanced processes were studied to enhance the degradation of SMX: photocatalysis (L), catalytic ozonation (O3), and catalytic oxidation with hydrogen peroxide (H2O2). The combination of two or more processes—photocatalytic ozonation (L/O3), photocatalysis with hydrogen peroxide (L/H2O2), catalytic ozonation with hydrogen peroxide (O3/H2O2), and photocatalytic ozonation with hydrogen peroxide (L/O3/H2O2)—for the degradation of SMX were also carried out. The processes cited above were also studied in detail in the absence of catalysts [33].
The main subject of this research is to study the degradation of sulfamethoxazole by different oxidation processes and in the presence of various catalysts. For that propose, four solid-state materials with optical semiconductor properties were used as catalysts and they were extensively characterized to better understand their performance. Carbon nanotubes (CNT) were chosen due to their strong catalytic activity with O3, especially for promoting the O3 decomposition and surface reactions. Titanium dioxide (TiO2) was used due to its stability and photocatalytic activity which promote the formation of oxidative radicals in the presence of light. A composite of carbon nanotubes and titanium dioxide (TiO2/CNT) was chosen because it can improve the reaction in the presence of light, once it avoids the recombination of the pair e−/h+ and enhances the activity of TiO2. Finally, iron supported on carbon nanotubes (Fe/CNT) were used since H2O2 can be decomposed in the presence of Fe, generating radicals. Since this work does not consider only photo-based processes and it is not a net photochemistry study, detailed photophysical information was not evaluated. The efficiency of various processes was critically compared in terms of SMX concentration, mineralization level, and formation of intermediate compounds (3-amino-5-methylisoxazole—AMI, p-benzoquinone—BZQ, oxamic acid—OXM, and oxalic acid—OXL) and ions (sulphate—SO42−, nitrate—NO3−, and ammonium—NH4+).

2. Materials and Methods

2.1. Reagents

Ammonium chloride (≥99%), hydrogen peroxide (wt 30%), iron (III) nitrate nonahydrate (≥98%), methanol (≥99.8%), nitric acid (90%), oxalic acid (≥99%), oxamic acid (≥96%), sodium carbonate (≥99%), sodium nitrate (≥99%), sulfamethoxazole (≥99%), titanium (IV) isopropoxide (97%), p-benzoquinone (≥99.5%), 2,6-pyridine dicarboxylic acid (≥99%), and 3-amino-5-methylisoxazole (≥98%) were provided by Sigma Aldrich (Saint Louis, MO, USA). Anhydrous sodium sulfate (≥99%) was acquired from Riedel-de Haën (Seelze, Germany), multiwalled carbon nanotubes (CNT) (≥95% C) from Nanocyl, ethanol (99.8%) from PanReac, sodium nitrite (≥99%) from Fluka (Honeywell International Inc., Charlotte, NC, USA), sodium sulfite (≥98.5%) from Acros (Fisher Scientific, Hampton, NH, USA), and sulfuric acid (95%–98%) from Labor. The standard solutions as well as pollutant solution and eluents were prepared with ultrapure water obtained from the Direct-Q Millipore system (Merck KGaA, Darmstadt, Germany).

2.2. Preparation and Characterization of Catalysts

For the evaluation of SMX degradation, by the tested catalytic processes, four catalysts were selected. CNTs (Nanocyl 3100, Nanocyl SA., Sambreville, Belgium) were used as received. TiO2 was prepared by the sol–gel method [34,35]. Briefly, the precursor titanium (IV) isopropoxide (C12H28O4Ti) was dropwise added to 125 mL of ethanol at room temperature under magnetic stirring, and the solution was maintained under stirring for 30 min. Then, 1 mL of nitric acid was added, and the solution was stirred until gel formation. After evaporation of the solvent at room temperature, the sample was ground, and the powder obtained was thermally treated at 400 °C under nitrogen flow for 2 h. The iron catalyst supported on carbon nanotubes (Fe/CNT) was prepared by the incipient wetness impregnation method using CNT as the support of the metal phase (Fe). For this, a solution of 324.8 mg Fe(NO3)3·9H2O was added dropwise through a peristaltic pump (Ismatec®, Wertheim, Germany) to 2.2 g of CNT in order to obtain a content of 2% of iron (% wt). The addition was performed under ultrasonic mixing. After impregnation, the sample was dried at 100 °C during 24 h. Finally, the material was thermally treated under nitrogen flow (purity of 99.999% purchased from Linde Portugal, Lda., Lisboa, Portugal) of 100 cm3 min−1 at 400 °C for 1 h, followed by a reduction under hydrogen (purity of 99.999% purchased from Linde Portugal, Lda.) with 100 cm3 min−1 flow rate during 3 h at 400 °C. The iron reduction temperature was determined by the temperature programmed reduction (TPR) technique. The composite TiO2/CNT was prepared in a ball milling, according to optimal conditions previously determined, during 30 min at 10 vibrations s−1 in a Retsch MM 200 equipment using 90% TiO2 and 10% of CNT [36].
To evaluate the chemical and textural properties, the prepared catalysts were characterized by several techniques. Thermogravimetric analyses were performed in an STA 409 PC/4/H Luxx equipment of Netzsch until 900 °C using helium as insert carrier gas and air as burning gas. Textural properties were evaluated by nitrogen adsorption isotherms at −196 °C, held in a Quantachrome NOVA 4200e apparatus. Approximately 0.1 g of each sample was previously submitted to a degassing program for 3 h at 150 °C. Additionally, the catalyst Fe/CNT was analyzed by temperature programmed reduction (TPR) in an AMI-200 (Altamira Instruments, Pittsburgh, PA, USA). Fe/CNT was reduced under a gas stream of 5% (v/v) of H2 diluted in Ar until 700 °C. The H2 consumption was measured by a thermal conductivity detector (TCD). The morphology of this sample was also analyzed by transmission electron microscopy (TEM) in a LEO microscope model 906E with an acceleration voltage of 120 kV. The sample was previously dispersed in ethanol in an ultrasonic bath. One drop of this suspension was deposited on a copper grid with a formvar film.
TiO2-based catalysts were also analyzed by X-ray diffraction, performed by a PANalytical X’Pert PRO diffractometer with a Cu Ka radiation source (λ = 1.54 nm). The voltage and current used were 50 kV and 40 mA, respectively. The results were collected in the range of 2θ between 10° and 90° with a speed of 0.017° s−1. The Rietveld refinement was used to analyze the results.

2.3. Catalytic Tests

All SMX degradation reactions were performed in the same photochemical glass reactor (60 mm diameter, 250 mm height). A glass reactor was chosen, since all processes studied can be performed in this kind of reactor. Therefore, it is possible to make an authentic comparison of the results. The initial SMX concentration used was 30 mg L−1 at natural pH (≈5.1). The initial SMX concentration selected for this study was 30 mg L−1, to allow easier comparison between the different treatments and to study the mineralization degree by total organic carbon (TOC) measurements. The experiments were carried out at the natural pH of the initial solution (≈5.1), avoiding adding additional chemicals for pH control. The pH and concentration used in this work were selected to clearly distinguish the different processes at the natural pH of the solution. If the experiments were carried out at lower concentrations, in the range of ng L−1, the comparison between the different processes would not be accurate, especially in terms of mineralization degree. The reactor has 250 mL capacity, and the reactions were performed under a constant agitation of 400 rpm.
In photoreactions, a Heraeus TQ150 medium pressure mercury vapor lamp was used as an irradiation source, delivering near-UV/Vis irradiation (λ > 350 nm; 50 mW cm−2). A recirculation glass jacket (Duran® 50, Mainz, Germany) placed around the lamp, with the main resulting emission lines at λexc = 365, 405, 436, 546, and 578 nm. A UV–vis spectroradiometer (USB2000+, Ocean Optics, Winter Park, FL, USA) was used to measure the light intensity and photon flux. The obtained values of UV dose and photon flux were 4.6 × 105 mJ cm−2 and 9.7 × 1016 photons cm−2 s−1, respectively.
In all catalytic reactions, 125 mg of catalyst (optimal amount) was added. The collected samples were centrifuged for 15 min at 13.5 rpm using a VWR MicroStar 12 centrifuge to ensure the absence of suspended particles during analytic analysis.
Ozone (O3) was generated from pure oxygen through a BMT 802X generator, and its concentration was monitored by a BMT 960 analyzer (BMT MESSTECHNIK GMBH, Stahnsdorf, Germany). The O3 flow rate and concentration used were of 150 cm3 min−1 and 50 g m−3, respectively. The gas stream charging was carried out through a diffuser with 1 cm of diameter, and the O3 gas, which had left the reactor, passed by washing bottles with potassium iodide (KI 20%). In all reactions where O3 was not involved, O2 was used to keep the same experimental conditions.
In H2O2-based reactions, a theoretical stoichiometric amount of H2O2 was added, determined by Equation (1), considering an excess of 50% (45.3 μL). Sodium sulfite (Na2SO3) was added to the samples collected in these reactions to ensure complete consumption of H2O2 and stop the reaction, according to Equation (2).
C10H11N3O3S + 33H2O2 → 10CO2 + 36H2O + H2SO4 + 3HNO3
Na2SO3 + H2O2 → Na2SO4 + H2O
All individual processes were tested, in the presence and absence of catalysts, as well as all possible combinations of the three tested processes (O3, light, and H2O2). The detailed information of non-catalytic runs with individual and combined processes was previously published [33].

2.4. Analytic Methods

SMX and primary degradation products, AMI and BZQ, as shown in Table 1, were detected by high-performance liquid chromatography (HPLC) with a Hitachi Elite LaChrom equipment with diode detector (DAD). The stationary phase was composed by LiChroCART Purospher STAR RP-18 (Merck Millipore, Burlington, MA, USA) column (250 × 4.6 mm), and the mobile phase was a gradient of water and methanol with a flow rate of 1 mL min−1 and an injection volume of 50 μL. The wavelengths used for SMX, AMI, and BZQ were 265, 210, and 225 nm, respectively.
The determination of final by-products of SMX degradation, OXM and OXL, as shown in Table 1, was performed by HPLC Hitachi Elite LaChrom (Hitachi High-Technologies Corporation, Kagoshima, Japan) equipped with a UV detector, using an Alltech AO-1000 (Fisher Scientific, Hampton, NH, USA) column (300 × 6.5 mm) and a mobile phase composed by 5 mM H2SO4 solution at a flow rate of 0.5 mL min−1 and injection volume of 15 μL. The wavelength used was 200 nm.
Ion chromatography was used to analyze the formation of ion species (SO42−, NO3−, and NH4+) that may be released during SMX degradation. This analysis was performed on a Metrohm 881 Compact IC Pro equipment. The SO42− and NO3− ions were detected in the Metrosep A Supp 7 column (250 × 4 mm) with a Metrosep P2 Guard/3.5 pre-column. The mobile phase was composed by a solution of 3.6 mM Na2CO3, flow rate of 0.7 mL min−1, and injection volume of 20 μL. The analysis was performed at 45 °C. A Metrosep C4 column (250 × 4.0 mm) from Metrohm with Metrosep C4-S-Guard/4.0 pre-column was used for NH4+ determination. The eluent was a solution of 0.7 mM of 2,6-pyridine dicarboxylic acid and a solution of 1.7 mM of nitric acid at 0.7 mL min−1 flow rate. The analysis was performed at 25 °C and with an injection volume of 20 μL.
The determination of total organic carbon (TOC) was performed in a L-TOC Total Organic Carbon Analyzer of Shimadzu coupled to an ASI-L auto sampler of the same brand, by the Non-Purgable Organic Carbon (NPOC) method. The collected samples, already centrifuged, were analyzed without any previous preparation.
The toxicity of treated samples was evaluated by the Microtox® (Guildford, UK) acute toxicity test according to the procedure established by standard methods (ISO/DIS 11348-3) [37].

3. Results

3.1. Catalyst Characterization

The textural properties of the catalysts are presented in Table 2. The highest surface areas (SBET) were verified in CNT and Fe/CNT samples, but Fe/CNT has a slightly lower area due to iron impregnated on the surface of the CNT. On the other hand, TiO2 has the lowest surface area and pore volume.
The results of the XRD analysis for TiO2 and TiO2/CNT are also shown in Table 2. The crystalline phases were identified by applying the Rietveld refinement. The crystal composition of TiO2 is 93% of anatase and 7% of rutile, while TiO2/CNT contains 97% of anatase and 3% of rutile. The difference in crystal percentage between TiO2 and TiO2/CNT probably occurs because of the method used in the mixing of catalysts, which can modify the TiO2 crystal phase. The results show that the TiO2-based catalysts are formed by a higher percentage of anatase form which corresponds to the most active crystal for photocatalytic reactions.
As expected, TGA analysis (results not shown) demonstrates that CNT and Fe/CNT have a higher mass loss due to the burning of carbon material during heating; furthermore, Fe/CNT has a lower mass loss due to the presence of iron. TiO2 presents little mass loss, as expected since TiO2 is thermodynamically stable and formed mainly by rutile and anatase crystals. The determined fractions of CNT and TiO2 in the composite are 15% and 85%, respectively.
TPR analysis of Fe/CNT under 5% of hydrogen flow determined the temperature of reduction of the metal. Two reduction peaks were observed—a first peak between 300 and 400 °C, where the metal is reduced to Fe3O4, and a second peak between 400 and 600 °C, which corresponds to a sequential reduction of Fe3O4 to FeO and Fe0 [6]. TEM analysis, as shown in Figure 1, shows the presence of impregnated iron in the catalyst with uniform particle size and uniform metal distribution on the surface of the CNT.

3.2. SMX and TOC Removal

SMX and TOC removals achieved during catalytic ozonation, photocatalysis, and photocatalytic ozonation are presented in Figure 2.
In ozonation catalyzed by CNT and Fe/CNT, SMX was removed faster in the early stages; however, after 10 min of reaction, SMX present in solution was removed entirely in all ozonation systems. Regarding the TOC removal, ozonation catalyzed by TiO2 promotes a removal of 41%, which is lower than the amount obtained by single ozonation; TiO2 is a photoactive catalyst and poorly reacts in the presence of O3. The catalytic ozonation in the presence of Fe/CNT led to the highest mineralization level; 75% of removal after 3 h of reaction.
Iron, like other transition metals, shows significant catalytic activity in ozonation, once it promotes the decomposition of dissolved O3 in hydroxyl radicals, especially in acidic conditions, as shown in Equation (3). In this case, the presence of CNT avoids hydrolysis and iron precipitation, while iron promotes the increase of the number of active centers on the catalyst surface; thus, the formation of OH● radicals increases and, consequently, the oxidation of intermediates formed during the reaction is promoted, leading to a higher mineralization [38,39]. Additionally, O3 adsorption and reactions on the surface of the CNT can occur, and generation of surface oxygen radicals is promoted, justifying the importance of the textural properties in these processes [3,5,26].
Fe3+ + O3 + H2O → FeO2+ + OH● + O2 + H+
Photocatalysis in the presence of CNT and Fe/CNT ensured higher SMX removal in the early stages, but after 120 min of reaction no differences were observed and SMX present in solution, as shown in Figure 2c, was degraded in all systems. On the other hand, a catalyst is required to achieve exceptional levels of mineralization, as can be seen in Figure 2d. The Fe/CNT led to the highest TOC removal reaching mineralization of 78%, while only 14% is removed by the non-catalytic process. The combination of CNT and TiO2 increases the catalytic activity in terms of TOC removal, probably due to the formation of more oxidizing radicals. CNT material is a photosensitizer, has a reducer character, and high electronic conductivity; thus, it can increase the mobility of electrons and hence the formation of radicals is improved, increasing the degradation, especially of the intermediaries, and consequently more significant mineralization was attained.
The results of SMX removal by catalytic oxidation with H2O2 are depicted in Figure 3, together with the adsorption results on TiO2 and CNT.
SMX adsorption was not observed on TiO2, which was expected since TiO2 is highly stable and it has a small surface area and pore volume. Abellán et al. [40], Baran et al. [41], and Su et al. [42] reported similar adsorption results to those obtained in this work. Moreover, adsorption on CNT removed 61% of SMX and reached a TOC removal of 52% after 3 h. The adsorption of SMX is more pronounced in the early stages of the contact time, remaining constant after the initial stage due to surface saturation. The high surface area and volume of pores of the CNT may justify the high adsorption values. Gonçalves et al. [5,26] presented a similar profile; however, the adsorption degree obtained was lower (between 30% and 50%), probably due to the lower catalyst concentration (0.143 g L−1) used.
SMX was not entirely removed by catalytic oxidation with H2O2, and its concentration remained constant during the 3 h of reaction in the presence of TiO2 and TiO2/CNT catalysts. The highest removals were achieved by the addition of CNT and Fe/CNT, removing approximately 50% of SMX after 3 h of reaction. Intermediates and ions were not detected in any reaction with H2O2. The reduction profile of SMX concentration and TOC verified in the oxidation of H2O2 with CNT and Fe/CNT was similar to adsorption on the CNT profile. Considering this similarity and the absence of intermediates in solution, it is possible that SMX removal, in this case, occurred due to adsorption and not by oxidation. However, when CNTs were combined with H2O2, less removal was observed, probably due to competition between H2O2 and SMX for the CNT active centers, reducing, therefore, the adsorption capacity of the catalyst [4,26,43].
In photocatalytic ozonation, as shown in Figure 2e,f, an improvement in the degradation of SMX was verified when compared to the non-catalytic process, except in the presence of TiO2. The presence of CNT, Fe/CNT, and TiO2/CNT accelerated SMX degradation; however, after 15 min of reaction, SMX was completely degraded by all tested systems. The TOC removal results show that the highest mineralization occurred in the presence of CNT (93%), while the remaining reactions allowed 84% of TOC removal at the end of the reaction.
Comparing the SMX degradation by photocatalytic ozonation with correspondent individual processes, photocatalysis, and catalytic ozonation, it is possible to observe that in the combined process carried out with CNT, SMX was degraded faster and higher mineralization was reached. This result demonstrates that the combination of radiation, O3, and catalyst is beneficial for SMX degradation.
The catalytic ozonation with H2O2 was insensitive to the used catalyst, as shown in Figure 4. In the case of TOC removal, a fast mineralization rate was observed when Fe/CNT and TiO2/CNT were added, removing approximately 75% of the organic matter after 3 h of reaction. Moreover, catalytic ozonation with H2O2 and TiO2 presented higher TOC in solution than the non-catalytic process, probably because TiO2 is not an ozonation catalyst.
The mineralization of the SMX was not increased during catalytic ozonation and catalytic ozonation with H2O2 in the presence of Fe/CNT catalyst, indicating that the addition of H2O2 to ozonation is not advantageous under the operating conditions used. As previously mentioned, the H2O2 added can adsorb on the catalyst surface and change its surface, reducing the available active centers and therefore decreasing the reaction as well as the formation of superficial radicals [5]. Furthermore, the amount of H2O2 added to the system may not be enough, so it would be necessary to optimize the H2O2 concentration and the pH of the solution to improve the results.
The presence of H2O2 in the photocatalytic reactions did not improve the SMX removal rates, as shown in Figure 4. However, except for the system with TiO2, most of the catalytic systems had better performance in TOC removal than non-catalytic combinations. Although some studies show that the addition of H2O2 to the photocatalysis with TiO2 improves the process, this was not observed in this work probably due to the use of non-optimized H2O2 concentration and pH [14,39]. TiO2 can decompose H2O2 into radicals different than OH●, promoting other reaction mechanisms and consequently the formation of other intermediates, unidentified in this work, which are less efficient.
Comparing the TOC results of photocatalysis and photocatalysis with H2O2, CNT and Fe/CNT samples had the highest removal of organic matter in both cases, but in the combined method (L/H2O2) the mineralization rates were lower. The reduction in the mineralization rate can be explained by the competition between H2O2 and SMX for the active centers of catalysts, as mentioned before, since H2O2 may be adsorbed on the active centers of the catalyst and they become unavailable for the reaction, which decreases surface reactions.
The results of photocatalytic ozonation with H2O2 presented in Figure 5 allowed the conclusion that the addition of catalysts, especially the composite TiO2/CNT, slightly increases the SMX degradation rate, but after 30 min no differences among the tested reactions were observed. Regarding the TOC removal, CNT and Fe/CNT had better efficiency than the non-catalytic process, and total mineralization of the solution was attained in the presence of the Fe/CNT catalyst.
Analyzing the results of photocatalytic ozonation and photocatalytic ozonation with H2O2, it is possible to observe that the addition of H2O2 improves the mineralization degree and L/O3/H2O2 in the presence of CNT and Fe/CNT achieved a better mineralization level, possibly due to the formation of higher amounts of oxidizing radicals. H2O2 can be decomposed in the presence of Fe or light and/or participate in the formation of other radicals with O3, as described in Equation (4) [44], Equation (5) [45], and Equation (6) [46], respectively. Furthermore, in the Fe/CNT sample, the presence of iron increases the available active centers in the CNT, which favors the decomposition of O3 in radicals and the reactions on the CNT surface.
Fe2+ + H2O2 → Fe3+ + HO− + HO●
H2O2 + hν → 2HO●
H2O2 + 2O3 → 2HO● + 3O2

3.3. By-Products and Intermediates Analysis

AMI is one of the first products of SMX degradation. In O3-based processes, the detection of AMI occurs during the first 30 min of reaction and, in most cases, AMI concentration is lower in the presence of CNT and Fe/CNT. However, in photocatalysis and photocatalysis with H2O2, AMI was not degraded after 180 min of reaction (results not shown).
BZQ was detected in most of the reactions, but in concentrations lower than the quantification limit (0.10 mg L−1); thus, it was not possible to determine the amount of BZQ released. Nevertheless, BZQ was quantified in photocatalysis in the presence of CNT and Fe/CNT, probably due to the low degradation kinetics which leads to a high BZQ concentration in solution. BZQ concentration was lower in photocatalysis than in photolysis, showing that the presence of catalysts led to a lower accumulation of this intermediary in solution (results not shown).
Carboxylic acids formed are hard to degrade and usually remain in solution because they are recalcitrant compounds [16,47]. The degradation of many pollutants by the different AOPs resulted in the presence of carboxylic acids. Maleic, fumaric, succinic, glyoxylic, oxalic, and formic acids were identified as end products of the oxidation of phenol in aqueous media by the electro-Fenton process [48]. Maleic, glyoxylic, succinic, and fumaric acids were the predominant carboxylic acids formed in the earlier stages of the treatment. Glyoxylic and succinic acids started to build in the first minutes, reaching a maximum concentration at 2 h. Glyoxylic and succinic acids disappeared, followed by the appearance of formic and oxalic acids as end products before total mineralization. During the degradation of salicylic acid by different electrochemical advanced oxidation processes, the formation of several intermediates was verified, including short-chain carboxylic acids [49]. In this study, it was suggested that α-ketoglutaric and glycolic acids are formed by a different pathway of malic, maleic, fumaric, and tartronic acids. Glycolic acid further transformed into glyoxylic acid. All these acids independently oxidized to oxalic acid as the ultimate by-product, which directly mineralized to CO2. The degradation of beta-blockers by electro-Fenton and solar photoelectro-Fenton treatments also confirmed the destruction of aromatic intermediates by hydroxyl radicals and, consequently, the formation of carboxylic acids [50]. The presence of oxalic and oxamic acids as end by-products was confirmed, contributing to the TOC in the treated final solution.
In most of the reactions, the concentration of carboxylic acids was lower in the presence of a catalyst than in the non-catalytic processes. For instance, in photocatalytic ozonation with H2O2, as shown in Figure 5d, the formation of OXM was always lower in the presence of any one catalyst than in the non-catalytic process, and in the presence of Fe/CNT and CNT, a total removal was observed. On the other hand, OXL concentration was higher in catalytic processes, probably due to the reaction mechanism which favored the formation of OXL during the degradation of SMX and primary intermediates.
The identification and quantification of SO42− and NH4+ ions were carried out in the processes without H2O2 due to the interference of Na2SO3 in the detection method. Ion concentrations increased along time; however, in most cases, their concentration in the non-catalytic processes was higher than in the catalytic treatments. Probably, it occurred due to adsorption of ionic species on the catalyst surface or, in the case of N-based ions, gas phase transfer could occur and ions transformed into N2 or NH3 forms (results not shown) [51].
In the cases where a small final concentration of detected intermediates and large amounts of organic matter (TOC/TOC0) were verified, it is supposed that a different reaction mechanism occurs, leading to the formation of other reaction products not identified in this work and, consequently, not quantified, but that contribute to the TOC amount.

3.4. Replicated and Cyclic Experiments

Duplicate tests and cyclic experiments were performed for the photocatalytic ozonation process, and the results are shown in Figure 6 and Figure 7, respectively.
Three repetitions of photocatalytic ozonation with H2O2 in the presence of CNT were performed following the procedure described in the methodology. The replicated tests demonstrated that the process is reproducible in terms of SMX removal and the small differences observed in the early stages are negligible.
CNT, Fe/CNT, and TiO2/CNT catalysts were selected for cyclic experiments of photocatalytic ozonation. Three cycles were performed, and after each cycle, the final solution was filtered, and the retained catalyst was dried for 24 h at 100 °C. No significant differences were observed in terms of SMX removal as can be seen in Figure 7a,c,e, whereas some differences were observed in terms of TOC removal as shown in Figure 7b,d,f. In the case of CNT, a significant decrease was observed between the first and second cycle, and this decline may be due to the introduction of oxygenated groups on the CNT surface promoted by O3 and/or H2O2 [2,4,7]. Oxygenated groups reduce the electron density on the CNT surface, decreasing O3 decomposition in oxidizing radicals and the degradation of organic pollutants becomes less efficient [12,14]. For Fe/CNT and TiO2/CNT, the differences in TOC removal are less significant over the three cycles which can be explained by the great stability of these materials. In the case of Fe/CNT, the stability of CNT is increased by the formation of Fe–O–C bonds during calcination of the catalyst [39]. The TiO2/CNT composite does not suffer significant surface changes because it has a small content of CNT (15%) and TiO2 is highly stable.

3.5. Toxicity Tests

Toxicity analyses were carried out in all reaction solutions and the results expressed in percentage of inhibition effect. Figure 8 only shows the results obtained in the processes that presented the best performance in terms of TOC removal: photocatalytic ozonation (a), catalytic ozonation with H2O2 (b), and photocatalytic ozonation with H2O2 (c).
Treated solutions by photocatalytic ozonation with CNT and TiO2/CNT showed lower toxicity than the non-catalytic treatment. However, no system that combines ozone and light presented lower toxicity than the initial solution (t = 0 min), leading to the conclusion that the intermediate compounds formed during this process are more toxic to Vibrio fischeri bacteria than the parent compound.
In catalytic ozonation with H2O2, only the treated solution with Fe/CNT presented less toxicity than the initial.
The addition of H2O2 in the photocatalytic ozonation has a crucial role in toxicity reduction. A significant decrease in toxicity was observed in all photocatalytic ozonation processes. The lowest toxicity was observed with the Fe/CNT catalyst that also presented the highest mineralization level (≈100%).
AOPs involve very complex reactions. Although photocatalytic ozonation with CNT presents 93% of mineralization, its final solution had high toxicity (approximately 40% of inhibition effect). On the other hand, catalytic ozonation with H2O2 and Fe/CNT achieved just 76% of TOC removal, a low level if compared with other reactions, even though, it also achieved low toxicity (8% of inhibition effect). This can be explained by different reaction mechanisms that may occur, leading to the formation of other non-detected products. These intermediates may have a small amount of carbon having a low contribution in TOC quantification; however, they can be very toxic.

4. Conclusions

The combination of advanced oxidation processes and catalysts was advantageous for sulfamethoxazole degradation, and the most promising catalysts are CNT and Fe/CNT. Photocatalytic ozonation in the presence of CNT removed all SMX in 15 min and presented high mineralization, removing 93% of TOC after 3 h of reaction. Photocatalytic ozonation with H2O2 in the presence of Fe/CNT totally degraded SMX after 30 min of reaction and showed significant improvements in terms of TOC and toxicity removal, reaching total mineralization and almost complete toxicity removal after 3 h of reaction.
The presence of Fe/CNT in photocatalysis, catalytic ozonation with H2O2, and photocatalytic ozonation with H2O2 reduced the toxicity of the initial solution, probably due to the formation of less toxic intermediates and a high mineralization degree. The reutilization of CNT, Fe/CNT, and TiO2/CNT samples did not change SMX degradation kinetics, but, concerning TOC removal, a significant decrease was observed between the first and second cycle with the CNT catalyst probably due to the introduction of oxygenated groups on the catalyst surface.
The photocatalytic ozonation with CNT quickly degraded SMX and had high mineralization, but the treated solution presented toxic compounds. On the other hand, the photocatalytic ozonation with H2O2 and Fe/CNT achieved full mineralization and low toxicity, which makes additional treatments unnecessary. However, considering economic terms, photocatalytic ozonation with CNT is more advantageous since it is not necessary to add H2O2 and prepare the supported catalyst.

Author Contributions

Conceptualization and supervision, O.S.G.P.S. and C.A.O.; investigation, J.M.; resources, discussion of the results, and review of the final manuscript, M.F.R.P. and J.L.F.; writing—original draft preparation, J.M.; writing—review and editing, O.S.G.P.S. and C.A.O.

Funding

This work is a result of: Project “AIProcMat@N2020—Advanced Industrial Processes and Materials for a Sustainable Northern Region of Portugal 2020”, with the reference NORTE-01-0145-FEDER-000006, supported by Norte Portugal Regional Operational Programme (NORTE 2020), under the Portugal 2020 Partnership Agreement, through the European Regional Development Fund (ERDF); Associate Laboratory LSRE-LCM—UID/EQU/50020/2019 and project POCI-01-0145-FEDER-031337—funded by national funds through FCT/MCTES (PIDDAC).

Acknowledgments

Jessica Martini acknowledges Professor Elvis Carissimi from Departamento de Engenharia Sanitária e Ambiental da Universidade Federal de Santa Maria (UFSM/CT).

Conflicts of Interest

The authors declare no conflict of interest.

References

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Applsci 09 02652 g001 550
Figure 1. TEM image from the Fe/CNT catalyst.
Figure 1. TEM image from the Fe/CNT catalyst.
Applsci 09 02652 g001
Applsci 09 02652 g002 550
Figure 2. Dimensionless SMX (a,c,e) and total organic carbon (TOC) (b,d,f) concentration during catalytic ozonation (O3), photocatalysis (L), and photocatalytic ozonation (L/O3) in the presence of CNT, Fe/CNT, TiO2, and TiO2/CNT.
Figure 2. Dimensionless SMX (a,c,e) and total organic carbon (TOC) (b,d,f) concentration during catalytic ozonation (O3), photocatalysis (L), and photocatalytic ozonation (L/O3) in the presence of CNT, Fe/CNT, TiO2, and TiO2/CNT.
Applsci 09 02652 g002
Applsci 09 02652 g003 550
Figure 3. Dimensionless SMX (a) and TOC (b) concentration during H2O2 catalytic oxidation and adsorption experiments (O2) on CNT, Fe/CNT, TiO2, and TiO2/CNT.
Figure 3. Dimensionless SMX (a) and TOC (b) concentration during H2O2 catalytic oxidation and adsorption experiments (O2) on CNT, Fe/CNT, TiO2, and TiO2/CNT.
Applsci 09 02652 g003
Applsci 09 02652 g004 550
Figure 4. Dimensionless SMX (a,c) and TOC (b,d) concentration during catalytic ozonation with H2O2 (O3/H2O2) and photocatalysis with H2O2 (L/H2O2) in the presence of CNT, Fe/CNT, TiO2, and TiO2/CNT.
Figure 4. Dimensionless SMX (a,c) and TOC (b,d) concentration during catalytic ozonation with H2O2 (O3/H2O2) and photocatalysis with H2O2 (L/H2O2) in the presence of CNT, Fe/CNT, TiO2, and TiO2/CNT.
Applsci 09 02652 g004
Applsci 09 02652 g005 550
Figure 5. Dimensionless concentration of SMX (a) and TOC (b) and evolution of AMI (c), OXM (d), OXL (e), and NO3− (f) concentrations during photocatalytic ozonation with H2O2 in the presence of CNT, Fe/CNT, TiO2, and TiO2/CNT.
Figure 5. Dimensionless concentration of SMX (a) and TOC (b) and evolution of AMI (c), OXM (d), OXL (e), and NO3− (f) concentrations during photocatalytic ozonation with H2O2 in the presence of CNT, Fe/CNT, TiO2, and TiO2/CNT.
Applsci 09 02652 g005
Applsci 09 02652 g006 550
Figure 6. Dimensionless SMX concentration during reproducibility runs of photocatalytic ozonation with H2O2 (L/O3/H2O2) in the presence of CNT.
Figure 6. Dimensionless SMX concentration during reproducibility runs of photocatalytic ozonation with H2O2 (L/O3/H2O2) in the presence of CNT.
Applsci 09 02652 g006
Applsci 09 02652 g007 550
Figure 7. Dimensionless SMX (a,c,e) and TOC (b,d,f) concentration during reutilization experiments of photocatalytic ozonation with H2O2 (L/O3/H2O2) in the presence of CNT, TiO2/CNT, and Fe/CNT.
Figure 7. Dimensionless SMX (a,c,e) and TOC (b,d,f) concentration during reutilization experiments of photocatalytic ozonation with H2O2 (L/O3/H2O2) in the presence of CNT, TiO2/CNT, and Fe/CNT.
Applsci 09 02652 g007
Applsci 09 02652 g008 550
Figure 8. Light emission inhibition of Vibrio fischeri bacteria when submitted to samples resulting from the treatment (after 180 min) of SMX by photocatalytic ozonation (a), catalytic ozonation with H2O2 (b), and photocatalytic ozonation with H2O2 (c).
Figure 8. Light emission inhibition of Vibrio fischeri bacteria when submitted to samples resulting from the treatment (after 180 min) of SMX by photocatalytic ozonation (a), catalytic ozonation with H2O2 (b), and photocatalytic ozonation with H2O2 (c).
Applsci 09 02652 g008
Table
Table 1. Characteristics of sulfamethoxazole (SMX) and intermediate compounds mentioned in this work.
Table 1. Characteristics of sulfamethoxazole (SMX) and intermediate compounds mentioned in this work.
CompoundStructureFormulaM
(g mol−1)		LOD *
(mg L−1)		r2
SMX Applsci 09 02652 i001C10H11N3O3S253.280.080.99989
AMI Applsci 09 02652 i002C4H6N2O98.10.050.99998
BZQ Applsci 09 02652 i003C6H4O2108.090.10.99984
OXM Applsci 09 02652 i004C2H3NO389.050.050.9995
OXL Applsci 09 02652 i005C2H2O490.030.50.99940
* LOD—Limit of detection.
Table
Table 2. Textural properties of the prepared catalysts and crystal properties of TiO2 and TiO2/carbon nanotube (CNT) samples.
Table 2. Textural properties of the prepared catalysts and crystal properties of TiO2 and TiO2/carbon nanotube (CNT) samples.
SampleSBET (m2 g−1)
(±10 m2 g−1)		VP (P/Po=0.95) (cm3 g−1)
(±0.005 cm3 g−1)		% Crystal PhaseCrystal Diameter (nm)
CNT2620.556--
Fe/CNT2520.689--
TiO21340.112Anatase 93%
Rutile 7%		Anatase 8.91
Rutile 14.7
TiO2/CNT1420.164Anatase 97%
Rutile 3%		Anatase 14.6
Rutile 40.7

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MDPI and ACS Style

Martini, J.; Orge, C.A.; Faria, J.L.; Pereira, M.F.R.; Soares, O.S.G.P. Catalytic Advanced Oxidation Processes for Sulfamethoxazole Degradation. Appl. Sci. 2019, 9, 2652. https://doi.org/10.3390/app9132652

AMA Style

Martini J, Orge CA, Faria JL, Pereira MFR, Soares OSGP. Catalytic Advanced Oxidation Processes for Sulfamethoxazole Degradation. Applied Sciences. 2019; 9(13):2652. https://doi.org/10.3390/app9132652

Chicago/Turabian Style

Martini, Jéssica, Carla A. Orge, Joaquim L. Faria, M. Fernando R. Pereira, and O. Salomé G. P. Soares. 2019. "Catalytic Advanced Oxidation Processes for Sulfamethoxazole Degradation" Applied Sciences 9, no. 13: 2652. https://doi.org/10.3390/app9132652

APA Style

Martini, J., Orge, C. A., Faria, J. L., Pereira, M. F. R., & Soares, O. S. G. P. (2019). Catalytic Advanced Oxidation Processes for Sulfamethoxazole Degradation. Applied Sciences, 9(13), 2652. https://doi.org/10.3390/app9132652

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