Ozonation with ultrasonic enhancement of p-nitrophenol wastewater

Ozonation with ultrasonic enhancement of p -nitrophenol wastewater first-author †E-mail:xxw118@zju.edu.cn †E-mail:xxw118@zju.edu.cn xxw118@zju.edu.cn Department of Environmental Science and Engineering, Zhejiang University, Hangzhou 310027, China Department of Environmental Science and Engineering, Zhejiang University, Hangzhou 310027, China Synergetic effects for p -nitrophenol degradation were observed in the ozonation with ultrasonic enhancement. The enhancements of removal rate for p -nitrophenol and TOC were around 116% and 294% respectively in comparison with the individual ultrasound and ozonation systems. The synergetic phenomenon is attributed to two physicochemical mechanisms: (1) Ultrasound decomposes ozone causing augmentation of the activity of free radicals; (2) Ultrasonic wave increased the concentration of O 3 in solution because of ultrasonic dispersion. Ozonolysis Sonolysis Synergetic effect p -nitrophenol degradation INTRODUCTION 1 Advanced oxidation processes (AOPs), in which high reactive and non-selective hydroxyl radicals in aqueous solution are generated, have aroused among scientists great interest in destroying toxic and biorefractory organics of wastewater. AOPs such as photocatalyzation, electrocatalyzation, ozonolyzation, and wet air oxidation have been intensivels studied. There is a trend in recent years to develop processes combining two or more AOPs such as O 3 /UV, O 3 /H 2 O 2 , O 3 /H 2 O 2 /UV, UV/H 2 O 2 in which synergetic effects have been observed (Staehelin and Hoigne, 1982 1982 ; Adams et al., 1994 1994 ; Peyton and Glaze, 1988 1988 ; Mokrini et al., 1997 1997 ; Guittoneau et al., 1990 1990 ). The process combining ultrasonic irradiation with ozonation is a less developed AOP. Under-developed AOP ultrasonic irradiation has been studied in the purification of aqueous organic and inorganic pollutants (Bhatnagar and Cheung, 1994 1994 ; Cheung et al., 1991 1991 ; Hoffmann et al., 1992a 1992a ; 1992b 1992b ; Pétrier et al., 1992 1992 ). Sound waves just above the audible level produce cavitation bubbles whose internal high temperatures and pressures lead to their collapse. The chemical destruction of compounds has been demonstrated either inside the cavitation bubble or on its interfacial sheath due to direct pyrolysis, hydroxylation, or radical reactions resulting from the gas-phase pyrolysis of H 2 O. Radicals escaping the cavitation bubble diffuse into solution and react near the cavity boundary. Secondary reactions also occur in the bulk aqueous phase. It has been demonstrated that sonolytic systems with ozone added increase the net transformation rates of a wide range of chemical species (Sierka and Amy, 1985 1985 ; Dahi, 1976 1976 ; Olson and Baraier, 1994 1994 ; Kang and Hoffmann, 1998 1998 ; Destaillats et al., 2000 2000 ). With the aim of exploring whether synergetic effects exist in the combined ozonolysis and sonolysis process, and investigating the possible synergetic effects mechanism, we selected p -nitrophenol the model pollutant, as it is a main EPA (Environment Protection Bureau) toxic pollutants and widely exists in wastewater, and pesticides and dyes. EXPERIMENT METHODS 1 Sonochemical experiments 2 The experiment was done with a 200 ml glass chamber reactor surrounded by a self-contained water jacket, constant gas flow, and a source of ultrasound (Fig. 1 1 ). The solution was kept constant at 25 °C with water bath flowing through the surrounding water jacket and O 3 or O 2 gas flowing out of a coarse fritted-glass diffuser at 40 ml/min. Before every experiment, a fixed amount of p -nitrophenol was dissolved in organic-free water and initial p -nitrophenol concentration was about 50 mg/L. pH was adjusted with phosphoric acid and sodium hydroxide. The ionic strength was stabilized at 0.1 mol/L. Aliquots (2.0 ml) were collected certain time. Thiosulfate (0.2 ml of 80 mmol/L) was used to eliminate residual ozone in solution in addition to determination of ozone and hydrogen peroxide concentration. All samples were filtered with 0.2 μm syringe filters before analysis. Total organic carbon (TOC) experiment was the only step not performed in triplicate, but TOC results were analyzed thrice. To analyze the possible stripping of p -nitrophenol in the oxidation, experiment without ultrasound was carried out. Measurements made before and after the experiment indicated there was no significant change in the concentration of p -nitrophenol. 1: O 3 /O 2 inlet; 2: Coarse fritted-glass diffuser; 3: Thermometer; 4: Transducer; 5: Sample out; 6: Vent gas; 7: Cooling water jacket; 8: Reactor; 9: Magnetic agitator Analysis 2 Concentration of p -nitrophenol and its degradation intermediates were determined through comparing the retention time of the standard compounds with a high-performance liquid chromatograph (HPLC, Gilson). Twenty-five μl aliquots of samples were injected into the HPLC running on mobile phase of phosphate buffer solution (pH 2)/methane alcohol at 70/30. The separation was performed using an ODS-18 reversed phase column at flow rate of 1.0 ml/min and temperature of 25 °C. An UV detector with the wavelength set at 280 nm was used. The ozone gas phase concentration was determined by standard methods (EPA, 1989 1989 ). The concentrations of ozone and hydrogen peroxide in the solution were measured by the indigo method and spectrophotometric determination method (Bader and Hoigne, 1981 1981 ; Sellers, 1980 1980 ), respectively. TOC analysis was performed using an Apollo 9000 TOC Combustion Analyzer (USA) operating in the nonpurgable organic carbon (NPOC) mode. RESULTS AND DISCUSSIONS 1 Synergetic effects 2 A systematic comparison of p -nitrophenol degradation and TOC removal was carried out by sonolysis and ozonolysis, with the combined process being shown in Fig. 2 2 . It was found that their removals in three processes fit the following pseudo-first-order kinetic equation: ln( c 0 / c )= kt where c 0 and c are the concentrations of TOC or p -nitrophenol at the initial time (mg/L) and at the reaction time t , respectively, and k is the pseudo-first-order reaction rate constant (min −1 ) obtained by least square method. The linear regression equation is y = mx + b . The simulated reaction rate constants are listed in Table 1 1 . Processes k for p -nitrophenol (10 2 min −1 ) k for TOC (10 2 min −1 ) US/O 2 0.196±0.005 0.0161±0.001 O 3 3.978±0.107 0.305±0.008 US/O 3 9.012±0.321 1.264±0.052 The combined process evidently had synergetic effect in enhancing the removal rate of both TOC and p -nitrophenol in comparison with sonolysis or ozonolysis alone. k for p -nitrophenol removal, for example, in the combined process (0.09012±0.00321 min −1 ) was much greater than its counterpart obtained either in the sonolysis process (0.00196±0.00005 min −1 ) or ozonolysis process (0.03978±0.00107 min −1 ). Factor ( f ) is put forward to evaluate the enhancement of the removal rate of around 116% obtained by using the following formula: f =[ k US/O 3 /( k US/O 2 + k O 3 )−1]×100% where k US/O 3 is the reaction rate constant in the sonolysis-ozonolysis process, k US/O 2 in sonolysis process and k O 3 in ozonolysis process. The enhancement factor of removal rate of TOC was up to 294%, which was much greater than that of p -nitrophenol. The experiments result indicated that the evolution of intermediates during p -nitrophenol degradation was significantly accelerated in the combined process. Degradation intermediates 2 Benzoquinone is one of the rather consistent byproducts and indicates the difficulty of ring opening. It was identified by sonolysis, ozonolysis or the combined process. This speculation above was confirmed by taking benzoquinone as the intermediate product during p -nitrophenol degradation. As shown in Fig. 3 3 , benzoquinone increased slowly in sonolysis. In ozonolysis, it reached maximum 24 min later and then gradually decreased. In the combined process, however, both formation and disappearance of benzoquinone were greatly accelerated. It reached its peak of almost 3.9 mg/L 12 min later and died away in no more than 90 min. Synergetic mechanisms 2 The process combining sonolysis and ozonolysis shows higher degradation rates for p -nitrophenol and TOC than either system alone. And two physicochemical mechanisms account for the synergetic phenomenon: (1) Ultrasound decomposes ozone causing augmentation of the activity of free radicals; (2) Ultrasonic wave increased the concentration of O 3 in solution because of ultrasonic dispersion. During acoustic cavitation, water is pyrolytically decomposed into hydroxyl and hydroperoxyl radicals as follows: H 2 O→H·+·OH H·+O 2 →HO 2 · In the bulk aqueous phase, ozone can be decomposed by hydroxide ion, OH − , or the conjugate base of H 2 O 2 (HO 2 − ) to yield HO 2 · and ·OH as follows: O 3 +OH − →HO 2 − +O 2 HO 2 − +H + →H 2 O 2 O 3 +HO 2 − →O 2 − +·OH+O 2 O 2 − +H + →HO 2 · O 3 +·OH→O 2 +HO 2 · O 3 +O 2 − →O 2 +O 3 − O 3 − +H 2 O→OH − +·OH+O 2 The coupling of sonolysis with ozonolysis increases ·OH because of thermolytical ozone decomposition which occur in the vapor phase of a cavitation bubble as follows (Hart and Henglein, 1986 1986 ): O 3 →O 2 +O The initiatal reaction yields atomic oxygen which reacts with water to form hydroxyl radical, and hydrogen peroxide are produced subsequently as described below: O+H 2 O→2·OH 2·OH→H 2 O 2 The p -nitrophenol and its byproducts pyrolyses either directly inside the cavitation bubble or in its interfacial sheath and react with ozone and one of the active species generated by the combined sonolyzation of water and ozone. The combination of sonolysis and ozonolysis proved effective in oxidation since in this method, two ·OH molecules are produced by consuming per O 3 molecule. Hydrogen peroxide accumulation in the aqueous phase is an indirect indicator of ·OH production in the vapor phase and interface between bubbles and solution. Ozone’s effect on the hydrogen peroxide formation was investigated. The [H 2 O 2 ] vs time profiles (Fig. 4 4 ) shows the combined O 3 /US system produces more [H 2 O 2 ] than the sonolysis system alone. H 2 O 2 produced by sonication rapidly reacts with p -nitrophenol in the beginning, and increases gradually during the irradiation period with the decrease of p -nitrophenol. Similar results were observed by Kang and Hoffmann ( 1998 1998 ). In addition, ultrasonic irradiation enlarges the ozone effective surface area by higher blending and collapse of bubbles as they enter the reactor. In this way, more ozone is allowed to enter solution than that in a nonirradiated system. As shown in Fig. 5 5 , higher O 3 concentration in solution was obtained under sonolysis-ozonolysis than under ozonolysis alone, which further confirms the results of Dahi ( 1976 1976 ), and Sierka and Amy ( 1985 1985 ). CONCLUSION 1 Experiment on the process combining sonolysis and ozonolysis showed that degradation rates for p -nitrophenol and TOC were higher than those of ultrasound or ozone system alone. The enhancement of removal rate for p -nitrophenol and TOC were around 116% and 294%, respectively. In the ozonolysis system, ozone is decomposed by hydroxide ion, OH − , or the conjugate base of H 2 O 2 (HO 2 − );into HO 2 · and ·OH in the bulk aqueous phase. While in the sonolysis system, H 2 O is pyrolytically decomposed into hydroxyl and hydroperoxyl radicals during acoustic cavitation. 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