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. 2018 Jun 18;3(6):6506–6512. doi: 10.1021/acsomega.8b00263

Catalytic Ozonation for the Degradation of 5-Sulfosalicylic Acid with Spinel-Type ZnAl2O4 Prepared by Hydrothermal, Sol–Gel, and Coprecipitation Methods: A Comparison Study

Qizhou Dai †,*, Zhuo Zhang †, Tingting Zhan †, Zhong-Ting Hu †, Jianmeng Chen ‡,*
PMCID: PMC6044642  PMID: 30023951

Abstract

graphic file with name ao-2018-00263h_0009.jpg

This study presents a novel spinel-type zinc aluminate nanometer catalyst and is applied in catalytic ozonation for wastewater treatment. The zinc aluminate (ZnAl2O4) catalysts were synthesized by hydrothermal, sol–gel, and coprecipitation methods, and their characteristics were analyzed by X-ray diffraction, transmission electron microscopy, energy-dispersive X-ray spectrum, Fourier transform infrared, and X-ray photoelectron spectroscopy (XPS) techniques. 5-Sulfosalicylic acid (SSal) was selected as the typical pharmaceutical and personal care product and used to evaluate the catalytic activity of ZnAl2O4. Compared to ozonation, an obviously higher removal efficiency for the SSal degradation was achieved with the nanocatalyst addition in catalytic ozonation. The removal of SSal and chemical oxygen demand reached 64.8 and 46.2%, respectively, after 60 min in the presence of ZnAl2O4, whereas it was only 49.4 and 33.2%, respectively, in ozonation. The comparison of catalysts showed that the ZnAl2O4 prepared by the hydrothermal method presented a better catalytic activity in ozonation. The effect of radical scavenger experiment results and the characterization of XPS implied that •OH was the main active oxidative species in catalytic ozonation. The reusability results showed that the ZnAl2O4 catalyst possessed a high stability and could be widely used in catalytic ozonation for wastewater treatment.

1. Introduction

The pharmaceutical and personal care products (PPCPs) are widespread in aquatic environments, and the pollution of PPCPs has received much attention by the environmental workers. 5-Sulfosalicylic acid (SSal) is a typical PPCP and widely used as the medical intermediate and fine chemical material.1 Because of the poor chemical oxidability and biodegradability, the industrial wastewater containing SSal is difficult to be treated by the conventional biological system. Thus, the effective removal of SSal from wastewater has a significant impact on the environment.

In recent decades, advanced oxidation processes (AOPs) such as ozonation, electrooxidation, photooxidation, and Fenton have been intensively investigated.2−6 AOPs could deal with organic pollutants in water through the formation of •OH (redox potential = 2.8 V ev, SHE), which could react rapidly and nonselectively with nearly all types of organic compounds.7−9 As one of the AOPs, ozonation has been widely applied in wastewater treatment for its strong oxidizing, simple operation, and environmental friendly properties.10 In general, organics degradation by ozonation includes two pathways: direct molecular ozone oxidation and indirect reaction via the decomposition of ozone to generate the hydroxyl radicals (•OH) to attack target pollutants. The direct oxidation with ozone is relatively slow and selective, so it could not remove the pollutants completely, especially some refractory organic compounds.11 Also, direct ozonation may require higher energy and cost in water treatment.12,13 Therefore, catalytic ozonation through indirect oxidation reaction has received considerable research attention.

As compared to homogeneous catalytic ozonation, heterogeneous catalytic ozonation could recycle the catalyst from the reaction solution without producing secondary pollution with solid catalysts, such as metal oxides (e.g., Al2O3, MnO2, CeO2, and TiO2) or supported metal oxides (e.g., Ni/CeO2, Co/Al2O3, and TiO2/Al2O3).12,14,15 Compared with other conventional catalysts, ZnAl2O4 is considered to be a promising ozonation catalyst with the advantages of being nontoxic and inexpensive and possessing good diffusion, high thermal stability, excellent activity, and relatively wide surface area.16−19 These characteristics make it very suitable for the application.

In this work, the ZnAl2O4 catalyst was prepared by hydrothermal, sol–gel, and coprecipitation methods and used in catalytic ozonation of wastewater. SSal was selected as the model pollutant to explore the catalytic performance of three different catalysts. The crystal structure, texture, morphology, size, and chemical form of the surface element and the atomic ratio of catalysts were characterized by X-ray diffraction (XRD), transmission electron microscopy (TEM), energy-dispersive X-ray spectrum (EDX), Fourier transform infrared (FT-IR), and X-ray photoelectron spectroscopy (XPS). In addition, the stability and reusability of the ZnAl2O4 catalyst was also discussed.

2. Results and Discussion

2.1. Characterization of ZnAl2O4

The crystallization phases of prepared catalysts were identified by XRD, which are presented in Figure 1. ZnAl2O4–C, ZnAl2O4–S, and ZnAl2O4–H exhibited the characteristic XRD peaks corresponding to (2 2 0), (3 1 1), (4 0 0), (3 3 1), (4 2 2), (5 1 1), (4 4 0), (6 2 0), and (5 3 3) planes reflection of ZnAl2O4 with a spinel cubic structure (JCPDS no. 05-0669). No impurity phases were observed. After comparison of the three catalysts, the diffraction peaks of ZnAl2O4–S were more intensive and sharper, which demonstrated higher crystallization. On the other hand, the wider peaks of ZnAl2O4–C indicated its smaller particle size. On the basis of Scherrer’s formula,20 the average crystallite sizes of ZnAl2O4–C, ZnAl2O4–H, and ZnAl2O4–S were calculated to be ca. 12, 14, and 25.3 nm, respectively, by full width at half-maximum intensity of the (3 1 1) plane of the ZnAl2O4 phase.

Figure 1.

Figure 1

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XRD patterns of ZnAl2O4 samples.

TEM and selected area electron diffraction (SAED) analysis are effective methods to identify the morphologies of the catalyst, whose results are in good accordance with XRD results.21Figure 2a–d showed the TEM micrographs of ZnAl2O4. It could be seen that the particle size distribution of three catalysts was very narrow, and the size was measured by a digital micrograph.22 The nanoparticle sizes of ZnAl2O4–C, ZnAl2O4–H, and ZnAl2O4–S varied from 11–14, 14–23, and 18–28 nm, respectively. A high-resolution TEM micrograph (inset in Figure 2d) of ZnAl2O4–H showed a lattice fringe of distance of about 0.247 nm corresponding to the (3 1 1) plane of the cubic zinc aluminate structure from XRD. Furthermore, the SAED pattern, presented in Figure 2e, exhibits the diffraction rings with d-spacings about 0.284, 0.247, 0.203, 0.156, and 0.142 nm, which are assigned to (220), (311), (400), (511), and (440) planes of the spinel phase, respectively. The same conclusion was drawn from ZnAl2O4–C and ZnAl2O4–S. EDX was used to analyze the element or chemical characterization of the catalyst qualitatively.10Figure 2f gave the EDX pattern of ZnAl2O4 samples. Clearly, the prepared catalyst samples were composed of Zn, Al, and O.

Figure 2.

Figure 2

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TEM micrographs of ZnAl2O4 samples: (a) ZnAl2O4–C; (b) ZnAl2O4–H; (c) ZnAl2O4–S; (d) high-resolution TEM micrograph of ZnAl2O4–H; (e) SAED pattern of ZnAl2O4–H; and (f) EDX pattern of ZnAl2O4–H.

The pHpzc could be used to determine the catalytic property. In this work, we obtained the pHpzc by the pH drift method. When pH < pHpzc, the hydroxyls groups at the surface of the catalyst become protonated and has a positive charge. On the contrary, when pH > pHpzc, the hydroxyl groups at the surface of the catalytic become deprotonated and have a negative charge. From Figure 3, the pHpzc values of 8.00, 7.13, and 7.00 for ZnAl2O4–H, ZnAl2O4–S, and ZnAl2O4–C were obtained, respectively. The surface hydroxyl groups were analyzed, which could promote the generation of •OH from aqueous ozone.23 For ZnAl2O4–H, ZnAl2O4–S, and ZnAl2O4–C, the densities of surface hydroxyl groups were 3.2, 2.5, and 2.3 mmol/g, respectively.

Figure 3.

Figure 3

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pHpzc of ZnAl2O4 samples.

2.2. Catalytic Activity of ZnAl2O4

SSal was used to be the target pollutant to evaluate the catalytic activity of ZnAl2O4 samples. The removal of SSal and chemical oxygen demand (COD) was investigated by ozonation degradation of SSal, and the results are presented in Figure 4. Figure 4a showed the efficiency of SSal removal in ozonation and catalytic ozonation with ZnAl2O4–H. After 60 min, the removal rate of SSal reached 64.8% in catalytic ozonation with ZnAl2O4–H, while it was only 49.4% in ozonation. Almost no pollutant was adsorbed on the ZnAl2O4–H surface with the results of adsorption experiments. Figure 4b showed the SSal removal in the presence of different ZnAl2O4 samples. All the three prepared samples demonstrated good catalytic activity for degradation SSal. The removal rate of SSal was 59 and 61.7% in catalytic ozonation for ZnAl2O4–C and ZnAl2O4–S, respectively.

Figure 4.

Figure 4

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SSal degradation efficiency with different processes (a) and with different catalyst samples (b), COD removal rate with different catalyst samples and the insertion shows the fitting results (c). Experimental conditions: initial SSal concentration: 500 mg/L, initial pH = 7.0, ozone dose: 5.0 mg/min (a,b) and 10.0 mg/min (c), catalyst dose: 0.2 g/L.

Figure 4c shows the results of COD removal using various ZnAl2O4 samples. It could be found that the COD was removed only by 33.2% with ozonation after 60 min, while it reached 36.6, 38.8, and 46.2% in the presence of ZnAl2O4–C, ZnAl2O4–S, and ZnAl2O4–H, respectively. On the basis of kinetic analysis, it was found that the results of COD removal were followed the pseudo-first order reaction.11 When ZnAl2O4–H was added, the pseudo first-order rate constants increased from 6.3 × 10–3 to 10.4 × 10–3 min–1 compared with ozonation (inset in Figure 4c). The results demonstrated that ZnAl2O4 displayed a good catalytic performance compared to ozonation for the degradation of SSal. Moreover, the effect of ZnAl2O4–H was better than ZnAl2O4–C and ZnAl2O4–S for both the removal of SSal and COD. According to the characterization results of ZnAl2O4 with the surface properties, it was found that the catalytic activity of ZnAl2O4 was positively related to the density of surface hydroxyl groups. Therefore, surface hydroxyl groups would be the critical factor to investigate active oxidative species in catalytic ozonation.

2.3. Investigation of Active Oxidative Species

The active oxidative species played an important part in the catalytic ozonation of SSal with ZnAl2O4, which enhanced the SSal removal and mineralization of organics. On the basis of the reaction mechanism of heterogeneous catalytic ozonation,10 a stronger hydroxyl radical scavenger of tert-butyl alcohol (TBA, 50 mmol/L) was used to verify the formation of •OH because of aqueous ozone decomposition in the presence of ZnAl2O4 and participated in the reaction with catalytic ozonation.24 TBA reacted with •OH rapidly and suppressed the chain reaction.25Figure 5 shows that the removal rate of SSal was decreased greatly in the ozonation/ZnAl2O4 when TBA was added. The result indicated that more •OH was formed in the presence of ZnAl2O4, and it played a crucial role as the active oxidative species for degradation of SSal.

Figure 5.

Figure 5

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Effect of radical scavenger TBA on catalytic ozonation of SSal.

Figure 6 shows the FT-IR spectra of the synthesis of ZnAl2O4 by the three methods. FT-IR is an appropriate technique to investigate the chemical adsorption or interaction.26 The band could be seen at around 3451 cm–1 corresponding to the stretching vibrations of −OH groups, which was contributed by the coordinated water.27,28 As the −OH group’s peak of ZnAl2O4 prepared by the hydrothermal method (ZnAl2O4–H) was stronger than the other two, which indicated that the ZnAl2O4–H had a higher density of surface −OH groups. The band at around 1632 cm–1 was present in all the samples, which could be assigned to the H–O–H bending vibrations of the adsorbed water molecule. The band at 1382 cm–1 was presented in the ZnAl2O4–H alone, which was the OH group in the metal alkoxides.29 In all the samples, the bands at around 666, 558, and 506 cm–1 were assigned to stretching and bending modes of the Al single bond O of octahedral AlO6 units; this suggested that the normal spinel-type ZnAl2O4 structure was formed.

Figure 6.

Figure 6

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FT-IR patterns of ZnAl2O4 samples.

The chemical composition and relative content of the surface element for environmental material are important to the effects in application of wastewater treatment.30−32 Therefore, XPS analysis was carried out to explore the characteristics of the ZnAl2O4 surface (Figure 7). The wide XPS spectra of ZnAl2O4 contained elements of Zn, Al, O, and C (Figure 7a), in which the presence of the carbon C 1s peak at 284.6 eV was mainly used to calibrate the binding energies of other elements. Figure 7b–d presents the O 1s spectra of the three catalysts with high resolution. In addition, they were fitted by Gauss–Lorentzian peak shapes with the nonlinear least-squares fit program. The results displayed three peaks with binding energies at about 530.0, 531.1, and 532.5 eV. The signal at 530.0 eV possibly comes from AlOx (Osite1, Al in the AlO6 octahedral site or AlO4 tetrahedral site).33 The peak at 531.1 eV can be ascribed to lattice oxygen (Osite2) in the ZnAl2O4 crystal lattice.34 Notably, the peak at 532.5 eV was assigned to surface-adsorptive hydroxyl oxygen species (Osite3). The relative content of Osite3 of catalyst samples can be calculated by the fitted peak area presented in Table 1.30 It was shown that the percentage of Osite3 for ZnAl2O4–H was 11.57%, which was higher than those of ZnAl2O4–S (8.6%) and ZnAl2O4–C (8.18%). Also, the Osite3 is taken as the initiators for •OH generation,35 and it plays an important role in the ozonation process. Thus, the analysis of XPS demonstrated that •OH could be the active oxidative species in the presence of ZnAl2O4. Furthermore, the ZnAl2O4–H which possesses the most percentage of Osite3 has a better catalytic activity.

Figure 7.

Figure 7

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Representative XPS characterization of ZnAl2O4 samples, wide spectrum (a); O 1s spectrum (b–d).

Table 1. Gaussian Fitting XPS Results of Osite3 for Catalyst Samples.

fitting parameter ZnAl2O4–H ZnAl2O4–S ZnAl2O4–C
B.E (eV) 532.37 532.43 532.5
area 530 332 310
rel. content (%) 11.57 8.60 8.18
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2.4. Catalyst Reusability

The reusability of the catalyst is an important parameter for the consideration of practice application in the future.36 To investigate the reusability of catalyst samples, a specific experiment was carried out to recycle the ZnAl2O4–H three times under identical conditions. The catalyst particles were separated with reaction solution by sediment and centrifugation, and then they can be collected for a new cycle. As shown in Figure 8, the removal efficiency of SSal was found to be 64.8–59.7% after being reused three times of catalyst, which indicated that the catalytic activity of ZnAl2O4–H was not significantly changed after cycling. The results suggested the high reusability and stability of ZnAl2O4 catalysts in the water treatment.

Figure 8.

Figure 8

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Degradation efficiency of SSal by ZnAl2O4–H for three times in ozonation.

3. Conclusions

In this paper, nanocrystalline ZnAl2O4 was prepared by hydrothermal, sol–gel, and coprecipitation methods. In addition, the catalysts were applied in ozonation for the degradation of pollutants. In the presence of three catalyst samples, the degradation of SSal was significantly enhanced compared to ozonation alone. Furthermore, the ZnAl2O4–H which was prepared by the hydrothermal method possessed the simplest operation with one step and displayed better catalytic activity in catalytic ozonation. Notably, some characterizations of ZnAl2O4, such as FT-IR and XPS, indicated that the surface of hydroxyl groups was the key during the degradation experiments. In addition, surface hydroxyl groups of the catalyst were regarded as the active sites for the generation of •OH. Accordingly, the experiment of adding TBA was done, which demonstrated that •OH was the active oxidative species in catalytic ozonation with ZnAl2O4. On the other hand, ZnAl2O4–H showed good recyclability by reusing the catalyst samples. This study could provide a method for novel catalyst preparation and determine the potentially promising applications of ZnAl2O4 in catalytic ozonation of wastewater treatment.

4. Experimental Section

4.1. Chemicals

SSal was selected as the model pollutant, and it was obtained from J&K scientific Co., Ltd. Zinc nitrate hexahydrate [Zn(NO3)2·6H2O] and aluminum nitrate nonahydrate [Al(NO3)3·9H2O] were purchased from Aladdin Reagent (China) Co., Ltd. Ammonium iron sulfate dodecahydrate [(NH4) Fe(SO4)2·12H2O] was purchased from Shanghai Macklin Chemical Reagent (China) Co., Ltd. TBA was chosen as the radical scavenger and purchased from Nanjing Chemical Reagent (China) Co., Ltd. The urea was obtained from Sinopharm Chemical Reagent Co., Ltd. Other reagents used in the work were of analytical grade. Ultrapure water was used in the research from Mili-Q water (18.2 MΩ cm in resistivity).

4.2. Preparation of ZnAl2O4

Three nanocrystalline ZnAl2O4 catalysts were synthesized by hydrothermal, sol–gel, and coprecipitation methods.

Hydrothermal Method

Zn(NO3)2·6H2O (8 mmol), Al(NO3)3·9H2O (16 mmol), and urea (0.16 mol) were added into a 160 mL of mixture solvent of water and ethanol (v/v = 1:1) with magnetic stirring. After dissolving completely, the clear solution was transferred into a 200 mL Teflon-lined stainless autoclave and heated at 180 °C for 24 h. When it cooled to room temperature, the supernatant catalyst was filtered by centrifugation, and then it was washed with ethanol and ultrapure water until the pH value got to neutral. The obtained catalyst was dried at 80 °C and denoted as ZnAl2O4–H.

Sol–Gel Method

Zn(NO3)2·6H2O (8 mmol) and Al(NO3)3·9H2O (16 mmol) were dissolved in 80 mL of ultrapure water, and then a mixture of metal nitrate (M1) was obtained. Then, the citric acid was dissolved in ultrapure water (M2), with the molar ratio of citric acid and the metal ions being 2:1. Then, M1 was added dropwise into M2 while stirring continuously. After 10 min of stirring, the solution was heated at 70 °C in a water bath until the sols were formed. The transparent thick gels were formed and then maintained at 150 °C for 2 h to obtain a fluffy polyporous powder. After grinding, the abovementioned powder was calcined at 700 °C for 8 h in the muffle furnace and then annealed at 400 °C for 3 h; it is denoted as ZnAl2O4–S.37

Coprecipitation Method

Zn(NO3)2·6H2O (8 mmol) and Al(NO3)3·9H2O (16 mmol) were dissolved in 10 mL of ultrapure water, wherein the molar ratio of Zn/Al was 1:2, and the two solutions were mixed sufficiently. Then, the aqueous ammonia solution (25 wt %) was dropped into the abovementioned solution, and the mixture was stirred fully until complete precipitation. The precipitate was filtered by centrifugation, washed with deionized water and ethanol, and dried at 80 °C. Then, the dry product was calcined at 700 °C for 8 h and denoted as ZnAl2O4–C.

4.3. Characterization of ZnAl2O4

The composition and phase of samples were determined by XRD with Cu Kα radiating (Rigaku D/MAX 2500 PC) under the condition of 40 kV voltage, 300 mA tube current, and continuous scan mode sampling. The scan speed was 4° min–1 with a range of 10°–90°. The morphologies and size of catalysts were characterized by TEM. For preparing the samples of TEM, the powder of the catalyst need to be dispersed by ethanol and then drops of each samples placed on a copper grid. Element composition of samples was investigated by EDX. The FT-IR spectrum was recorded on a Nicolet Magna-IR 6700 infrared spectrometer. The XPS was analyzed using a PHI5700 spectrometer.

The density of surface hydroxyl groups of catalysts was measured by a saturated deprotonating method.38 The procedure was as follows: 0.3 g of ZnAl2O4 was added to 50 mL of 2–100 mmol/L NaOH solution, and the suspensions were shaken at 25 °C for 24 h.

The pH at the point of zero charge (pHpzc) of catalysts was determined by a pH drift method.39 The 0.1 M NaCl solution was prepared as an electrolyte, and N2 was bubbled through the solution to expel the dissolved CO2. Then, the pH was adjusted to successive initial values by NaOH and HNO3 as pHi. After that, the ZnAl2O4 (0.1 g) was added to the solution. These suspensions were shaken for 24 h with the temperature at 25 °C. The final pH was measured by a pH meter called pHf and using the equation of ΔpH = pHf – pHi to calculate a series of ΔpH. ΔpH was plotted against the initial pH. The pH at which the curve crosses the X-axis is taken as the pHpzc.

4.4. Experimental Procedures

The degradation experimental equipment of SSal consisted of a cylindrical pyrex glass reactor, an ozone generator (CFY-3, Hangzhou Rongxin Electronic Equipment Co., Ltd., China), a mass flowmeter, and an exhaust treatment system. The ozone reactor consists of three parts with inner pipe, outer pipe and pedestal, and an ozone diffuser fixed in the bottom. When the reaction started, as ozone was diffusing, the wastewater and catalyst were flowed circularly between the two pipes, which formed a system of a circulating fluidized bed. The initial concentration of SSal is 500 mg/L, 1.5 L of SSal solution, and 0.30 g of catalyst was added into the reactor, and then ozone was bubbled from the bottom continuously. To test the performance of ZnAl2O4, other experiments were carried out without the catalyst and absorption on the catalyst under the same condition. In addition, x, the dosage of ozone, was controlled by adjusting the mass flowmeter, the pH of SSal solution was adjusted by HCl and NaOH, and pH was adjusted in 7.0 with ozonation and catalytic ozonation. All the tests were performed three times, and the final results were averaged.

The concentration of SSal was analyzed by adding ferric ion in excess, for SSal can react with the ferric ion to form the colored metal complex of [Fe(SSal)]3+, which presents characteristic absorbance at 500 nm.40 Before measuring, the pH value of samples was adjusted to lower than 2.5 by 0.01 mol/L HClO4. The absorbance of [Fe(SSal)]3+ was measured via a Hach UV–vis spectrophotometer (Hach DR6000, USA).

The COD is CODcr and it was analyzed by the fast digestion spectrophotometric method. The samples were digested at 150 °C for 2 h, and the absorbance was determined at 440 nm by the Hach UV–vis spectrophotometer.

Acknowledgments

The authors are grateful for the financial support provided by the Basic Public Projects of Zhejiang Province (LGJ18E080001) and National Natural Science Foundation of China (21306175).

The authors declare no competing financial interest.

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