Journal Information
Vol. 9. Issue 1.
Pages 168-179 (January - February 2020)
Share
Share
Download PDF
More article options
Visits
...
Vol. 9. Issue 1.
Pages 168-179 (January - February 2020)
Original Article
DOI: 10.1016/j.jmrt.2019.10.042
Open Access
A novel preparation of visible light driven Durio zibethinus shell ash supported CuO nanocomposite for the photocatalytic degradation of acid dye
Visits
...
P.T. Lum, K.Y. Lim, N.A. Zakaria, K.Y. Foo
Corresponding author
k.y.foo@usm.my

Corresponding author.
River Engineering and Urban Drainage Research Centre (REDAC), Engineering Campus, Universiti Sains Malaysia, Seri Ampangan, 14300 Nibong Tebal, Penang, Malaysia
Article information
Abstract
Full Text
Bibliography
Download PDF
Statistics
Figures (13)
Show moreShow less
Tables (4)
Table 1. Surface physical characteristics of DSA and CuO/DSA derived nanocomposite.
Table 2. The apparent kinetic rate constants for the photodegradation of AR 88 at different initial concentrations.
Table 3. A comparison of the photocatalytic performance of different photocatalysts for the degradation of AR 88.
Table 4. A comparison of the photocatalytic performance of different regenerated photocatalysts for the decolorization of dye pollutants.
Show moreShow less
Additional material (1)
Abstract

In this work, a novel Durio zibethinus shell ash (DSA) supported copper (II) oxide (CuO) nanocomposite has been successfully synthesized via a single-step hydrothermal method. The resulting visible light responsive nanocomposite was subjected to the Scanning Electron Microscopy- Energy Dispersive X-Ray Spectroscopy (SEM-EDX), Photoluminescence (PL), X-ray Diffraction (XRD), Transmission Electron Microscopy (TEM), Fourier Transform Infrared Spectroscopy (FT-IR), and nitrogen adsorption–desorption analysis. The major preparation and operational parameters, including the ash impregnation ratio, catalyst loadings, initial dye concentration, irradiation time and solution pH on the photoreaction were examined. Morphological study revealed that DSA served as an excellent supporting surface for the CuO nanoparticles to offer the synergistic adsorption–photodegradation reaction, verified by the rising porosity, and changing bandgap energy and surface functionalities. A complete degradation of Acid Red 88 with the high concentration of 500mg/L was achieved within 2h. Reusability test ascertained the high durability of the nanocomposite, with greater than 95% of decolourization efficiency even after five regeneration cycles. This study provides a new insight for the design of a low cost, eco-friendly and visible light driven photocatalyst, and innovative conversion of Durio zibethinus shell ash into a highly valuable nanocomposite for the effective purification of water contaminants.

Keywords:
Durio zibethinus shell ash
Dye
Nanocomposite
Photocatalyst
Visible light
Full Text
1Introduction

Semiconductor metal oxides have gained considerable interests in the technological development, with specific applications in the electronic devices and sensor manufacturing industries during the second half of the twentieth century. Taking the advantage of the interaction of light with solar energy transformation [1], to date, their promising potential for energy conversion have been successfully exploited. The exclusive properties of good light utilization, unique arrangement of electronic structure, effective charge transport characteristics and high capability of generating photo-induced charge carriers make them amenable to photocatalysis application [2]. Semiconductor-mediated photocatalysis, also known as heterogeneous photocatalysis, is recognized as one of the best and “green” environmental friendly technology to confront with the challenges of environmental pollutions, owing to the excellent photocatalytic degradation capacity, non-destructive, lower energy consumption, relatively inexpensive, extremely stable, reproducible, and ease of operation for large-scale applications [3]. This technique involves predominantly advanced oxidation process (AOP), a reliable process that generates highly reactive and non-selective radicals in the presence of energy sources to completely mineralize noxious pollutants to carbon dioxide and water, and free from the generation of toxic intermediate products [4].

Among these transition metal oxides, CuO, a representative of p-type semiconductor oxide, also regarded as a visible light photocatalyst with a narrow bandgap 1.2eV to 2.1eV [5], has attracted enormous attention by the virtue of its non-toxicity, relatively low cost, excellent pigment properties, and unique photochemical and photoconductive characteristics [6]. Under the irradiation of visible light, CuO particles could get activated by the photons energy equal or greater than its band gap, and the transfer of photo-excited electron would take place from the valence band (VB) to the conduction band (CB). The excited electron from CB is further scavenged by an electron acceptor O2 molecules to form superoxide (•O2−), and the holes from VB would react and split the H molecules to generate hydroxyl radicals (•OH−). These highly reactive radicals are responsible for the oxidation of water contaminants expressed by:

In the major interest of upgrading the photocatalytic efficacy of CuO, intense efforts have been focused on improvement of their surface morphologies, crystalline structures, sizes and architectures with different synthesis technique: sol-gel, pyrolysis, wet chemical, electrodeposition, solvothermal synthesis, or conjugation with noble metals [7], carbonaceous or porous materials [8]. In parallel, a series of CuO nanostructure, nanotubes, nanocubes, nanorods, nanowires, nanoflowers, hollow structure and nanoparticles of CuO [9] have been successfully prepared. However, there are still a paucity of researches on the synthesis of agricultural ash supported CuO photocatalysts.

Within this framework, the potential of Durio zibethinus shell ash, a major by-product entitled by the Durio zibethinus fruit processing industries, with the annual generation of exceeding 250,000 metric tons/year [10], has been highlighted as an eco-friendly and feasible precursor to be conjugated with CuO as a renewable photocatalytic nanocomposite for the efficient and cost-effective water pollutants treatment. In this work, a novel Durio zibethinus shell ash supported CuO nanocomposite was prepared by a simple one step hydrothermal technique. The textural morphology, surface chemistry, porosity and functional characteristics of the newly prepared nanocomposite was evaluated. The effects of ash impregnation ratio, catalyst loadings, solution pH and initial concentrations and irradiation time, on the photocatalytic performance were examined. Moreover, the kinetic analysis and the photostability of the nanocomposite were outlined.

2Materials and methods2.1Model pollutant

Acid Red 88, an anionic azo dye, with the molecular structure of C20H13N2O4SNa, and molecular weight of 400.8g/mole, was selected as the targeted model contaminant. A standard stock solution with the concentration of 500mg/L was prepared in deionized water, and experimental working solutions were prepared by serial dilutions to the desired concentrations.

2.2Adsorbent

Durio zibethinus shell (DS), a major by-product abundantly available from the fruit processing industries was chosen as the initial raw precursor. The content of C, N, H, O and S elements analyzed using an elemental analyzer (Heraeus, CHN-O-RAPID) was identified to be 457.37g/kg, 30.6g/kg, 66.93g/kg, 443.5g/kg and 1.6g/kg, respectively. The Durio zibethinus shell ash was prepared by controlled burning of DS in a muffle furnace at 700°C under purified oxygen gas for 30min. The as-prepared Durio zibethinus shell ash was washed extensively with deionized water to remove the adhering dirt particles from the surface, dried, screened through a sieve of 250–500μm, and acid functionalized with 1M of hydrochloric acid. The modified Durio zibethinus shell ash (DSA) was rinsed with deionized water till a constant pH was acquired in the washing solution. The estimated composition of the representative DSA was identified by the Energy Dispersive X-Ray Spectroscopy (EDX) analysis (Element Silicon Drift Detector (SDD)). DSA composed of mainly carbon (35.42 Wt%; 63.54 At%), sodium (0.06 Wt%; 0.05 At%), magnesium (7.57 Wt%; 6.71 At%), aluminum (0.47 Wt%; 0.37 At%), silicon (3.78 Wt%; 2.90 At%), phosphorus (12.37 Wt%; 8.61 At%), chloride (0.31 Wt%; 0.19 At%), calcium (14.35 Wt%; 7.72 At%), manganese (1.91 Wt%, 0.75 At%), and iron (23.78 Wt%; 9.18 At%).

2.3Photocatalytic nanocomposite

The CuO/DSA derived nanocomposites were synthesized by a single-step hydrothermal method, by mixing the requisite amount of DSA in a dissolved Cu(NO3)2 solution with the impregnation ratio (CuO:DSA) of 1:1 to 1:5. The solution mixture was hydrothermally heated at 140°C in a tightly sealed Teflon- lined autoclave for 10h in an oven. The newly prepared nanocomposites were filtered, washed sequential with deionized water, dried at 80°C, and kept in air tight bottles for further analysis.

2.4Physical and chemical characterizations

The surface morphology was evaluated by using the Scanning Electron Microscopy (SEM, Zeiss Supra 35VP, Germany). The crystalline phase composition was characterized with X-ray Diffraction (XRD) technique by using the Bruker AXS D8 Diffractometer with monochromatic Cu Kα radiation (λ=1.5406Å), while the High Resolution Transmission Electron Microscopy (HR-TEM) images were recorded by Bionand’s FEI Tecnai™ G2 20 S-TWIN microscope with an accelerating voltage of 200kV. The surface functional groups were detected by Fourier Transform Infrared (FTIR) Spectroscopy (FTIR-2000, PerkinElmer) by using the KBr pellet method in the scanning range of 4000–400cm−1. The nitrogen adsorption–desorption isotherm was conducted at 77K by using an automatic Micromeritics ASAP 2020 Volumetric Adsorption Analyzer. Prior to the measurement, the samples were degassed for 8h at 573K under a vacuum condition. The specific surface area was calculated by the Brunauer–Emmett–Teller (BET) equation, while the micropore surface area, external surface area and micropore volume were deduced using the t-plot method. The determination of point of zero charge (pHzpc) was conducted by adjusting the pH of 50cm3 of 0.01M NaCl solution to a value between 2 and 12. 0.15g of sample was added, and the final pH was measured after 48h under agitation. The pHzpc is the point where pHintialpHfinal=0. The photoluminescence (PL) spectra were obtained using a Raman & Photoluminescence Spectrophotometer (HR 800 UV), equipped with HeCd and Argon ion laser lamps with the excitation wavelength of 224–248nm at room temperature.

2.5Photocatalytic analysis

The photocatalytic analysis was examined by the photodegradation of AR 88 in a self-assembled photocatalytic reactor, equipped with four visible light sources (400W metal halide lamps, λ=380–780nm), circulating water jackets, thermocouples and a cooling fan. The schematic diagram of the photocatalytic reactor is displayed in Supplemental Fig. 1. A prefixed amount of photocatalyst was added into 100mL of AR 88 solution. Prior to the irradiation, the aqueous suspension was stirred in darkness for 30min until the adsorption–desorption equilibrium was achieved. The aliquots of the reaction mixture were withdrawn at specific time interval, filtered using a syringe filter (Nylon Millipore 0.25μm) as to minimize the interference of catalyst fines with the analysis, and the concentration of AR 88 was measured using a UV–Vis Spectrophotometer (UV-1800 Shimadzu, Japan) at 506nm. The degradation rate was defined as:

which C0 and Ct are referred to the initial concentration of AR 88 and at time t (min), respectively.

The effect of catalyst loading on the photodegradation reaction was examined by varying the catalyst dosage from 0.01g/100mL to 0.06g/100mL in 500mg/L of AR 88 solution at the irradiation time of 30min. The effect of initial concentration and irradiation time was evaluated at the initial concentration from 100mg/L to 500mg/L at the optimum catalyst loading. The effect of solution pH on the removal efficiency was conducted at the pH range of 2 to 12, with the pH adjustment by using 0.1M of HCI or NaOH under the optimized experimental conditions.

2.6Kinetic study

To quantify the kinetic analysis of the photodegradation process, the photocatalytic reaction is assumed to obey the first order kinetics. At low initial concentrations, the kinetic rate expression could be simplified as:

where C is denoted to the concentration of AR 88, t is the time of reaction (min), and Kapp is the apparent first order rate constant (min−1). When the adsorption–desorption equilibrium was reached, the equilibrium concentration of AR 88 is defined as the initial concentration applied for the kinetic analysis. Eq. (7) can be integrated (the limit of C=C0 at t=0 when the equilibrium is achieved), and the simplified equation is given by:

2.7Reusability test

The reusability test was conducted with respect to five successive degradation cycles of AR 88 at the initial concentration of 100mg/L under the optimized experimental condition. For each experiment, the nanocomposites were regenerated through filtration, washed with deionized water till a constant pH was acquired in the washing solution, subsequent by drying at 120°C for 1h. The regenerated nanocomposites were applied for the next consecutive degradation runs.

3Results and discussions3.1Preparation of DSA supported CuO photocatalyst

The effect of ash impregnation ratio is an important prerequisite step for the preparation of photocatalysts with the highest activity. The variation of photocatalytic performance of the DSA supported nanocomposites at different ash impregnation ratio is presented in Fig. 1. Decreasing the ash impregnation ratio of CuO:DSA from 1:5 to 1:1 showed a drastically enhancement of the degradation efficiency from 54% to 80%, as compared with the degradation rate of 35% for the raw DSA. The result is mainly ascribed to the synergistic effect of the nanocomposites, which promotes the unique bi-functional properties of adsorption behavior and photocatalytic capability [11]. Similarly, the higher performance of the DSA supported CuO nanocomposite is well supported by a greater availability of the surface sites at the higher content of DSA, to accelerate the larger deposition of CuO, as the catalytic center of the nanocomposite [12]. The representative structure of the nanocomposite is illustrated in Fig. 2 (a). Similarly, with a larger surface area, the newly prepared nanocomposite would provide more adorptive sites for the targeted pollutants than the photocatalyst itself, to allow the migration of adsorbed AR 88 to the photoactive degradation center of CuO [13].

Fig. 1.

Effect of ash impregnation ratio (CuO:DSA) on the photodegradation of AR 88 (catalyst loading=0.01g/100mL, C0=500mg/L, t=30min).

(0.06MB).
Fig. 2.

Schematic diagram of CuO/DSA derived nanocomposite at the (a) optimum impregnation ratio and (b) beyond the optimal impregnation ratio.

(0.09MB).

However, beyond the optimal impregnation ratio of 1:4, the degradation efficiency was gradually decreased. This phenomenon could be inferred to the excessive loading of DSA that turned to be unfavorable for the photodegradation process, due to the agglomeration of ash particles within the CuO nanoparticles [Fig. 2 (b)]. It could be an obstacle to confine the pathway of light from reaching to the CuO catalyst surface, and triggers to the lower generation of photo-induced electron-hole pairs, and eventually inhibits the photocatalytic efficiency of the nanocomposites [14]. Hence, the optimum impregnation ratio of 1:4 was applied for the further evaluations.

3.2Physical and chemical characterizations

The representative scanning electron micrographs (SEM) of DSA and CuO/DSA derived nanocomposite, with a magnification of 500 X, are depicted in Fig. 3. Generally, the raw DSA exhibited an irregular, rough and compact surface, with an uneven distribution of agglomerated flake particles. This morphological structure was highly porous, with the presence of different cavities over the surface, indicating good availability of surface area for the deposition of CuO. Conversely, the CuO anchored nanocomposite revealed a uniform configuration of spherical CuO nanocrystalline structure deposited over the entire surface of DSA, indicating the significant morphological transformation and size modification of the nanocomposite under hydrothermal treatment. Similar chemical restructuring process has been reported by Visa and Chelaru [15] and Yao et al. [16] under hydrothermal process within the ash and TiO2 nanoparticles. The surface morphological alteration ascertained the successive preparation of CuO/DSA nanocomposite, which would accelerate the photocatalytic activity by enhancing a greater availability to be activated by light, with the generation of the highly hydroxyl radicals as the foundation of the photodegradation process [17].

Fig. 3.

Scanning electron micrographs of (a) DSA and (b) CuO/DSA derived nanocomposite.

(1.1MB).

Nitrogen adsorption–desorption curve is a standard procedure elucidating qualitative information on the textural structure and surface properties of the composites. According to the classification of the International Union of Pure and Applied Chemistry (IUPAC), the nitrogen adsorption isotherm analysis (Fig. 4) resembles the type I-II hybrid isotherms, suggesting a combination of microporous–mesoporous structure. The initial part of isotherm curve showed a greater uptake of nitrogen at the relative pressure between 0 and 0.5, that may be correlated with micropore filling. However, further increase of the nitrogen adsorption found at the relative pressure higher than 0.5, illustrates the presence of mesoporous structure. The surface physical properties of DSA and the CuO/DSA derived nanocomposite are given in Table 1. The BET surface area, Langmuir surface area and total pore volume of the raw DSA were identified to be 5.59m2/g, 7.96m2/g, and 0.023cm3/g, respectively. However, the BET surface area, Langmuir surface area and total pore volume of the CuO/DSA derived nanocomposite were found to be 36.41m2/g, 53.52m2/g, and 0.108cm3/g, respectively, suggesting the positive development of surface porosity under hydrothermal treatment process. The findings were in the agreement with the results reported by Kim et al. [18] on the synthesis of multifunctional fly ash derived nanocomposites, which supported the vital role of DSA as a suitable backbone, and for the homogeneous and in-situ deposition of CuO nanoparticles, that in turn improved the overall surface area of the nanocomposite. Accordingly, Gao et al. [19] have suggested that hydrothermal treatment could promote crystalline nucleation and pore development, which has essentially improved the CuO/DSA framework.

Fig. 4.

Nitrogen adsorption-desorption curve of CuO/DSA derived nanocomposite.

(0.07MB).
Table 1.

Surface physical characteristics of DSA and CuO/DSA derived nanocomposite.

Properties  DSA  CuO/DSA nanocomposite 
BET surface area (m2/g)  5.59  36.41 
Langmuir surface area (m2/g)  7.96  53.52 
External surface area (m2/g)  3.27  30.01 
Micropore surface area (m2/g)  2.32  6.40 
Total pore volume (cm3/g)  0.023  0.108 
Micropore volume (cm3/g)  0.001  0.003 
Mesopore volume (cm3/g)  0.022  0.105 
Pore size (nm)  16.15  11.50 

The efficiency of the charge carrier trapping, immigration and transfer, and the fate of electron-hole pairs in semiconductor particles could be evaluated by the photoluminescence (PL) spectra of the DSA and CuO/DSA derived nanocomposite, as illustrated in Fig. 5. The two emission peaks are observed at 545nm and 585nm, which is generally attributed to the recombination of free excitons at the near-band edge. It is worth noting that the UV emission intensity of the CuO/DSA derived nanocomposite exhibits a distinct decrease as compared to the pure DSA. The PL emission was mainly resulted from the recombination of photogenerated electron-hole pairs, and a lower PL intensity may indicate a lower recombination rate of electron-hole pairs and better photocatalytic activity [20]. This PL analysis therefore suggested that the CuO/DSA derived nanocomposites would demonstrate a great better photocatalytic activity as compared to the pure DSA. The optical bandgap energy for the strong intense blue light emission peaks in the PL spectra was within the range of 3.29 and 3.54eV. The obtained higher values of the bandgap of CuO nanostructures as compared with that of bulk CuO (Eg=1.39eV) [21], could be ascribed to the quantum confinement effect, in which the nanocomposite with a smaller particle size demonstrated a higher bandgap value [22].

Fig. 5.

PL spectra of DSA and CuO/DSA nanocomposite.

(0.09MB).

The XRD patterns of the pure CuO (JCPDS File No. 41-0254), DSA and CuO/DSA derived nanocomposite are given in Fig. 6. All of the diffraction peaks for the pure CuO are corresponded to the monoclinic structure of CuO, which is in good agreement with the standard JCPDS data. The absence of diffraction peaks related to Cu(OH)2 or Cu2O indicated the high purity of the as-synthesized samples. The CuO diffraction peaks were located at 2θ=32.5°, 35.6°, 38.8°, 48.7°, 53.4°, 58.3°, 61.5°, 66.2°, 67.8°, 72.4° and 75.0°, mainly ascribed to the (110), (002), (111), (2¯ 02), (020), (202), (1¯ 13), (3¯ 11), (220), (311) and (2¯ 22) planes, respectively. This pattern has been indexed as the monoclinic phase of CuO, with the lattice constants a=4.84°, b=3.47°, and c=5.33°, which is consistent with the standard values for bulk CuO. Conversely, the crystalline peaks of the CuO/DSA derived nanocomposite corresponding to (101), (211), (002), (111), (110), (040), (002), (222), (111), (2¯ 02), (020), (202), (1¯ 13), (3¯ 11), (220), (100), (311) and (2¯ 22) planes diffraction planes at 2θ angles of 14.9°, 21.2°, 26.7°, 28.4°, 32.5°, 34.8°, 35.6°, 36.1°, 38.8°, 48.7°, 53.4°, 58.3°, 61.5°, 66.2°, 67.8°, 69.8°, 72.4° and 75.0°, respectively, were recorded.

Fig. 6.

XRD patterns of the DSA and CuO/DSA derived nanocomposite.

(0.15MB).

The TEM patterns of the DSA and CuO/DSA derived nanocomposite are illustrated in Fig. 7. Generally, the HR-TEM image of the pure DSA consisted of an agglomeration of spherical and oral nanoparticles [Fig. 7(a)], whereas CuO/DSA derived nanocomposite showed a flower-shaped hierarchical architecture consisting of interpenetrating CuO thin nanosheets [Fig. 7 (b)]. The particle size distribution depicted in Fig. 7 (c) revealed that the diameter of the nanoparticles ranged from 2.77 to 69.0nm, with an average diameter of 35.89nm. The fringe spacing, also known as the difference between the two atomic layers, as indicated in Fig. 7 (d) has been measured to be 0.25nm, which is related to the (002) crystal plane of monoclinic structure of the CuO phase (JCPDS File No. 41-0254).

Fig. 7.

HR-TEM images of (a) DSA and the (b) CuO/DSA derived nanocomposite; (c) Histogram of particle size distribution of CuO nanostructures; and (d) d-spacing.

(0.84MB).

The representative FT-IR spectra of DSA and CuO/DSA nanocomposite are presented in Fig. 8. The broad band at 3411cm−1 is assigned to the stretching of the hydroxyl group. The vibration at 2968/2962cm-1 is identical to the CH stretching of alkane group, while the transmittance at 2355cm−1 is related to the stretching of CC in alkyne group. The IR peak at 1608/1602cm−1 is corresponded to the bending vibration of hydroxyl group. The region between 1495–1409cm−1 is ascribed to the symmetrical stretching of SiOSi bond, while the signals at 1063/1031cm−1, and 692–559cm−1 are attributed to the bending vibration of SiO bonds, and representative of the CH stretching in aromatic compounds, respectively. The presence of extra bond at 867cm−1 for the FTIR spectrum verified the formation hydrogen bonding of CuOH generated by the Cu(NO3)2 of the CuO/DSA derived nanocomposite. Additionally, the lower peak intensity and peak deconvolution at 2962/2928, 2355 and 867cm−1 justified the homogeneous deposition of CuO onto DSA through the matrix via Van der Waals interaction, which renders the pattern interpretation of the spectra. Such interactions have been reported in the TiO2-deposited fly ash derived composite [23].

Fig. 8.

Fourier-Transform Infrared spectra of DSA and CuO/DSA derived nanocomposite.

(0.14MB).
3.3Photodegradation process3.3.1Effect of catalyst loading

Catalyst loading is the major influencing parameter to determine the operation cost, and the feasibility for large-scale practical applications. The effect of catalyst loading on the photocatalytic degradation of AR 88 was examined by varying the catalyst loading from 0.01g/100mL to 0.06g/100mL under the irradiation of visible light for 30min, as illustrated in Fig. 9. An increase of catalyst loading showed a superior improvement on the degradation efficacy of AR 88. The degradation efficacy increased linearly from 80% to 93%, with an increase of catalyst loading from 0.01g/100mL to 0.03g/100mL. The finding could be ascribed to the larger availability of surface active sites at higher catalyst loading for the greater exposure and adsorption of AR 88 molecules [24]. Meanwhile, higher number of surface catalytic sites at higher catalyst loading would contribute to the higher light absorption by the photocatalyst, to promote a greater formation of photo-induced hydroxyl radicals [25], which in turn enhanced the rate of photocatalytic decomposition reaction.

Fig. 9.

Effect of catalyst loading on the photodegradation of AR 88 (C0=500mg/L, t=30min).

(0.06MB).

Beyond the catalyst loading of 0.03g/100mL, no appreciable enhancement of the degradation efficacy was observed, in which the removal efficacy increased only slightly from 93% to 96%. This finding could be rationalized in terms of further increase of catalyst slurry dosage above the saturation limit, that might induce the excessive agglomeration of catalyst particles, with some part of the catalyst surface that has been blocked for the photon absorption [26]. Additionally, the aggregation of catalyst may cripple the transparency of the tested solution, which in turn reduced the light penetration into the solution, and affected the incidence of photons striking from the catalyst surface [3]. These obstacles could directly reduce the number of photo-generated hydroxyl or superoxide radicals, and consequently decline the degradation rate of AR 88 [27]. According to Ameta et al. [28], an excessive catalyst loading may trigger to the collision among catalyst particles, and induce a further impact on the deactivation of catalyst. Hence, a lower collision rate between the catalyst with the dyes pollutants would retard the overall photocatalytic process. This finding suggested a good balance between the catalyst loading with the tested pollutants should be well optimized for a better performance.

3.3.2Effect of initial concentration and irradiation time

The variation of AR 88 removal as a function of initial concentration and irradiation time, under the optimized experimental conditions is depicted in Fig. 10. In the present work, increasing the initial concentration of AR 88 from 100mg/L to 500mg/L showed a rising irradiation time from 8min to 105min for the complete degradation of dye pollutant. Similar observation has been reported for the photodegradation of AR 88 over the TiO2-SiO2 derived nanocomposite by Balachandran et al. [29]. The findings could be ascribed to the saturation of surface active sites and ineffective action of hydroxyl radicals, as additional dye molecules were adsorbed onto the surface of the photocatalysts at the higher initial concentrations with the constant catalyst loading [30]. Similarly, the rising concentration would lead to a collision, or blockage of the overloaded adsorbed dye molecules, and longer contact and irradiation time is required to accomplish the successive degradation of these dye molecules. The finding was in agreement with the research outputs concluded by Gao et al. [19] on the adsorption–photocatalytic degradation of AR 88 by activated carbon supported TiO2.

Fig. 10.

Plot of degradation of AR 88 as a function of initial concentrations and irradiation time.

(0.1MB).

Meanwhile, according to Ahmed et al. [30], the generated intermediate products from the photocatalytic process might diffuse slowly onto the catalyst surface, and deactivate the surface binding sites when the pollutants were overloaded. Similarly, a higher initial concentration would enhance the opacity of the solution, to induce a light scattering effect, that subsequently reduced the light utilization and the photocatalytic activity of the photocatalyst, owing to the lesser photons activation limit, and formation of reactive species radicals throughout the photodegradation process. At this stage, the photolysis of dye molecules rather than the photocatalysis of dye molecules might take place [31]. As a result, the removal rate of AR 88 would be rapidly retarded as the initial concentration increased.

3.3.3Effect of solution pH

Solution pH is the key factor affecting the degradation reaction by the generation of hydroxyl radicals, catalyst surface properties, surface charge, ionization and the adsorption ability of the dye molecules. The degradation efficacy of AR 88 with the changing solution pH from 2 to 12 is presented in Fig. 11. The photocatalytic efficacy was decreased remarkably from 98% to 20% with an increase of solution pH from 2 to 12. Higher degradation efficiency was attained at pH 2 to 4, as similar to the observation reported by Song et al. [32]. The effect of solution pH on the photodegradation process could be explained by the acid-base property of the dye molecules, in term of pKa value [33]. At the solution pH lower than the pKa value of AR 88 (10.7), the dye molecules would predominant in the molecular state, with a hydrophobic behavior, which they are readily to be degraded by the hydroxyl radicals, due to the higher accessibility to the solid-water interface. In the basic medium, the dye molecules would undergo ionization by the hydrogen loss from the protonated sites, and turned hydrophilic in the bulk solution [34]. The condition of this bulk solution may reduce the concentration of hydroxyl radicals, and further retard the degradation efficiency of AR 88.

Fig. 11.

Effect of solution pH on the photodegradation of AR 88 (catalyst loading=0.03g/100mL, C0=500mg/L; t=30min).

(0.05MB).

The changing degradation rate with the rising solution pH could also be explained according to the theory of point of zero charge (pHzpc) of the photocatalysts. The point of zero charge (pHzpc) of the newly prepared CuO/DSA derived nanocomposite was identified to be 4.5. Hence, at the acidic condition (pH<pHzpc), a higher formation of H+ radicals would protonate the surface of the photocatalytic nanocomposites, to enhance the electrostatic attraction between AR 88 with the protonated nanocomposites, which favoring the adsorption of the negatively charged AR 88. This phenomenon resulted in a higher degradation efficacy of AR 88, as reported by Saharan et al. [34]. Conversely, as the solution pH increased beyond 4.5 (>pHzpc), the functional groups of the nanocomposites turned less protonated, and unfavorable to the uptake of anionic AR 88, mainly ascribed to the formation of electrostatic repulsive force. Consequently, a lower removal efficacy of AR 88 was observed in the basic medium.

4Kinetic analysis

Kinetic analysis provides an invaluable insight into the controlling mechanism of the degradation process, which in turn governs mass transfer and the residence time. A kinetic plot of ln (C0/Ct) versus irradiation time (t), with respect to different initial concentrations of AR88 is displayed in Fig. 12. From Fig. 12, the linear relationship of the stimulation curve, with the determination coefficient, R2 greater than 0.97 for all of the tested concentrations, ascertained the great configuration to the first order kinetics model. The kinetic parameters, in terms of apparent rate constant, Kapp (min−1), yielded from the slope of the plots, together with the determination of coefficient, R2 for the photodegradation process are given in Table 2. From the presented findings, the kinetic rate constants for the degradation reactions revealed a decreasing Kapp from 0.841min−1 to 0.094min−1, as the initial concentration increased from 100mg/L to 500mg/L. The obtained results illustrated a proportional relationship between the kinetic rate constant with the changing initial dye concentration.

Fig. 12.

Plot of kinetic study for the photodegradation of AR 88 at different initial concentrations.

(0.1MB).
Table 2.

The apparent kinetic rate constants for the photodegradation of AR 88 at different initial concentrations.

Initial concentration (mg/L)  Kapp (min −1R2 
100  0.841  0.995 
200  0.300  0.977 
300  0.143  0.984 
400  0.108  0.992 
500  0.094  0.997 

Accordingly, this degradation process appeared to be driven primarily by the lower kinetic order. By following the first-order kinetics, it could be suggested that the photocatalytic degradation of AR 88 was more inclined towards physisorption, which involved intermolecular forces between the catalyst with AR 88, and the diffusion of photogenerated hydroxyl radicals were inferred to be the major rate-limiting factors in the photocatalytic system, specifically at the higher initial concentrations of dye pollutants [35]. With the aforementioned statement, a similar conclusion has been drawn by Dimitrakopoulou et al. [36] in the activity evaluation of TiO2 for the photocatalytic treatment of amoxicillin, who indicated the transition from the kinetic controlled reaction at the lower solute concentration to mass transfer controlled at the higher solute concentrations. Few recent studies pertaining to the photocatalytic performance of different photocatalyst for the decolourization of AR 88 are summarized in Table 3[19,31,37,38]. As a comparison, the CuO/DSA derived nanocomposite prepared in this work showed a comparable and higher photocatalytic degradation efficacy for the complete mineralization of AR 88, even at the higher initial concentration of 100mg/L.

Table 3.

A comparison of the photocatalytic performance of different photocatalysts for the degradation of AR 88.

Photocatalyst  Initial concentration (mg/L)  Irradiation time (min)  Removal (%)  Reference 
CuO/DSA nanocomposite  100  100  Present study 
ZnO/biosilica nanocomposite  20  30  96  [31] 
TiO2/Activated carbon-Darco-G60  40  180  93  [19] 
Ni- TiO2  50  35  97  [37] 
TiO2 on glass plate  20  90  93  [38] 
5Stability test

Photochemical stability is an essential key issue concerning the cost-effectiveness and long-term photocatalytic application of the nanocatalysts. The reusability of the newly-synthesized bio-ash supported nanocomposites was accessed by performing five sequential cyclic experiments by using AR 88, under the optimized experimental conditions, as depicted in Fig. 13. From the figure, it could be clearly revealed that the nanocomposite could retain a relatively high photocatalytic activity, with the removal efficacy for AR 88 of exceeding 95% even after five successive cycles. An inconspicuous decrease of the removal efficiency suggested that the present nanocomposite demonstrated excellent and stable photocatalytic activity. This result can be attributed to the fact that the structural integrity of the heterostructure of nanocomposite was well maintained, and it was not easily photo corroded and deactivated against the photodegradation process [39].

Fig. 13.

Reusability test of CuO/DSA derived nanocomposite for the photodegradation of AR 88 (catalyst loading=0.03g/100mL, C0=100mg/L; t =30min).

(0.07MB).

It could be deduced that DSA could serve as the adsorptive support to anchor or immobilize the dispersion of CuO onto the adsorbent surface, to protect against the destruction of the surface binding catalytic sites. This hybrid adsorptive and degradation surface active sites have contributed to both adsorptive force and the generation of photoinduced reactive species for the effective photodegradation reaction [40]. However, further recovery resulted in a slight decrease of the photocatalytic activity, mainly related to the changes in the mesoporous–microporous structures, or blockage of the surface binding active sites of this nanocomposite, and the possible leaching of the surface fragment of the catalyst after several successive adsorption and photocatalytic reactions.

Table 4 provides a comparison of the photocatalytic performance of different regenerated photocatalysts for the decolourization of different dye pollutants. The CuO/DSA derived nanocomposite synthesized in this work showed a comparable excellent reusability potential to maintain the degradation efficiency at above 95% even after the fifth regeneration cycles, at the initial concentration of 100mg/L. The result justified the great photostability of the newly prepared photocatalyst, with high capability to extend the lifespan for the photocatalytic degradation of different organic water pollutants.

Table 4.

A comparison of the photocatalytic performance of different regenerated photocatalysts for the decolorization of dye pollutants.

Regenerated photocatalyst  Dye pollutants  Initial concentration (mg/L)  Reusability cycles  Removal (%)  Reference 
CuO/DSA nanocomposite  Acid Red 88  100  97.4  Present study 
TiO2/fly ash cenospheres  Methylene Blue  25  97.2  [41] 
N, S- TiO2/fly ash bead  Methyl Orange  20  70.9  [42] 
CeO2/fly ash  Brilliant Green  10  75.5  [43] 
Co/lignite fly ash  Acid Red 1  10  93.0  [44] 
Rice husk ash-TiO2  Methylene Blue  25  50.0  [45] 
BiVO4/fly ash cenospheres  Methyl Orange  10  82.0  [46] 
6Conclusion

A novel CuO/DSA derived nanocomposite has been successfully prepared using a simple one step hydrothermal synthesis method. This newly prepared CuO/DSA derived nanocomposite demonstrated a synergistic function of adsorption and photodegradation, with the enhanced photocatalytic performance for the complete removal of AR 88 from a lower concentration of 100mg/L to the higher concentration of 500mg/L, within a short duration of 8 to 105min. Morphological evaluation verified structural transformation, supported by the BET surface area and total pore volume of 36.41m2/g and 0.108cm3/g. Stability analysis revealed the great photostability of the nanocomposite, even after five regeneration cycles. This study suggested an alternative pathway of Durio zibethinus shell derived ash as a renewable resource for preparation of high quality photocatalyst for the decontamination of water pollutants.

Conflicts of interest

The author declares no conflicts of interest.

References

[36,40].

Acknowledgements

The authors acknowledge the financial support provided by Universiti Sains Malaysia under the USM Short Term grant scheme (Project No. 304/PREDAC/6315111).

Appendix A
Supplementary data

The following is Supplementary data to this article:

References
[1]
A.A. Aboud, H. Al-Kelesh, W.M. El Rouby, A.A. Farghali, A. Hamdedein, M.H. Khedr.
CO2 responses based on pure and doped CeO2 nano-pellets.
J Mater Res Technol, 7 (2018), pp. 14-20
[2]
M. Elkady, H. Hamad, N. El Essawy.
Modification of optical and electrical properties of nanocrystalline VO2·0.5H2O/ZrV2O7: influence of Cs, Cr and Ga doping.
J Mater Res Technol, 8 (2019), pp. 1212-1223
[3]
K.Y. Foo, B.H. Hameed.
Decontamination of textile wastewater via TiO2/activated carbon composite materials.
Adv Colloid Interface Sci, 159 (2010), pp. 130-143
[4]
N.K. Soliman.
Factors affecting CO oxidation reaction over nanosized materials: a review.
J Mater Res Technol, 8 (2019), pp. 2395-2407
[5]
Y. Wei, C. Liu, S. Luo, J. Ma, Y. Zhang, H. Feng, et al.
Deep oxidation and removal of arsenite in groundwater by rationally positioning oxidation and adsorption sites in binary Fe-Cu oxide/TiO2.
Chem Eng J, 354 (2018), pp. 825-834
[6]
J.R. Schilz, K. Reddy, S. Nair, T.E. Johnson, R.B. Tjalkens, K.P. Krueger, et al.
Removal of trace elements by cupric oxide nanoparticles from uranium in situ recovery bleed water and its effect on cell viability.
J Visualized Exp, 100 (2015), pp. 1-12
[7]
W. Zhang, B. Wang, C. Hao, Y. Liang, H. Shi, L. Ao, et al.
Au/Cu2O Schottky contact heterostructures with enhanced photocatalytic activity in dye decomposition and photoelectrochemical water splitting under visible light irradiation.
J Alloys Compd, 684 (2016), pp. 445-452
[8]
J. Zhang, H. Cui, B. Wang, C. Li, J. Zhai, Q. Li.
Preparation and characterization of fly ash cenospheres supported CuO–BiVO4 heterojunction composite.
Appl Surf Sci, 300 (2014), pp. 51-57
[9]
S.B. Wang, X.Q. Wang, H.L. Zhang, W.B. Zhang.
Hollow CuO microspheres with open nanoholes: fabrication and photocatalytic properties.
J Alloys Compd, 685 (2016), pp. 22-27
[10]
K.Y. Foo, B.H. Hameed.
Transformation of durian biomass into a highly valuable end commodity: trends and opportunities.
Biomass Bioenergy, 35 (2011), pp. 2470-2478
[11]
A.N. Ökte, D. Karamanis.
A novel photoresponsive ZnO-flyash nanocomposite for environmental and energy applications.
Appl Catal B, 142-143 (2013), pp. 538-552
[12]
H.Y. Yu, G.Y. Chen, Y.B. Wang, J.M. Yao.
A facile one-pot route for preparing cellulose nanocrystal/zinc oxide nanohybrids with high antibacterial and photocatalytic activity.
Cellul, 22 (2015), pp. 261-273
[13]
S. Liu, J. Zhu, Q. Yang, P. Xu, J. Ge, X. Guo.
Preparation of SnO2–TiO2/fly ash cenospheres and its application in phenol degradation.
Photochem Photobiol, 91 (2015), pp. 1302-1308
[14]
S.S. Khan.
Enhancement of visible light photocatalytic activity of CdO modified ZnO nanohybrid particles.
J Photochem Photobiol B, 142 (2015), pp. 1-7
[15]
M. Visa, A.M. Chelaru.
Hydrothermally modified fly ash for heavy metals and dyes removal in advanced wastewater treatment.
Appl Surf Sci, 303 (2014), pp. 14-22
[16]
M. Yao, J. Zhao, S. Lv, K. Lu.
Preparation and hydrogenation of urchin-like titania using a one-step hydrothermal method.
Ceram Int, 43 (2017), pp. 6925-6931
[17]
M.G. Alalm, A. Tawfik, S. Ookawara.
Enhancement of photocatalytic activity of TiO2 by immobilization on activated carbon for degradation of pharmaceuticals.
J Environ Chem Eng, 4 (2016), pp. 1929-1937
[18]
H.J. Kim, M.K. Joshi, H.R. Pant, J.H. Kim, E. Lee, C.S. Kim.
One-pot hydrothermal synthesis of multifunctional Ag/ZnO/fly ash nanocomposite.
Colloids Surf A, 469 (2015), pp. 256-262
[19]
B. Gao, P.S. Yap, T.M. Lim, T.T. Lim.
Adsorption-photocatalytic degradation of Acid Red 88 by supported TiO2: effect of activated carbon support and aqueous anions.
Chem Eng J, 171 (2011), pp. 1098-1107
[20]
S.M. Lam, J.C. Sin, A.Z. Abdullah, A.R. Mohamed.
Investigation on visible-light photocatalytic degradation of 2, 4-dichlorophenoxyacetic acid in the presence of MoO3/ZnO nanorod composites.
J Mol Catal A Chem, 370 (2013), pp. 123-131
[21]
R. Mallampati, S. Valiyaveettil.
Biomimetic metal oxides for the extraction of nanoparticles from water.
Nanoscale, 5 (2013), pp. 3395-3399
[22]
L. Zhu, M. Hong, G.W. Ho.
Fabrication of wheat grain textured TiO2/CuO composite nanofibers for enhanced solar H2 generation and degradation performance.
Nano Energy, 11 (2015), pp. 28-37
[23]
B. Wang, C. Li, J. Pang, X. Qing, J. Zhai, Q. Li.
Novel polypyrrole-sensitized hollow TiO2/fly ash cenospheres: synthesis, characterization, and photocatalytic ability under visible light.
Appl Surf Sci, 258 (2012), pp. 9989-9996
[24]
A. Petica, A. Florea, C. Gaidau, D. Balan, L. Anicai.
Synthesis and characterization of silver-titania nanocomposites prepared by electrochemical method with enhanced photocatalytic characteristics, antifungal and antimicrobial activity.
J. Mater. Res. Technol., 8 (2019), pp. 41-53
[25]
F. Sheng, X. Zhu, W. Wang, H. Bai, J. Liu, P. Wang, et al.
Synthesis of novel polyoxometalate K6ZrW11O39Sn·12H2O and photocatalytic degradation aqueous azo dye solutions with solar irradiation.
J Mol Catal A Chem, 393 (2014), pp. 232-239
[26]
M.R. Chandra, T.S. Rao, S.V.N. Pammi, B. Sreedhar.
An enhanced visible light active rutile titania–copper/polythiophene nanohybrid material for the degradation of rhodamine B dye.
Mater Sci Semicond Process, 30 (2015), pp. 672-681
[27]
G. Sangami, N. Dharmaraj.
UV-visible spectroscopic estimation of photodegradation of rhodamine-B dye using tin(IV) oxide nanoparticles.
Spectrochim Acta A, 97 (2012), pp. 847-852
[28]
N. Ameta, J. Sharma, S. Sharma, S. Kumar, P.B. Punjabi.
Copper modified iron oxide as heterogeneous photo-Fenton reagent for the degradation of coomasie Brilliant Blue R-250.
Indian J Chem, 51A (2012), pp. 943-948
[29]
K. Balachandran, R. Venckatesh, R. Sivaraj, P. Rajiv.
TiO2nanoparticles versus TiO2–SiO2 nanocomposites: a comparative study of photo catalysis on Acid Red 88 Spectrochim.
Acta A, 128 (2014), pp. 468-474
[30]
S. Ahmed, M.G. Rasul, W.N. Martens, R. Brown, M.A. Hashib.
Heterogeneous photocatalytic degradation of phenols in wastewater: a review on current status and developments.
Desalin, 261 (2013), pp. 3-18
[31]
R.D.C. Soltani, A. Khataee, M. Mashayekhi.
Photocatalytic degradation of a textile dye in aqueous phase over ZnO nanoparticles embedded in biosilica nanobiostructure.
Desalin Water Treat, 57 (2016), pp. 13494-13504
[32]
Y.L. Song, J.T. Li, H. Chen.
Degradation of C.I. Acid Red 88 aqueous solution by combination of Fenton’s reagent and ultrasound irradiation.
J Chem Technol Biotechnol, 84 (2009), pp. 578-583
[33]
M.T. Uddin, Y. Sultana, M.A. Islam.
Nano-sized SnO2 photocatalysts: synthesis, characterization and their application for the degradation of Methylene Blue dye.
J Sci Res, 8 (2016), pp. 399-411
[34]
V.K. Saharan, A.B. Pandit, P.S. Satish Kumar, S. Anandan.
Hydrodynamic cavitation as an advanced oxidation technique for the degradation of Acid Red 88 dye.
Ind Eng Chem Res, 51 (2012), pp. 1981-1989
[35]
B. Agarwal, P. Sengupta, C. Balomajumder.
Equilibrium, kinetic and thermodynamic studies of simultaneous co-adsorptive removal of phenol and cyanide using chitosan.
Life, 2 (2013), pp. 5
[36]
D. Dimitrakopoulou, I. Rethemiotaki, Z. Frontistis, N.P. Xekoukoulotakis, D. Venieri, D. Mantzavinos.
Degradation, mineralization and antibiotic inactivation of amoxicillin by UV-A/TiO2 photocatalysis.
J Environ Manage, 98 (2012), pp. 168-174
[37]
M.E. Olya, A. Pirkarami, M. Soleimani, M. Bahmaei.
Photoelectrocatalytic degradation of acid dye using Ni-TiO2 with the energy supplied by solar cell: mechanism and economical studies.
J Environ Manage, 121 (2013), pp. 210-219
[38]
M.A. Behnajady, N. Modirshahla, M. Mirzamohammady, B. Vahid, B. Behnajady.
Increasing photoactivity of titanium dioxide immobilized on glass plate with optimization of heat attachment method parameters.
J Hazard Mater, 160 (2008), pp. 508-513
[39]
D. Malwal, P. Gopinath.
Enhanced photocatalytic activity of hierarchical three dimensional metal oxide@CuO nanostructures towards the degradation of Congo red dye under solar radiation.
Catal Sci Technol, 6 (2016), pp. 4458-4472
[40]
R. Chatti, S.S. Rayalu, N. Dubey, N. Labhsetwar, S. Devotta.
Solar-based photoreduction of methyl orange using zeolite supported photocatalytic materials.
Sol Energy Mater Sol Cells, 91 (2007), pp. 180-190
[41]
P.K. Surolia, R.J. Tayade, R.V. Jasra.
TiO2-coated cenospheres as catalysts for photocatalytic degradation of methylene blue, p-nitroaniline, n-decane, and n-tridecane under solar irradiation.
Ind Eng Chem Res, 49 (2010), pp. 8908-8919
[42]
J. Lv, T. Sheng, L. Su, G. Xu, D. Wang, Z. Zheng, et al.
N, S co-doped-TiO2/fly ash beads composite material and visible light photocatalytic activity.
Appl Surf Sci, 284 (2013), pp. 229-234
[43]
G. Sudha, E. Subramanian.
Synthesis, characterization and photocatalytic study of cerium oxide/zeolite-NaX catalyst with brilliant green dye degradation.
J Adv Chem Sci, 1 (2015), pp. 117-120
[44]
P.V.S. Giribabu, G. Swaminathan.
Synergetic degradation of reactive dye Acid Red 1 by cobalt-doped lignite fly ash.
Desalin Water Treat, 57 (2016), pp. 16955-16962
[45]
S.A. Hassan, R.A. El-Salamony.
Photocatalytic disc-shaped composite systems for removal of hazardous dyes in aqueous solutions.
Can Chem Trans, 2 (2014), pp. 57-71
[46]
Y.X. Sun, J. Zhang.
Photocatalytic degradation of methyl orange and phenol by BiVO4-loaded fly ash cenospheres (FACs) composite.
Adv Mater Res, 821-822 (2013), pp. 471-475
Journal of Materials Research and Technology

Subscribe to our newsletter

Article options
Tools
Supplemental materials
Cookies policy
To improve our services and products, we use cookies (own or third parties authorized) to show advertising related to client preferences through the analyses of navigation customer behavior. Continuing navigation will be considered as acceptance of this use. You can change the settings or obtain more information by clicking here.