Next Article in Journal
Photoelectrochemical Performance of a CuBi2O4 Photocathode with H2O2 as a Scavenger
Previous Article in Journal
Older but Stronger: Development of Platinum-Based Antitumor Agents and Research Advances in Tumor Immunity
 
 
Search for Articles:
Title / Keyword
Author / Affiliation / Email
Journal
Article Type
 
 
Advanced Search
 
Section
Special Issue
Volume
Issue
Number
Page
 
Journals
Inorganics
Volume 11
Issue 4
10.3390/inorganics11040146
inorganics-logo
Submit to this Journal Review for this Journal Propose a Special Issue
► Article Menu

Article Menu

share Share announcement Help format_quote Cite question_answer Discuss in SciProfiles thumb_up
...
Endorse textsms
...
Comment
first_page
settings
Order Article Reprints
Font Type:
Arial Georgia Verdana
Font Size:
Aa Aa Aa
Line Spacing:
Column Width:
Background:
Article

Dependency of Crystal Violet Dye Removal Behaviors onto Mesoporous V2O5-g-C3N4 Constructed by Simplistic Ultrasonic Method

by
Mohamed Ali Ben Aissa
1,*,
Abueliz Modwi
1,
Abuzar E. A. E. Albadri
2 and
Sayed M. Saleh
2,3
1
Department of Chemistry, College of Science and Arts, Qassim University, Ar-Rass 51921, Saudi Arabia
2
Department of Chemistry, College of Science, Qassim University, Buraidah 51452, Saudi Arabia
3
Chemistry Branch, Department of science and mathematics, Faculty of Petroleum and Mining Engineering, Suez University, Suez 43721, Egypt
*
Author to whom correspondence should be addressed.
Inorganics 2023, 11(4), 146; https://doi.org/10.3390/inorganics11040146
Submission received: 4 March 2023 / Revised: 24 March 2023 / Accepted: 27 March 2023 / Published: 30 March 2023
(This article belongs to the Section Inorganic Materials)
Browse Figures
Review Reports Versions Notes

Abstract

:
This research examined the production of a V2O5-g-C3N4 nanocomposite to remove organic dyes from wastewater. To generate the V2O5-g-C3N4 nanocomposite, the sonication method was applied. The testing of V2O5-g-C3N4 with various dyes (basic fuchsin (BF), malachite green (MG), crystal violet (CV), Congo red (CR), and methyl orange (MO)) revealed that the nanocomposite has a high adsorption ability towards BF, MG, CV, and CR dyes in comparison with MO dye. It was established that the modification of pH influenced the removal of CV by the V2O5-g-C3N4 nanocomposite and that under optimal operating conditions, efficiency of 664.65 mg g−1 could be attained. The best models for CV adsorption onto the V2O5-g-C3N4 nanocomposite were found to be those based on pseudo-second-order adsorption kinetics and the Langmuir isotherm. According to the FTIR analysis results, the CV adsorption mechanism was connected to π–π interactions and the hydrogen bond.

Graphical Abstract

1. Introduction

With rapid industrialization, the environmental damage caused by organic dye wastewater is intensifying and becoming more severe. Organic dyes are commonly employed in cosmetics, food additives, paper-making, leather, and textile industries [1,2,3]. Consequently, substantial quantities of organic dyes are generated, and significant amounts of dyes are discharged into wastewater, which can cause highly hazardous byproducts in the environment [4,5,6]. Due to their aromatic character, organic dyes such as crystal violet (CV) include several functional groups that are persistent and difficult to decompose. CV is utilized in the manufacture of black and blue inks for ballpoint pens and printer ink jets [7,8]. CV is also used to produce waxes, leather, varnish, fertilizers, detergents, medications, and color paints [9,10,11]. However, CV, similar to most dyes, is a toxic carcinogenic with a recalcitrant classification because of its non-biodegradability, persistence in various environments, and nasty microbial metabolization [12,13,14]. Moreover, CV generates unpleasant colorations of water bodies, resulting in reduced light penetration for photosynthetic activities, negatively impacting aquatic life, such as the development of tumors in fish [10,15]. In order to ensure the life of aquatic organisms and humans, CV must be removed from wastewater before release.
Graphitic carbon nitride (g-C3N4), a 2D metal-free semiconductor, has acquired traction in energy storage and environmental applications, and as a photocatalyst for CO2 reduction [16], hydrogen production [17], and contaminant degradation [18,19] due to its facile fabrication method, excellent thermal stability, low cost, and environmental friendliness [20,21,22,23]. Despite the plethora of research on g-C3N4 as a photocatalyst, there are only a few papers on its adsorption uses [24,25,26]. Even though photocatalytic degradation can totally eliminate environmental contaminants, it is hampered by the formation of byproducts and relatively high running costs [27,28]. On the contrary, adsorption can remove significant quantities of contaminants without producing byproducts.
Due to its limited specific surface area (˂10 m2/g) and single surface functional group [29], pure g-C3N4 is not commonly employed in adsorption procedures [30]. Over the years, numerous modification techniques have been developed to increase the application of g-C3N4 [31,32,33,34]. In order to improve the removal efficiency of hazardous dyes, researchers have increasingly concentrated on modifying pure g-C3N4 by element doping, controlling its morphology, semiconductor recombination, and stripping [29]. Doping with heteroatoms is an excellent method for improving the adsorption of carbon-based compounds [33,35,36,37,38,39]. Vanadium pentoxide (V2O5), which possesses high oxidation ability, chemical inertness, and long-term stability against photochemical degradation, has been extensively utilized in numerous applications, including sensors, batteries, and catalysts [40,41,42].
We think this is the first study to successfully synthesize V2O5 incorporated with g-C3N4 with high surface area and efficient elimination of organic dyes, which opens up new avenues for the applications of g-C3N4 materials.

2. Results and Discussions

2.1. The V2O5-g-C3N4 Nanosorbent Characteristics

The morphologies and microstructures of the V2O5-g-C3N4 nanosorbent were further investigated using transmission electron microscopy (TEM). Figure 1a reveals that thin layers of g-C3N4 wrap V2O5 nanoparticles.
Figure 1d–g display the energy dispersive X-ray spectrometer (EDS) maps of the elements V, N, O, and C. EDS maps illustrate the interface between V2O5 and carbon nitride. It is clearly seen that the components are dispersed uniformly, this result confirmed the successful combination of these nanomaterials.
The XRD technique was utilized to investigate the produced materials’ structure, purity, and phase composition. Figure 2a displays the XRD patterns of the as-fabricated V2O5, g-C3N4, and the V2O5-g-C3N4 nanosorbent. The two distinctive diffraction peaks at 12.9° and 27.4° are attributed to the (100) and (002) planes of g-C3N4, respectively. In addition, the orthorhombic crystal structure of V2O5 is shown by the prominent diffraction peaks at 2θ = 34.08°, 31.07°, 26.19°, 20.31°, and 15.42° corresponding to the (310), (301), (110), (001), and (200) planes (JCPDS 41–1426) [43]. Both the definite diffraction peaks of g-C3N4 and the orthorhombic phase of V2O5 are observable in XRD patterns of V2O5-g-C3N4, and no other impurities are detected, confirming the purity of the fabricated nanocomposites. Figure 2b depicts the N2 adsorption-desorption isotherms of the V2O5-g-C3N4 nanosorbent as manufactured. The isotherms are type IV, confirming the mesoporous structure of the V2O5-g-C3N4 nanocomposites. The V2O5-g-C3N4 surface area is 61.04 m2/g. Thus, the nanocomposites featured a greater surface area and additional active sites, favoring adsorption efficiency.
The graph of point zero charges (Figure 2d) was generated by plotting the difference between the beginning and final pH against the initial pH. The V2O5-g-C3N4’s point zero charges (pzc) were 3.83. The surface of the V2O5-g-C3N4 nanosorbent is positively charged when the pH is less than pzc and negatively charged when the pH is higher than pzc.
X-ray photoelectron spectra (XPS) were used to examine the surface chemical compositions of the V2O5-g-C3N4 nanosorbent. The XPS spectra of the V2O5-g-C3N4, depicted in Figure 3a, demonstrate that the nanosorbent consisted of vanadium, oxygen, nitrogen, and carbon. Figure 3b displays the XPS spectra of C1s. The presence of two characteristic peaks at 285.2 and 281.9 eV can be deduced from the data in Figure 3b, attributed to the carbon sp2 (C=N-) and carbon sp3 hybridization (C-C) [44]. Figure 3c shows the XPS spectra of N1s. Two characteristic peaks were found at 395.7 and 397.4 eV, attributed to the nitrogen sp2 (-C=N-) and sp3 hybridization (-N-C), respectively [45]. Figure 3d depicts the XPS spectra of O1s, in which the distinctive peak of the oxygen atom in V2O5 was shown to have a binding energy of 527.4 eV [46]. The V2p’s XPS spectral (Figure 3e) highlights the presence of two peaks at 527.9 and 514.7 eV, which correspond to V2p1/2 and V2p3/2, respectively.

2.2. Dyes Adsorption onto the V2O5-g-C3N4 Nanocomposite

2.2.1. Adsorption Capability of the V2O5-g-C3N4 Nanocomposite towards Organic Dyes

The V2O5-g-C3N4 nanocomposite was tested with various organic dye solutions for constant concentrations equal to 50 ppm. Experiments on dye removal were conducted under magnetic stirring by combining 10 mg of the V2O5-g-C3N4 nanocomposite with 25 mL of the dye’s aqueous solution for 24 h (Figure 4a). The ability of the V2O5-g-C3N4 nanocomposite to absorb various dyes from an aqueous solution was evaluated. Figure 4b depicts the percentage of elimination of various dyes by the V2O5-g-C3N4 nanocomposite. Results confirmed that the removal ability percentages of BF, MG, CV, CR, and MO were 94%, 76.8%, 98.9%, 94.4%, and 5.4%, respectively. This result suggests that the V2O5-g-C3N4 nanocomposite is an efficient sorbent for eliminating CV, MG, BF, and CR dyes from wastewater.

2.2.2. Impact of Initial pH and Concentration on CV Dyes Elimination

Monitoring the effectiveness of nanoadsorbents in wastewater treatment relies heavily on pH levels [1,47]. The fluctuations in pH lead to modifications in the surface characteristics of the adsorbent and the degree of ionization of adsorptive molecules [2,48]. As is evident from Figure 4c, pH fluctuations significantly impact the percentage of CV dye removed from a solution. With an initial CV concentration of 50 ppm and a nanoadsorbent dosage of 10 mg, the effect of pH was investigated in the range between 2 and 12. Figure 4b demonstrates that as the pH of the solution reached 7, the CV dye removal percentage achieved its greatest values. The V2O5-g-C3N4 nanocomposite revealed removal percentages of 15, 62, 99, 85, and 77% for CV dye at pH 2, 4, 7, 9, and 12, respectively. The V2O5-g-C3N4 nanocomposite surface was positively charged at lower pH, resulting in electrostatic repulsion with the cationic CV dye molecules and, as a result, a decreased adsorption efficiency. Wathukarage et al. showed that woody biochar interacts electrostatically with CV molecules at a pH higher than pzc, whereas the biochar surface covered with positive charges below pzc develops electrostatic repulsion with the cationic CV molecules [49].
The influence of CV dye concentration on the amount adsorbed was also studied. The investigations were carried out with 20 mg of the V2O5-g-C3N4 nanocomposite at a pH value equal to 7. The CV adsorption capacity increased dramatically from 62.9 to 429.6 mg g−1 when the concentration of CV dye was raised from 25 to 200 ppm, as seen in Figure 4d. Increasing the CV’s initial concentration furnished an effective driving force to overcome all resistance to the migration of CV molecules from the aqueous solution [47].

2.2.3. Adsorption Isotherms Modeling

The adsorption result for CV dye was based on widely analyzed adsorption isotherm models (Langmuir and Freundlich) to estimate the maximum adsorption capacity presented by the V2O5-g-C3N4 nanocomposite for CV dye. The Langmuir model depicts chemical adsorption and implies that the adsorption process occurs on a homogeneous monolayer surface with comparable adsorption energy requirements for all active sites [50]. The Freundlich model describes physical adsorption and assumes it occurs on a multilayer heterogeneous surface with different adsorption sites and variable affinities [50]. Table 1 presents the nonlinear formulas for the used isotherms. The results of nonlinear isotherm graphs for CV adsorption onto V2O5-g-C3N4 are shown in Figure 5a, and the estimated isotherm parameters are listed in Table 1.
The correlation coefficient (R2) for the fitted plot of the Langmuir isotherm is 0.995, which is greater than the R2 for the Freundlich isotherm (0.974). This result indicates that the Langmuir model is well-fitted, indicating the monolayer adsorption of CV molecules on the V2O5-g-C3N4 nanocomposite. Following the Langmuir model, it was established that the maximum adsorption capacity of V2O5-g-C3N4 was 664.65 mg/g. In addition, the equilibrium parameter RL ( = 1 1 + K L . C 0 ) was used to determine whether or not the adsorption was favorable. The RL value was found to be 0.08, which was in the 0–1 range, affirming that the adsorption was favorable. The capacity of V2O5-g-C3N4 nanocomposite to adsorb CV dye has been compared to several adsorbents mentioned in the literature (Table 2).

2.2.4. Contact Time and Adsorption Kinetics Modeling

In order to establish the optimal time required for the maximal uptake of CV dye by the V2O5-g-C3N4 nanocomposite, the impact of contact time on the CV adsorption was investigated for various contact times ranging from 3 to 1440 min at 25 °C. The effects of contact time on the adsorption process are illustrated in Figure 5b. The adsorption capabilities of the V2O5-g-C3N4 nanocomposite grew rapidly during the first 20 min and reached equilibrium, with no significant changes after that. At the start of the process, the adsorption rate was very fast due to the availability of many active sites on the surface of the V2O5-g-C3N4 nanocomposite. As a result, the concentration of the remaining active sites decreased at equilibrium, and the sorption rate decreased dramatically. As a result, beyond this optimum value, the elimination of CV molecules remained unaltered.
For the optimal selection of the adsorption kinetics model, CV adsorption over the V2O5-g-C3N4 nanocomposite at a concentration of 100 ppm CV was investigated. The pseudo-first order (PFO) and pseudo-second order (PSO) plotting graphs were presented in Figure 5c by plotting qt against time. The parameters of adsorption kinetics denoted by k1, k2, qe, and R2 of the evaluation model were determined theoretically using nonlinear fitting and are reported in Table 3. The R2 values indicated that CV adsorption on the V2O5-g-C3N4 nanocomposite is well-defined using the PSO model, which agrees with the experimental result.
Weber’s intraparticle diffusion was used to fit the experimental data in order to comprehend the adsorption kinetics and rate-controlling stages better. The intraparticle diffusion model is chosen as the application model by graphing qt against t1/2. Figure 5d depicts the intraparticle diffusion process curves of CV adsorbed over the V2O5-g-C3N4 nanocomposite. The adsorption procedure consists of two steps. The initial stage is film diffusion, wherein CV molecules diffuse from the solution to the outer surface of the V2O5-g-C3N4 nanocomposite. The intraparticle diffusion stage is the second step, and is influenced by the surface morphology as well as the number of void sites that are present in the V2O5-g-C3N4 nanocomposite. Kdif1 was considerably greater than Kdif2, indicating that the intraparticle diffusion phase was a smooth process [63]. The intercept at the second step was larger than that at the first step, which indicates a greater contribution of surface adsorption in the step that controls the rate [64]. In addition, the R2 values in the two phases were, respectively, 0.983 and 0.908, which indicates that Weber’s intraparticle diffusion model had great application in investigating the CV adsorption mechanism.

2.2.5. Adsorption Mechanism

The mechanism of CV dye adsorption onto the V2O5-g-C3N4 nanocomposite may imply electrostatic interactions, physical adsorption, π–π interactions, and hydrogen bonds [65,66]. To comprehend the adsorption process, the FTIR spectra of V2O5-g-C3N4 before and after CV dye adsorption were recorded in the range of cm−1 (Figure 6a). Hydrogen bonding may have a significant role in CV dye adsorption. The broadband between 3000 and 3500 cm−1, attributed to the O–H and terminal amino group stretching modes, slightly shifted, revealing the embroilment of the OH and amino groups of the nanocomposite in the adsorption process. As a result, the existence of hydrogen bonds between CV dyes and V2O5-g-C3N4 can be confirmed. The π–π interactions represent an essential mechanism between the π-electrons in organic molecules with aromatic rings and those in a carbon nitride substance, according to several investigations that have validated this phenomenon [67]. The vibrational triazine ring mode at 883 cm−1 was shifted after CV dye adsorption, and this confirmed the π-π interaction between the aromatic rings of CV molecules and the π-electron clouds of V2O5-g-C3N4. Figure 6b depicts the possible CV adsorption mechanism onto the V2O5-g-C3N4 nanocomposite.

2.2.6. Reusability Test

Along with having a high adsorption capacity, an ideal adsorbent should also have high reusability, as this would help to keep the overall cost of the adsorption process to a minimum. The reusability tests for the V2O5-g-C3N4 nanocomposite for the removal of CV dye was conducted four times with the same adsorbent dose, as shown in Figure 7. Following the adsorption experiment, the previously utilized V2O5-g-C3N4 nanocomposites were first recovered using filtering and then calcined at a temperature of 500 degrees Celsius for one hour. Following that, the obtained V2O5-g-C3N4 was utilized again. As a result of the reusability performance trial, depicted in Figure 7, it is possible to notice that V2O5-g-C3N4 can perform the CV elimination process effectively for at least four cycles, with a mean value of around 92%.

3. Materials and Methods

3.1. Chemicals

Ammonium vanadate (NH4VO3 ≥ 99.0%), urea (≥98.0%), crystal violet (CV ≥ 90%), malachite green (MG ≥ 90%), basic fuchsin (BF ≥ 85%), Congo red (CR ≥ 97.0%), methyl orange (MO ≥ 98%), sodium hydroxide (NaOH ≥ 99%), sodium chloride (NaCl ≥ 99%), and hydrochloric acid (HCl ≥ 37%) purchased from Merck Company were used without further purification. The required CV concentrations (25 to 200 ppm) were obtained by diluting CV stock solution (500 ppm).

3.2. Nanomaterials Synthesis

V2O5 nanomaterials were fabricated by thermal decomposition of ammonium vanadate (NH4VO3) at 400 °C for 2 h in the air atmosphere. The g-C3N4 nanostructures were generated by the thermal polymerization approach [68]. In the typical method, 4000 mg of urea powder was calcined at 550 °C in an alumina crucible with a cap in an electric furnace at a heating rate of 4.6 °C/min for 120 min. A yellowish solid powder was formed after cooling to ambient temperature through natural means.
For the V2O5-g-C3N4 nanocomposite fabrication, 800 mg of solid g-C3N4 powder was distributed in 115 mL of ethanol and sonicated for 30 min. After adding 1800 mg of V2O5 nanoparticles, the mixed solution was rapidly agitated for 60 min. The suspension was then heated at 75 degrees Celsius for 24 h to evaporate the organic solvent. The resultant solid was then annealed at 150 °C for 120 min to generate the V2O5-g-C3N4 nanocomposite.

3.3. The V2O5-g-C3N4 Nanocomposite Characterization

Employing JEOL, JEM-2100 transmission electron microscopy (TEM), the production and distribution of the V2O5-g-C3N4 nanocomposite were investigated. The nanocomposite morphology was investigated by JEOL, JEM-6700F field emission scanning electron microscopy (FESEM). Energy dispersive X-ray spectrometer (EDS) analysis was performed to determine the notional stoichiometry composition of nonmaterial surfaces. The crystallinity grade and phase construction were scrutinized through X-ray diffraction (XRD) using a Bruker D8–Advance equipped with a Cu-K source (λ = 0.15418 nm). The porosity and BET surface area were measured using N2 adsorption-desorption at 77 K and a Micromeritics 2010 device. Using FTIR (Nicolet 6700) in the 4000–400 cm−1 range with a resolution of 4 cm−1, the chemical bonding and stretching vibration of the produced samples before and after CV dye adsorption were analyzed.

3.4. CV Dye Adsorption Procedure

Batch removal studies were conducted by contacting 20 mg of the V2O5-g-C3N4 nanocomposite sorbent with 50 mL of CV dye solution at varying starting concentrations (25–200 mg/L). In 50 mL screw-top bottles, the mixture was swirled on a magnetic stirrer at 400 rpm for 24 h, which was longer than necessary to achieve equilibrium. A comparison with other organic dyes (malachite green (MG), basic fuchsin (BF), Congo red (CR), and methyl orange (MO)) was also performed by dissolving 20 mg of the V2O5-g-C3N4 nanocomposite in 50 mL of dye solution (50 ppm) and magnetically stirring for 24 h. After each experiment, the solutions were centrifuged and the residual dye concentrations were measured with a SHIMADZU UV-1650PC spectrophotometer. The residual dye concentrations were determined at a maximum wavelength of 590 nm for CV, 617 nm for MG, 545 nm for BF, 497 nm for CR, and 467 nm for MO. Then, the concentration of dyes was obtained, and equilibrium dye capacity (qe (mg g−1)) was calculated using the following equation:
q e = V ( C 0 − C e ) m
where m is the mass of the adsorbent (g), V is the volume of the solution (L), and C0 and Ce (mg L−1) are the dye concentrations at time equal to 0 and equilibrium, respectively.
For the kinetic experiment, the volume and initial concentration of dyes were 150 mL and 250 ppm, respectively, while the mass of the V2O5-g-C3N4 nanocomposite was 60 mg. The test was conducted in the dark while magnetic stirring was taking place. Later, 5 mL of the suspension was withdrawn and centrifuged at predetermined intervals to determine the remaining CV dye concentration. The following equation was employed to determine the adsorbed quantity qt (mg g−1) at time t:
q t = V ( C 0   −   C t ) m
The Origin 2016b program was used to plot and model the experimental data.

4. Conclusions

The V2O5-g-C3N4 nanocomposite with a greater surface area was successfully synthesized using the sonication method. The study findings demonstrated a good CV dye removal efficiency. The evaluation of V2O5-g-C3N4 as a possible adsorbent for various dyes (BF, MG, CV, CR, and MO), demonstrated the overall high potential of the nanocomposite for the removal of dyes from wastewaters. In order to improve V2O5-g-C3N4’s effectiveness in removing CV dye, an investigation into the influence of pH was carried out. The removal of CV dye by the V2O5-g-C3N4 nanocomposite was found to be pH-dependent. The greatest adsorption capacity for CV pollutants was found at a pH of 7, 664.65 mg g−1. Several kinetic and adsorption models were utilized in this study to evaluate the removal of CV by V2O5-g-C3N4. The PSO kinetics and the Langmuir adsorption isotherm models were found to fit the data best. According to the FTIR analysis results, the CV adsorption mechanism was connected to π–π interactions and the hydrogen bond.

Author Contributions

The study design, preparation of materials, data collection, and analysis were contributed by all authors. Each author provided feedback on prior drafts of the article. The final manuscript was read and approved by all authors. All authors have read and agreed to the published version of the manuscript.

Funding

The authors extend their appreciation to the Deputyship for Research & Innovation, Ministry of Education, Saudi Arabia for funding this research work through the project number (QU-IF-4-5-1--31384).

Data Availability Statement

Not applicable.

Acknowledgments

The authors extend their appreciation to the Deputyship for Research & Innovation, Ministry of Education, Saudi Arabia for funding this research work through the project number (QU-IF-4-5-1--31384). The authors also thank to Qassim University for technical support.

Conflicts of Interest

We declare that we do not have any commercial or associative interest that could potentially influence or bias the submitted work.

References

  1. Aissa, B.; Khezami, L.; Taha, K.; Elamin, N.; Mustafa, B.; Al-Ayed, A.; Modwi, A. Yttrium oxide-doped ZnO for effective adsorption of basic fuchsin dye: Equilibrium, kinetics, and mechanism studies. Int. J. Environ. Sci. Technol. 2021, 19, 9901–9914. [Google Scholar] [CrossRef]
  2. Rahali, S.; Ben Aissa, M.A.; Khezami, L.; Elamin, N.; Seydou, M.; Modwi, A. Adsorption behavior of Congo red onto barium-doped ZnO nanoparticles: Correlation between experimental results and DFT calculations. Langmuir 2021, 37, 7285–7294. [Google Scholar] [CrossRef] [PubMed]
  3. Adam, F.A.; Ghoniem, M.; Diawara, M.; Rahali, S.; Abdulkhair, B.Y.; Elamin, M.; Aissa, M.A.B.; Seydou, M. Enhanced adsorptive removal of indigo carmine dye by bismuth oxide doped MgO based adsorbents from aqueous solution: Equilibrium, kinetic and computational studies. RSC Adv. 2022, 12, 24786–24803. [Google Scholar] [CrossRef] [PubMed]
  4. Li, J.; Xiong, Y.; Wan, H.; Chen, J.; Fang, S.; Song, X.; Li, R.; Duan, M.; Hu, R. In-situ investigation of dye pollutant adsorption performance on graphitic carbon nitride surface: ATR spectroscopy experiment and MD simulation insight. J. Hazard. Mater. 2021, 418, 126297. [Google Scholar] [CrossRef]
  5. Largo, F.; Haounati, R.; Ouachtak, H.; Hafid, N.; Jada, A.; Addi, A.A. Design of organically modified sepiolite and its use as adsorbent for hazardous Malachite Green dye removal from water. Water Air Soil Pollut. 2023, 234, 183. [Google Scholar] [CrossRef]
  6. Ouachtak, H.; Akhouairi, S.; Addi, A.A.; Akbour, R.A.; Jada, A.; Douch, J.; Hamdani, M. Mobility and retention of phenolic acids through a goethite-coated quartz sand column. Colloids Surf. A Physicochem. Eng. Asp. 2018, 546, 9–19. [Google Scholar] [CrossRef]
  7. Alizadeh, N.; Shariati, S.; Besharati, N. Adsorption of crystal violet and methylene blue on azolla and fig leaves modified with magnetite iron oxide nanoparticles. Int. J. Environ. Res. 2017, 11, 197–206. [Google Scholar] [CrossRef]
  8. Ouachtak, H.; El Guerdaoui, A.; El Haouti, R.; Haounati, R.; Ighnih, H.; Toubi, Y.; Alakhras, F.; Rehman, R.; Hafid, N.; Addi, A.A. Combined molecular dynamics simulations and experimental studies of the removal of cationic dyes on the eco-friendly adsorbent of activated carbon decorated montmorillonite Mt@AC. RSC Adv. 2023, 13, 5027–5044. [Google Scholar] [CrossRef]
  9. Pathak, A.; Khandegar, V.; Kumar, A. Statistical Investigation in Conjunction with a Box–Behnken Design for the Removal of Dyes Using Electrocoagulation. J. Hazard. Toxic Radioact. Waste 2022, 26, 04022001. [Google Scholar] [CrossRef]
  10. Kyi, P.P.; Quansah, J.O.; Lee, C.-G.; Moon, J.-K.; Park, S.-J. The removal of crystal violet from textile wastewater using palm kernel shell-derived biochar. Appl. Sci. 2020, 10, 2251. [Google Scholar] [CrossRef]
  11. Nguyen, T.A.; Juang, R.-S. Treatment of waters and wastewaters containing sulfur dyes: A review. Chem. Eng. J. 2013, 219, 109–117. [Google Scholar] [CrossRef]
  12. Chakraborty, S.; Chowdhury, S.; Saha, P.D. Adsorption of crystal violet from aqueous solution onto NaOH-modified rice husk. Carbohydr. Polym. 2011, 86, 1533–1541. [Google Scholar] [CrossRef]
  13. Thekkedath, A.; Sugaraj, S.; Sridharan, K. Nanomaterials in Advanced Oxidation Processes (AOPs) in Anionic Dye Removal. In Advanced Oxidation Processes in Dye-Containing Wastewater; Springer: Berlin/Heidelberg, Germany, 2022; pp. 129–165. [Google Scholar]
  14. Varjani, S.; Rakholiya, P.; Shindhal, T.; Shah, A.V.; Ngo, H.H. Trends in dye industry effluent treatment and recovery of value added products. J. Water Process Eng. 2021, 39, 101734. [Google Scholar] [CrossRef]
  15. Ali, H.; Muhammad, S.K. Biosorption of crystal violet from water on leaf biomass of Calotropis procera. J. Environ. Sci. Technol 2008, 1, 143–150. [Google Scholar] [CrossRef]
  16. Lin, J.; Pan, Z.; Wang, X. Photochemical reduction of CO2 by graphitic carbon nitride polymers. ACS Sustain. Chem. Eng. 2014, 2, 353–358. [Google Scholar] [CrossRef]
  17. Yang, W.; Godin, R.; Kasap, H.; Moss, B.; Dong, Y.; Hillman, S.A.; Steier, L.; Reisner, E.; Durrant, J.R. Electron accumulation induces efficiency bottleneck for hydrogen production in carbon nitride photocatalysts. J. Am. Chem. Soc. 2019, 141, 11219–11229. [Google Scholar] [CrossRef] [PubMed]
  18. Xie, K.; Fang, J.; Li, L.; Deng, J.; Chen, F. Progress of graphite carbon nitride with different dimensions in the photocatalytic degradation of dyes: A review. J. Alloys Compd. 2022, 901, 163589. [Google Scholar] [CrossRef]
  19. Toghan, A.; Modwi, A. Boosting unprecedented indigo carmine dye photodegradation via mesoporous MgO@g-C3N4 nanocomposite. J. Photochem. Photobiol. A Chem. 2021, 419, 113467. [Google Scholar] [CrossRef]
  20. Shvalagin, V.V.; Korzhak, G.V.; Kuchmiy, S.Y.; Skoryk, M.A.; Selyshchev, O.V.; Zahn, D.R. Facile preparation and high photocatalytic activity of crystalline graphitic carbon nitride in hydrogen evolution from electron donor solutions under visible light. J. Photochem. Photobiol. A Chem. 2020, 390, 112295. [Google Scholar] [CrossRef]
  21. Yan, L.; Gao, H.; Chen, Y. Na-Doped Graphitic Carbon Nitride for Removal of Aqueous Contaminants via Adsorption and Photodegradation. ACS Appl. Nano Mater. 2021, 4, 7746–7757. [Google Scholar] [CrossRef]
  22. Ding, P.; Ji, H.; Li, P.; Liu, Q.; Wu, Y.; Guo, M.; Zhou, Z.; Gao, S.; Xu, W.; Liu, W. Visible-light degradation of antibiotics catalyzed by titania/zirconia/graphitic carbon nitride ternary nanocomposites: A combined experimental and theoretical study. Appl. Catal. B Environ. 2022, 300, 120633. [Google Scholar] [CrossRef]
  23. Zhu, Y.; Cai, W.; Zhao, Y.; Mu, X.; Zhou, X.; Chu, F.; Wang, B.; Hu, Y. Graphite-like Carbon Nitride/Polyphosphoramide Nanohybrids for Enhancement on Thermal Stability and Flame Retardancy of Thermoplastic Polyurethane Elastomers. ACS Appl. Polym. Mater. 2022, 4, 121–128. [Google Scholar] [CrossRef]
  24. Yang, J.; Wang, H.; Jiang, L.; Yu, H.; Zhao, Y.; Chen, H.; Yuan, X.; Liang, J.; Li, H.; Wu, Z. Defective polymeric carbon nitride: Fabrications, photocatalytic applications and perspectives. Chem. Eng. J. 2022, 427, 130991. [Google Scholar] [CrossRef]
  25. Alaghmandfard, A.; Ghandi, K. A Comprehensive Review of Graphitic Carbon Nitride (g-C3N4)–Metal Oxide-Based Nanocomposites: Potential for Photocatalysis and Sensing. Nanomaterials 2022, 12, 294. [Google Scholar] [CrossRef]
  26. Khezami, L.; Aissa, M.A.B.; Modwi, A.; Ismail, M.; Guesmi, A.; Algethami, F.K.; Ticha, M.B.; Assadi, A.A.; Nguyen-Tri, P. Harmonizing the photocatalytic activity of g-C3N4 nanosheets by ZrO2 stuffing: From fabrication to experimental study for the wastewater treatment. Biochem. Eng. J. 2022, 182, 108411. [Google Scholar] [CrossRef]
  27. Fernandes, E.; Drosopoulou, S.; Mazierski, P.; Miodyńska, M.; Gołaszewska, D.; Zaleska-Medynska, A.; Martins, R.C.; Gomes, J. Carbon nitride photoactivation evaluation and degradation of a mixture of parabens by ozone assistance. J. Water Process Eng. 2022, 49, 103018. [Google Scholar] [CrossRef]
  28. Falletta, E.; Longhi, M.; Di Michele, A.; Boffito, D.C.; Bianchi, C.L. Floatable graphitic carbon nitride/alginate beads for the photodegradation of organic pollutants under solar light irradiation. J. Clean. Prod. 2022, 371, 133641. [Google Scholar] [CrossRef]
  29. Wang, T.; Huang, M.; Liu, X.; Zhang, Z.; Liu, Y.; Tang, W.; Bao, S.; Fang, T. Facile one-step hydrothermal synthesis of α-Fe2O3/gC3N4 composites for the synergistic adsorption and photodegradation of dyes. RSC Adv. 2019, 9, 29109–29119. [Google Scholar] [CrossRef]
  30. Liu, G.; Qiao, X.; Gondal, M.; Liu, Y.; Shen, K.; Xu, Q. Comparative study of pure g-C3N4 and sulfur-doped g-C3N4 catalyst performance in photo-degradation of persistent pollutant under visible light. J. Nanosci. Nanotechnol. 2018, 18, 4142–4154. [Google Scholar] [CrossRef]
  31. Wang, A.; Wang, C.; Fu, L.; Wong-Ng, W.; Lan, Y. Recent advances of graphitic carbon nitride-based structures and applications in catalyst, sensing, imaging, and LEDs. Nano-Micro Lett. 2017, 9, 47. [Google Scholar] [CrossRef]
  32. Dong, J.; Zhang, Y.; Hussain, M.I.; Zhou, W.; Chen, Y.; Wang, L.-N. g-C3N4: Properties, Pore Modifications, and Photocatalytic Applications. Nanomaterials 2021, 12, 121. [Google Scholar] [CrossRef]
  33. Modwi, A.; Khezami, L.; Ghoniem, M.; Nguyen-Tri, P.; Baaloudj, O.; Guesmi, A.; AlGethami, F.; Amer, M.; Assadi, A. Superior removal of dyes by mesoporous MgO/g-C3N4 fabricated through ultrasound method: Adsorption mechanism and process modeling. Environ. Res. 2022, 205, 112543. [Google Scholar] [CrossRef]
  34. Toghan, A.; Abd El-Lateef, H.M.; Taha, K.K.; Modwi, A. Mesoporous TiO2@g-C3N4 composite: Construction, characterization, and boosting indigo carmine dye destruction. Diam. Relat. Mater. 2021, 118, 108491. [Google Scholar] [CrossRef]
  35. Modwi, A.; Ismail, M.; Idriss, H.; Aissa, M.; Khezami, L.; Bououdina, M. Efficient Removal of Cd (II) from Aquatic Media by Heteronanostructure MgO@TiO2@g-C3N4. J. Nanomater. 2022, 2022, 1458442. [Google Scholar] [CrossRef]
  36. Mirhosseini, H.; Shamspur, T.; Mostafavi, A. Novel adsorbent g-C3N4/ZnV2O4 for efficient removal of crystal violet dye: Removal process optimization, adsorption isotherms, and kinetic modeling. Appl. Organomet. Chem. 2022, 36, e6867. [Google Scholar] [CrossRef]
  37. Wei, S.; Kamali, A.R. Waste plastic derived Co3Fe7/CoFe2O4@carbon magnetic nanostructures for efficient dye adsorption. J. Alloys Compd. 2021, 886, 161201. [Google Scholar] [CrossRef]
  38. Wei, S.; Kamali, A.R. Trifunctional mesoporous magnetic adsorbent-photocatalyst nanocomposite for efficient removal of potassium ethyl xanthate from mining wastewater. J. Water Process Eng. 2022, 49, 103067. [Google Scholar] [CrossRef]
  39. Modwi, A.; Idriss, H.; Khezami, L.; Albadri, A.; Ismail, M.; Assadi, A.A.; Nguyen-Tri, P. Ba2+ removal from aquatic medium via TiY2O5@g-C3N4 nanocomposites. Diam. Relat. Mater. 2023, 135, 109830. [Google Scholar] [CrossRef]
  40. Zang, Y.-N.; Yang, S.-S.; Ding, J.; Zhao, S.-Y.; Chen, C.-X.; He, L.; Ren, N.-Q. A biochar-promoted V2O5/gC3N4 Z-Scheme heterostructure for enhanced simulated solar light-driven photocatalytic activity. RSC Adv. 2021, 11, 15106–15117. [Google Scholar] [CrossRef]
  41. Sajid, M.M.; Shad, N.A.; Javed, Y.; Khan, S.B.; Zhang, Z.; Amin, N.; Zhai, H. Preparation and characterization of Vanadium pentoxide (V2O5) for photocatalytic degradation of monoazo and diazo dyes. Surf. Interfaces 2020, 19, 100502. [Google Scholar] [CrossRef]
  42. Ali, H.; Ismail, A. Honeycomb-like V2O5 based films: Synthesis, structural, thermal, and optical properties for environmental applications. J. Inorg. Organomet. Polym. Mater. 2022, 32, 3012–3029. [Google Scholar] [CrossRef]
  43. Chen, H.; Chen, L.; Meng, J.; Yang, Z.; Wu, J.; Rong, Y.; Deng, L.; Shi, Y. Synergistic effects in V3O7/V2O5 composite material for high capacity and long cycling life aqueous rechargeable zinc ion batteries. J. Power Sources 2020, 474, 228569. [Google Scholar] [CrossRef]
  44. Gao, Y.; Zhu, Y.; Lyu, L.; Zeng, Q.; Xing, X.; Hu, C. Electronic structure modulation of graphitic carbon nitride by oxygen doping for enhanced catalytic degradation of organic pollutants through peroxymonosulfate activation. Environ. Sci. Technol. 2018, 52, 14371–14380. [Google Scholar] [CrossRef]
  45. Wang, H.; Yuan, X.; Wu, Y.; Zeng, G.; Chen, X.; Leng, L.; Li, H. Synthesis and applications of novel graphitic carbon nitride/metal-organic frameworks mesoporous photocatalyst for dyes removal. Appl. Catal. B Environ. 2015, 174, 445–454. [Google Scholar] [CrossRef]
  46. Zhang, X.; Jia, X.; Duan, P.; Xia, R.; Zhang, N.; Cheng, B.; Wang, Z.; Zhang, Y. V2O5/Pg-C3N4 Z-scheme enhanced heterogeneous photocatalytic removal of methyl orange from water under visible light irradiation. Colloids Surf. A Physicochem. Eng. Asp. 2021, 608, 125580. [Google Scholar] [CrossRef]
  47. Khezami, L.; Aissa, M.A.B.; Modwi, A.; Guesmi, A.; Algethami, F.K.; Bououdina, M. Efficient removal of organic dyes by Cr-doped ZnO nanoparticles. Biomass Convers. Biorefinery 2022, 1–14. [Google Scholar] [CrossRef]
  48. Ghoniem, M.G.; Ali, F.A.M.; Abdulkhair, B.Y.; Elamin, M.R.A.; Alqahtani, A.M.; Rahali, S.; Ben Aissa, M.A. Highly selective removal of cationic dyes from wastewater by MgO nanorods. Nanomaterials 2022, 12, 1023. [Google Scholar] [CrossRef]
  49. Wathukarage, A.; Herath, I.; Iqbal, M.; Vithanage, M. Mechanistic understanding of crystal violet dye sorption by woody biochar: Implications for wastewater treatment. Environ. Geochem. Health 2019, 41, 1647–1661. [Google Scholar] [CrossRef]
  50. Kalam, S.; Abu-Khamsin, S.A.; Kamal, M.S.; Patil, S. Surfactant adsorption isotherms: A review. ACS Omega 2021, 6, 32342–32348. [Google Scholar] [CrossRef]
  51. Al-Ghouti, M.A.; Razavi, M.M. Water reuse: Brackish water desalination using Prosopis juliflora. Environ. Technol. Innov. 2020, 17, 100614. [Google Scholar] [CrossRef]
  52. Ayawei, N.; Ebelegi, A.N.; Wankasi, D. Modelling and interpretation of adsorption isotherms. J. Chem. 2017, 2017, 3039817. [Google Scholar] [CrossRef]
  53. Homagai, P.L.; Poudel, R.; Poudel, S.; Bhattarai, A. Adsorption and removal of crystal violet dye from aqueous solution by modified rice husk. Heliyon 2022, 8, e09261. [Google Scholar] [CrossRef] [PubMed]
  54. Yadav, A.; Bagotia, N.; Yadav, S.; Sharma, N.; Sharma, A.K.; Kumar, S. Environmental application of Saccharum munja biomass-derived hybrid composite for the simultaneous removal of cationic and anionic dyes and remediation of dye polluted water: A step towards pilot-scale studies. Colloids Surf. A Physicochem. Eng. Asp. 2022, 650, 129539. [Google Scholar] [CrossRef]
  55. Quansah, J.O.; Hlaing, T.; Lyonga, F.N.; Kyi, P.P.; Hong, S.-H.; Lee, C.-G.; Park, S.-J. Nascent rice husk as an adsorbent for removing cationic dyes from textile wastewater. Appl. Sci. 2020, 10, 3437. [Google Scholar] [CrossRef]
  56. El Naeem, G.A.; Abd-Elhamid, A.; Farahat, O.O.; El-Bardan, A.A.; Soliman, H.M.; Nayl, A. Adsorption of crystal violet and methylene blue dyes using a cellulose-based adsorbent from sugercane bagasse: Characterization, kinetic and isotherm studies. J. Mater. Res. Technol. 2022, 19, 3241–3254. [Google Scholar]
  57. Adenan, N.H.; Lim, Y.Y.; Ting, A.S.Y. Nocardiopsis sp. for the removal of triphenylmethane dyes: Decolorization and optimization studies. Water Air Soil Pollut. 2021, 232, 414. [Google Scholar] [CrossRef]
  58. Mashkoor, F.; Nasar, A. Facile synthesis of polypyrrole decorated chitosan-based magsorbent: Characterizations, performance, and applications in removing cationic and anionic dyes from aqueous medium. Int. J. Biol. Macromol. 2020, 161, 88–100. [Google Scholar] [CrossRef]
  59. Mahmoud, M.E.; Amira, M.F.; Seleim, S.M.; Nabil, G.M.; Abouelanwar, M.E. Multifunctionalized graphene oxide@nanopolyaniline@zirconium silicate nanocomposite for rapid microwable removal of dyes. J. Nanostruct. Chem. 2021, 11, 645–662. [Google Scholar] [CrossRef]
  60. Nasiri, J.; Motamedi, E.; Naghavi, M.R.; Ghafoori, M. Removal of crystal violet from water using β-cyclodextrin functionalized biogenic zero-valent iron nanoadsorbents synthesized via aqueous root extracts of Ferula persica. J. Hazard. Mater. 2019, 367, 325–338. [Google Scholar] [CrossRef]
  61. Lagergren, S.K. About the theory of so-called adsorption of soluble substances. Sven. Vetenskapsakad. Handingarl 1898, 24, 1–39. [Google Scholar]
  62. Chien, S.; Clayton, W. Application of Elovich equation to the kinetics of phosphate release and sorption in soils. Soil Sci. Soc. Am. J. 1980, 44, 265–268. [Google Scholar] [CrossRef]
  63. Alatalo, S.-M.; Mäkilä, E.; Repo, E.; Heinonen, M.; Salonen, J.; Kukk, E.; Sillanpää, M.; Titirici, M.-M. Meso-and microporous soft templated hydrothermal carbons for dye removal from water. Green Chem. 2016, 18, 1137–1146. [Google Scholar] [CrossRef]
  64. Cheng, J.; Zhan, C.; Wu, J.; Cui, Z.; Si, J.; Wang, Q.; Peng, X.; Turng, L.-S. Highly efficient removal of methylene blue dye from an aqueous solution using cellulose acetate nanofibrous membranes modified by polydopamine. ACS Omega 2020, 5, 5389–5400. [Google Scholar] [CrossRef] [PubMed]
  65. Liu, D.; Gu, W.; Zhou, L.; Wang, L.; Zhang, J.; Liu, Y.; Lei, J. Recent advances in MOF-derived carbon-based nanomaterials for environmental applications in adsorption and catalytic degradation. Chem. Eng. J. 2022, 427, 131503. [Google Scholar] [CrossRef]
  66. Sun, W.; Liu, T.; Xia, K.; Zhou, J.; Liu, X.; Zhang, X. Preparation of Adsorbent Based on Polyacrylate Latex Solid Waste and Its Application in the Treatment of Dye Wastewater. ACS Omega 2022, 7, 13243–13253. [Google Scholar] [CrossRef]
  67. Gupta, K.; Khatri, O.P. Reduced graphene oxide as an effective adsorbent for removal of malachite green dye: Plausible adsorption pathways. J. Colloid Interface Sci. 2017, 501, 11–21. [Google Scholar] [CrossRef]
  68. Ali, M.; Modwi, A.; Idriss, H.; Aldaghri, O.; Ismail, M.; Ibnaouf, K. Detoxification of Pb (II) from aquatic media via CaMgO2@g-C3N4 nanocomposite. Mater. Lett. 2022, 322, 132501. [Google Scholar] [CrossRef]
Inorganics 11 00146 g001 550
Figure 1. (a) TEM image, (b) SEM image, (c) EDX, and (d–g) elemental mapping of the V2O5-g-C3N4 nanosorbent.
Figure 1. (a) TEM image, (b) SEM image, (c) EDX, and (d–g) elemental mapping of the V2O5-g-C3N4 nanosorbent.
Inorganics 11 00146 g001
Inorganics 11 00146 g002 550
Figure 2. (a) XRD patterns of V2O5-g-C3N4, V2O5, and g-C3N4, (b) nitrogen adsorption–desorption isotherm, (c) pore size distribution, and (d) plot for the determination of pHZPC for the V2O5-g-C3N4 nanosorbent.
Figure 2. (a) XRD patterns of V2O5-g-C3N4, V2O5, and g-C3N4, (b) nitrogen adsorption–desorption isotherm, (c) pore size distribution, and (d) plot for the determination of pHZPC for the V2O5-g-C3N4 nanosorbent.
Inorganics 11 00146 g002
Inorganics 11 00146 g003 550
Figure 3. (a) XPS spectrum of the V2O5-g-C3N4 nanosorbent, and XPS spectra survey of (b) C 1s, (c) N 1s, (d) O1s and (e) V 2p3/2 for the V2O5-g-C3N4 nanosorbent.
Figure 3. (a) XPS spectrum of the V2O5-g-C3N4 nanosorbent, and XPS spectra survey of (b) C 1s, (c) N 1s, (d) O1s and (e) V 2p3/2 for the V2O5-g-C3N4 nanosorbent.
Inorganics 11 00146 g003
Inorganics 11 00146 g004 550
Figure 4. (a) UV−Vis curves for various organic dye solutions before and after adsorption, (b) adsorption ability, (c) pH effect, and (d) concentration impact on CV removal by the V2O5-g-C3N4 nanocomposite.
Figure 4. (a) UV−Vis curves for various organic dye solutions before and after adsorption, (b) adsorption ability, (c) pH effect, and (d) concentration impact on CV removal by the V2O5-g-C3N4 nanocomposite.
Inorganics 11 00146 g004
Inorganics 11 00146 g005 550
Figure 5. (a) Adsorption isotherms modeling, (b) contact time effect, (c) adsorption kinetics modeling, and (d) intraparticle diffusion of CV adsorption onto the V2O5-g-C3N4 nanocomposite.
Figure 5. (a) Adsorption isotherms modeling, (b) contact time effect, (c) adsorption kinetics modeling, and (d) intraparticle diffusion of CV adsorption onto the V2O5-g-C3N4 nanocomposite.
Inorganics 11 00146 g005
Inorganics 11 00146 g006 550
Figure 6. (a) FTIR spectra of CV@V2O5-g-C3N4 and (b) proposed adsorption mechanism of CV onto V2O5-g-C3N4.
Figure 6. (a) FTIR spectra of CV@V2O5-g-C3N4 and (b) proposed adsorption mechanism of CV onto V2O5-g-C3N4.
Inorganics 11 00146 g006
Inorganics 11 00146 g007 550
Figure 7. Reusability efficiency of the V2O5-g-C3N4 nanocomposite.
Figure 7. Reusability efficiency of the V2O5-g-C3N4 nanocomposite.
Inorganics 11 00146 g007
Table
Table 1. Equilibrium isotherm constants models for CV dye adsorption by the V2O5-g-C3N4 nanosorbent.
Table 1. Equilibrium isotherm constants models for CV dye adsorption by the V2O5-g-C3N4 nanosorbent.
Equilibrium ModelNon-Linear FormParametersValues
Langmuir [51] q e = q m a x K L   C e 1 + K L   C e qm (mg g−1)664.65
KL (mg g−1)0.058
RL (L. mg−1)0.08
R20.995
Freundlich [52] q e = k F C e 1 / 2 n2.33
KF (L. mg−1)73.25
R20.974
Table
Table 2. Observation of CV adsorption capacities of the V2O5-g-C3N4 nanocomposite with the different nanomaterials’ adsorbents.
Table 2. Observation of CV adsorption capacities of the V2O5-g-C3N4 nanocomposite with the different nanomaterials’ adsorbents.
Adsorbents qe (mg g−1)pHReferences
Xanthated Rice husks90.0210[53]
Saccharum munja biomass-functionalized carbon nanotubes180.517[54]
Nascent Rice Husk24.4710[55]
Cellulose based on sugarcane107.508–13[56]
Nocardiopsis sp15.907[57]
MChs-Ppy11.848[58]
GO@NPANI@ZrSiO415.817[59]
Fe noparticles/βCD1009[60]
V2O5-g-C3N4 nanocomposite664.657This paper
Table
Table 3. Kinetics models for CV adsorption by the V2O5-g-C3N4 nanocomposite.
Table 3. Kinetics models for CV adsorption by the V2O5-g-C3N4 nanocomposite.
Kinetics ModelsEquationsParametersValues
PFO [61] q t = – ( 1 − e − 1 k 1 t )     qe (mg g−1)242.71
k1 (min−1)0.95
R20.606
PSO [61] q t = t   k 2 q e 2 k 2 q e t + 1     qe(calculated) (mg g−1)244.69
qe(experimental) (mg g−1)
k2 (g mg−1·min−1)0.018
R20.932
IPD [62] q t = k d i f t + C     C1 (mg g−1)223.53
Kdif1 (mg g−1 min1/2)3.77
R20.983
C2 (mg g−1)244.35
Kdif2 (mg g−1 min1/2)0.02
R20.908
Disclaimer/Publisher’s Note: The statements, opinions and data contained in all publications are solely those of the individual author(s) and contributor(s) and not of MDPI and/or the editor(s). MDPI and/or the editor(s) disclaim responsibility for any injury to people or property resulting from any ideas, methods, instructions or products referred to in the content.

Share and Cite

MDPI and ACS Style

Ben Aissa, M.A.; Modwi, A.; Albadri, A.E.A.E.; Saleh, S.M. Dependency of Crystal Violet Dye Removal Behaviors onto Mesoporous V2O5-g-C3N4 Constructed by Simplistic Ultrasonic Method. Inorganics 2023, 11, 146. https://doi.org/10.3390/inorganics11040146

AMA Style

Ben Aissa MA, Modwi A, Albadri AEAE, Saleh SM. Dependency of Crystal Violet Dye Removal Behaviors onto Mesoporous V2O5-g-C3N4 Constructed by Simplistic Ultrasonic Method. Inorganics. 2023; 11(4):146. https://doi.org/10.3390/inorganics11040146

Chicago/Turabian Style

Ben Aissa, Mohamed Ali, Abueliz Modwi, Abuzar E. A. E. Albadri, and Sayed M. Saleh. 2023. "Dependency of Crystal Violet Dye Removal Behaviors onto Mesoporous V2O5-g-C3N4 Constructed by Simplistic Ultrasonic Method" Inorganics 11, no. 4: 146. https://doi.org/10.3390/inorganics11040146

Note that from the first issue of 2016, this journal uses article numbers instead of page numbers. See further details here.

Article Metrics

Back to TopTop