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International Journal of Photoenergy
Volume 2019, Article ID 1540271, 11 pages
https://doi.org/10.1155/2019/1540271
Research Article

Photocatalytic Degradation of 2,4-Dichlorophenol by TiO2 Intercalated Talc Nanocomposite

Zhejiang University, Marine Science Department, Zhoushan 316000, China

Correspondence should be addressed to Pingping Zhang; moc.qq@110niram

Received 12 October 2018; Revised 11 January 2019; Accepted 4 February 2019; Published 3 March 2019

Academic Editor: K. R. Justin Thomas

Copyright © 2019 Manqing Ai et al. This is an open access article distributed under the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.

Abstract

Novel nanocomposites have been prepared by intercalating TiO2 nanoparticles into talc. The nanocomposites have been verified by X-ray diffraction (XRD) from the appearance of a characteristic diffraction peak of TiO2. Thermal behavior of the prepared samples is examined by thermogravimetric analyzer (TGA), scanning electron microscope (SEM), and energy dispersive spectrometer (EDS), which have shown no TiO2 particles on the surface of the talc. The TiO2 particles are found in the layers of talc by transmission electron microscopy (TEM) and the Brunauer-Emmett-Teller (BET) method, which have shown the increase of specific surface areas and total pore volumes and the decline of average pore diameters. As the strong adsorption ability of talc can intensify the power of photon absorption and capture-recombination carriers, more than 99.5% of 2,4-dichlorophenol can be degraded in 1 h by the nanocomposite under an ultraviolet lamp in neutral solution and room temperature after reaching adsorption equilibrium, and the result of adsorbance is in accord with the first-order kinetic. The degradation rate was maintained at about 99% after 20 times. Therefore, the prepared talc/TiO2 nanocomposite is an efficient, stable, and recyclable material for wastewater treatment.

1. Introduction

Phenolic compounds have been widely used in industrial and agricultural manufacture and are ranked as one of the most harmful and extensive organic contaminants [1]. Among the phenolic compounds, the chlorophenols can cause deterioration of water quality and may threaten human health and survival of other organisms [2, 3]. As one of the most widely used chlorophenols, 2,4-dichlorophenol (2,4-DCP) can produce hazardous secondary pollution [49]. It has been demonstrated that while 2,4-DCP can be decomposed by a variety of methods, the degradation efficiency is low. For example, Luo et al. have shown that 6.8 mg 2,4-DCP was degraded by ZnO in 1 h in UV light [10]; Li et al. have shown that 29 mg 2,4-DCP was degraded by nanobamboo charcoal in 1 h [2]; Mohammadi and Sabbaghi prepared MWCNT (multiwall carbon nanotubes)/TiO2 which takes 2 hours to transform about 47 mg 2,4-DCP into harmless substance in 1 L alkaline solution [11]; Yang and coworkers made TiO2 film which degrades only about 5.5 mg 2,4-DCP in 2 hours [12]. So a safe, efficient, and environment friendly way to degrade 2,4-DCP is required.

TiO2 has superior photocatalytic performance due to its strong oxidizing ability, nontoxicity, and long-term stability of photochemistry [1217]. Among the various crystalline structures of TiO2, anatase is confirmed to be the most active photocatalyst, which has been a research focus to degrade the pollutants therefore [18]. Medical talc also possesses the characteristics of talc such as chemical stability, good flame resistance, and strong adsorption and is shiny white, nontoxic, and nonpolluting after undergoing purification from raw talc [1922]. Talc can intensify the power of photon absorption and capture-recombination carriers due to its strong adsorption ability, which may thus improve the photocatalysis of TiO2 [16]. Talc has been used to produce a kind of nanocomposite to degrade dye [23], and talcum powder is in widespread use in plastics and coatings [2426]. These show that talc can improve the efficiency of photodegradation of 2,4-DCP and reduce the cost of wastewater treatment when used in the production of plastics or metal coatings.

In order to improve the purification efficiency of wastewater and promote the application of the talc in photocatalysis, we prepared TiO2/medical talc nanocomposites under two different temperature conditions through the full-scan UV–Vis absorption spectra and total organic carbon (TOC) analyzer, establishing whether the benzene ring was decomposed and confirming that 2,4-DCP was mineralized into inorganic substances. Finally, the photocatalytic stability of the nanocomposite was verified by repeated trails.

2. Materials and Method

2.1. Chemical and Materials

Medical talc obtained from talc powder plant of You County, Hunan Province, China, with a particle size of 38 μm, was used without further purification. Tetrabutyl titanate (TNBT) was purchased from Aladdin Industrial Co., Ltd., Shanghai, China. Absolute ethyl alcohol (analytical reagent grade) and 2,4-dichlorophenol (2,4-DCP, ≥99%) were purchased from Sinopharm Chemical Reagent Co., Ltd., Shanghai, China. Deionized water with a resistivity of 18.2 mΩ was used for preparing aqueous solutions.

2.2. Preparation of TiO2-Medical Talc Nanocomposites

The medical talc (50 g) was dried at 80°C for 8 h and was marked as MT. TNBT solution was added dropwise into absolute ethanol with stirring for 2 h; distilled water was added into the mixture dropwise until there was no sedimentation. The obtained product was named as HTO.

50 g of TNBT solution was mixed with 10 g of MT in a mortar, and the mixture ground till it became pasty, and dried after cleaning to acquire intercalating composite, T-H. All three samples were calcined at 400°C for 2 h at a heating rate of 2°C min-1. The products were labeled as T-400, H-400, and T-H-400, respectively, [23]. The sample list is shown in Table 1.

Table 1: The list of samples that were prepared during each stage.
2.3. Characterization

X-ray diffraction (XRD) spectra of samples were examined by a Rigaku D/Max 2550 X-ray Diffractometer (Japan) using Cu Kα radiation () at 450 mA and 60 kV. Thermal behavior of the prepared samples was examined by thermogravimetric analyzer (TGA) model Precisa DSC3+ (Switzerland) from 50°C to 700°C. The microstructures and the energy dispersive spectra (EDS) of the samples were observed through an SU-8010 scanning electron microscope (SEM, Japan). The microstructures of the samples were observed using transmission electron microscopy (TEM) (JEM-2100PLUS, JEOJ). The BET surface area and pore characteristics were analyzed by using nitrogen adsorption-desorption (AUTOSORB-IQ-MP, USA) at 77 K. The total organic carbon (TOC) content was analyzed by ASI-L TOC analyzer (Shimadzu, Japan).

2.4. Photocatalytic Performance

For the adsorption experiment, the mixture (50 ppm 2,4-DCP solution and 2 g·L-1 sample) was stirred vigorously in darkness. After 25 min, the platform of 2,4-DCP solution removal was reached indicating that an adsorption/desorption equilibrium has been achieved. The mixture was then irradiated with a 250 W high-pressure mercury ultraviolet (UV) lamp (main emission wavelength: 365 nm, intensity: 327.3 kJ·mol-1, Shenzhen Guyou Special Light Source Co., Ltd., China) for certain times. After the UV irradiation, the mixture was centrifuged, and its absorbance was analyzed by using a UV–Vis spectrophotometer (Shimadzu UV-2550, Japan) at a wavelength of 283 nm [12], and the degraded solution was analyzed by ASI-L TOC analyzer (Shimadzu, Japan). The repeated trials proceeded at the same condition: add 2 g L-1 T-H-400 into the initial 50 ppm 2,4-DCP solution, turn on the UV lamp after reaching the adsorption equilibrium, and photodegrade the initial solution for 1 h, then obtain the liquid sample and dry the T-H-400 for the next repetitive degradation. Removal rate and relative removal rate are calculated according to the following equations: where , , , and are the initial 2,4-DCP concentration, the 2,4-DCP concentration after degradation, the 2,4-DCP concentration after adsorption under dark, and the 2,4-DCP concentration after photodegradation, respectively. All experiments were carried out three times, and the average values and standard errors were then used.

3. Results and Discussion

3.1. Characterization of the TiO2/Medical Talc Nanocomposite

Figure 1 shows the XRD spectra of the samples. From the XRD results of MT and T-400, shown in Figures 1(a) and 1(b), respectively, we found that after calcination, the crystallite size increased slightly (MT: 337 nm, T-400: 374 nm). The difference between MT and T-400 suggests that the calcination reduced the crystallinity of the talc, although the reduction was not significant. The weak characteristic peak of anatase appeared at 2 in the HTO which indicates that the TiO2 has been generated after hydrolyzing the TNBT [2730]. As the temperature of the calcination rose, the crystallite size increased in H-400 (HTO: 86 nm, H-400: 124 nm), which means the crystallinity of anatase was improved. Comparing the ratios of the intensity peaks of MT and T-H at 2 and 28.6°, the ratio has declined (MT: 0.599, T-H: 0.261), which indicates the number of crystal lattices has decreased in the talc, due to the insertion of TiO2 (diameter 5 nm) between the layers of the talc lattice. The crystallite size of T-H also declined to 273 nm compared with MT. After calcination, the T-H-400 has similar variation with T-H compared with T-400; it has also decreased the ratios of the intensity peaks of T-400 and T-H-400 at 2t and 28.6° (T-400: 0626, T-H-400: 0.353), and the crystallite size of T-H-400 also declined to 142 nm compared with T-400 [31, 32]. From the results, it can be concluded that, by the reason of the lower atomic radius of TiO2, the number of crystal lattices decreased in the talc when TiO2 is inserted into the layers of talc, and there is no chemical reaction when intercalating the TiO2 into the medical talc [33, 34].

Figure 1: XRD spectra of samples ((a) XRD spectra of samples: MT, HTO, and T-H; (b) XRD spectra of samples: T-400, H-400, and T-H-400).

Figure 2 shows the TG curves of all samples. The thermogram can be divided into three stages. In the first stage, there is a heat release from all samples, due to the evaporation of bound water (desorption of water physically bound to the surface), around 60°C to 80°C. The second stage is divided into two kinds of behavior, depending on the nature of the sample: one kind is around 240°C to 260°C; there are distinct heat release peaks in the two kinds of TiO2 (HTO and H-400) and nanocomposites (T-H and T-H-400), generated by the oxidation of TNBT and other hydrolytic organic matter (the residue during the preparation of samples); the other kind of behavior is due to two types of talc (MT and T-400) and nanocomposites; the small but discernible heat release is at about 510°C (nanocomposites) and 560°C (talc), due to the evaporation of bound water which exists in the layers of talc. The third stage is also divided similarly to the second stage: the first kind of behavior relates to the two kinds of TiO2 and nanocomposites, with a weak heat release peak around 540°C to 580°C, ascribed to the lattice deformation of TiO2; the second is attributed to the oxidation of hydroxide radical of talc; subtle heat release peak shows up around 580°C to 590°C [35, 36].

Figure 2: TG curves of all samples.

The morphology of samples is displayed in Figures 3 and 4. The SEM pattern of MT and T-400 (Figures 3(a) and 3(b)) reveals that the medical talc has laminar structure and the layers are more compact in the T-400 compared with MT because high temperature can cause expansion of the laminar structure. Figures 3(c) and 3(d) depict the SEM patterns of HTO and H-400; the result shows that the laminar structure has appeared in H-400, which is different from HTO which has globular structure. Also, H-400 has a better degree of crystallinity which benefits from the reinforcement by the crystal structure of anatase [21]. Figures 4(a)4(d) depict the SEM patterns of T-H and T-H-400, respectively, at different magnifications; few globular features due to TiO2 appear on the surface of the layer, indicating that most of the TiO2 is intercalated within the talc lattice.

Figure 3: SEM images of (a) medical talc (MT), (b) medical talc after calcining at 400°C (T-400), (c) hydrolyzing TiO2 (HTO), and (d) TiO2 after calcining at 400°C (H-400).
Figure 4: SEM images of (a, b) medical talc intercalated with TNBT (T-H) and (c, d) medical talc intercalated with TNBT after calcining at 400°C (T-H-400).

Figure 5 represents the EDS spectrum of the nanocomposites. From the results, we find that the content of Ti is 0.73% in the T-H and 13.73% by weight in the T-H-400. The maldistribution of TiO2 in the layer of talc contributes to the different content of Ti in the composites. Comparing with the results of SEM, there is little TiO2 on the surface of layers of medical talc; hence, we can conclude that the nanocomposites have been prepared successfully.

Figure 5: EDS spectrum of the nanocomposites ((a) T-H; (b) T-H-400).

The microstructures of the samples are shown in Figure 6. We find no distinct difference between MT and T-400 (regular laminar structure without globular nanoparticles), conforming with the results of XRD and SEM. After intercalating the TiO2, there are many tiny TiO2 nanoparticles (about 6 nm) without different kind of lattice fringe in the TEM image of nanocomposites, shown in Figures 6(c) and 6(d), indicating that the TiO2 particles exist between layers and not on the surface of talc. More important, the obvious lattice fringe can be found in Figure 6(d), indicating that the samples possess high crystallinity. Photocatalytic activity of talc is expected to be enhanced by the uniform dispersion of TiO2 nanoparticles in the layers of talc [28]. This is consistent with the XRD and SEM results and suggests that the TiO2 has intercalated into the layers of talc.

Figure 6: TEM images of all samples ((a) MT; (b) T-400; (c) T-H; (d) T-H-400).

Figure 7(a) shows the nitrogen adsorption-desorption isotherms of all samples. According to the hysteresis loops and curves, the nitrogen sorption curves of talc (MT and T-400) and TiO2 (HTO and H-400) show type III and type V isotherm, respectively [37]. When the talc was intercalated with TiO2, the isotherm type then changed to type V and the type of hysteresis loop which is H3 appeared (T-H and T-H-400) [38]. The changes represent the intercalation of TiO2 nanoparticles within the layers of talc that has formed slit-type holes. From the pore diameter distribution curves of all samples shown in Figure 5(b), the dominant pore diameters of T-H and T-H-400 have changed to 6 nm and 8 nm, while the mesopores (>15 nm) have disappeared compared with MT and T-400. The changes of nanocomposites are due to the insertion of TiO2, which has lower pore diameters between layers of talc.

Figure 7: (a) Nitrogen adsorption-desorption isotherms for all samples; (b) pore diameter distribution curves of all samples.

The specific surface areas (), total pore volumes (), and average pore diameter () of the samples are listed in Table 2. From the results, after calcination, there are slight changes in T-400 and H-400, compared with MT and HTO, respectively, which may result in their similar adsorption performance. However, after calcination, T-H-400 has larger average pore diameter (9.10 m) than T-H (2.74 nm) while their total pore volumes are similar, and this may contribute to the higher adsorption capacity of T-H-400 [23]. On account of the intercalation of TiO2, the and of nanocomposites (T-H and T-H-400) have increased and the average pore diameter has declined compared with talc (MT and T-400), which may result in a decrease of the adsorption capacity. As a result, the differences in BET between talc and nanocomposites can further verify that the TiO2 has been intercalated into talc successfully.

Table 2: Specific surface area () of the samples.
3.2. Photocatalytic Performance

In order to examine the photocatalytic degradation capacities of the TiO2/medical talc for 2,4-DCP, all samples were tested in the dark to first obtain the adsorption data. The plateau of adsorptions of the 2,4-DCP of all samples was reached after 25 min, indicating that they have reached the adsorption equilibrium. From Figure 8, the maximum adsorption rates were 77.8% for MT and 75.6% for T-400 due to their larger average pore diameters. Sample HTO showed better adsorption ability than H-400 due to its larger specific surface area and total pore volume. Sample T-H has lower adsorption rate, being only 2%, compared to 21.9% for T-H-400, because of its lower average pore diameters and the larger atom of 2,4-DCP, corresponding with the result in Figure 5(b) and Table 2 (almost all pore diameters of T-H are smaller than 3 nm).

Figure 8: The effect of the adsorption on the degradation of 2,4-DCP solution by all samples in the dark.

Figure 9 denotes the full-scan UV–Vis absorption spectrums of 2,4-DCP solution after treatments by all samples. After arriving the adsorption equilibrium, the absorption peak of 2,4-DCP has changed from 283 nm to 243 nm by MT and T-400 in the dark. The blue shift may be caused by the decrease of pH in the solution, as the 2,4-DCP is low-acid ion compound, and the H+ of 2,4-DCP in the solution has increased with the proceed of adsorption. Another reason may be because the –Cl has dropped off the ben zing, the generation of phenol, or other organics with ben zing [24, 39, 40]. When the TiO2 intercalated into the layers of talc, there is great removal of 2,4-DCP without blue shift at 283 nm, which means that the pollutants were not only physical adsorption but also were degraded, even though, it cannot reach the environmental target.

Figure 9: Full-scan UV–Vis absorption spectrums of 2,4-DCP solution after treatments by all samples. Initial 2,4-DCP concentration: 50 mg L-1.

From the results shown in Figures 8 and 9, it can be concluded that without the addition of photocatalysis, adsorption capacity of medical talc, TiO2, and nanocomposites cannot achieve the target of degrading most of the pollutant without secondary pollution in a short time [41].

After reaching the adsorption equilibrium, the UV lamp was turned on to examine the photocatalytic performance of the samples. From Figure 10, which shows the photodegradation rate of 2,4-DCP solution in 1 h for all samples, the MT and T-400 appear the alike in photocatalytic capacity; however, the relative removal rate is negative because of the red shift in the characteristic peak of 2,4-DCP shown in Figure 10. The H-400 has higher degradation rate -82.5% compared with 59.3% for HTO, attributed to the better anatase structure. The degradation rates of T-H and T-H-400 are 66.3% and 99.5%, respectively, and they have better photocatalytic power than talc (MT and T-400) and TiO2 (HTO and H-400) at the same temperature. Among all the samples, the maximum 2,4-DCP removal rate was generated by T-H-400.

Figure 10: Photodegradation rate of 2,4-DCP solution for 1 h by all materials. Total absorption is in accordance with equation (1). Relative absorption is in accordance with equation (2).

Figure 11 shows the full-scan UV–Vis absorption spectra of 2,4-DCP solutions after treatments by all samples for 1 h, and the absorption peak has changed from 243 nm to 255 nm compared with the characteristic peak of 2,4-DCP concentration after absorption by MT and T-400. The red shift is because the temperature of solution has increased with the lighting of lamp, and the pH has increased due to the combination of H+ and C6H6Cl2O-24, 40. In summary, the photodegradation of the medical talc fails to achieve the expectation which will not cause secondary pollutant.

Figure 11: The full-scan UV–Vis absorption spectra of 2,4-DCP solutions for all samples after photodegradation by for 1 h.

Apart from the medical talc, which has little or no photocatalytic ability on its own, the time dependence of the removal rates of the 2,4-DCP by T-H-400, T-H, H-400, and HTO are shown in Figure 12. Initially, there was a slight decrease in removal by T-H because of the effect of the evaporation of the water and the desorption of the material, whereas the degradation rates of other three samples increased continuously. From 40 min to 60 min, the T-H showed a major increase in the degradation of the pollutant, while H-400 was surpassed and became the last one. The leap is because the 2,4-DCP solution began to degrade under the UV lamp without photocatalysis, which resulted in a blue shift of the absorption peak (from 283 nm to 222 nm); similar with the dark adsorption of talc, there is generation of phenol or other aromatics [1]. From 60 min to the end of the experiment, the total degradation of T-H-400 increased from 99.5% to 100% slightly; the second one is the total degradation of H-400 which increased from 82.5% to 92.6%. Overall, T-H-400 showed the best photocatalytic performance.

Figure 12: The change of the removal rate of the 2,4-DCP by T-H, T-H-400, H-400, and HTO.

Figure 13 shows the full-scan UV–Vis absorption spectra of 2,4-DCP solution after treatments by T-H-400. The absorption peak value at 283 nm decreased over time, and the peak disappeared in 60 min. After 60 min, the absorption spectra of 2,4-DCP solution was close to a line without the peaks representing the benzene ring.

Figure 13: Full-scan UV–Vis absorption spectrums of 2,4-DCP solutions after treatments by T-H-400 for 0 min, 40 min, 60 min, and 90 min.

It has been measured for the total oxygen carbon of the initial 2,4-DCP concentration and the 2,4-DCP concentration after treatment by T-H-400 under UV lamp for 2 h. The NPOC declined from 16.04 mg·L-1 to 0.91 mg·L-1 which is positively correlated with the concentration of TOC in the solution, indicating that the benzene rings in the 2,4-DCP have been almost completely broken down. Compared with the result shown in Figure 11, we can conclude that a part of 2,4-DCP has been mineralized to CO2, H2O, and ions [42].

From the proposed pathway for 2,4-DCP degradation by TiO2/medical talc which has been investigated [3, 810, 42], we can summarize as follows: medical talc not only has high absorption capacity but also can enhance the power of photon absorption and capture-recombination carriers; therefore, medical talc has increased the photon utilization for TiO2. Also in T-H-400, there is synergy between TiO2 and medical talc in photocatalysis. As a result, the photocatalytic power of TiO2 has been intensified significantly, and nanocomposite T-H-400 can mineralize the pollutant in a short time. The pathway of the decomposition of 2,4-DCP is effected through the bombarding of OH, through which the benzene ring is disassembled. Finally, the 2,4-DCP is mineralized to CO2, H2O, and ions (chloride and others) (Figure 14).

Figure 14: The pathway of decomposition of 2,4-DCP.

In order to establish the stability of photocatalytic degradation, the T-H-400 has been recycled 20 times to photodegrade the initial 2,4-DCP solution under the UV lamp for 1 h after 25 min in the dark, and the result is shown in Figure 15. From Figure 15, the removal rate is about 99% in spite of few fluctuation, and the sample standard deviation is only 0.0037 according to equation (3). The nanocomposite shows the excellent photocatalytic stability for decomposing the 2,4-DCP, which will extend the photocatalytic life in the practical application. Consequently, the T-H-400 nanocomposite is a sustainable and recyclable material for photocatalytic degradation of 2,4-DCP. where , , , and are the sample standard deviation, the repeated times, and sample average, respectively.

Figure 15: The removal rate of the initial 2,4-DCP solution by T-H-400 under the UV lamp for 1 h after 25 min in the dark.

4. Conclusions

The 99.5% decomposition of the pollutant can be achieved in 1 h. The optimum condition is in neutral aqueous solution at room temperature under a UV lamp. This clearly enhances the photocatalytic capacity of TiO2. The excellent photocatalytic performance can be achieved by a few of nanocomposites. The degree of degradation can be maintained at about 99% after 20 iterations with the same nanocomposite material.

In situ formation of TiO2 nanoparticles in the layers of medical talc thus has marked effect on the purification of the initial solution, indicating that medical talc can significantly enhance the photocatalytic activity of TiO2. This remarkable photocatalytic power will promote the potential applications of medical talc in wastewater treatment.

Data Availability

The data used to support the findings of this study are included within the article.

Conflicts of Interest

The authors declare that they have no conflicts of interest.

Acknowledgments

We thank Professor Benjamin Kneller for polishing the manuscript. This work has been supported by the National Oil and Gas Project 529000-RE1201.

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