Azadeh Ebrahimain Pirbazari*
Fouman Faculty of Engineering, College of Engineering, University of Tehran, Iran
Received Date: April 11, 2017 Accepted Date: April 18, 2017 Published Date: April 29, 2017
Citation: Pirbazari AE (2017) Photocatalytical Treatment of Synthetic Wastewater Containing Chlorophenols by TiO2 Nanoparticles Sensitized with Cobalt Phthalocyanine Under Visible Light. J Chem Eng Process Technol 8: 333. doi: 10.4172/2157-7048.1000333
Copyright: © 2017 Pirbazari AE. This is an open-access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.
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In this paper, sensitization TiO2 nanoparticles with sulphonated cobalt phthalocyanine(CoPcS-TNP) has been reported. The prepared samples characterized by different analysis such as: XRD, FT-IR, EDX, nitrogen physisorption, TG and TEM techniques. The XRD, TEM and nitrogen physisorption results showed the prepared samples containing only the pure anatase phase with crystal sizes in the range of 7-10 nm and high surface areas of 133-280 m2/g. The presence of CoPcS in photocatalysts confirmed by FT-IR and EDX analysis. The CoPcS-TNP samples showed efficient activity for photocatalytic degradation of 4-chlorophenol (4-CP) and 2,4-dichlorophenol (2,4-DCP) under visible light. The sample CoPcS-TNP (2.24) was the best photocatalyst for degradation of chlorophenols under visible light. The degradation reactions follow first-order kinetics. Reusing experiments of the photocatalyst showed a reduction activity from 95% to 60% for chlorophenols degradation after four cycles. The major intermediates of degradation were oxalic acid, pyruvic acid and malonic acid which identified by gas chromatography-mass spectrometry (GC/MS).
TiO2; Nanoparticles; Phthalocyanine, Degradation; Chlorophenols
The production and usage of chemicals in industry has led to the entry of many xenobiotics into the environment. Chlorophenols (CPs) are used as flea repellents, fungicides, wood preservatives, fungus inhibitors, antiseptics, disinfectants and antigumming agents for gasoline during the industrial production of pesticides, herbicides, dyes, pigments, phenolic resins and paper. Also, some. Wastewater of paper and pesticides industries contains chlorophenols [1-3]. The widespread occurrence of phenols in wastewater and associated environmental hazards has heightened concern over public health .
Activated carbon adsorption, membrane filtration, chemical coagulation, ion exchange on synthetic adsorbent resins are the conventional wastewater purification systems that generate secondary wastes during the treatment of contaminated water, which requires additional steps and cost. Heterogeneous photocatalytic oxidation (HPO) process as a promising new route for the degradation of persistent organic pollutants, employing TiO2 and UV light has emerged, and produced more biologically degradable and less toxic substances [5,6]. This process is largely dependent on the in-situ generation of hydroxyl radicals under ambient conditions which are capable of converting a wide spectrum of toxic organic compounds including the nonbiodegradable ones into relatively innocuous end products such as CO2 and H2O. Destruction of recalcitrant organics in the HPO process, is governed by the combined actions of an energetic radiation source, an oxidizing agent and a semiconductor photocatalyst . The sun produces 0.2-0.3 mol photons m-2 h-1 in the range of 300-400 nm with a typical UV flux of 20-30 Wm2 near the earth's surface, this suggests using sunlight as an economically and ecologically sensible light source . Many attempts have been made to develop of an efficient wastewater treatment process for large scale applications have received considerable attention. Recently photocatalytic degradation of phenol and substituted phenols in wastewater has been widely investigated. Several reviews [9,10] focusing briefly on the available technologies for the abatement of phenolic compounds in wastewater have recently been published. TiO2- type semiconductor photocatalysts have attracted considerable attention because of their good physicochemical stability and their ability to catalyze the effective elimination of organic refractory contaminants from the aquatic environment [7,11-14]. The main focus of the recent TiO2 photocatalysis research is How to improve the photocatalytic efficiency of TiO2 in the visible region? [15,16]. Researches have been made to achieve the utilization of visible light for TiO2 material, such as transitional metal ion doping [17-19], nonmetal element doping [20,21] and dye sensitization [22,23]. In the dye-sensitized photocatalysis process, the dye absorbs the light and a subsequent electron transfer from the excited state of the dye to the conduction band of TiO2 semiconductor. The electron transferring from excited state of the dye to the conduction band of TiO2 depends strongly on the adsorption property of dye molecules ; and by the competitive adsorption of other coexisting species in the solution.. Because of low cost and efficiency relative to the conventional solid-state conversion of visible light into chemical energy, the use of phthalocyanines and porphyrins has attracted significant attention. The main steps in a photocatalytic process based on TiO2-phthalocyanine nanoparticles can be described as below :
(1) A macrocycle compound attached to the TiO2 surface absorbs visible light, thereby
(2) Promoting electron injection into the TiO2 conduction band.
(3) direct oxidation of the organic compound
(4) Internal cross systems processes at the excited dye
(5) Singlet oxygen produced by the interaction of dye in an excited triplet state with molecular oxygen
(6) Reduction of dissolved oxygen produced hydroxyl radical, hydroxyl anion and singlet oxygen
(7) Superoxide radical reacts with the sensitizer cation and produced hydroxyl radical
(8) Singlet oxygen reduced at the sensitizer and produced hydroxyl radical
(9) Environmental global reaction: organic compound oxidation by the two main oxidants: hydroxyl radicals and singlet oxygen.
To the best of knowledge, there is some works have been devoted to the characteristics and application of TiO2 nanoparticles containing phthalocyanines and in these reports the photocatalysts prepared by the impregnation method [26-30]. A common disadvantage of this method is a low degree of molecular distribution of the dye molecules in the TiO2 structure. Incorporation of phthalocyanines into TiO2 gel has also been reported [31-33]. Due to the incomplete characterization and uncertain validation of the photocatalytic activity mechanism, complementary study is still needed. The enhanced photocatalytic activity of TiO2 sentisized by iron (III) phthalocyanine has been ascribed to the effective formation of hydroxyl radicals generated from both components . The photocatalytic activity of TiO2 containing copper phthalocyanine has been assigned to a dye-sensitized TiO2 photocatalytic mechanism . Although this photocatalyst functions under visible light but it cannot achieve complete degradation of methyl orange as a model pollutant. The aim of this work is, preparation of TiO2 nanoparticles containing different amounts of sulphonated cobalt phthalocyanine (CoPcS) by the hydrothermal method. The prepared samples were characterized by different analysis and used for the heterogeneous photocatalytic degradation of 4-chlorophenol (4-CP) and 2,4-dichlorophenol (2,4-DCP) under visible light, which revealed enhanced photocatalytic activity as compared to the pure TiO2. The kinetic of chlorophenols degradation were investigated and the reaction intermediates during degradation were identified by GC-MS analysis.
Materials and reagents
Cobalt phthalocyanine complex (CoPc) was purchased from (Alfa Aesar No. A16658). The sulphonated form of complex was obtained by a conventional procedure . Sulphonation of CoPc carried out by chlorosulfuric acid, HClSO4 (Fluka No. 26388). Tetraisopropylorthotitanat (Merck No. 8.21895), ethanol, acetylacetone and deionized water were used for photocatalyst synthesis. High-purity 4- chlorophenol(4-CP) (Merck No. 802254) and 2,4-dichlorophenol (2,4-DCP) (Merck No. 803774) were used as a model of organic pollutant for photocatalytic tests. H2O2 (Merck No. 1.08597) was used as accelerating oxidant in the photocatalytic tests.
Cobalt phthalocyanine sulphonation
According to reported procedure in Ref. , 0.5 g of CoPc and 25 mL HClSO4 were treated and the mixture was heated to 150°C for 2 h. The resultant slurry was quenched over crushed ice. A deep blue solid was isolated by suction filtration and hydrolyzed to yield CoPcS. This compound was characterized by UV-Vis spectroscopy.
TiO2 nanoparticles containing different amounts of CoPcS and pure TiO2 were synthesized by the described procedure in Ref. . 20 mL Ti(OC3H7)4, 20 mL ethanol and 1.62 mL acetylacetone was prepared and stirred for 30 min at room temperature (solution A). Then, a new mixture (solution B), containing X mg CoPcS (X: 30, 60, 120 and 180 mg), 80 mL ethanol and 2 mL H2O was added into the solution A, which led to a coloured solution. This solution was transferred into an autoclave, and then heated to 240°C at a heating rate of about 2°C min- 1. Finally, the temperature was kept at 240°C for 6 h. After cooling, the obtained solid washed with ethanol and water and dried at 150°C for 2 h in air. From now on, these photocatalysts are labelled as CoPcSTNP( x), where (x) is the nominal weight percentage of CoPcS in the final solid. A solution without CoPcS was also preparedto obtain a control sample. This photocatalyst contains only TiO2 prepared by an identical procedure.
A Siemens D500 automatic diffractometer with a Cu Kα monochromatized radiation source was used for recording of the X-ray diffraction (XRD) patterns of various solid phases. The peak intensities were fitted by a pseudo-Voigt function assuming a linear background. The standard error was ~ ± 5%. Transmission electron microscopy (TEM) studies were carried out with a Hitachi-H- 8100 instrument (accelerating voltage up to 200 kV, LaB6 filament). The samples were prepared by dispersing in an ultrasonic bath for 20 min in ethanol. The nitrogen physisorption measurements were carried out with a Quantachrome Autosorb-1-MP. The BET areas were determined by static nitrogen physisorption at ~196°C subsequent to out-gassing at 180°C, until the pressure was lower than 5 mbar. Diffuse reflectance spectra were recorded with a Perkin Elmer Spectrophotometer equipped with an integrating sphere assembly. The spectra were recorded at room temperature against barium sulphate. Fourier-transform infrared (FT-IR) spectra were recorded with a Shimadzu FT-IR spectrometer (Model 8400). Elemental chemical analysis (Vario EL, Elementar) was performed to determine the carbon and sulphur contents of the samples. The thermogravimetric analyses of the samples were carried out with a Cahn TG 2131 thermobalance in the temperature range of 25-900°C at a heating rate of 5°C/min in 100% pure helium. The reaction intermediates were identified by GC-MS in an Agilent 190915-433 instrument equipped with a HP-5MS capillary column (30 m × 0.25 mm). The column temperature was programmed at 50°C for 2 min, and from 50 to 250°C at a rate of 10°C min-1. The samples used for GC-MS analysis were prepared according to the following procedure: The obtained degradation product was acidified to pH 1 and subsequently extracted with dichloro-methane. After dichloromethane was evaporated to dryness under vacuum, 10 mL methanol was added to dissolve the residue. Then, 1 mL concentrated sulfuric acid was added and the combined solution was refluxed for about 3 h. The solution was further extracted with dichloromethane followed by concentrating to about 1 mL under reduced pressure. The released chloride ions originating from the degradation of chlorophenols were identified and determined by the AgNO3 method.
Photocatalytic degradation of chlorophenols
The photcatalytic activity of prepared photocatalysts was investigated for degradation of chlorophenols. The suspension containing optimum dose of photocatalyst and 50 mL aqueous solution of each chlorophenols (Conc: 40 mg/L) was stirred first in the dark for 10 min to establish adsorption/desorption equilibrium. Irradiation experiments were carried out in a self-built reactor. In some experiments, H2O2 (as an oxidant) was also added to the solution before light irradiation. A visible (Halogen, ECO OSRAM, 500W) lamp was used as irradiation source. At certain intervals, small aliquots (2 mL) were withdrawn and filtered to remove the photocatalyst particles. These aliquots were used for monitoring the degradation progress, with Biochrom WPA, Biowave II spectrophotometerat λmax=224 nm.
Characterization of synthesized photocatalysts
X-ray diffraction analysis: The XRD patterns of synthesized samples were shown in Figure 1. The patterns indicated that TiO2 nanoparticles and the CoPcS-TNP samples consist of the pure anatase phase (PDF 24-1272). The XRD patterns showed that presence of CoPcS complex into TiO2 structure didn’t change the diffraction positions and lattice parameters of TiO2 (Figure 1). The diffraction patterns of pure TiO2 and CoPcS-TNP samples shown considerable line width, indicating small crystal. Based on the Scherrer equation, the crystal size of the prepared photocatalysts can be calculated from the width of the anatase (101) diffraction width. The crystallite dimensions were determined using the equation:
D(hkl)=0.9 λ/ β Cos θ (1)
Where D(hkl) is the crystal thickness in the h k l direction, λ is the wavelength of the X-ray radiation, β is the peak width at half-maximum corrected for instrumental broadening, and θ is the Bragg angle of the diffraction peak. The crystal size of the pure TiO2 and CoPcS-TNP photocatalysts are in the range from 7.5 to 9.5 nm (Table 1).
|Sample||Phase||Crystal Size (nm)|
Table 1: Crystalline phase and crystal size identified by XRD.
Diffuse reflectance spectroscopy: The diffuse reflectance spectra of the synthesized samples are shown in Figure 2. Pure TiO2 has no significant absorbance in the visible region because of the large band gap energy (3.1 eV), and exhibits only a fundamental absorption band in the UV region (Figure 2a). The diffuse reflectance spectra of CoPcS-TNP samples exhibit absorption bands in the 600-700 nm regions (Figure 2b-2e). The two maxima in the visible region correspond to the Q absorption bands originating from π→π* transitions of CoPcS, which demonstrate that the absorption spectra of CoPcS-TNP samples extend to the visible region. The monomeric and aggregated form of CoPcS complex exhibited the absorption bands at about 680 and 620 nm, respectively . The band gap energy was calculated from the DR spectra according to below equation  for the pure TiO2 and CoPcS-TNP samples.
|Sample||Colour||? (nm)||Band gap energy (eV)|
|CoPcS-TNP (3.36)||Pale blue||400||3.10|
Table 2: Colour, wavelength and band gap energy of the prepared samples.
Where Ebg is the band gap energy (eV) and λ is wavelength (nm) obtained from the DR spectra. The Ebg data and the colour of samplesare summarized in Table 2. The band gap energy for all the samples except CoPcS-TNP (1.12) are within 3.10-3.11 eV. The lower band gap energy of 2.97 eV observed for CoPcS-TNP (1.12) may be due to the very low degree of incorporation of CoPcS into TiO2. It may be concluded part of CoPcS molecules have been decomposed during the hydrothermal synthesis, and some of the cobalt species were inserted into the TiO2 bulk decreasing the band gap energy.
FT-IR spectroscopy: The FT-IR spectra of the CoPcS, pure TiO2 and CoPcS-TNP (2.24) sample are shown in Figure 3a and Figure 3b Some of the characteristic bands of CoPcS (Figure 3c) appeared in the 1700-1000 cm-1 regions . The spectrum b in Figure 3 originates from the CoPcS-TNP (2.24) sample. The vibration about 1400 cm-1 can be attributed to cobalt phthalocyanine species in the synthesized photocatalysts , which is labelled with an asterix in Figure 3. The intensity of the 1400 cm-1 vibration is weak, because the amount of CoPcS incorporated into TiO2 is low. The vibrations at about 670 cm-1 (Figure 3c) due to the sulfonic groups of CoPcS  disappeared in the CoPcS-TNP (2.24) sample, which is most likely due to the formation of TiO-SO3 - bond (Figure 4). Covalent grafting of sulphonated iron (III) phthalocyanine onto TiO2 nanoparticles was carried out by Sorokin et al.  through sol-gel procedure. Their obtained characterization results showed that sulfonic groups are chemisorbed onto the TiO2 nanoparticles and sulphonated iron (III) phthalocyanine complex acts as a bridging ligand and controls the molecular self-assembly hydrolytic process. Recently Núñez and etal reported modification of TiO2 surface with copper(II) phthalocyanine-tetrasulfonic acid tetrasodium (CuPculfunic acid) and their FT-IR data showed, the S-O-Ti characteristic stretching signals at 1150 and 1210 cm-1 suggest chemisorptions of CuPc complex through acid bond formation (TiO-SO3 -) between Ti-OH and CuPc-sulfonic . Their adsorption isotherm investigation showed that each CuPc molecules adsorbed onto TiO2 surface nanoparticles using two or more sulfonic acid moieties. Therefore, the CuPc molecules may have more planar distribution on the TiO2 surface and prevents CuPc molecule multi anchoring at the TiO2 surface .
Transmission electron microscopy (TEM): The particle size and morphology of the prepared samples were analyzed by TEM. The TEM micrographs (Figure 5) revealed that the samples consist of nanoparticles with diameters in the range from 7 to 10 nm. The samples are not agglomerated, which is useful to increase the photocatalytic activity of the prepared samples. The chemical analysis results are summarized in Table 3. The obtained data from sulfur content suggest an average of two sulphonate groups per CoPc complex. Also the carbon amount is relatively high for CoPcS-TNP (1.12) that may be indicated decomposition of CoPcS complex during the hydrothermal synthesis and fractions of other organic compounds (such as acetylacetone or ethanol) remained as separated phase.
Table 3: Elemental chemical analysis of the prepared samples.
N2 adsorption-desorption: Figure 6 shows N2 adsorptiondesorption isotherms of the pure and CoPcS-TNP samples. The sorption isotherms for all of the samples except CoPcS-TNP (1.12) correspond to the type IV isotherm according to the IUPAC classification . Textural and structural parameters of the CoPcSTNP samples are summarized in Table 4. Specific surface areas were calculated according to the BET method, pore volumes, and radii were derived from the desorption branch according to the BJH model. The specific surface areas of the CoPcS-TNP samples are lower than that of pure TiO2 suggesting that incorporation of the CoPcS complex reduces the surface area of TiO2 nanoparticles. Reduction of the surface area for CoPcS-TNP samples does not involve distortion of the TiO2 crystal structure as shown by XRD analysis.
|Sample||SBET (m2/g)||Pore radius (A°)||Pore volume (cm3/g)|
Table 4: Textural and structural parameters of the prepared samples.
Thermogravimetric analysis: Thermogravimetric analysis curves of the prepared samples in helium atmosphere are shown in Figure 7. In the thermogram for pure TiO2, three weight loss stages can be observed. The first weight loss is at about 90°C, which corresponds to desorption of physically adsorbed species such as H2O and CO2. The second weight loss at about 250°C is ascribed to the removal of hydroxyl groups from the surface of TiO2 . The third weight loss at about 370°C is for organic species decomposition, which used for preparation of TiO2. We also observed three weight loss stages in the thermograms of the CoPcS-TNP samples (Figure 7). The first and the second weight loss at about at 90 and 370°C can again be attributed to desorption of water and decomposition of organic species, respectively. However, a new weight loss starting at about 500°C for CoPcS-TNP (2.24) and CoPcS-TNP (3.36) can be attributed to the decomposition of CoPcS complex. The phthalocyanines and their metallo derivatives are stable up to 400°C . These results may indicate that CoPcS molecules immobilized onto TiO2 nanoparticles through covalent bonding are more stable and decomposed at higher temperature (Figure 4). We did not observe dehydroxylation weight loss for CoPcS-containing TiO2 samples at 250°C. This also is an indication of the strong interaction between TiO2 and CoPcS through hydroxyl groups.
Photocatalytic degradation of chlorophenols
The photocatalytic efficiency of the CoPcS-TNP samples was investigated for degradation of chlorophenols. Elimination time of chlorophenols in the presence of the prepared photocatalysts is shown in Table 5. All of the CoPcS-TNP samples are more efficient in the degradation of chlorophenols compared to pure TiO2, and the degradation rate of chlorophenols is the highest in presence of CoPcSTNP (2.24). Obtained results can be confirmed the role of CoPcS complex as sensitizer on the surface of TNP: By the photon absorption, the electrons in the ground state of CoPcS complex are excited and then injected into the conduction band of TiO2. Highly active species such as OH• and O2 •- are generated at the TiO2 surface, where the photoelectrons and holes become effectively separated. The aggregated form of the CoPcS complex shortens the excited triplet state lifetimes by enhancement of internal conversion and therefore reducing their photosensitizing efficiency . Consequently, a monomolecular distribution of the dye on the TiO2 surfaces favors improved photocatalytic activity.
elimination time (min)
elimination time (min)
Table 5: Elimination time of chlorophenols in presence of the prepared samples.
Figure 8 show the photocatalytic degradation of 4-CP (Figure 8a) and 2,4-DCP (Figure 8b) under various conditions and in the presence of the best photocatalyst (CoPcS-TNP (2.24)) respectively. Control experiments showed that the optimal dosage of photocatalyst is 0.3 g L-1, and t a H2O2 concentration of 0.01 mol L-1 is adequate for photocatalytic degradation of chlorophenols. Complete elimination of 4-CP and 2,4-DCP are possible within 90 and 180 min in the presence of the CoPcS-TNP (2.24), H2O2, and visible light. Thus, the enhancement of the catalytic activity observed for the CoPcS-TNP samples compared to pure TiO2 can be demonstrated synergetic effect of the sensitizer (CoPcS complex). CoPcS complex has a strong absorption around 600- 650 nm (Figure 2), it has strong Q-band absorption and it can be excited under visible light. The excited CoPcS molecules inject electrons to the conduction band (CB) of TiO2, the CB acts as a mediator and transfer electron acceptors on the TiO2 surface, the valence band (VB) remains unaffected.
In the presence of hydrogen peroxide the activity of the photocatalyst may even be better (Figure 8). Almost 50% of 4-CP and 2,4-DCP are degraded within 90 and 180 min, when there is no H2O2 added. More hydroxyl radicals are produced in the presence of H2O2 according to the below reaction:
H2O2+O2 -•→OH•+OH-+O2 (3)
This photocatalyst did not exhibit any photoactivity in the dark, neither in the absence nor in the presence of H2O2 (Figure 8), suggesting that it is necessary to photoexcite the sensitizer (CoPcS). The hydroxyl radicals are responsible for the degradation of the chlorophenols, yielding some intermediate compounds and mineralization products. The hydroxyl radical production was checked by Gao et al. proposed method [45,46], based on Nash’s method . It noticed that the production of hydroxyl radicals would produce a yellow color owing to the synthesis of diacetyldihydrolutidin . The yellow color was observed when photocatalyst, H2O2 and the radiation were employed and the intensity of the color increased with increasing the time of irradiation. According to equation 3, the production of the hydroxyl radicals depends on the presence of superoxide radicals , therefore, the observation may suggest that the superoxide radicals are involved. During the photocatalytic degradation of chlorophenols, hydrogen peroxide could react with superoxide radicals to generate hydroxyl radicals.
GC/MS analysis: To obtain information about intermediates species formed during chlorophenols degradation process, GC/MS technique was employed. Figure 9 and Table 6 give major reaction intermediates containing carboxylic acid functional species. Formation of these intermediates can be explained as: After hydroxyl radiacals formation, the hydroxyl radicals attack to chlorophenols, converting them to chlorocatechol and then to chlorobenzoquinone, then hydroxyl radicals break the aromatic ring of chlorobenzoquinone, transferring them into simple acids like oxalic acid and acetic acid as the final products [48-50]. Chaliha and et al.  and Bian et al.  identified the main ring-opened products resulting from 4-CP degradation by GC/MS and discussed the formation mechanism of them. In the proposed mechanism by Chaliha et al. , an electrophilic OH radical adds onto the 4-CP ring at an ortho- or para-position, leading to the formation of chlorocatechol and hydroquinone. On further oxidation, chlorocatechol is likely to be converted to aliphatic acids and hydroquinone to p-benzoquinone, which is easily oxidized to the corresponding dicarboxylic acid, 2,5-dioxo-3-hexenedioic acid. This acid produces maleic acid, which decomposes to oxalic acid, formic acid, acrylic acid, malonic acid and acetic acid. If there are no additional radical competitors in the solution, these low molecular weight organic acids can gradually be mineralized to carbon dioxide, the ultimate oxidation product. Also, a number of the intermediates identified in this work (Table 6) are in agreement with those reported in ref . Benzoic acid formation with higher carbon compare chlorophenols can be illustrated according to the Rao et al. report (Figure 10) . They proposed that radical I and a chloride radical (Cl•) formed by homolytic cleavage of aryl-Cl bond or by interaction of 2-CP with electrons on the surface of TiO2 . In a second step, radical I may dimerize to yield [1,1'-biphenyl]-2,2'-diol or combine with formyl radical produced in-situ to give 4-hydroxybenzaldehyde and benzoic acid formed by oxidation of hydroxybenzaldehyde. Hydroxyl radicals can attack the aromatic moiety due to their electrophilic nature . Progress of the photocatalytic degradation was detected by chloride ion measurement through AgNO3 test method. The presence of Cl- in the reaction media accounts up almost 100% for chlorophenols degradation if compared to the maximum achievable concentration.
|Retention time (min)||Identified intermediate||Molecular formula|
|11.99||Benzoic acid, methyl ester||C6H5COOCH3|
Table 6: The main intermediates of chlorophenols degradation determined by GC/MS.
Photocatalyst reuse: The stability of the anchored photocatalysts is very important for its application in environmental technology. Therefore, the effectiveness of photocatalyst reuse was examined for degradation of each chlorophenols during a four cycle experiment.
Each experiment was carried out under identical conditions (Figure 11). 50 mL of each chlorophenols with an initial concentration of 40 mg/L, 15 mg photocatalyst and 0.03 mol/L H2O2 and 90 and 180 min irradiation time under visible light were used. Recycling experiments showed a photocatalytic activity reduction from 95% to 60% after four catalytic cycles. The main reasons for reduction of photocatalytic activity are permanent adsorption of intermediate species or probable attack of OH radicals to the anchored phthalocyanine complex.
The effect of the initial concentration: The photocatalytic degradation of chlorophenols is a first-order reaction and and its kinetics may be expressed as ln(C0/C)=kobst. In this equation kobst (min−1) is the apparent rate constant, C0 and C are the initial concentration and concentration at reaction time t of each chlorophenols, respectively. The kobs are found from the slopes of the straight lines obtained by plotting ln(C0/C) versus irradiation time. The reaction rates, rate constants and half-lifes (t1/2) at various initial concentrations of each chlorophenols are given in Table 7. The results summarized in Table 7 show that the reaction rate of photocatalytic degradation of chlorophenols is faster at higher initial concentration. However, the rate constants decrease to some extent when the initial concentrations increase. The initial degradation rate of chlorophenols increased by increasing of chlorophenols concentration because the oxygen active species formed on the CoPcS surface have a limited lifetime and react with the chlorophenoles near the photocatalyst surface.
|Initial Conc. (µg/mL)||kobs
Table 7: First-order reaction rate constants and correlation coefficients for different concentrations of chlorophenols.
In this work, TiO2 nanoparticles containing different amounts of CoPcS (CoPcS-TNP) were synthesized and characterized by different analysis such as: XRD, FTIR, TEM, TG, nitrogen physisorption and DRS. The nitrogen physisorption and FTIR analysis results indicate that CoPcS molecules act as bridge ligand and attached on the surface of TiO2 nanoparticles through SO2-O-TiO2 bonds. The CoPcS-TNP samples should contain an optimum amount of CoPcs anchored to the TiO2 surfaces for better photocatalytic activity. The obtained results for degradation of chlorophenols showed that the incorporation of 2.24 wt% CoPcS provides the most photoactive sample. The kinetics of the reaction is first-order and the main intermediates of reaction identified by GC/MS.
The author wish to acknowledge the financial support of Iran National Science Foundation (Grant No: 92025598). Also, I am so thankful to University of Tehran for supporting of this research.