Scholarly article on topic 'Application of Glass Fiber-Based N-Doped Titania under Visible-Light Exposure for Photocatalytic Degradation of Aromatic Pollutants'

Application of Glass Fiber-Based N-Doped Titania under Visible-Light Exposure for Photocatalytic Degradation of Aromatic Pollutants Academic research paper on "Chemical engineering"

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International Journal of Photoenergy
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Academic research paper on topic "Application of Glass Fiber-Based N-Doped Titania under Visible-Light Exposure for Photocatalytic Degradation of Aromatic Pollutants"

Hindawi Publishing Corporation International Journal of Photoenergy Volume 2014, Article ID 219317, 9 pages

Research Article

Application of Glass Fiber-Based N-Doped Titania under Visible-Light Exposure for Photocatalytic Degradation of Aromatic Pollutants

Wan-Kuen Jo,1 Seung-Ho Shin,1 and Ho-Hwan Chun2

1 Department of Environmental Engineering, Kyungpook National University, Daegu 702-701, Republic of Korea

2 Department of Naval Architecture and Ocean Engineering, Pusan National University, 63 Jangjeon-dong, Geumjeong-gu, Busan 609-735, Republic of Korea

Correspondence should be addressed to Wan-Kuen Jo;

Received 5 February 2014; Revised 13 March 2014; Accepted 13 March 2014; Published 31 March 2014 Academic Editor: Jiaguo Yu

Copyright © 2014 Wan-Kuen Jo 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.

Flexible glass fiber-supported nitrogen-doped titanium dioxide (GF-N-TiO2) photocatalysts with different N/Ti ratio were prepared using a dip-coating method followed by a low-temperature heat-treatment process. In addition, their photocatalytic activities were evaluated for the degradation of aromatic volatile organic compounds (VOCs) under visible-light irradiation. The prepared GF-N-TiO2 photocatalysts were characterized using scanning electron microscopy, energy-dispersive X-ray spectroscopy, X-ray diffraction spectroscopy, and UV-visible spectroscopy. A control photolysis test performed using an uncoated GF displayed no detectable degradation of the target compounds under visible-light irradiation. The outlet-to-inlet concentration ratios of the target pollutants obtained using the GF-N-TiO2 photocatalysts were lower than that obtained using the GF-TiO2 photocatalyst. The photocatalytic activity of GF-N-TiO2 photocatalyst increased as the N-to-Ti ratio increased from 0.06 to 0.08 but decreased gradually as the N-to-Ti ratio increased further to 0.12, suggesting the existence of optimal N/Ti ratios. The outlet-to-inlet concentration ratio of all the target compounds displayed an increasing trend as both air flow rate and inlet concentration increased. Overall, the GF-N-TiO2 photocatalysts could be applied effectively for the degradation of aromatic VOCs under visible-light irradiation when operation conditions are optimized.

1. Introduction

A significant amount of concern has been directed to volatile organic compounds (VOCs) due to not only their widespread presence in various environments but also their environmental health hazards. Particularly, monocyclic aromatic VOCs, including toluene, ethyl benzene, and xylene (TEX), which originate mainly from traffic emissions in urban environments, industrial combustion processes, solvent and petroleum handling, and other industrial processes, are frequently measured at high concentration levels [1]. Ambientair TEX can infiltrate buildings, exacerbating indoor air pollution [2]. Indoor air quality can be worsened due to TEX emissions from various indoor sources, such as building finishing materials, furniture, and household products [3, 4]. Moreover, TEX even at sub-ppm concentrations are

potentially toxic to human beings [5], necessitating the development of control tools to lower health risks to building occupants from indoor air exposure.

Titanium dioxide (TiO2) is a representative semiconductor photocatalyst that has been extensively used for environmental pollutant purifications. However, it has a major drawback in its practical application in that it is functional under only UV exposure conditions because of its wide band gap [6]. To address this drawback of TiO2, several strategies have been applied by a great deal of research groups; these strategies have included nonmetal deposition [7, 8], metal deposition [9, 10], dye sensitization [11], semiconductor coupling [12], and carbon materials coupling [13, 14]. Among them, nonmetal N-doping has received special attention for environmental applications, mainly because N can be easily incorporated into two different sites of the

bulk phase of TÍO2 owing to its atomic size comparable with oxygen and small ionization energy [15, 16]. Even though there are certain questions that remain to be answered to understand the photocatalytic mechanism and behavior of N-doped TiO2 (N-TiO2) under visible-light exposure [17-20], several research groups foundthat N-TiO2 photocatalysts had superior photocatalytic activity to unmodified TiO2 under visible-light irradiation for decomposition of a variety of gaseous and aqueous environmental pollutants [8,15,21,22].

Application of nanomaterials for environmental treatments necessitates a supporting substrate to minimize the separation of suspended powders in aqueous media or their uncontrolled dispersion in treated air, problems encountered in water, and air applications, respectively [23,24]. A range of substrates as a nanomaterial support have been investigated for the photocatalytic degradation of environmental pollutants, including activated carbon powders [25], activated carbon fiber [26, 27], glass beads [28, 29], glass tubes [21], and polymer materials [30,31]. Among these substrates, glass fiber has received particular attention primarily because of its flexibility, which enables the materials to be fitted in various geometrical-shape photocatalytic reactors [32, 33]. Moreover, Panniello et al. [32] reported that glass fiber-supported Fe-doped TiO2 prepared by a combined hydrolysis and dip-coating method displayed superior photocatalytic performance to a reference P25 TiO2 for degradation of aqueous orange dye. However, the feasibility of other types of photocatalysts, including N-TiO2, which are supported by glass fiber for the treatment of environmental pollutants, is another recent topic of research that requires further examination. Consequently, in this study, the feasibility of applying glass fiber-supported N-TiO2 (GF-N-TiO2) under visible-light exposure to degradation of TEX at sub-ppm concentrations typically associated with indoor air quality issues was investigated.

2. Experimental

2.1. Preparation and Characterization of GF-N-TiO2 and GF-TiO2. GF (11.5 x 22.0 cm, Hyundai Fiber) was thermally pretreated and then cleaned using methanol and distilled water. The GF was heated at 350oC for 4h in an electric furnace to burn away organic residues on the GF surface. The pretreated GF was washed sequentially with 2-propanol, acetone, and distilled water, after which it was dried at 125oC for 2 h in a dry oven. The dried GF was further treated with NaOH (98%, Sigma-Aldrich) and distilled water and then dried at 125oC for 2 hin the dry oven.

N-TiO2 powder was prepared using commercially available P25 TiO2 powder and urea asaN source. Briefly, 10 g of TiO2 powder was added to specified amounts of urea solution (0.7 M, Sigma-Aldrich) in a Pyrex flask and then rigorously stirred for 2 h under room temperature conditions. Urea solutions of 19, 25, 31, and 37 mL were used to synthesize N-TO2 powders having N-to-Ti ratios of 0.06, 0.08, 0.10, and 0.12, respectively. The flask was wrapped with aluminum foil to prevent transmission gain of light from laboratory fluorescent lamps and then kept for 24 h. Subsequently, the mixture in the flask was dried for 48 h under reduced pressure conditions to

Figure 1: Photograph of as-prepared N-TiO2 powder.

give a white p owder. This powder was calcined at 55 0° C for 5 h in an electric furnace, after which it was washed with diluted H2SO4 (10%, Sigma-Aldrich), and then distilled water until the pH value of washed water reached 7. The washed powder was vacuum-dried for 12 h and then pulverized using an agate mortar to obtain N-TiO2 powder (Figure 1).

The GF-N-TiO2 photocatalyst was prepared using a dip-coating method followed by a low-temperature heat-treatment process. Specifically, 50 mL titanium (IV) isopropoxide (TTIP, 97%, Sigma-Aldrich) was added to 10 mL glacial acetic acid (99%, Sigma-Aldrich) with stirring. This solution was mixed with 1000 mL distilled water followed by addition of 10 mL nitric acid (98%, Sigma-Aldrich) to this solution. Subsequently, the mixture was stirred, until a white precipitate was observed, and then heated at 80°C for 5hinan oil bath to obtain a transparent sol. The previously prepared N-TiO2 powder (2 g) was added to this sol, after which this mixture was sonicated for 1 h to obtain the final coating solution. The previously cleaned GF was dipped into the coating solution (500 mL) in a home-made glass container (12 cm x 23 cm x 2 cm) for 10 min, taken out slowly, and dried at room temperature for 2h. These dip-coating and drying processes were conducted in triplicate to give high coating amounts. GF-N-TiO2 powders having N-to-Ti ratios of 0.06, 0.08, 0.10, and 0.12 were named as GF-N-TiO2-0.06, GF-N-TiO2-0.08, GF-N-TiO2-0.10, and GF-N-TiO2-0.12, respectively. In addition, a reference photocatalyst, GF-TiO2, was prepared using P25 TiO2 instead of N-TiO2, following the same coating procedure as used for the preparation of GF-N-TiO2. The characteristics of as-prepared GF-N-TiO2, GF-TiO2, and pretreated GF were determined using scanning electron microscopy (SEM, Hitachi S-4300 FE-SEM), energy-dispersive X-ray spectroscopy (EDX, Hitachi EDX-350), X-ray diffraction spectroscopy (XRD, Rigaku D/max-2500 diffractometer), and UV-visible spectroscopy (Varian CARY 5G). For the EDX analysis, the sample was pretreated using a Pt-coating system (Hitachi E-1030).

2.2. Determination of Aromatic VOC Degradation Efficiencies. The degradation efficiencies of aromatic VOCs were

investigated using GF-N-TiO2, GF-TiO2, and GF, which were placed in a cylindrical photocatalytic reactor. The reactor was prepared using a Pyrex tube (a length of 26.5 cm and an inner diameter of 3.8 cm), where a cylindrical-shaped daylight lamp (F8T5DL, Youngwha Lamp Co.) with a spectral range of 400720 nm was inserted. The light intensities provided by the daylight lamp were 3.2 mW cm-2 at a distance from the light source to the surface of photocatalysts. The inner surface of the Pyrex tube was covered by a GF-Fe-TiO2, GF-TiO2, or GF sheet. Zero-grade dried air was supplied by an air cylinder and was allowed to flow through a carbon filter for repurification. The dried air stream flowed through two water-containing impingers in tandem, which were partially immersed in a water bath, for air humidification. The relative humidity (RH) levels were adjusted by controlling the mixing ratio of dried with humidified air flows. Standard compounds were prepared by adjusting the mixing ratio of the humidified air with TEX prepared by vaporizing liquid standards, which were injected into a heated glass chamber via a syringe pump (KDS 210, KD Scientific). Lastly, the prepared standard compounds were transferred to the reactor for photocatalytic decomposition efficiency tests. The degradation efficiency tests were conducted under different operational conditions by controlling two important factors: air flow rate (AFR:

1.0, 2.0, 3.0, and 4.0Lmin-1) and initial concentration (IC: 0.1, 0.5, 1.0, and 2.0 ppm). When evaluating a specific factor, the other factor was held constant at the following values: IC, 0.1 ppm, and AFR, 1.0Lmin-1. In addition, the RH was fixed at 45%, which represents a comfortable value for typical indoor life.

Air measurements were carried out at the inlet and outlet ports of the cylindrical reactor by drawing air through a stainless steel tubing trap containing Tenax GC adsorbent. Gaseous species collected in the adsorbent trap were analyzed using a gas chromatograph/mass spectrometer (Perkin Elmer Clarus SQ 8) (GC/MS) coupled to a thermal desorbing device (Perkin Elmer ATD 350). The gases were qualitatively analyzed based on both their retention times and mass spectra (Wiley 275 software library). Each chemical species was qualitatively analyzed based on calibration curves, which were determined using five concentrations standardized to an internal standard chemical. For the quality control program, a laboratory blank and spiked standard trap samples were analyzed. The entire experimental procedure was repeated three times to give more reliable data and the average values are presented in this paper.

3. Results and Discussion

3.1. Characteristics of As-Prepared Photocatalysts. The surface characteristics of a representative GF-N-TiO2 with a N-to-Ti ratio of 0.08 (GF-N-TiO2-0.08) as well as a reference photocatalyst (GF-TiO2) were examined using SEM, EDX, XRD, and UV-visible absorption analyses. Based on the SEM micrographs (Figure 2), GF-N-TiO2-0.08 showed a better coating of N-TiO2 on GF relative to GF-TiO2. The enhanced coating efficiency for GF-N-TiO2-0.08 was ascribed to the strong agglomerating nature of N-TiO2 [17]. Consistently, previous researchers [22,34] have found a higher aggregation

Figure 2: Scanning electron microscopy of GF-N-TiO2 with a N-to-Ti ratio of 0.08 (GF-N-TiO2-0.08) and GF-TiO2.

property of N-TiO2 as compared to pure TiO2 by SEM analysis.

As illustrated in Figure 3, the EDX spectrum of GF-N-TiO2-0.08 showed peaks of Ti, O, and N atoms, whereas the spectrum of GF-TiO2 showed only Ti and O atom bands; those bands assigned to Ti and O atoms were associated with TiO2, while the N atom band was ascribed to N atoms embedded in the TiO2 lattice. Therefore, EDX spectra analysis demonstrated that N atoms could be successfully incorporated into TiO2 to allow the prepared photocatalyst be activated under visible-light irradiation conditions. In agreement with our results, Gurkan et al. [22] found the existence of N atoms for N-TiO2 synthesized using a wet incorporation process through EDX analysis. The undesignated peaks in the EDX spectra were attributed to Pt, which was used for sample coating prior to EDX analysis; no other evident impurities were observed in the samples.

Figure 4 illustrates the XRD spectra of GF-N-TiO2-0.08 and the reference GF-TiO2 photocatalyst. Both photocatalysts displayed an anatase phase with a major band at 25.3° 2d and a rutile phase with a major band at 27.3° 20. These diffractograms were similar to those of Degussa P25 TiO2 reported in other studies [22, 35], indicating that N incorporated into TiO2 for the GF-N-TiO2-0.08 photocatalyst did not alter the crystal structures of TiO2. Gurkan et al. [22] also reported that the XRD patterns of N-TiO2 were similar to those of pure P25 TiO2. However, any N dopant-associated bands were not found in the spectrum of GF-N-TiO2-0.08. These findings suggest that N atoms would not chemically

4 5 6 Energy (keV)

Figure 3: Energy-dispersive X-ray images of GF-N-TiO2 with a N-to-Ti ratio of 0.08 (GF-N-TiO2-0.08) and GF-TiO2.

react to produce new crystalline structures, such as TiN, but are rather incorporated interstitially and substitutionally into the TiO2 structure [15]. Otherwise, low amounts of N atoms impregnated into TiO2 in GF-N-TiO2-0.08 could not be detected by XRD possibly due to its limited measurement sensitivity.

The sizes of crystal phases of the GF-N-TiO2 photocatalysts and reference GF-TiO2 were estimated based on the Scherrer formula [36]. The anatase crystallite size of GF-N-TiO2-0.08 (36.61 nm) was smaller than that of GF-TiO2 (39.31 nm), while the crystallite sizes of GF-N-TiO2-0.06, GF-N-TiO2-0.10, and GF-N-TiO2-0.12 were 36.49, 36.72, and 37.04 nm, respectively. Gurkan et al. [22] also reported a smaller crystallite size for N-TiO2 powder relative to that of pure TiO2 powder. The reduction in the crystallite size observed for GF-N-TiO2-0.08 was ascribed to the formation of compressive strain in the crystallite structure, which would likely be due to the transformation of electronic structure resulting from N dopant ion incorporation into TiO2 [22].

Figure 5 shows the UV-visible spectra of the GF-N-TiO2 photocatalysts and reference GF-TiO2. The reference GF-TiO2 exhibited an absorption edge at a wavelength of around 420 nm, which was in good agreement with that reported in previous studies [22, 34]. In contrast, the UV-visible spectra

R GF-N-TiO2-0.08


R RlJ,

20 (deg)

A: Anatase R: Rutile

Figure 4: X-ray diffraction patterns of GF-N-TiO2 with a N-to-Ti ratio of 0.08 (GF-N-TiO2-0.08) and GF-TiO2.

300 400 500 600 700 800

Wavelength (nm)

- GF-N-TiO2-0.06 GF-N-TiO2-0.12

...... GF-N-TiO2-0.08 -- - GF-TiO2

Figure 5: UV-visible spectra of GF-N-TiO2-0.06, GF-N-TiO2-0.08, GF-N-TiO2-0.10, GF-N-TiO2-0.12, and GF-TiO2.

of GF-N-TiO2 photocatalysts were highly shifted toward the visible region, which was consistent with the results reported by Gurkan et al. [22]. These shifts toward the visible region of the spectrum were attributed to the generation of a narrowed band gap level, which is located between the valence and conduction bands of TiO2. Overall, it was suggested that the prepared GF-N-TiO2 photocatalysts could be functional under visible-light irradiation as well.

3.2. Photocatalytic Degradation of Aromatic VOCs. The photocatalytic degradation of TEX was conducted using the prepared GF-N-TiO2 photocatalysts with different N-to-Ti ratios and GF-TiO2 under visible-light irradiation following three-hour adsorption process. As shown in Figure 6, a control photolysis test performed using an uncoated GF displayed no degradation of TEX at all under visible-light irradiation,

GF-N-TiO2 -0.10

0.9 0.8

0.7 1 i

с и 0.6 i ! / !

0.5 i ' / ■ /

0.4 ¡//s

0.3 '/ / // // / ,/ /

0.2 '¡/У/


1.0 0.9 0.8 0.7 0.6 0.5 0.4 0.3 0.2 0.1 0.0

1 2 Time (h)

1 2 Time (h)

Time (h)

-•- GF-N-TiO2-0.06 GF-N-TiO2-0.12

-■о-- GF-N-TiO2-0.08 GF-N-TiO2

GF-N-TiO2-0.10 --□- GF

Figure 6: Time-series ratios (Cout/Cin) of outlet-to-inlet concentrations of (a) toluene, (b) ethyl benzene, and (c) o-xylene as obtained using GF-N-TiO2 photocatalysts with different N-to-Ti ratios (GF-N-TiO2-0.06, GF-N-TiO2-0.08, GF-N-TiO2-0.10, and GF-N-TiO2-0.12), GF-TiO2, and GF.

which was demonstrated by similar values for inlet and outlet concentrations of TEX. In addition, Figure 5 shows the outlet to inlet concentrations of TEX determined for four GF-N-TiO2 photocatalysts (GF-N-TiO2-0.06, GF-N-TiO2-0.08, GF-N-TiO2-0.10, and GF-N-TiO2-0.12) and the reference GF-TiO2 photocatalyst over three-hour photocatalytic process. The outlet-to-inlet concentration ratios of the three target pollutants obtained using the GF-N-TiO2 photocatalysts were lower than that of the GF-TiO2 photocatalyst, indicating that GF-N-TiO2 photocatalysts had higher photocatalytic activity toward the degradation of TEX. For example, the average outlet-to-inlet concentration ratios of TEX for GF-N-TiO2-0.06 were 0.51, 0.18, and 0.09, respectively, while those of the GF-TiO2 photocatalyst were 0.90,0.76, and 0.67, respectively. Similarly, Gurkan et al. [22] demonstrated a higher photocatalytic activity for the degradation of cefazolin in the aqueous phase relative to undoped TiO2 under sunlight irradiation.

Jo and Kim [21] also reported that daylight lamp-irradiated N-TiO2, which was coated directly onto the inner wall of a Pyrex tubing reactor, showed superior performance for the degradation of aromatic VOCs compared to unmodified TiO2. The superior photocatalytic activity of the GF-N-TiO2 photocatalysts under visible-light irradiation was ascribed to their predisposition for visible-light absorbance owing to large specific surface area and the reduced impurity level localized in the top of valence band, as demonstrated from their UV-visible spectra (Figure 5), since the photocatalytic reaction rates are proportional to the amount of photon absorption by the photocatalysts [6, 37-40]. The smaller crystallite size of GF-N-TiO2 photocatalysts relative to the GF-TiO2 photocatalyst would also enhance their photocatalytic activity. Consequently, it was suggested that GF-N-TiO2 photocatalysts with visible-light activation can be applied to effectively degrade aromatic VOCs.

С 0.6 -

и 0.4 -

0.2 - i

Time (h) (a)

1L min 2 L min-

Time (h)

3L min-4L min-

Time (h) (b)

Figure 7: Time-series ratios (Cout/Cin) of outlet-to-inlet concentrations of (a) toluene, (b) ethyl benzene, and (c) o-xylene as obtained using GF-N-TiO2-0.08 according to air-stream flow rates.

As also demonstrated in Figure 6, the photocatalytic activity of the GF-N-TiO2 photocatalyst increased as the N-to-Ti ratio increased from 0.06 to 0.08, but then decreased gradually as the N-to-Ti ratio increased further to 0.12. These results indicate that there is an optimal N-to-Ti ratio range for the synthesis of GF-N-TiO2 photocatalysts. The decreasing pattern for high N-to-Ti ratios was attributed to increased particle aggregation due to high amounts of N dopant, which results in the reduction in photocatalyst surface area [22]. The high amounts of N dopant might also decrease the separation distance of charge carriers, which result in an increase in the recombination of electron-hole pairs.

Figure 7 illustrates the outlet-to-inlet concentration ratios of TEX obtained using GF-N-Ti02-0.08 according to AFRs. The outlet-to-inlet concentration ratio of all the target compounds displayed an increasing trend as AFR increased, indicating that the photocatalytic activity of GF-N-Ti02-0.08 decreased with increasing AFRs. Particularly, the average ratios of TEX increased from 0.47 to 0.82, 0.11 to 0.71,

and 0.09 to 0.59, respectively, as the AFR increased from 1 to 4 L min- . In agreement with our results, Jeong et al. [41] reported that the photocatalytic activity of Degussa P25 TiO2 for the degradation of benzene and toluene under UV irradiation showed a decreasing trend with increasing AFRs. These results might be ascribed to the mass transfer rate of the pollutant molecules from the air stream to the photocatalyst surface as well as photocatalytic reaction kinetics [42]. Unlike batch reactors, the mass transfer rates of gas-phase compounds in continuous-flow photocatalytic reactors are closely associated with the linear face velocities of the air stream [43]. In the present study, the linear face velocities increased as the AFR increased: the linear face velocities for AFRs of 1, 2, 3, and 4 L min-1 were 4.8,9.6,14.4, and 19.2 cm s-1,respectively. These results suggested that the photocatalytic activity of the GF-N-TiO2-0.08 would increase as the AFR increased, owing to high mass-transfer rates; rather, the photocatalytic activity of GF-N-TiO2-0.08 decreased with increasing AFR. As such, the low photocatalytic activity of GF-N-TiO2-0.08 at

0.9 0.8 0.7 a °.6 1 0.5

<J 0.4 0.3 0.2 0.1 0.0

iT — " ■ /

!/?..... /7if_

Hi/ Hi </•/

Time (h) (a)

u 0.5 -

Time (h) (b)

■ —A--------A---- ---A

0.1 ppm 0.5 ppm

Time (h)

1.0 ppm 2.0 ppm

Figure 8: Time-series ratios (Cout /Cin) of outlet-to-inlet concentrations of (a) toluene, (b) ethyl benzene, and (c) o-xylene as obtained using according to inlet concentrations.


high AFRs was attributed to an insufficient reaction time in the photocatalytic reactor, suggesting that the photocatalytic activity of GF-N-Ti02-0.08 was likely limited by reaction kinetics on the photocatalyst surfaces. The reaction times for AFRs of 1, 2, 3, and 4 Lmin-1, which were calculated by dividing the empty-space reactor volume by the AFRs, were 6.1, 3.1, 2.0, and 1.5 s, respectively.

Figure 8 shows the outlet-to-inlet concentration ratios of TEX obtained using GF-N-Ti02-0.08 according to ICs. For all target compounds, the outlet-to-inlet concentration ratio increased as IC increased, indicating that the photocatalytic activity of GF-N-Ti02-0.08 decreased with increasing ICs. At the lowest IC (0.1 ppm), the average ratios of TEX were 0.41, 0.10, and 0.07, respectively, whereas those at the highest IC (2.0 ppm) were 0.79, 0.49, and 0.42, respectively. Devahasdin et al. [44] also found that the photocatalytic degradation efficiencies of unmodified Ti02 for degradation of NO under UV irradiation decreased from 70-15% when IC was increased from 5-60 ppm. In addition, Jeong et al. [41] reported that the photocatalytic degradation efficiency of toluene determined

using Degussa P25 Ti02 decreased gradually as IC increased from 0.6-10 ppm. The descending trend in photocatalytic activity with increasing IC was ascribed to competitive adsorption among TEX molecules on the catalyst surface; adsorption of chemical molecules onto the catalyst surface is known to be a crucial factor influencing the photocatalytic degradation of organic compounds [6].

4. Conclusions

This study investigated the applicability of glass fiber-based N-doped titania (GF-N-Ti02) under visible-light exposure for the photocatalytic degradation of aromatic V0Cs. SEM results indicated the formation of aggregates for the GF-N-Ti02 photocatalyst, while EDX spectral analysis demonstrated that N elements were successfully incorporated into the Ti02 crystal lattice. The UV-visible spectra suggested that GF-N-Ti02 photocatalysts could be functional under visible-light exposure. The prepared GF-N-Ti02 photocat-alysts showed superior photocatalytic performances to the

reference GF-TiO2 photocatalyst for degradation of aromatic VOCs under visible-light irradiation. The prepared GF-N-TiO2 photocatalysts also showed a different dependence of N-to-Ti ratios on photocatalytic degradation of aromatic VOCs, indicating that there is optimal range of N-to-Ti ratios for the synthesis of GF-N-TiO2 photocatalysts. In addition, AFR and IC were both found to be major influential factors on the photocatalytic performance of the GF-N-TiO2 photocatalysts. Overall, the GF-N-TiO2 photocatalysts could be applied effectively for the degradation of aromatic VOCs under visible-light irradiation at optimal operation conditions.

Conflict of Interests

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


This work was supported by the National Research Foundation of Korea (NRF) Grant funded by the Korea government (MEST) (no. 2011-0027916) and through the GCRC-SOP (no. 2011-0030013).


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