Selective Removal of Perfluorooctanoic Acid Using Molecularly Imprinted Polymer-Modified TiO<sub>2</sub> Nanotube Arrays

Wu, Yunbo; Li, Yi; Tian, Aijun; Mao, Kai; Liu, Jian

doi:https://doi.org/10.1155/2016/7368795

International Journal of Photoenergy

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Abstract Introduction Materials and Methods Results and Discussion Conclusions Acknowledgments References Copyright Related Articles

Research Article | Open Access

Volume 2016 | Article ID 7368795 | https://doi.org/10.1155/2016/7368795

Selective Removal of Perfluorooctanoic Acid Using Molecularly Imprinted Polymer-Modified TiO₂ Nanotube Arrays

Yunbo Wu,^1,2Yi Li,¹Aijun Tian,²Kai Mao,²and Jian Liu²

Academic Editor: Meenakshisundaram Swaminathan

Received11 Nov 2015

Revised21 Jan 2016

Accepted26 Jan 2016

Published24 Feb 2016

Abstract

Perfluorinated chemicals have attracted worldwide concern owing to their wide occurrence and resistance to most conventional treatment processes. In this work, a novel photocatalyst was fabricated by modifying TiO₂ nanotube arrays with molecularly imprinted polymers. The molecularly imprinted polymer-modified TiO₂ nanotubes (MIP-TiO₂ NTs) were characterized and tested for the selective removal of perfluorooctanoic acid (PFOA) from water. The amount of PFOA adsorbed by the MIP-TiO₂ NTs was as high as 0.8125 μg/cm². PFOA decomposition and defluorination by the MIP-TiO₂ NTs reached 84% and 30.2% after 8 h reaction, respectively. The Freundlich model and pseudo-first-order kinetics were used to describe the observed adsorption and decomposition of PFOA, respectively. Compared with TiO₂ NTs and nonmolecularly imprinted polymer-modified TiO₂ NTs, the MIP-TiO₂ NTs exhibited not only a higher PFOA degradation rate but also enhanced selectivity for target chemicals. The MIP-TiO₂ NTs could also selectively and rapidly remove PFOA from secondary effluent, exhibiting a decomposition of 81.1%, almost as high as that observed in pure water. Investigation of the effects of scavengers on the photocatalytic reaction indicated that photogenerated holes were the main oxidant for PFOA decomposition, and the PFOA degradation mechanism and pathway were proposed.

1. Introduction

Perfluorinated chemicals (COOH, PFCs) are a class of anthropogenic organic compounds that have a wide range of applications, including in textiles, stain repellents, corrosion inhibitors, surfactants, and firefighting [1]. Owing to the high binding energy of C-F, PFCs have high chemical stability. This property makes PFCs persistent and bioaccumulative and has resulted in them becoming ubiquitously distributed in aquatic environments [1, 2]. Some PFCs, especially perfluorooctanoic acid (PFOA) and perfluorooctane sulfonate (PFOS), are commonly detected in surface water, sediments, and wastewater treatment plants (WWTPs) [3–5]. The evidence shows that these PFCs pose a potential risk to human health and aquatic organisms. For these reasons, the PFCs have had fixed strict limitations on the environmental surfactants concentration by some regulatory organizations and national governments [6].

Recently, much attention has been focused on eliminating PFCs from the environment using effective techniques under different conditions. Methods such as adsorption and advanced oxidation processes have been developed to remove PFCs from water [2, 7, 8]. Among these, adsorption is considered as suitable technology for PFCs from water or wastewater, such as activated carbon and molecularly imprinted polymers; the efficient adsorbents have high and selective adsorption for PFCs [2]. TiO₂ photocatalysis is shown to be an effective process without harmful byproducts due to its capability to remove a wide range of pollutants and is coupled with other advantages in terms of high photochemical stability, being environmentally friendly, and low cost. It has previously been reported that TiO₂ and modified TiO₂ catalyst-mediated heterogeneous photocatalysis can be applied to PFC removal, with a considerable amount of the pollutant being degraded [8–12].

Adsorption throughout the degradation is a critical process that controls the reaction rate. However, in aquatic environments, especially in wastewater, there are many compounds and colloids that compete with PFCs and thus decrease the adsorption capacity of the adsorbent. Therefore, the development of affinity media that selectively removes PFCs from water and wastewater is of significant interest. Some researchers have reported that TiO₂ alone displays low degradation capacity for organic compounds [9, 13]. Many studies seek to hybridize TiO₂ with selective adsorbents leveraging the advantages of both materials.

Molecular imprinting is a useful technique for preparing polymeric materials as specific molecular recognition receptors [14–16]. Molecularly imprinted polymers (MIPs) are prepared by polymerizing in the presence of cross-linkers and the polymerizable complexes formed from template species and monomers, which results in binding sites complementary to the template molecule. Du et al. reviewed methods for the preparation of MIPs with high selectivity and their adsorption behavior for PFCs (mainly PFOA and PFOS) [2]. Takayose et al. tried to synthesize a polymeric sorbent selective for PFOA using different monomers and cross-linkers and suggested that the MIP recognized PFOA via hydrogen bonding and fluorine-fluorine interactions [14]. Tran et al. developed a photoelectrochemical sensor fabricated by surface modification of TiO₂ nanotube arrays with MIP. They reported that the as-prepared sensor was highly sensitive to PFOS and exhibited outstanding selectivity [16]. The results of the abovementioned studies show that MIP adsorption is an effective method for the selective removal of targeted PFCs from water.

However, most of the existing studies have merely focused on the development and adsorption mechanism of adsorbents for PFCs. So far, there have been no reports regarding the selective removal of PFCs using a technology that combines MIP adsorption and TiO₂ photocatalysis. However, it has previously been reported that surface fluorination of the catalyst (P25 TiO₂) induced by fluoride ions released during the photodegradation of PFOA results in catalyst deactivation [6, 8]. Additionally, the studies focused on photodegradation of PFCs were mostly carried out in deionized water, rather than real wastewater or WWTP secondary effluent, and some ions and other organics were shown to have significant effects on the photocatalytic degradation efficiency.

In the present paper, a new MIP-modified TiO₂ nanotube (MIP-TiO₂ NT) photocatalyst was developed to achieve selective removal of PFCs. The characteristics, sorption behaviors, and photocatalytic activity of the MIP-TiO₂ NTs were studied in detail. The proposed removal mechanism and possible surface fluorination during the photocatalysis process were investigated. The photocatalytic decomposition of PFCs from real secondary effluent using the MIP-TiO₂ NTs was also evaluated.

2. Materials and Methods

2.1. Reagents

Titanium sheets (99.60%, 0.06 mm thick) were purchased from Haiji Ltd. for Titanium & Nickel, China. Perfluorooctanoic acid (PFOA), perfluorooctane sulfonate (PFOS, potassium salt), acrylamide, 2,4-Dichlorophenoxyacetic acid (2,4-D), and perfluoroheptanoic acid (PFHA) were obtained from Sigma-Aldrich. 2,2′-Azobis (2-methylpropionitrile) (AIBN), ethylene glycol dimethacrylate (EGDMA), 3-methacryloxypropyl trimethoxysilane (MPTS), and 3-aminopropyltriethoxylsilane (APTS) were all purchased from Sinopharm Chemical Reagent Co., Ltd., China. Analytical standards for chromatography analyses were purchased from Sigma-Aldrich.

2.2. Preparation of MIP-TiO₂ TNs

First, the preparation of TiO₂ NTs was carried out on titanium foils using a procedure based on those used in our previous studies [15, 17]. The anodization was performed in a cylindrical electrochemical reactor with a DC power supply, with the Ti foil as the anodic electrode and nickel sheet as the cathode. A constant potential of 20 V was applied to the foils in an electrolyte containing 0.083 M H₂C₂O₄·2H₂O and 0.5 wt% NH₄F with magnetic stirring at room temperature. After the anodization, the samples were rinsed with deionized water, air-dried, and thermally annealed at 500°C for 2 h. Highly ordered and vertically aligned TiO₂ NTs were obtained.

The as-synthesized TiO₂ NTs were pretreated in 0.5 M NaOH solution for 30 min to hydrolyze the TiO₂ surface to form Ti-OH groups and then rinsed with deionized water and air-dried. The molecularly imprinted polymers were fabricated on the TiO₂ NTs as follows [14–16]: the TiO₂ NTs were immersed into anhydrous toluene solution containing 1% (v/v) APTS and 1% (v/v) MPTS. The mixture was then purged with nitrogen gas for 15 min and heated at 60°C for 4 h. The resulting APTS- and MPS-modified TiO₂ NTs were washed with toluene and acetonitrile, respectively, and dried in nitrogen gas. Next, 10 mM of the template (PFOA) was added to a mixture containing 12 mL methanol/acetonitrile (1/1, v/v) solution, 0.2 M functional monomer (acrylamide), 1.4 M cross-linker (EGDMA), and 40 mM initiator agent (AIBN). The solution was mixed uniformly by sonication for 5 min and then was slowly dropped onto two sides of the TiO₂ NT sample to obtain a uniform coating. The coated TiO₂ NTs were inserted into a columniform quartz tube, which was sealed and purged with nitrogen for 20 min. Polymerization was then carried out under 352 nm UV light irradiation for 12 h. The molecular template was removed by immersing the prepared samples in methanol/deionized water (1/1, v/v) until no molecular template was detected in the eluate.

Nonmolecularly imprinted polymer-modified TiO₂ NTs (NIP-TiO₂ NTs) were also fabricated as a reference using the same method but without the addition of the template. The TiO₂ NTs surface modified with molecularly imprinted polymers was denoted as MIP-TiO₂ NTs.

2.3. Characterization

The morphology of the TiO₂ NTs was characterized by field-emission scanning electron microscopy (FESEM; Hitachi S-4800). The crystal structure of the photocatalyst was identified by X-ray diffraction (XRD) using a Rigaku D/max-rA diffractometer with Cu Ka radiation. The completion of the polymerization reaction in the preparation of the MIP-TiO₂ NTs was confirmed by Fourier-transform infrared spectroscopy (FT-IR; ThermoFisher Nicolet iS10). UV-vis diffuse reflectance spectra (DRS) were recorded on a Varian Cary 5000 spectrophotometer with an integrating sphere.

2.4. Batch Experiments

Adsorption of the chosen PFCs on the prepared materials was carried out in solution. In all batch adsorption experiments, four pieces of the prepared material (active area of 800 cm²/L) were placed into 250 mL flasks containing 150 mL of PFOA/PFOS solution. All the experiments were carried out at 130 rpm in a shaker bath for 36 h at 25°C, and the sorption kinetics and sorption equilibrium were examined. Sorption isotherm experiments were conducted with initial PFOA concentrations ranging from 2 to 80 mg/L and an initial pH of 5 for 48 h.

Similar to previous studies [15, 17], the photocatalytic experiments were conducted in a cylindrical quartz photocatalytic reactor. A quartz tube containing a low-pressure UV lamp (23 W, UV-C light at 254 nm) was placed at the reactor center. The reaction solution contained an initial PFOA concentration of 30 mg/L in the presence/absence of four pieces of MIP-TiO₂ TNs or NIP-TiO₂ NTs. Prior to UV irradiation, the reaction mixture was stirred under dark conditions for 30 min to obtain adsorption-desorption equilibrium among the PFCs, TiO₂, and oxygen. The temperature was controlled at °C using a circulating water bath. The initial pH value of the reaction solution was adjusted with HNO₃ or NaOH. Aliquots were taken from the system at desired time intervals and analyzed by HPLC.

To investigate the selectivity of the MIP-TiO₂ TNs, 150 mL of solution containing PFOA, PFOS, 2,4-D, or PFHA was added to the 250 mL reaction flask. The initial pH of the solution was adjusted to 5.

2.5. Analytical Methods

The concentrations of PFOA, PFOS, and PFHA in the reaction solutions were measured with an e2695-HPLC equipped with a 432 conductivity detector and an XBridge C18 column (4.6 mm × 250 mm) (Waters Technologies, USA). A mixture of methanol and 0.02 M aqueous NaH₂PO₄ (75/25, v/v) was used as the mobile phase, with a flow rate of 1.0 mL/min at 40°C. The concentration of 2,4-D was determined using the same HPLC but with a mobile phase consisting of 70% methanol and 30% phosphoric acid buffer at pH 2.3. The wavelength was established at 214 nm [18].

The total organic carbon (TOC) analysis was used to evaluate and to monitor the trend of the carbon content of the PFOA by photocatalysis of MIP-TiO₂ NTs. TOC analyses were performed with a TOC analysis system (Shimadzu® TOC 5000A) with a combustion/nondispersive infrared (NDIR) gas analysis method.

According to a previous study [13], the concentration of fluoride ions generated in the degradation samples was monitored with an ion chromatography system (Dionex ICS-2000) equipped with a degasser, an autosampler, a guard column (IonPac AG11-HC), a separation column (IonPac AS11-HC), a column heater (30°C), and a conductivity detector with a suppressor. The mobile phase was an aqueous solution of KOH (30 mmol/L) with a flow rate of 1.0 mL/min. The suppressor current was set at 124 mA.

3. Results and Discussion

3.1. Characterization of Prepared Materials

The surface morphology of the prepared TiO₂ NTs and MIP-TiO₂ NTs is shown in Figure 1. In both cases, well-ordered and uniform TiO₂ nanotubes were grown over the entire titanium substrate. The TiO₂ NTs had an inner pore diameter ranging from 70 to 100 nm and wall thickness of approximately 14 nm. After molecularly imprinted polymerization, the molecularly imprinted polymer was uniformly deposited onto the surface of the TiO₂ NTs. The TiO₂ NTs covered with a thin MIP layer still kept their open-top character and only decreased in average diameter to approximately 10 nm, as shown in Figure 1(b). Figure 2 shows the XRD patterns of the unmodified TiO₂ NTs and MIP-TiO₂ NTs, which indicate that the TiO₂ NTs were mainly anatase and rutile in phase.

(a)

(b)

The UV-vis spectra of the TiO₂ NTs, NIP-TiO₂ NTs, and MIP-TiO₂ NTs are presented in Figure 3. Compared with that of the naked TiO₂ NTs, it is clear that the absorption intensity of the NIP-TiO₂ NTs and MIP-TiO₂ NTs was significantly increased in the UV and visible light range. The spectra of the latter two materials also showed a red shift, which was attributed to the imprinted polymer layer on the TiO₂ surface. Moreover, the absorption intensity of MIP-TiO₂ NTs was lower than that of NIP-TiO₂ NTs at wavelengths between 250 and 350 nm. This may be because the surface imprinted layer covered the active sites of TiO₂.

The FT-IR is a highly sensitive method to characterize structure of molecular-imprinted TiO₂ film. Figure 4 shows the FT-IR spectra of acrylamide, TiO₂ NTs, NIP-TiO₂ NTs, and MIP-TiO₂ NTs. The unmodified TiO₂ NTs showed no significant absorptions (curve (a)). After the surface modification of the TiO₂ NTs, a N-H bending mode at around 1612 cm⁻¹, C=O amide stretching mode at around 1672 cm⁻¹, C-N stretching mode at around 1134 cm⁻¹, =C-H and =CH₂ out-of-plane bending modes at around 958 cm⁻¹, and N-H stretching mode at around 3360 cm⁻¹ were observed (curve (b)), all of which were consistent with the characteristic peaks of the functional monomer acrylamide (curve (b)). Among the characteristic peaks of PFOA, signals in the range of 1300–1100 cm⁻¹ are attributed to C-F stretching [6, 13]. These characteristic peaks were not present in the spectra of the MIP- and NIP-TiO₂ NTs (curves (c) and (d)), which confirmed that PFOA was removed after the rinsing of the samples with CH₃OH solution.

3.2. Adsorption Performance

The amount of PFOA sorption by the different adsorbents as a function of residual PFOA concentration in the test solution is presented in Figure 5. Percentage of PFOA adsorption for different adsorbents at various initial concentrations was given in Table 1. The amount bound to both the MIP and NIP-TiO₂ NTs clearly increased as the PFOA concentration was increased. Moreover, the amount of PFOA adsorbed by the MIP-TiO₂ NTs was much greater than that by the NIP-TiO₂ NTs or TiO₂ NTs, revealing that the imprinting polymerization process had a significant influence on PFOA adsorption. The amount of PFOA adsorbed on the MIP-TiO₂ NTs reached 0.8125 μg/cm² when the initial concentration of PFOA was 80 mg/L.

Based on the observed adsorption performance of the MIP-TiO₂ NTs in aqueous solution, the Freundlich model was used to describe the adsorption isotherm: where is the amount of PFOA adsorbed per unit active surface area of the MIP (mg/cm²); is the adsorption equilibrium constant representative of the adsorption capacity; is a constant indicative of the adsorption intensity; and is the equilibrium concentration (mg/L). is square of correlation coefficient. The calculated adsorption coefficients of the adsorption isotherms are listed in Table 2. The coefficients and of the MIP-TiO₂ NTs were higher than those of the other samples. These results indicated that the observed difference in adsorption capacity and intensity should be attributed to the footprint cavities existing in the imprinted polymers. The enhanced adsorption of PFOA on the absorbents was caused by the presence of special binding sites [14, 16, 19]. Only the template molecules could be bound in these sites, which required not only specific functional groups (-NH₂) but also matching target molecule size. The acrylamide monomer and PFOA target molecules polymerized together. The target molecules were removed and left a special polymer with voids of particular shape and size [16]. However, some functional monomers that did not form complexes remained on the surface of the polymer after polymerization. These monomers and remaining cross-linker provided the possibility of nonspecific adsorption via hydrogen bonding [15]. Hence, the NIP-TiO₂ NTs exhibited enhanced absorption capacity compared with that of the TiO₂ NTs. The present imprinted polymerization process is therefore thought to result in high recognition of the target pollutant and its removal.

3.3. Photocatalytic Degradation of PFOA

3.3.1. Degradation Kinetics

The photocatalytic activity of the MIP-TiO₂ NTs, NIP-TiO₂ NTs, and TiO₂ NTs was evaluated in aqueous PFOA solution. Figure 6 shows the decomposition of PFOA by the catalysts under UV irradiation. No significant changes in PFOA concentration were observed during control tests (without UV irradiation). Moreover, the maximum amount of PFOA adsorbed during adsorption equilibrium experiments was just 0.52 mg/L for an initial concentration of 30 mg/L. It is therefore obvious that PFOA decomposition was mainly attributed to photolysis or photocatalysis. Direct photolysis caused 22.6% PFOA degradation after 8 h UV irradiation. PFOA can be efficiently photodecomposed under light of 220–460 nm wavelengths [12, 20]. The degradation of PFOA in the presence of TiO₂ NTs or NIP-TiO₂ NTs (41% and 67%, resp.) was more efficient than that of the direct photolysis. In the presence of MIP-TiO₂ NTs, the decomposition ratio of PFOA dramatically increased to over 84% after 8 h irradiation. The photocatalytic reaction kinetics followed the Langmuir-Hinshelwood model [6]:

The reaction mechanism can be approximated to a pseudo-first-order kinetic reaction. In (2), is the reaction rate, is the PFOA concentration of the solution, is the time, and is the first-order rate constant. PFOA decomposition followed pseudo-first-order kinetics with rate constants of 0.0006, 0.0011, 0.0022, and 0.0036 min⁻¹ for direct photolysis (Table 3), and degradation in the presence of TiO₂ NTs, NIP-TiO₂ NTs, and MIP-TiO₂ NTs, respectively. Thus, it is clear that the MIP-TiO₂ NTs showed the greatest photocatalytic activity for PFOA decomposition, with a higher decomposition rate than the other methods.

The enhanced adsorptivity of the MIP layer increased the opportunity of contaminants coming into contact with the TiO₂ material [21–23]. It is reported that the adsorption of contaminants on photocatalyst surfaces is a prerequisite for photodecomposition, because the degradation reaction occurs on the surface of a catalyst rather than in bulk solution [15]. Based on the above analysis of adsorption performance, the MIP layer on the TiO₂ NTs surface provided special binding sites and hydrogen bonding for PFOA adsorption, which caused the MIP-TiO₂ NTs to exhibit outstanding adsorption capacity and photocatalytic activity towards the template compounds. Furthermore, negatively charged surface was formed after PFOA (C₇F₁₅COO⁻) was adsorbed on the surface of the MIP-TiO₂ NTs. When the titanium dioxide was excited under UV irradiation, electrostatic attraction between this negatively charged and the catalyst surface would have retarded charge recombination and promote surface reactions with valence band holes (h⁺), which are advantageous in PFOA decomposition and defluorination [9, 24].

The amount of fluoride ions (F⁻) present in the reaction solutions was determined by IC. The changes in the concentration of PFOA and F⁻ are shown in Figure 7. The defluorination ratios were calculated as follows:where is concentration of fluoride ions (μmol/L), is the initial concentration of PFOA (72.5 μmol/L), and the factor of 15 corresponds to the number of fluorine atoms in one PFOA molecule. After 8 h irradiation, the defluorination of PFOA by direct photolysis, TiO₂ NTs, NIP-TiO₂ NTs, and MIP-TiO₂ NTs was 5.4%, 9.7%, 15.7%, and 30.2%, respectively. Figure 7(b) shows that the amount of that responded to the change of PFOA concentration gradually increased with irradiation time in the presence of MIP-TiO₂ NTs. The PFOA defluorination ratios were much smaller than the PFOA decomposition ratios. This implies that intermediate products formed during photocatalysis [8, 10, 11]. Figure 7(c) shows the trends of TOC that responded to the change of PFOA concentration in the presence of MIP-TiO₂ NTs. As can be seen, almost 46% of TOC was removed. It is possible that the total F content of the aqueous reaction solutions consisted of four parts, that is, remaining PFOA, shorter-chain PFCs, , and PFCs adsorbed on the catalyst surface [11, 13].

(a)

(b)

(c)

3.3.2. Selective Photocatalysis

To investigate the selectivity of the MIP-TiO₂ NTs, the photocatalytic activity of the material for PFOA decomposition was compared with that observed for PFOS, PFHA, and 2,4-D decomposition in the presence of MIP-TiO₂ NTs or NIP-TiO₂ NTs. Although these pollutants all exhibit anionic property in aqueous solution, they have different molecular structures. All of the degradation experiments were carried out under the same conditions, and the pollutants were all the same concentration of 50 μmol/L. The results are given in Table 4. As expected, the MIP-TiO₂ NTs exhibited the highest degradation efficacy for PFOA among the pollutants and markedly enhanced photodegradation for all the target pollutants. The apparent rate constant () for PFOA degradation and the selectivity () in single-solute are also shown in Table 4. Comparison of the observed of the MIP and NIP-TiO₂ NTs for the three pollutants suggests that the MIP is selective for PFOA but nonselective for the other pollutants. PFOS and PFOA are linear C8 compounds, while 2,4-D has a benzene ring in its molecular structure, which affected the recognition effect and resulted in low removal rates [16, 19]. PFHA and PFOA have similar molecular structures with long-chain -CF₂ and end carboxylic groups, so the PFHA removal rate was closer to that of PFOA. The higher rate constant observed for 2,4-D using the MIP-TiO₂ may be attributed to its carboxylic groups similar to those of PFOA. Moreover, the results indicated that MIP-modified TiO₂ might selectively remove a group of PFCs from water.

Competitive degradation experiments were carried out by measuring the concentration of the photocatalytic target PFOA (50 μmol/L) in the absence or presence of competitors (25 μmol/L). The results are shown in Figure 8. Here, the PFOA removal rate is given to display the effects of the competitors on the photodegradation. When no competitive pollutant was added, the PFOA removal percentage was 89% in the presence of MIP-TiO₂ NTs. The removal percentage was decreased to 65.8%, 74.3%, and 83.7% when PFHA, PFOS, and 2,4-D were added as competitors, respectively. Obviously, the displacement of the competitors was dependent on their structure; the two competitive pollutants (PFHA and PFOS) with similar structure to that of the target (PFOA) significantly inhibited the photodegradation of the target [16, 21]. In the presence of NIP-TiO₂ NTs, the pollutants displayed competitive adsorption on the catalyst surface and absorption of reactive oxygen species. Therefore, the above results demonstrate that MIP not only had high photocatalytic efficiency, but also possessed a strong ability to selectively photodegrade PFCs in mixed solutions.

3.4. Degradation in Secondary Effluent

In both WWTP secondary effluent and natural water, PFOA generally coexists with other chemical compounds, such as organic pollutants, natural organic matter, nitrate, and bicarbonate, which may reduce the PFOA decomposition efficiency by TiO₂ photocatalysis [13, 25]. To evaluate the feasibility of MIP-TiO₂ NTs to decompose PFOA in real wastewater, we investigated the decomposition of PFOA added to secondary effluent taken from a municipal wastewater plant (in Suzhou, China), in which the anaerobic-anoxic-oxic process was used as a secondary treatment.

The secondary effluent contained a total organic content (TOC) of 10.2 mg/L and had a pH of 7.2. The pH of the reaction solution was adjusted to 5.0. The experiments of PFOA degradation in secondary effluent (SE) and pure water (PW) were carried out. Figure 9 shows the decomposition of PFOA by only UV and in the presence of the photocatalysts in both the secondary effluent (SE) and pure water (PE). After 8 h reaction in pure water, 22.6%, 67%, and 84% of the PFOA were decomposed. Additionally, 18%, 50.2%, and 81.1% were decomposed in the secondary effluent by UV, UV/NIP-TiO₂ NTs, and UV/MIP-TiO₂ NTs, respectively. It is evident that the degradation of PFOA was almost inhibited in secondary effluent.

Without any photocatalyst, PFOA decomposed more efficiently in pure water than in secondary effluent under UV light irradiation. Giri et al. found that water quality profoundly impacted PFOA photomineralization [26]. Therefore, the difference in the photoreaction results can be explained by the fact that organic and inorganic matters were directly or indirectly responsible for the decreased PFOA degradation observed in the organic-rich (SE) water rather than acting as natural sensitizers for promotion of PFOA degradation [26, 27]. For the NIP-TiO₂ NTs, the superior degradation efficiency observed in pure water could be attributed to the lower amounts of organic and inorganic matters coexisting compared with those in the secondary effluent. Organic matter in the secondary effluent may have competed for adsorption sites on the surface of the NIP-TiO₂ NTs and scavenge hydroxyl radicals [17, 25]. Additionally, any inorganic salts present could also act as scavengers of hydroxyls and other oxidizing radical species and produce less reactive ion-radicals. However, anions have been reported to have little influence on the sorption of target PFCs by MIP or NIP-adsorbents at low salt concentrations [19].

Moreover, the MIP-TiO₂ NTs exhibited significant photocatalytic activity in the secondary effluent, in which the PFOA removal efficiency was about the same as that in pure water owing to the considerable selectivity of the MIP-TiO₂ NTs. Thus, water quality had little influence on PFOA degradation by the MIP-TiO₂ NTs. Footprint cavities generated on the surface of the MIP-TiO₂ NTs may have inhibited the competitive adsorption between PFOA and organic matter. Furthermore, PFOA was preferentially adsorbed to the surface of MIP-TiO₂ NTs and was ionized to anionic PFOA (C₇F₁₅COO⁻) because the initial pH of the solution was 5 [9, 24]. Thus, to a certain extent, the negatively charged surface formed on the MIP-TiO₂ NTs would have produced a repulsion that decreased the scavenging of hydroxyl and other oxidizing radical species. It is deduced that this effect may be one of the main factors accounting for the observed difference in PFOA removal by the MIP-TiO₂ NTs and NIP-TiO₂ NTs in secondary effluent. This reason may also explain the slight difference in PFOA removal observed in secondary effluent and pure water.

3.5. Effects of Scavengers

To clarify whether photogenerated oxidation species induced PFOA decomposition, the effects of chosen scavengers, namely, bulk water hydroxyl radicals (t-butanol), oxidant holes (2-propanol), electrons (KBrO₃), and superoxide radicals (p-benzoquinone), were investigated at pH 5 in aerated solution [28–30].

As shown in Figure 10, the presence of t-butanol, 2-propanol, and p-benzoquinone in reaction solution suppressed PFOA photocatalytic degradation. Among them, t-butanol and p-benzoquinone slightly inhibited photocatalysis, suggesting that hydroxyl radicals or superoxide radicals rarely participate in the photocatalytic degradation of PFOA. However, 2-propanol obviously restrained the oxidation of PFOA into short-chain perfluorinated compounds. The 2-propanol acted as a hole-scavenger to decrease the chance of reaction between hole and perfluoroalkyl anions (C₇F₁₅COO⁻). These results indicated that photogenerated holes are the main oxidant for PFOA decomposition, which also verifies why the MIP-TiO₂ NTs were superior to the other catalysts in the degradation kinetics experiments. KBrO₃ was found to enhance the PFOA oxidation process, partially owing to increased charge separation. This effect was caused by the acceptance of conduction band electrons by KBrO₃ [29]:

Based on the present results and those reported in the literature [6, 9, 10, 24], PFOA degradation is mediated predominantly through the action of holes generated on the TiO₂ surface. The proposed PFOA degradation mechanism is initiated by the excitation of TiO₂ caused by UV irradiation; holes generated from excited TiO₂ accept one electron from dissociated PFOA (C₇F₁₅COO⁻), generating PFOA radicals [6, 9, 10]. PFOA exists as anionic compound when it enters the reaction solution [24] and is absorbed on the MIP-TiO₂ surface. This part of PFOA (C₇H₁₅COO⁻) reacts with valence band holes (h⁺) to form perfluoroperoxy radicals (6), which is confirmed by various studies in which the start of PFOA decomposition was reported to depend on the carboxylic functional group:

The radicals are highly unstable and thus spontaneously undergo Kolbe decarboxylation to form radicals via (7) [6, 9, 24]. The formed might subsequently react with water and electrons () on the TiO₂ surface and further undergo H⁺ and F⁻ elimination to form C₆F₁₃COF. After hydrolysis, C₆F₁₃COF is converted to C₆F₁₃COOH with removal of CF₂ units. Similarly, shorter-chain forms stepwise over time accompanied by the loss of a CF₂ unit:

4. Conclusions

Molecularly imprinted polymer-modified TiO₂ nanotubes were synthesized. The molecular-imprinted polymer provided the TiO₂ NTs with enhanced adsorption and selective photocatalytic activity toward PFOA. Our results indicate that these enhanced properties should mainly be attributed to footprint cavities and hydrogen bonding on the surface of the catalyst. Furthermore, the negative charge formed on the MIP-TiO₂ NTs surface retarded charge recombination to further accelerate PFOA decomposition. The modified TiO₂ NTs had outstanding selectivity for the target compound PFOA and anti-interference properties toward other substances in secondary effluent. The effects of chosen scavengers on reactive oxygen species clarified that the PFOA degradation behavior of the present catalysts is mediated predominantly through the action of generated holes on the TiO₂ surface. The proposed PFOA degradation mechanism was given. Photocatalytic oxidation using MIP-TiO₂ NTs is expected to be a promising approach for effectively eliminating PFCs from water.

Conflict of Interests

The authors declare that there is no conflict of interests regarding the publication of this paper.

Acknowledgments

The study was financially supported by the National Natural Science Foundation of China (nos. 51322901 and 51479066), Foundation for Innovative Research Groups of the National Natural Science Foundation of China (51421006), a Project Funded by the Priority Academic Program Development of Jiangsu Higher Education Institutions, Foundation of Jiangsu Province Key Laboratory of Environmental Engineering (ZX2014003), and the Major Science and Technology Program for Water Pollution Control and Treatment (2012ZX07506-002).

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Copyright © 2016 Yunbo Wu 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.

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