Constructing a visible-light-driven photocatalytic membrane by g-C3N4 quantum dots and TiO2 nanotube array for enhanced water treatment

Photocatalytic membranes that driven by visible light are highly desired for water treatment. Here g-C3N4 quantum dots (QDs) assembled into TiO2 nanotube array (TNA) membranes were fabricated for the first time as a visible-light-driven g-C3N4/TNA membrane. Benefiting from the synergistic effect of membrane filtration and photocatalysis, more than 60% of rhodamine B could be removed from water under visible light irradiation. Meanwhile, the g-C3N4/TNA membrane presented an enhanced anti-fouling ability during filtering water containing Escherichia coli under visible light irradiation, and a permeate flux of 2 times higher than that of filtration alone was obtained by integrated process. This study offers a promising strategy for the potential application of the visible-light-driven membranes in water treatment.

the strong quantum confinement and edge effects when the QD size is down to 10 nm could render excellent optical properties. Therefore, in this work, g-C 3 N 4 QDs were immobilized into a free-standing TNA membrane to fabricate the g-C 3 N 4 /TNA membrane and the size of g-C 3 N 4 QDs might effectively avoid the blocking of TNA membrane. Furthermore, TNA membrane structure with straight channels and highly self-ordered arrangements could have a promising performance for water treatment. This strategy provides a very interesting opportunity for further application of visible-light-driven photocatalytic membrane in water treatment. Figure 1a is a digital photograph of the g-C 3 N 4 /TNA membrane, showing that it is smooth and crack-free.   Figure 1e shows a representative TEM image of the g-C 3 N 4 /TNA with a hollow tube-like structure. The high-resolution TEM image of the g-C 3 N 4 /TNA exhibited that the material was crystalline with an interplanar spacing of 0.353 nm (bottom left of Fig. 1e), which corresponded to the (101) planes of anatase TiO 2 22-25 . The lattice spacing of 0.336 nm (top left of Fig. 1e) is indexed to the (002) planes of hexagonal g-C 3 N 4 26, 27 . The membrane hydrophilicity of g-C 3 N 4 /TNA membrane was evaluated by measuring their water contact angles. A good hydrophilicity is beneficial to the permeating performance of membranes. Figure 1f presents that the water contact angle of all the g-C 3 N 4 /TNA membranes is lower than 12°. Meanwhile, it can be also seen that the effect of g-C 3 N 4 QDs on g-C 3 N 4 /TNA membrane hydrophilicity is neglected. Figure 2a presents the pore size distribution obtained from the g-C 3 N 4 /TNA membranes. For comparison, the pore size distribution of TNA membrane was also measured. Apparently, all the samples exhibit the same mean pore size of about 190 nm, which indicated that the deposition of g-C 3 N 4 QDs did not markedly affect the pore size distribution of membranes and the mean pore size did not decreased with the increasing of g-C 3 N 4 QDs deposition time. The results of mean pore size measurement were in agreement with the observation of SEM image of g-C 3 N 4 /TNA membranes. On the other hand, the porosity of TNA membrane and g-C 3 N 4 /TNA membranes is displayed in Fig. 2b. The porosity of both TNA membrane and g-C 3 N 4 /TNA membrane 1, 2 and 3 were same at about 72%. Since the porosity of traditional separation membranes is lower than 36% 28 , the high porosity of g-C 3 N 4 /TNA membrane could be attributed to its unique membrane structure including straight channels and highly self-ordered arrangements. Meanwhile, it can be seen from Fig. 2b that the effect of deposition of g-C 3 N 4 QDs on the membrane porosity could be neglected.
The membrane permeability was evaluated by testing pure water flux of membranes. As shown in Fig. 3a, compared with the TNA membrane, the pure water flux of all the g-C 3 N 4 /TNA membranes is about 250 L · m −2 · h −1 (0.075 MPa). This indicated that the effect of g-C 3 N 4 QDs immobilization on the pure water flux of TNA membrane could be negligible under present experimental conditions. Figure 3b exhibits the pressure dependence of pure water flux for g-C 3 N 4 /TNA membrane. The flux increased linearly with applied pressures (0.02~0.08 MPa), indicating a high compressive resistance of the membranes used for filtration.    Fig. 4b. In dark, the permeate concentration of RhB was the same as the feed concentration, indicating that the membrane separation alone could not remove RhB. However, under visible light irradiation, more than 60% of RhB was removed. This indicated that the g-C 3 N 4 /TNA membrane 3 exhibited an attractive synergistic effect of membrane filtration and photocatalysis for RhB removal under visible light irradiation. In previous reports, Albuet al. 29 demonstrated that TiO 2 nanotube membrane can be used as a flow-through photoactive membrane for pollutant removal under UV light illumination, Liao et al. 30 reported that a dramatic increase in photocatalytic activity is obtained when CdS nanoparticles are combined with TiO 2 nanotube membrane under simulated sunlight irradiation.
In order to further investigate the mechanism of RhB photodegradation under visible light irradiation, radical trapping experiments were performed using 10 mM p-benzoquinone (BQ, ·O 2 − scavengers), triethanolamine (TEOA, holes scavengers) and tert-butyl alcohol (TBA, ·OH scavengers). Compared to the RhB photocatalytic process without scavengers, the presence of TEOA and TBA scarcely affected the photocatalytic activity of the g-C 3 N 4 /TNA membrane, whereas the photocatalytic activity was greatly suppressed by the addition of BQ. This result indicated that ·O 2 − is the most active species in RhB photodegradation, where holes and ·OH play a less crucial role.
To evaluate the antifouling performance of the g-C 3 N 4 /TNA membrane, the removal of E. coli was also carried out. Meanwhile, the permeation flux of E. coli was measured with and without visible light irradiation. As shown in Fig. 5a, since the size of E. coli was larger than that of mean pore size of the g-C 3 N 4 /TNA membrane, all the E. coli could be removed in outlet by membrane filtration. As presented in Fig. 5b, compared with the permeation flux continually declined to 30 L · m −2 · h −1 after 180 min in dark, the permeation flux of E. coli was stable at about 60 L · m −2 · h −1 from 60 to 180 min under visible light irradiation. This enhancement of the permeation flux could be ascribed to the synergistic effect of membrane filtration and photocatalysis.
The antibacterial effect on the g-C 3 N 4 /TNA membrane surface without and with visible light irradiation was further confirmed by the fluorescence microscopy images as shown in Fig. 5(c) and (d). The viable cells appear green color under a fluorescent microscope on the surface of g-C 3 N 4 /TNA membrane in the dark (Fig. 5c). However, as shown in Fig. 5d, under light irradiation, the same membrane exhibited the capability of killing E. coli as manifested in the higher portion of dead cells (red color) on its surface. This demonstrated that E. coli formed "biofouling layer" by massively gathering on the surface of g-C 3 N 4 /TNA membrane through the membrane filtration alone. On the contrary, the number of E. coli obviously decreased under visible light irradiation, which benefited for reducing the membrane fouling 31 . Based on the results described above, the reason of the enhanced performance of g-C 3 N 4 /TNA membrane for water treatment is that such an electron transition between g-C 3 N 4 and TiO 2 can reduce the recombination of charge carriers and prolong the charge lifetime [31][32][33][34][35] .
In summary, a facile approach has been proposed to fabricate a novel visible-light-driven photocatalytic membrane by immobilizing g-C 3 N 4 QDs in a highly ordered TNA membrane. Benefiting from an attractive heterostructure between g-C 3 N 4 and TiO 2 leading to a unique photogenerated charge separation, meanwhile, since the g-C 3 N 4 /TNA membrane has a distinctive well-ordered nanotube structure with a mean pore size of 190 nm, this membrane had an impressive performance for E. coli removal and enhanced anti-fouling capability. Especially, the distinguish property of this obtained g-C 3 N 4 /TNA membrane is that it could be used under visible light irradiation. This visible-light-driven photocatalytic membrane shows extensive and attractive ability for water treatment.

Methods
Preparation of g-C 3 N 4 QDs. Grinded bulk g-C 3 N 4 powders were heated at 500 °C for 2 h to fabricate g-C 3 N 4 nanosheets. Then, the g-C 3 N 4 nanosheets (0.05 g) were treated in concentrated H 2 SO 4 (10 mL) and HNO 3 (30 mL) for 16 h with ultrasonication. Afterwards, the obtained g-C 3 N 4 nanoribbons were washed with deionized water (200 mL) to remove the acids. Finally, the g-C 3 N 4 nanoribbons were carefully redispersed in 16 mL deionized water under ultrasonication. The suspension was transferred to a Teflon-lined autoclave and heated at 200 °C for 10 h. After cooling to room temperature, the final product of yellowish g-C 3 N 4 QD solution (about 0.14 g/L) was obtained 36 .
Preparation of g-C 3 N 4 /TNA membranes. A vertically oriented and free-standing g-C 3 N 4 /TNA membrane was fabricated via potentiostatic anodization in a two-electrode electrochemical cell. The anodization was performed by using a commercial Ti foil (purity 99.7%) as a working electrode, and a Pt plate as a counter electrode in an electrolyte composed of 0.5 wt.% NH 4 F and 2 vol.% deionized water in ethylene glycol at 60 V for 4 h. Then, the electrodeposition of g-C 3 N 4 QDs was performed using an electrophoresis apparatus (DYY-6C) where the pre-anodized Ti foil and Pt plate were connected with the negative pole and positive pole of the electrophoresis apparatus, respectively. The electrolyte solution consisted of isopropyl alcohol (100 mL), magnesium nitrate (5 mg), and g-C 3 N 4 QDs (0.14 g/L, 10 mL). Electrodeposition at 20 V was maintained for a duration of 1 h (g-C 3 N 4 /TNA membrane 1), 2 h (g-C 3 N 4 /TNA membrane 2) or 3 h (g-C 3 N 4 /TNA membrane 3), respectively. Subsequently, the g-C 3 N 4 /TNA substrate was anodized for the second time at 60 V and at room temperature for 4 h. Finally, a larger anodic voltage (150 V) was applied for 5 min to get a through-hole g-C 3 N 4 /TNA membrane. The obtained samples were annealed at 500 °C for 2 h.
Characterization. The morphology of the g-C 3 N 4 /TNA membrane was analyzed using scanning electron microscopy (SEM, Quanta 200 FEG) and transmission electron microscopy (TEM, JEM-2100F). The crystallinity of the sample was determined by X-ray diffraction (XRD) using a diffractometer with Cu Kα radiation (Shimadzu LabX XRD-6000). BET surface area and pore volume distribution were analyzed using an automated surface area and pore size analyzer (QuantachromeAutosorb-1 MP). The UV-vis absorption spectrum of the g-C 3 N 4 / TNA membrane was investigated using UV-vis diffuse reflectance spectroscopy (DRS) (Shimadzu UV-2450). Fourier transform infrared spectra (FTIR) of the samples were obtained in KBr pellets on a Nicolet 5DXC IR spectrometer (Nicolet, Madison). X-ray photoelectron spectroscopy (XPS, ESCALAB250) was used to analyze the elemental composition of the g-C 3 N 4 /TNA membrane. The photoluminescence spectrum of the sample was measured at room temperature using a 380 nm excitation wavelength (F-4500). Membrane pore size distribution was measured by using a Porometer (Porolux 1000) under a room temperature of 25 °C. The water contact angle of the g-C 3 N 4 /TNA membranes was tested using a contact angle and surface tension measurement system (Physics Instruments Ltd., Germany).
Measurement of pore size and pure water flux. The permeate flux of membranes was carried out using the ultrapure water (18.2 Ω · cm) under different transmembrane pressures. The pure water flux of g-C 3 N 4 /TNA membrane is calculated with the following formula:  (1) where J is the pure water flux, V is the water volume permeating membrane in a certain time t, S is the total effective area of membrane and p is the pressure. The porosity (ε) of the g-C 3 N 4 /TNA membranes was investigated by a gravimetric method and calculated using the following formula: where m 1 is the mass of dry membrane, m 2 is the mass of wet membrane, ρ is the water density, V is the volume of membrane. The rejection rate was calculated by the formula: where R(%) is the percent solute rejection, and C p and C f are the concentrations of solute in the permeate and feed, respectively.
Membrane performance tests. The performance of the g-C 3 N 4 /TNA membrane was investigated by the removal of RhB (3 mg · L −1 ). As shown in Fig. 4a, the test was performed in a paired-cell quartz reactor (with a volume of 30 mL). A piece of g-C 3 N 4 /TNA membrane was glued to a holder and mounted between the two half-cells. A 500 W xenon arc lamp (LSH-X500, Zolix, 100 mW · cm −2 ) was used as a light source with a 400 nm cut-off filter. The RhB solution was permeated the membrane under a pump (50 r/min). The concentration of RhB was determined by measuring the optical absorption at 554 nm with a JASCO UV-vis spectrophotometer (V550, Japan).
To evaluate the anti-biofouling capability of the g-C 3 N 4 /TNA membrane, the removal of E. coli was also investigated. Briefly, E. coli was incubated in Luria Bertani nutrient solution at 37 °C for 12 h with shaking and then washed with 0.9% saline. After centrifugation, the cell was re-suspended with 0.9% saline. The experiment of photocatalytic disinfection was carried out by using the set-up shown in Fig. 4a under the 500 W xenon arc lamp. NaCl was added into the feed water that contained E. coli and its concentration was adjusted at 0.9%. At the certain time intervals, 1 mL of suspension was sampled and immediately diluted 10-fold serially with sterilized saline. In order to measure the density of viable E. coli cell, 0.2 mL of the diluted solution was spread on the nutrient agar and incubated at 37 °C for 12 h. The number of cfu was counted to determine the number of viable cells. Each set of experiment was performed in triplicate and their average values with statistical deviation were used in the data analysis.