Next Article in Journal
Nurses’ Competencies in Disaster Nursing: Implications for Curriculum Development and Public Health
Next Article in Special Issue
Behavior of VOCs and Carbonyl Compounds Emission from Different Types of Wallpapers in Korea
Previous Article in Journal
A Tale of Two City Blocks: Differences in Immature and Adult Mosquito Abundances between Socioeconomically Different Urban Blocks in Baltimore (Maryland, USA)
Previous Article in Special Issue
The Influence of Proximity to City Parks on Blood Pressure in Early Pregnancy
Font Type:
Arial Georgia Verdana
Font Size:
Aa Aa Aa
Line Spacing:
Column Width:

Feasibility of Silver Doped TiO2/Glass Fiber Photocatalyst under Visible Irradiation as an Indoor Air Germicide

Department of Civil and Environmental Engineering, University of Ulsan, Daehakro 93, Namgu, Ulsan 680-749, Korea
Author to whom correspondence should be addressed.
Int. J. Environ. Res. Public Health 2014, 11(3), 3271-3288;
Submission received: 20 January 2014 / Revised: 18 February 2014 / Accepted: 14 March 2014 / Published: 20 March 2014


This study investigated the feasibility of using Ag-TiO2 photocatalyst supported on glass fiber (Ag-TiO2/GF) prepared by a sol-gel method as an indoor air germicide. An experimental model was designed to investigate the bacterial disinfection efficiency of Staphylococcus (Staph), the most popular bacterium in hospitals in Korea, by the Ag-TiO2/GF photocatalyst. The silver content in Ag/TiO2 was altered from 1 to 10% to investigate the optimal ratio of Ag doped on TiO2/glass fiber (TiO2/GF) for photocatalytic disinfection of Staph. This study confirmed that Ag in Ag-TiO2/GF could work as an electron sink or donor to increase photocatalytic activity and promote the charge separation of electron-hole pairs generated from TiO2 after photon absorption. Ag also acts as an intermediate agent for the transfer of photo-generated electrons from the valence band of TiO2 to an acceptor (O2 gas) to promote photo-oxidation processes. The photocatalytic disinfection activity of Ag-TiO2/GF under visible light increased with the increase in silver content up to 7.5% and then slightly decreased with further increasing silver content. The highest disinfection efficiency and disinfection capacity of Staph using 7.5% Ag-TiO2/GF were 75.23% and 20 (CFU∙s−1∙cm2) respectively. The medium level of humidity of 60% ± 5% showed better photocatalytic disinfection than the lower (40% ± 5%) or higher (80% ± 5%) levels.

1. Introduction

The World Health Organization (WHO) has stated that air pollution is the sixth-leading cause of death globally, inducing over 2.4 million premature deaths per year worldwide in 2002, 1.5 million of which were attributable to indoor air pollution [1]. Exposure to bioaerosols can be associated with a wide range of adverse health effects including infectious diseases, acute toxic effects, allergies and cancer [2]. A bioaerosol is usually defined as a suspension of airborne particles that contain living organisms or is released from living organisms [3]. Bacteria, fungi, viruses, high molecular weight (HMW) allergens, bacterial endotoxins and mycotoxins are the main components of bioaerosols [2]. Among them, pathogenic bacteria can spread easily and rapidly in an aerosol, causing serious diseases, such as anthrax, tuberculosis, pneumonia, syphilis, gastroenteritis, etc. [4]. High efficiency particulate air (HEPA) filters are widely used in air conditioning systems to remove airborne particulates and microorganisms. However, filter application methods only transfer the microorganisms to another phase rather than eliminating them. In addition, air filters may themselves become a source of microbes if those retained microorganisms proliferate and are re-entrained into the filtered air [5]. Recently, the integration of photocatalysts into air purifiers has become more popular for dealing with the problems or drawbacks associated with the air filtration of bioaerosols [5,6,7,8,9].
Over the past decades titanium dioxide (TiO2) has been one of the most popular and successful photocatalysts for the remediation of contaminated water and air due to its exceptional optical and electronic properties, chemical stability, non-toxicity and low cost [10,11,12]. Matsunaga et al. first demonstrated the use of TiO2 as a biocide in 1985 [13]; since, there have been numerous studies on biological disinfection including the destruction of bacterial species [14,15,16,17,18], viruses [13,19], algae [20] and fungi [13,21]. The mechanisms of photocatalytic disinfection have been reported in various studies [22,23,24,25]. To be used as a photocatalyst, however, TiO2 should be irradiated with ultraviolet (UV) radiation. As energy that is higher than the band gap energy between the valence and the conduction bands is provided to the TiO2 catalyst, an electron in the valence band could be excited to jump to the conduction band, leaving a hole behind. The hole in the valence band reacts with surrounding water molecules or moisture to produce hydroxyl radicals (∙OH), while the electrons in the conduction band react with molecular oxygen to produce superoxide radical anions (∙O2). These oxy radical species participate in oxidation reactions to attack vital organic components of microorganisms such as cell membranes, RNA, DNA, proteins and lipids, resulting in the death of microorganisms. Because of the wide band gap of TiO2 (3.2 eV) between the valence and conduction bands, however, visible light cannot be used as a light resource to excite electrons to initiate the photocatalytic disinfection of microorganisms. Thus, enhancing the photocatalytic activity of TiO2 to expand its application under visible light is one of the most important tasks for the practical application of TiO2 in the future.
A large number of studies have been carried out to improve the photocatalytic activity of TiO2 [26,27,28,29,30]. Compared with pure TiO2, modified TiO2 techniques have many advantages in light absorption, charge recombination dynamics, interfacial charge transfer kinetics, surface structure and charge and adsorption of substrates, resulting in photocatalytic enhancement. Ag is of particular interest as a doping agent to enhance TiO2 photocatalytic activity due to its ability to act as both an electron sink and redox catalyst [31]. While acting as an electron sink to attract photoelectrons, Ag promotes the charge separation of electron-hole pairs from TiO2 after photon absorption, resulting in prevention of the fast recombination of photogenerated charge carriers [32]. The plasmon resonance in metallic silver (Ag particles) can also enhance the electric fields, facilitating electron–hole production [32]. Ag is one of the most promising metals for improving the photocatalytic disinfection property of TiO2 due to its strong and broad bactericides [33]. It is difficult to separate and regenerate photocatalytic powders from purification systems after being used as photocatalysts for water or air purification [34]. To overcome the disadvantages of photocatalysis powders, various methods have been developed, including a technique for coating TiO2 on many substrates [35]. In this study, glass fiber was used as a substrate for Ag-TiO2 coating to prepare photocatalyst Ag-TiO2/GF for photocatalytic disinfection of bioaerosols under visible light.
There have been few studies applying photocatalytic disinfection in the bioaerosol field [36]. Humidity plays a vital role regarding hydroxyl radical production in TiO2 photocatalytic systems. However, the effect of humidity on photocatalytic disinfection has not been clearly reported yet. The main purpose of this study is to investigate optimum loading ratios of photocatalyst Ag-TiO2/GF to improve photocatalytic efficiencies for bioaerosol disinfection under visible light, which has many advantages compared to UV irradiation in terms of energy consumption and application feasibility. This study also aims to investigate the effect of humidity on photocatalytic disinfection of Ag-TiO2/GF for bioaerosol removal.

2. Materials and Methods

2.1. Catalyst Preparation

A clear solution of titania was prepared from the dissolution of tetraisopropyl orthotitanate (TIOT) and nitric acid (HNO3) in distilled water with stirring for 8 h. The clear solution was used to prepare a colloidal solution of titania by holding the temperature at 60 °C for 8 h. The glass fiber with area 240 cm2 was immersed in the colloidal solution to prepare the TiO2-coated glass fiber, which was dried at 60 °C for 6 h after being removed from the colloidal solution. The designated thickness of the TiO2 layer was produced using two repeated processes and was obtained as the weight fraction of TiO2 in the TiO2/GF at 3%. A solution of 0.05 M AgNO3 was dropped on the 3% TiO2/GF to prepare Ag-TiO2/GF photocatalyst. These Ag-TiO2/GF photocatalysts with weight fractions of 1, 2.5, 5, 7.5 and 10% Ag in the Ag/TiO2 ratio were prepared by adjusting the volume addition of the AgNO3 solution. Before being used for the bacterial disinfection process all the catalyst materials were calcined at 200 °C for 2 h.

2.2. Catalyst Characterization

A Hitachi S-4700 scanning electron microscope (SEM) was used to determine the surface morphologies of the Ag-TiO2/GF photocatalytic materials. X-ray diffraction (XRD) patterns were obtained using a Bruker AXN model with a Cu-Kα radiation (λ = 1.5418 Å) source operated at a scan rate of 0.02 s−1 over a 2θ range of 10–80°. A Varian Cary 500 was used to record the UV-visible diffuse reflectance spectra (DRS) of photocatalysis materials. X-ray photoelectron spectroscopy (XPS) measurements were performed using a Thermo Fisher K-alpha model to determine the chemical composition of Ag-TiO2/GF photocatalysts.

2.3. Disinfection Experiment

For bacterial disinfection efficiency tests, this study used Staphylococcus obtained from an environmental bioengineering laboratory, University of Ulsan, Korea. For the cultivation of Staph, we applied a Luria-Bertani medium containing bacto tryptone (10 g/L), bacto yeast extract (5 g/L) and NaCl (5 g/L). Bacteria were incubated at 37 °C for 12 h on a rotary shaker and then the cultures of bacteria were centrifuged at 5,000 rpm for 10 min in a bench centrifuge and the cells were coated on cotton. The Staph cotton was placed on the center of the bacterial source cask bottom to use as a Staph source for each disinfection experiment (Figure 1). Tris-buffered saline (TBS) solution, a mixture of 0.15 M NaCl and 0.05 M Tris-HCl at pH 7.5, was used to transfer Staph from the filter to a test solution. Then, the test solution was diluted with saline and spread onto an agar plate. The agar plate was kept at 37 °C for 8 h, and then the bacteria colonies were counted. The number of bacteria in the original filter was used as a basis to calculate the dilution factor.
Figure 1. Schematic model of the bacterial photocatalytic disinfection system.
Figure 1. Schematic model of the bacterial photocatalytic disinfection system.
Ijerph 11 03271 g001
An experimental model was designed with a two-parallel-pipes system for bioaerosol photocatalytic disinfection (Figure 1). The amount of Staph and humidity inside the model could be easily adjusted before each photocatalytic disinfection experiment. More details regarding the model design and safe conditions were presented in a sister paper [37]. The constant temperature inside the experimental model system was 25 °C during the disinfection process. Four 20 W white-light lamps were used to obtain visible light to initiate the electron transfer from the valence band to the conduction band of TiO2. The effective power density was 0.025 W/cm2. The reaction time of each photocatalytic disinfection experiments was 1 h.
In this study, the photocatalytic disinfection efficiencies of Staph using 1, 2.5, 5, 7.5 and 10% Ag-TiO2/GF photocatalysts were compared in order to investigate the optimal content of Ag doped on the TiO2/GF. The identified optimal photocatalyst was used for photocatalytic disinfection of Staph under different relative humidity (RH) conditions (40% ± 5%, 60% ± 5%, 80% ± 5%) to determine the effect of humidity on photocatalytic disinfection. This study also analyzed the effects of different input amounts of Staph to determine disinfection capacity of the identified optimal photocatalyst while keeping the same reaction conditions of time, temperature and relative humidity. The Staph disinfection efficiency was calculated by Equation (1):
Ijerph 11 03271 i001
The Staph disinfection capacity was calculated using Equation (2) with a disinfection time (t) of 3,600 seconds and a photocatalytic area (S) of 240 cm2:
Ijerph 11 03271 i002

3. Results and Discussion

3.1. Photocatalyst Characterization

3.1.1. SEM Observation

Figure 2 shows the SEM images of 0, 1, 2.5, 5, 7.5 and 10% Ag-TiO2/GF photocatalysts. Glass fiber was used as the substrate for TiO2 deposition. TiO2 in the TiO2/GF was flat-deposited on the surface of the glass fiber (Figure 2A).
Figure 2. SEM photographs of 0 (A), 1 (B), 2.5 (C), 5 (D), 7.5 (E) and 10% (F) Ag-TiO2/GF.
Figure 2. SEM photographs of 0 (A), 1 (B), 2.5 (C), 5 (D), 7.5 (E) and 10% (F) Ag-TiO2/GF.
Ijerph 11 03271 g002
Figure 2 shows that some Ag particles were dispersedly deposited on the surface of the TiO2 layer while other Ag particles slightly overlapped on the TiO2 layer. The Ag particle size simultaneously increased with increasing Ag content. Ag clustered into big particles on the TiO2 layer at high Ag-doping. Too much Ag gathering into larger particles of silver could create negative effects, including light eclipsed by the large silver particles with TiO2 and the uneven distribution of silver on the TiO2 layer, which could result in the decrease of photocatalytic activity. At lower silver doping (1% and 2.5% Ag-TiO2/GF), the doped amount of silver resulted in few interactions between silver and TiO2 and was therefore not enough to enhance the photocatalytic activity of TiO2. The optimal ratio of silver doped on TiO2 was determined based on characterization methods such as XRD, UV-VIS and XPS as well as Staph photocatalytic disinfection efficiency and capacity.

3.1.2. XRD Analysis

In the Ag-TiO2/GF catalyst system, the intensity of the X-ray diffraction peaks of the TiO2 coated on the glass fiber was too weak for phase analysis due to the limited availability of TiO2 particles coated on the glass fiber. To determine the crystalline phase of TiO2 and Ag deposited on TiO2 using XRD peak analysis, TiO2 powder and 1, 2.5, 5, 7.5 and 10% Ag doped TiO2 powder were prepared from the colloidal solution of TiO2 without the immersion of the glass fiber. Figure 3A shows that the anatase phase of TiO2 was identified in XRD patterns of TiO2 and 1, 2.5, 5, 7.5 and 10% Ag doped TiO2.
Figure 3. (A) XRD patterns of the TiO2 and 1, 2.5, 5, 7.5, and 10% Ag-TiO2; (B) XRD patterns of the TiO2 and 1, 2.5, 5, 7.5, and 10% Ag-TiO2 in the 2θ range of 20–30°; (C) XRD patterns of the TiO2 and 1, 2.5, 5, 7.5, and 10% Ag-TiO2 in the 2θ range of 30–70°.
Figure 3. (A) XRD patterns of the TiO2 and 1, 2.5, 5, 7.5, and 10% Ag-TiO2; (B) XRD patterns of the TiO2 and 1, 2.5, 5, 7.5, and 10% Ag-TiO2 in the 2θ range of 20–30°; (C) XRD patterns of the TiO2 and 1, 2.5, 5, 7.5, and 10% Ag-TiO2 in the 2θ range of 30–70°.
Ijerph 11 03271 g003
To analyze changes in X-ray peak intensity of the anatase peak of TiO2 as a function of the amount of doped Ag, this study magnified the XRD patterns of TiO2 and 1, 2.5, 5, 7.5 and 10% Ag doped TiO2 in the 2θ range 20–30°(Figure 3B). In the XRD patterns, the diffraction angles shown at 26° in 2θ corresponds to the anatase (101) peak of TiO2. The anatase peak intensity and shape of the TiO2 in the Ag doped TiO2 samples decreased and broadened, respectively, with increasing Ag doping, compared to the pure TiO2 sample. This is possibly due to the fact that Ag+ ions are deposited onto the surface of TiO2 particles. In addition, a slight shift of the anatase (101) peak to a smaller diffraction angle was recorded for the Ag doped TiO2 samples. This is because Ag+ entered the crystal structure of TiO2 and consequently induced distortion in the crystal lattice of TiO2. Liu et al. reported that silver could defect the lattice of TiO2 because the substitution of silver ions into the lattice sites of TiO2 induced O vacancies or deficiencies of Ti4+ [38]. In the TiO2 lattice, the radius of Ti4+ ion is 68 Å. However, the ionic radius of Ag+ ions is 126 Å. As such, substitution or replacement of Ag+ ions for Ti4+ ions in TiO2 lattice requires high energy [39] and therefore only a small amount of Ag+ ions would enter the TiO2 lattice and distort the lattice structure. The more Ag doping onto TiO2, the more distortion there is in the TiO2 lattice, which results in greater peak broadening, increased shifting to lower angles and greater decreases in anatase peak intensity.
Figure 3C shows XRD patterns of TiO2 and 1, 2.5, 5, 7.5, and 10% Ag doped TiO2 in the 2θ range of 30–70°. An Ag metallic peak was observed at 44.4° in Ag doped TiO2 samples. When the Ag content increased up to 5%, one more weak Ag metallic peak occurred at 64.5°. A weak Ag2O peak was also notably observed at 33.1° when the Ag content in Ag doped TiO2 samples increased from 5% to 10%.
The occurrence of a small amount of silver oxide (Ag2O) in the samples suggested that at the calcination temperature around 200 °C, thermal decomposition of AgNO3 into Ag2O was observed in the main process of decomposition of AgNO3 into Ag metallic via Ag2O. Gao et al. reported that the thermal decomposition of Ag2O phases to Ag and oxygen atoms transpires at Ta ≥ 200 °C [40]. Even though, the Ag-O bonding in Ag2O is much weaker than Ag-Ag bonding in Ag lattice at 200°C, there is a possibility of small amounts of Ag2O remaining from the decomposition of AgNO3 [41]. The Ag and Ag2O produced from thermal decomposition of AgNO3 is explained by the following reaction scheme:
Ijerph 11 03271 i003

3.1.3. UV-Visible Spectra

Figure 4 shows the optical absorption properties of the TiO2/GF and 1, 2.5, 5, 7.5 and 10% Ag-TiO2/GF. The Ag-TiO2/GF samples exhibited an obvious red-shift of absorbance edge and a significant enhancement of light absorption in the region of 300–800 nm. Since the Fermi level of Ag is lower than that of TiO2, Ag on the surface of the TiO2 layer acts as an intermediate agent for the transfer of photo-generated electrons from the valence band of TiO2 to an acceptor (O2 gas) [42]. Therefore, Ag can enhance the photogenerated electron-hole pair separation of TiO2 and inhibit their recombination resulting in increased visible light absorption.
Figure 4. UV-Visible diffuse reflectance spectra of the TiO2/GF and 1, 2.5, 5, 7.5 and 10% Ag-TiO2/GF.
Figure 4. UV-Visible diffuse reflectance spectra of the TiO2/GF and 1, 2.5, 5, 7.5 and 10% Ag-TiO2/GF.
Ijerph 11 03271 g004
The visible light adsorption of Ag-TiO2/GF increased as the Ag content increased up to 7.5% and then began to drop when Ag content was increased up to 10%. The visible adsorption of Ag-TiO2/GF proportionally increased with increasing Ag content. The plasmon resonance of Ag particles dispersing into the TiO2 layer increased with increasing Ag content. The increase in the plasmon resonance can enhance electric fields, which can facilitate electron-hole production resulting in increased visible adsorption [43]. However, when the Ag content is too high, e.g., 10% in Ag-TiO2/GF, the plasmon resonance can inhibit the electron-hole separation of TiO2, resulting in decreased visible light adsorption. At the high silver loading, the size of the silver clusters became too large, thus blocking light from reaching the TiO2 surface. Therefore, the chances of visible light reaching the TiO2 layer decreased resulting in less visible light for adsorption to the photocatalyst [44].

3.1.4. XPS Studies

Figure 5A shows the high-resolution XPS spectra of titanium (Ti) in TiO2/GF and 1, 2.5, 5, 7.5 and 10% Ag-TiO2/GF. The Ti 2p3/2 peak and the Ti 2p1/2 peak of TiO2 in the TiO2/GF samples appeared at binding energies of 459.18 eV and 465.18 eV, respectively. The doublet splitting energy of Ti 2p peaks was 6.0 eV, which was attributed to Ti4+ in the lattice of titanium. The narrow and sharp peaks of Ti 2p in XPS spectra of TiO2/GF indicated that all Ti ions in TiO2 existed in the Ti4+ state [45]. Figure 5A shows peak broadening and a shift into lower binding energy of the Ti 2p peaks of TiO2 in Ag-TiO2/GF materials. The peak broadening of Ti 2p1/2 and Ti 2p3/2 in Ag-TiO2/GF implies that the ion state of titanium in Ag-TiO2/GF was not only Ti4+. Gaussian multipeak shapes were applied to fit Ti 2p peaks of TiO2 in the Ag-TiO2/GF (Figure 5B). XPS spectra of the Ag-TiO2/GF photocatalysis showed the presence of two peaks matching Ti3+ and Ti4+ [46]. The Ti3+ might have formed during the calcination process (oxidation of tetra isopropyl ortho titanate (TIOT)) to prepare the TiO2 layer with the assistance of Ag or Ag+ ion. Ag or Ag+ ion can extract an electron from isopropyl radical (C3H7) during the calcination process, and then the extracted electron transfers to Ti4+ to form Ti3+ [47,48]. These reactions are summarized as follows:
e + Ag → Ag
Ag + Ti4+ → Ag + Ti3+
Ti4+ and O2− from TIOT during the calcination process would experience rearrangement to produce TiO2. The rearrangement can be disturbed by Ag+ resulting in changes in the TiO2 lattice [38,49]. When an Ag ion replaces Ti4+ ion in a lattice site, it would induce O vacancies or deficiencies of Ti4+ in the TiO2 lattice, resulting in some changes of Ti4+ ions into Ti3+ ions [38,39]. As explained in the XRD analysis section, the radius of Ag+ (126 Å) is much larger than that of Ti4+ (68 Å). The replacement of Ag+ into the TiO2 lattice requires energy and thus only a small fraction of Ti4+ is replaced by Ag+ leading to only small amounts of Ti3+. This indicates that the fraction of Ti4+ in TiO2 lattice is dominant compared to Ti3+ and thus the peak intensity of Ti4+ is much higher than that of Ti3+ (Figure 5B). The Ti4+ and Ti3+ peak positions also shifted into lower binding energy fields as the doped amount of silver in the TiO2 lattice increased (Figure 5B). The plasmon resonance of silver could expand the titanium ion radius resulting in electron movement far from the titanium nuclei; therefore, the peaks of Ti 2p shifted into a lower binding energy [50]. The increase of the plasmon resonance of silver was proportional to the increase in silver content. The Ag+ present on the outside of the titanium ions can contribute to the expansion of the electron cloud around titanium nuclei thereby increasing the titanium radius and the further release of electrons. This phenomenon is observed through Ti 2p peak shifts into lower binding energies (Figure 5B). The occurrence of Ti3+, which contains one more electron than Ti4+, might promote electron generation from TiO2 when the Ag-TiO2 photocatalysts are excited by irradiation. Ag in TiO2 lattice can affect expansion of the titanium ion radius, which is demonstrated by the Ti3+ and Ti4+ peak shifts into lower binding energies (Figure 5B). Hence, the easily developed charge separation of electron-hole pairs from TiO2 could require relatively lower energy to reach excitation for photoreaction. This is the reason that photocatalytic activity can occur even under visible light. If the silver content is too high, i.e. 10%, silver ions can make more complexes around titanium. If silver ions exist at the opposite site of the titanium molecules, an electron cloud can develop opposite, thus withdrawing forces onto titanium. This kind of plasmon resonance can decrease the expansion power of the titanium radius. Therefore, the peaks of Ti 2p in 10% Ag-TiO2/GF shift slightly into higher binding energy fields compared to 7.5% Ag-TiO2/GF.
Figure 5C shows the XPS result of Ag 3d of 7.5% Ag-TiO2/GF. The Gauss multipeak shapes showed that the Ag 3d XPS peak was decomposed into two peaks for Ag2O and Ag metallic. The simultaneous occurrence of Ag and Ag2O in Ag-TiO2 was also reported by Zhang et al. [45]. At the calcination temperature around 200 °C, AgNO3 decomposed into Ag as well as Ag2O due to the reciprocal conversion between Ag0 and Ag+. This conversion is described by the following reaction:
Ijerph 11 03271 i004
Hence, the Ag-TiO2/GF essentially includes Ag and Ag2O, which are deposited on the TiO2/GF. However, both Ag metallic and Ag2O are able to enhance photocatalytic activity of TiO2 via sensitization by their plasmon resonance [45,50].
Figure 5. (A) XPS spectra of Ti 2p of TiO2/GF and 1, 2.5, 5, 7.5 and 10% Ag-TiO2/GF, (B) High resolution XPS spectra of Ti 2p in X% Ag-TiO2/GF, (C) XPS of Ag 3d in 7.5% Ag-TiO2/GF.
Figure 5. (A) XPS spectra of Ti 2p of TiO2/GF and 1, 2.5, 5, 7.5 and 10% Ag-TiO2/GF, (B) High resolution XPS spectra of Ti 2p in X% Ag-TiO2/GF, (C) XPS of Ag 3d in 7.5% Ag-TiO2/GF.
Ijerph 11 03271 g005

3.2. Disinfection Results

3.2.1 Optimum Ag Doping

Table 1 shows the Staph disinfection results at different Ag loading in Ag-TiO2/GF under visible light. The Ag-TiO2/GF photocatalyst showed very high disinfection efficiencies of Staph, even under visible light. This great improvement of Staph disinfection by the photocatalyst Ag-TiO2/GF is a result of the Ag doping. Ag enhanced the electron-hole separation of TiO2 resulting in improved photocatalytic activity under visible light. The electron-hole pairs could be easily generated when the Ag-TiO2/GF was irradiated even by visible light, and then the generated electron-hole pairs reacted with water and molecular oxygen absorbed on the photocatalysis surface to form hydroxyl radicals (∙OH) and superoxide radical anions (∙O2) [41]. These oxy radicals participate in the oxidation of organic components of Staph resulting in bacterial death [51]. Ag also acted as an intermediate agent for the transfer of photo-generated electrons from the valence band of TiO2 to an acceptor (O2 gas) to produce superoxide radicals. The Ag-TiO2/GF system mainly undergoes the following reactions:
TiO2 + hν → e + h+
h+ + H2O → H+ + ∙OH
e + Ag → Ag
Ag + O2 → Ag + O2
O2 + e + H+ → H2O2
H2O2 → ∙OH
∙OH + organic compounds (DNA, RNA, lipid) → CO2 + H2O
Table 1. Staph disinfection results of different Ag loading in Ag-TiO2/GF.
Table 1. Staph disinfection results of different Ag loading in Ag-TiO2/GF.
Ag Doping in TiO2 (%) 012.557.510
Staph input (CFU)2.14E + 072.11E + 072.08E + 072.03E + 072.16E + 072.06E + 07
Staph output (CFU)2.08E + 079.75E + 067.90E + 066.50E + 065.35E + 065.95E + 06
Disinfection efficiency (%)2.8053.7962.0267.9875.2371.12
Table 1 shows the disinfection efficiency of Staph by the Ag-TiO2/GF photocatalysts with different amounts of silver doping. The disinfection efficiency gradually increased with increasing Ag content in Ag-TiO2/GF photocatalyst. The highest disinfection efficiency was 75.23% with Ag-TiO2/GF at 7.5% Ag loading. When the silver content was increased up to 10%, the disinfection efficiency began to drop. This result coincided with the preliminary conclusion inferred from the results in the SEM observation, UV-Vis spectra and XPS studies. When the silver content is increased too much, Ag clustered into larger size and non-uniform particles on the TiO2 surface. This leaded to limit the amount of light, H2O and O2 that were able to reach the TiO2 layer, resulting in decreased hydroxyl radical generation, which is a main factor for Staph disinfection [52]. The shrinkage of the titanium ion radius was evident in the peak shift to the high binding energy of Ti 2p in the photocatalytic system with 10% Ag-TiO2/GF. This result indicates that the 10% Ag-TiO2/GF has relative difficultly in generating electron-hole pairs compared to the 7.5% Ag-TiO2/GF. This also means the photocatalytic disinfection ability of Staph of the 10% Ag-TiO2/GF will be lower than that of the 7.5% Ag-TiO2/GF.

3.2.2. Humidity Effects

The effects of relative humidity on photocatalytic disinfection efficiency of Staph are shown in Table 2. Among the three tested relative humidity (RH) conditions, the highest disinfection efficiency of 75.23% was observed at RH 60% ± 5%. Under the dry humidity condition (40% ± 5% RH), the disinfection efficiency was 52.93%. The decrease in disinfection efficiency under the dry humidity condition was due to the lack of available H2O molecules for hydroxyl radical generation by photocatalytic reaction. Hydroxyl radical generation or availability is a major factor affecting bacterial disinfection [52]. Therefore, the lack of hydroxyl radical would greatly decrease disinfection efficiency. At the humid condition (80% ± 5% RH), the disinfection efficiency of Staph was 65.95%. This was higher than the disinfection efficiency in the dry condition, but lower than that of the medium humidity condition (60% ± 5%). According to the explanation of this phenomenon by Li et al., high humidity could induce reactivation of organisms, or water may occupy most of the TiO2 sites resulting in fewer sites available for disinfection or adsorption of microorganisms [53]. At a certain humidity level, the presence of water vapor could promote hydroxyl radical formation, however, the radical formation would not always increase with increasing water vapor. Sometimes, the radicals can even decrease due to the occupation of the adsorption site on the TiO2 surface, resulting in decreased disinfection efficiency at high humidity conditions [53]. Peccia et al. reported that biopolymers interior to the cell or protein structure could be changed at a certain level of relative humidity [54]. The protein structure change could affect the DNA repair enzyme, including cell wall characteristics, and hence could protect the microorganism from oxidation by hydroxyl radicals. Therefore, microorganisms can better survive when humidity is high, resulting in a slight decrease in the disinfection efficiency of Staph.
Table 2. Effects of relative humidity on photocatalytic disinfection efficiency of Staph.
Table 2. Effects of relative humidity on photocatalytic disinfection efficiency of Staph.
Relative Humidity (%)40 ± 560 ± 580 ± 5
Staph input (CFU)2.05E + 072.16E + 072.10E + 07
Staph output (CFU)9.65E + 065.35E + 067.15E + 06
Disinfection efficiency (%)52.9375.2365.95

3.2.3. Staph Disinfection Capacity of Optimal Photocatalysis

Table 3 shows the disinfection capacity of Staph by 7.5% Ag-TiO2/GF photocatalyst under visible light when the Staph input amount ranged from 1.58 × 107 to 2.91 × 107 (CFU). The disinfection capacity was calculated in CFU∙s−1 as well as CFU.s−−2. The disinfection capacity of the photocatalysis increased as the Staph input increased. The disinfection capacity almost reached the limit when Staph input was higher than 2.38 × 107 (CFU). The disinfection capacity increased from 3,247 (CFU∙s−1) to 4,806 (CFU∙s−1) when the Staph input increased from 1.58 × 107 to 2.91 × 107 (CFU). The disinfection capacity seemed to be stable around 4,750 (CFU∙s−1). Thus, there was only a slight increase in the disinfection efficiency accompanying the substantial increase in Staph remaining without disinfection even with further increased in Staph input. This is due to the limited number of available hydroxyl radicals generated per second by the photocatalytic activity resulting in an increase in untreated Staph, i.e., those not disinfected by the photocatalytic system. Although there is slight increase in disinfection capacity above 4,750 (CFU∙s−1) the disinfection capacity in CFU∙s−1∙cm2 did not increase further after reaching 20 (CFU∙s−1∙cm2) (Figure 6).
Table 3. Disinfection capacity of 7.5% Ag-TiO2/GF with different Staph inputs.
Table 3. Disinfection capacity of 7.5% Ag-TiO2/GF with different Staph inputs.
Staph Input (CFU)Staph Output (CFU)Disinfection CapacityStaph Remained (CFU·s−1)
1.58E + 074.11E + 063,247141,142
1.85E + 074.67E + 063,842161,297
2.16E + 075.35E + 064,514191,486
2.38E + 076.80E + 064,722201,889
2.67E + 079.60E +064,750202,667
2.91E + 071.18E + 074,806203,278
Figure 6. Disinfection capacity of Staph by 7.5% Ag-TiO2/GF photocatalyst at different Staph inputs.
Figure 6. Disinfection capacity of Staph by 7.5% Ag-TiO2/GF photocatalyst at different Staph inputs.
Ijerph 11 03271 g006
Figure 7 shows the Staph which was still alive and on the filter after the disinfection experiments. When the Staph input changed from 1.58 × 107 to 2.16 × 107 (CFU), the Staph remaining on the filter after the disinfection experiments increased from 1,142 (CFU∙s−1) to 1,486 (CFU∙s−1), which is only a small increase.
Figure 7. Remaining Staph at different input amounts.
Figure 7. Remaining Staph at different input amounts.
Ijerph 11 03271 g007
This slight change suggests that there was a small amount of Staph input that was not affected by hydroxyl radicals available on the surface of the photocatalyst. However, there was great increase in the Staph that was still alive and on the filters after the photocatalytic disinfection as the Staph input increased from 2.16 × 107 (CFU) to 2.91 × 107 16 × 107 (CFU). This means that a large amount of Staph was just passing through the photocatalytic pipe without being disinfected even with hydroxyl radicals generated from the surface of the photocatalyst. This also indicates there is a limited number of generated hydroxyl radicals available for disinfection under the given photocatalytic system.

4. Conclusions

This study investigated the chemical mechanism of photocatalytic disinfection of Staph using Ag-TiO2/GF under visible light. Silver doping influenced the microstructure of the photocatalyst. Increased silver loading produced a greater number of radicals, which can increase Staph disinfection via increased electron-hole separation and the formation of more intermediate agents to facilitate the transfer of electrons from valence band to acceptor (O2 gas). Loading too much silver decreased the photocatalytic disinfection efficiency because too much silver on the TiO2 layer blocked effective contact between TiO2 and H2O as well as between Staph and oxidative radicals.
Too dry and too humid environmental conditions both decreased the photocatalytic disinfection efficiency because of the lack of available H2O to produce hydroxyl radicals in the dry condition (40% ± 5% RH) and because of the blockage of effective contact between Staph and radicals by too much H2O in the high humid condition (80% ± 5% RH). The identified optimum silver loading and humidity conditions for the disinfection of Staph were 7.5% Ag loading in the Ag-TiO2/GF photocatalyst and 60% ± 5% RH, respectively. The photocatalytic disinfection capacity of Staph under the optimum silver loading and humidity conditions was 4,750 (CFU∙s−1) or 20 (CFU∙s−1∙cm2)


This work was supported by the National Research Foundation of Korea (NRF) grant funded by the Ministry of Education (2013R1A2A2A03013138).

Author Contributions

Thanh-Dong Pham: Synthesized photocatalysts, designed and manufactured the experimental model, did disinfection experiments, analysized data and wrote a preliminary manuscript. Byeong-Kyu Lee: Scientific supervisor of all processes including writing.

Conflicts of Interest

The authors declare they have no conflict of interests.


  1. The World Health Report 2002, Annex Table 9. Available online: (accessed on 20 January 2014).
  2. Douwes, J.; Thorne, P.; Peace, N.; Heederik, D. Bioaerosol health effects and exposure assessment: Progress and prospects. Ann. Occup. Hyg. 2003, 47, 187–200. [Google Scholar]
  3. Christopher, S.C.; Wathes, C.M. Bioaerosols Handbook; Lewis Publishers: Chelsea, MI, USA, 1995. [Google Scholar]
  4. Ivnitski, D.; Hamid, I.A.; Atanasov, P.; Wilkins, E. Biosensors for detection of pathogenic bacteria. Biosens. Bioelectron. 1999, 14, 599–624. [Google Scholar] [CrossRef]
  5. Chuaybamroong, P.; Chotigawin, R.; Supothina, S.; Sribenjalux, P.; Larpkiattaworn, S.; Wu, C.Y. Efficacy of photocatalytic HEPA filter on microorganism removal. Indoor Air. 2010, 20, 246–254. [Google Scholar] [CrossRef]
  6. Sung, W.P.; Tsai, T.T.; Wu, M.J.; Wang, H.J.; Surampalli, R.Y. Removal of indoor airborne bacteria by nano-Ag/TiO2 as photocatalyst: Feasibility study in museum and nursing institutions. J. Environ. Eng. 2011, 137, 163–170. [Google Scholar]
  7. Zhao, J.; Yang, X. Photocatalytic oxidation for indoor air purification: A literature review. Build. Environ. 2003, 38, 645–654. [Google Scholar] [CrossRef]
  8. Shintani, H.; Kurosu, S.; Miki, A.; Hayashi, F.; Kato, S. Sterilization efficiency of the photocatalyst against environmental microorganisms in a health care facility. Biocontrol. Sci. 2006, 11, 17–26. [Google Scholar] [CrossRef]
  9. Portela, R.; Tessinari, R.F.; Suarez, S.; Rasmussen, S.B.; Alonso, M.D.H.; Canela, M.C.; Avila, P.; Sanchez, B. Photocatalysis for continuous air purification in wastewater treatment plants: From lab to reality. Environ. Sci. Technol. 2012, 46, 5040–5048. [Google Scholar] [CrossRef]
  10. Hu, X.; Li, G.; Yu, J.C. Design, fabrication and modification of nanostructured semiconductor materials for environmental and energy applications. Langmuir 2010, 26, 3031–3039. [Google Scholar] [CrossRef]
  11. Gaya, U.I.; Abdullah, A.H. Heterogeneous photocatalytic degradation of organic contaminants over titanium dioxide: A review of fundamentals, progress and problems. J. Photoch. Photobio. 2008, 9, 1–12. [Google Scholar] [CrossRef] [Green Version]
  12. Han, F.; Kambala, V.S.R.; Srinivasan, M.; Rajarathnam, D.; Naidu, R. Tailored titanium dioxide photocatalysts for the degradation of organic dyes in wastewater treatment: A review. Appl. Catal. AGen. 2009, 359, 25–40. [Google Scholar] [CrossRef]
  13. Matsunaga, T.; Tomoda, R.; Nakajima, H. Photoelectrochemical sterilization of microbial cells by semiconductor powders. FEMS Microbiol. Lett. 1985, 29, 211–214. [Google Scholar] [CrossRef]
  14. Ibanez, J.A.; Litter, M.I.; Pizarro, R.A. Photocatalytic bactericidal effect of TiO2 on Enterobacter cloacae: Comparative study with other Gram (−) bacteria. J. Photochem. Photobiol. AChem. 2003, 157, 81–85. [Google Scholar] [CrossRef]
  15. Madrid, P.A.; Moorillon, G.V.N.; Borunda, E.O.; Yoshida, M.M. Photoinduced bactericidal activity against Pseudomonas aeruginosa by TiO2 based thin films. FEMS Microbiol. Lett. 2002, 211, 183–188. [Google Scholar] [CrossRef]
  16. Melian, J.A.H.; Rodriguez, J.M.D.; Suarez, A.V.; Rendon, E.T.; Campo, C.V.D.; Arana, J.; Pena, J.P. The photocatalytic disinfection of urban waste waters. Chemosphere 2000, 41, 323–327. [Google Scholar] [CrossRef]
  17. Saito, T.; Iwase, T.; Horie, J.; Morioka, T. Mode of photocatalytic bactericidal action of powdered semiconductor TiO2 on mutans streptococci. J. Photochem. Photobio. B 1992, 14, 369–379. [Google Scholar] [CrossRef]
  18. Kim, B.; Kim, D.; Cho, D.; Cho, S. Bactericidal effect of TiO2 photocatalyst on selected food-borne pathogenic bacteria. Chemosphere 2003, 52, 277–281. [Google Scholar] [CrossRef]
  19. Watts, R.J.; Kong, S.; Orr, M.P.; Miller, G.C.; Henry, B.E. Photocatalytic inactivation of coliform bacteria and viruses in secondary waste-water effluent. Water Res. 1995, 29, 95–100. [Google Scholar] [CrossRef]
  20. Cornish, B.J.P.A.; Lawton, L.A.; Robertson, P.K.J. Hydrogen peroxide enhanced photocatalytic oxidation of microcystin-LR using titanium dioxide. Appl. Catal. B Environ. 2000, 25, 59–67. [Google Scholar] [CrossRef]
  21. Kuhn, K.P.; Chaberny, I.F.; Massholder, K.; Stickler, M.; Benz, V.W.; Sonntag, H.G.; Erdinger, L. Disinfection of surfaces by photocatalytic oxidation with titanium dioxide and UVA light. Chemosphere 2003, 53, 71–77. [Google Scholar] [CrossRef]
  22. Wamer, W.G.; Yin, J.J.; Wei, R.R. Oxidative damage to nucleic acids photosensitized by titanium dioxide. Free Rad. Biol. Med. 1997, 23, 851–858. [Google Scholar] [CrossRef]
  23. Yu, K.P.; Lee, G.W.M.; Lin, S.; Huang, C.P. Aerosol removal by unipolar ionization in indoor environments. J. Aerosol. Sci. 2004, 35, 923–941. [Google Scholar] [CrossRef]
  24. Chen, F.; Yang, X.; Mak, H.K.C.; Chan, Q.W.T. Photocatalytic oxidation for antimicrobial control in built environment: A brief literature overview. Build. Environ. 2010, 45, 1747–1754. [Google Scholar] [CrossRef]
  25. Estivill, S.; Hargreaves, D.M.; Puma, G.L. Evaluation of the intrinsic photocatalytic oxidation kinetics of indoor air pollutants. Environ. Sci. Technol. 2007, 41, 2028–2035. [Google Scholar] [CrossRef]
  26. Yamashita, H.; Anpo, M. Application of an ion beam technique for the design of visible light-sensitive, highly efficient and highly selective photocatalysts: Ion-implantation and ionized cluster beam methods. Catal. Surveys. Asia 2004, 8, 35–45. [Google Scholar]
  27. Bae, E.; Choi, W.; Park, J.; Shin, H.S.; Kim, S.B.; Lee, J.S. Effects of surface anchoring groups (carboxylate vs. phosphonate) in ruthenium-complex sensitized TiO2 on visible light reactivity in aqueous suspension. J. Phys. Chem. B 2004, 108, 14093–14101. [Google Scholar] [CrossRef]
  28. Karunakaran, C.; Abiramasundari, G.; Gomathisankar, P.; Manikandan, G.; Anandi, V. Cu-doped TiO2 nanoparticles for photocatalytic disinfection of bacteria under visible light. J. Colloid Interf. Sci. 2010, 352, 68–74. [Google Scholar] [CrossRef]
  29. Young, C.; Lim, T.M.; Chiang, K.; Scott, J.; Amal, R. Photocatalytic oxidation of toluene and trichloroethylene in the gas-phase by metallised (Pt, Ag) titanium dioxide. Appl. Catal. B Environ. 2008, 78, 1–10. [Google Scholar] [CrossRef]
  30. Paramasivam, I.; Macak, J.M.; Schmuki, P. Photocatalytic activity of TiO2 nanotube layers loaded with Ag and Au nanoparticles. Electrochem. Commun. 2008, 10, 71–75. [Google Scholar] [CrossRef]
  31. Sheel, D.W.; Brook, L.A.; Ditta, I.B.; Evans, P.; Foster, H.A.; Steele, A.; Yates, H.M. Biocidal silver and silver/titania composite films grown by chemical vapour deposition. J. Photochem. Photobio. A Chem. 2007, 187, 53–63. [Google Scholar] [CrossRef]
  32. Herrmann, J.M.; Tahiri, H.; Ait-Ichou, Y.; Lassaletta, G.; Gonzalez-Elipe, A.R.; Fernandez, A. Characterization and photocatalytic activity in aqueous medium of TiO2 and Ag-TiO2 coatings on quartz. Appl. Catal. B Environ. 1997, 13, 219–228. [Google Scholar] [CrossRef]
  33. Zhao, L.; Wang, H.; Huo, K.; Cui, L.; Zhang, W.; Ni, H.; Zhang, Y.; Wu, Z.; Chu, P.K. Antibacterial nano-structured titania coating incorporated with silver nanoparticles. Biomaterials 2011, 32, 5706–5716. [Google Scholar] [CrossRef]
  34. Zheng, S.K.; Wang, T.M.; Xiang, G.; Wang, C. Photocatalytic activity of nanostructured TiO2 thin films prepared by dc magnetron sputtering method. Vacuum 2001, 62, 361–366. [Google Scholar] [CrossRef]
  35. Kawakami, H.; Ilol, R.; Straka, L.; Papul, S.; Romu, J.; Hanninen, H.; Mahlberg, R.; Heikkila, M. Photocatalytic activity of atomic layer deposited TiO2 Coatings on austenitic stainless steels and copper alloys. J. Electrochem. Soc. 2008, 155, 62–68. [Google Scholar]
  36. Gamage, J.; Zhang, Z. Applications of photocatalytic disinfection. Int. J. Photoenergy 2010, 2010. [Google Scholar]
  37. Pham, T.D.; Lee, B.K.; Nguyen, M.V.; Lee, C.H. Germicide feasibility of TiO2/glass fiber and Ag-TiO2/glass fiber photocatalysts. Adv. Mat. Res. 2012, 518-523, 864–868. [Google Scholar] [CrossRef]
  38. Liu, Y.; Yan, L.C.; Hui, R.Q.; Zhang, Z.; Yi, W.C. Effects of silver ion doping on the surface defect characteristics of TiO2. Res. Chem. Intermediat. 2004, 30, 569–577. [Google Scholar] [CrossRef]
  39. Cui, X.S. The Basic Theory of Solid Chemistry; Beijing Institute of Technology Printing: Beijing, China, 1991. [Google Scholar]
  40. Gao, X.; Zhao, M.; Zhang, Z.; Chen, C.; Ma, J.; Lu, J. Effects of hydrogen annealing on the microstructure and optical properties of single-phased Ag2O film deposited using direct-current reactive magnetron sputtering. Thin Solid Films 2011, 519, 6620–6623. [Google Scholar] [CrossRef]
  41. He, C.; Yu, Y. Influence of silver doping on the photocatalytic activity of titania films. Appl. Surf. Sci. 2002, 200, 239–247. [Google Scholar] [CrossRef]
  42. Seery, M.K.; George, R.; Floris, P.; Pillai, S.C. Silver doped titanium dioxide nanomaterials for enhanced visible light photocatalysis. J. Photochem. Photobiol. A Chem. 2007, 189, 258–263. [Google Scholar] [CrossRef]
  43. Vohra, A.; Goswami, D.Y.; Deshpande, D.A.; Block, S.S. Enhanced photocatalytic disinfection of indoor air. Appl. Catal. BEnviron. 2006, 65, 57–65. [Google Scholar]
  44. Behnajady, M.A.; Modirshahla, N.; Shokri, M.; Rad, B. Enhancement of photocatalytic activity of TiO2 nanoparticles by silver doping: Photodeposition versus liquid impregnation methods. Global NEST J. 2008, 10, 1–7. [Google Scholar]
  45. Zhang, H.; Wang, G.; Chen, D.; Li, X.; Li, J. Tuning photoelectrochemical performances of Ag-TiO2 nanocomposites via reduction/oxidation of Ag. Chem. Mater. 2008, 20, 6543–6549. [Google Scholar] [CrossRef]
  46. Fu, Y.; Du, H.; Zhang, S.; Huang, W. XPS characterization of surface and interfacial structure of sputtered TiNi films on Si substrate. Mater. Sci. Eng. A 2005, 403, 25–31. [Google Scholar] [CrossRef]
  47. Rengaraj, S.; Li, X.Z. Enhanced photocatalytic activity of TiO2 by doping with Ag for degradation of 2,4,6-trichlorophenol in aqueous suspension. J. Mol. Catal. A Chem. 2006, 243, 60–67. [Google Scholar] [CrossRef]
  48. Meng, F.; Sun, Z. Enhanced photocatalytic activity of silver nanoparticles modified TiO2 thin films prepared by RF magnetron sputtering. Mater. Chem. Phys. 2009, 118, 349–353. [Google Scholar] [CrossRef]
  49. Chao, H.E.; Yun, Y.U.; Xingfang, H.U.; Larbot, A. Effect of silver doping on the phase transformation and grain growth of sol-gel titania powder. J. Eur. Ceram. Soc. 2003, 23, 1457–1464. [Google Scholar] [CrossRef]
  50. Chen, X.; Mao, S.S. Titanium dioxide nanomaterials: Synthesis, properties, modifications, and applications. Chem. Rev. 2007, 107, 2891–2959. [Google Scholar] [CrossRef]
  51. Sunada, K.; Watanabe, T.; Hashimoto, K. Studies on photokilling of bacteria on TiO2 thin film. J. Photochem. Photobiol. A Chem. 2003, 156, 227–233. [Google Scholar] [CrossRef]
  52. Yu, J.; Xiong, J.; Cheng, B.; Liu, S. Fabrication and characterization of Ag-TiO2 multiphase nanocomposite thin films with enhanced photocatalytic activity. Appl. Catal. B Environ. 2005, 60, 211–221. [Google Scholar] [CrossRef]
  53. Li, Y.; Wu, C.Y. Role of moisture in adsorption, photocatalytic oxidation, and reemission of elemental mercury on a SiO2-TiO2 nanocomposite. Environ. Sci. Technol. 2006, 40, 6444–6448. [Google Scholar] [CrossRef]
  54. Peccia, J.; Werth, H.M.; Miller, S.; Hernandez, M. Effects of relative humidity on the ultraviolet induced inactivation of airborne bacteria. Aerosol. Sci. Technol. 2001, 35, 728–740. [Google Scholar] [CrossRef]

Share and Cite

MDPI and ACS Style

Pham, T.-D.; Lee, B.-K. Feasibility of Silver Doped TiO2/Glass Fiber Photocatalyst under Visible Irradiation as an Indoor Air Germicide. Int. J. Environ. Res. Public Health 2014, 11, 3271-3288.

AMA Style

Pham T-D, Lee B-K. Feasibility of Silver Doped TiO2/Glass Fiber Photocatalyst under Visible Irradiation as an Indoor Air Germicide. International Journal of Environmental Research and Public Health. 2014; 11(3):3271-3288.

Chicago/Turabian Style

Pham, Thanh-Dong, and Byeong-Kyu Lee. 2014. "Feasibility of Silver Doped TiO2/Glass Fiber Photocatalyst under Visible Irradiation as an Indoor Air Germicide" International Journal of Environmental Research and Public Health 11, no. 3: 3271-3288.

Article Metrics

Back to TopTop