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Article

Equilibrium and Kinetic Study of Anionic and Cationic Pollutants Remediation by Limestone–Chitosan–Alginate Nanocomposite from Aqueous Solution

by
Inas A. Ahmed
1,
Ahmed H. Ragab
1,*,
Mohamed A. Habila
2,
Taghrid S. Alomar
3,* and
Enas H. Aljuhani
4
1
Department of Chemistry, Faculty of Science, King Khalid University, Abha 62224, Saudi Arabia
2
Chemistry Department, College of Science, King Saud University, Riyadh 11451, Saudi Arabia
3
Department of Chemistry, College of Science, Princess Nourah Bint Abdulrahman University, Riyadh 11671, Saudi Arabia
4
Department of Chemistry, Collage of Applied Science, Umm Al-Qura University, Mecca 21955, Saudi Arabia
*
Authors to whom correspondence should be addressed.
Molecules 2021, 26(9), 2586; https://doi.org/10.3390/molecules26092586
Submission received: 23 March 2021 / Revised: 18 April 2021 / Accepted: 20 April 2021 / Published: 29 April 2021
(This article belongs to the Special Issue Bioproduct Production from Biomass and Residual Resources)
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Abstract

:
In this work, low-cost and readily available limestone was converted into nanolimestone chitosan and mixed with alginate powder and precipitate to form a triple nanocomposite, namely limestone—chitosan–alginate (NLS/Cs/Alg.), which was used as an adsorbent for the removal of brilliant green (BG) and Congo red (CR) dyes in aqueous solutions. The adsorption studies were conducted under varying parameters, including contact time, temperature, concentration, and pH. The NLS/Cs/Alg. was characterized by SEM, FTIR, BET, and TEM techniques. The SEM images revealed that the NLS/Cs/Alg. surface structure had interconnected pores, which could easily trap the pollutants. The BET analysis established the surface area to be 20.45 m2/g. The recorded maximum experimental adsorption capacities were 2250 and 2020 mg/g for CR and BG, respectively. The adsorption processes had a good fit to the kinetic pseudo second order, which suggests that the removal mechanism was controlled by physical adsorption. The CR and BG equilibrium data had a good fit for the Freundlich isotherm, suggesting that adsorption processes occurred on the heterogeneous surface with a multilayer formation on the NLS/Cs/Alg. at equilibrium. The enthalpy change (ΔH0) was 37.7 KJ mol−1 for CR and 8.71 KJ mol−1 for BG, while the entropy change (ΔS0) was 89.1 J K−1 mol−1 for CR and 79.1 J K−1 mol−1 BG, indicating that the adsorption process was endothermic and spontaneous in nature.

1. Introduction

In recent decades, rapid industrialization and urbanization have caused a disturbing global increase in water pollution. Removing dyed water is an absolutely crucial matter. Among many substances that pollute lakes and rivers, those of unnatural texture are very common [1]. About 1.0 × 105 synthetic dyes and pigments, and more than 7.0 × 105 tons of them, are consumed by industry annually [2]. Incomplete dying results in the discharge of polluted wastewater that can contaminate groundwater and surface water resources. Approximately 15% of organic dyes are released into the environment, causing environmental pollution [3]. The toxicity of effluents from textile industries is characterized by multiple variations in BOD, turbidity, color, COD, pH, odor, and salinity [4]. Azo dyes, such as Congo red, are highly toxic, carcinogenic, and mutagenic. They are hazardous to the respiratory system because of their vapor, and they are dangerous in cases of skin contact, eye contact, and swallowing [5,6,7,8,9,10]. During their degradation, carbon dioxide, nitrogen oxide, and sulfur oxides may form. Therefore, there is an urgent need to separate these dyes from wastewater [11,12,13,14,15,16,17].
Due to the potential toxicity of dyes in natural water ecosystems, the presence of dyes in surface water and groundwater represents a serious problem. The most recommended and applied technique to remove toxic dye is adsorption. Some cost-effective organic and inorganic adsorbents include peat [18], grapefruit peel [19], rice husks [20], peanut husks [21], banana peel [22], wood apple shells [23], orange peel [24], and mushroom waste [25]. Carbon [26] and polymers [27,28] are also used.
In this study, we made an environmentally friendly nanocomposite from sedimentary solid rock for the efficient removal of Congo red (CR) and brilliant green (BG) dyes from contaminated water. The limestone–chitosan–alginate (NLS/Cs/Alg.) nanocomposite adsorption capacity was examined using many techniques. The authors sought to quantify the effects of pH, dye concentration, and adsorbent dose on contact time. Sorption models were used to study the adsorption mechanism and the reaction order. The enthalpy, the Gibbs free energy, and the entropy of reaction were studied.

2. Results and Discussion

2.1. Structural and Surface Characterization of the Adsorbent

In order to identify different functional groups on the surface of the sorbent responsible for the binding of CR and BG dyes, FTIR spectral analysis was necessary. In Figure 1a, the band at 3449 cm−1 may be related to the (OH) groups present in the alginate, while the band at 1420 cm−1 may be due to the calcium ions in the nanocompound. The FTIR spectrum of the CR or BG with the NLS/Cs/Alg. nanocomposite showed some interesting features. In Figure 1b, a feature at 1799 cm−1 could be linked to the amide group stretching vibrations, while a more complex feature observed at 3499 cm−1 was due to -NH2 groups [29]. In Figure 1c, the key features here are a UV absorption band at around 1614 cm−1, probably due to the oxime group present in the brilliant green dye, and stretching bands at 874 cm−1 may be due to SO3− groups [30].

2.1.1. SEM Study

SEM images revealed that the adsorbent’s surface morphology had unique characteristics. Figure 2A–C shows examples of SEM images of CR and BG dyed on the NLS/Cs/Alg. polymers. The nanocomposites had varied surface shapes (before and after dye adsorption). The SEM images showed that before adsorption, the nanocomposite surface was rough and made of holes and small openings, whereas, after adsorption, a well-distributed pore structure was supported by high porosity and a large number of open pores [31].

2.1.2. TEM Study

Figure 3 illustrates the properties of the NLS/Cs and the NLS/Cs/Alg. nanocomposite. The TEM micrograph reveals that the constructed NLS/Cs/Alg. showed a multilayer structure with a crystal size of ≈8 nm. The elements of the NLS composite were spherical and sparsely distributed with spherical crystals of ≈13 nm on the particle surfaces, as shown in figure. This irregular surface indicates that nucleation occurred when the NLS was dropped onto the alginate. In other words, the film covering the particles nucleated on the alginate [32].

2.2. Effect of pH

In order to evaluate the effects of pH in the sorption of CR and BG dyes, the tests were carried out in the pH range of 3.0 to 9.0, and 12 mg·L of each dye and 0.02 g·L of NLS/Cs/Alg. nanocomposite were added to a conical flask with stirring for 90 min. The variation of the adsorption capacity of the nanocomposite with pH is shown in Figure 4A. The surface of the nanolimestone was slightly negatively charged according to the zeta potential measurements [33].
The pH optimum for Congo red was pH 6.5~7. The removal efficiency of the chitosan/alginate was significantly higher at pH 6.5 due to the protonation of the -NH2 groups of chitosan to produce positively charged -NH3+ groups of alginates at a lower pH, which would be suitable for anionic dyes such as CR, while the maximum uptake for BG was observed at pH 8. This could be explained by the fact that below the point zero of charge pH PZC value of 7.3 the surface of the NLS/Cs/Alg. was protonated and changed; thus, it became more positively charged and also the functional sites that were mainly carbonates (CO32−) were converted to (HCO3−). This implies that the positively charged surface enhanced the repulsive forces between the NLS/Cs/Alg. surface and the BG dye. Therefore, the electrostatic attraction between the (HCO3−) active sites and the BG dye was minimal and resulted in low removal. However, increasing the pH of the solution resulted in the surface of the NLS/Cs/Alg. being progressively deprotonated and negatively charged, leading to enhanced electrostatic interactions between the active sites and the BG dye and to higher adsorption [11,34].

2.3. Effect of Contact Time

The variation of the amount of adsorbed dye as a function of time is a significant feature of this experiment because it indicates how fast the adsorption is, from 5 to 90 min. The variation of the adsorption capacity of the nanocomposite with time is shown in Figure 4B. The experiments were carried out in a solution of pH 6.5 with 260 mg·L−1 of CR dye, and of pH 8 with 140 mg·L−1 of BG dye, along with 0.1 g·L−1 of NLS/Cs/Alg. nanocomposite. Due to fast adsorption kinetics, the adsorption was initially very rapid and subsequently slow in the later stages. This effect was presumed to be due to the electrostatic effect. If adsorption is slower, it is because the number of adsorption sites decreases. Equilibrium was established for the CR and BG dye concentrations in 60 min.

2.4. Sorption Model

Different kinetic models can be used for studying the adsorption phenomenon, and fitting the experimental data with the models permitted the elucidation of the adsorption mechanism. The kinetics parameters for the sorption of CR and BG dyes on the NLS/Cs/Alg. nanocomposite are represented in Table 1. Generally speaking, there are three steps in an adsorption process: (i) Film diffusion, which is the external mass transfer of the adsorbate from the bulk solution to the external surface of the adsorbent; (ii) pore diffusion or intraparticle diffusion, which is the transport of adsorbate particles from the external surface into the pores of the adsorbent medium; and (iii) the sorption itself, i.e., the surface reaction to attach the adsorbate particles to the internal surface of the sorbent [35,36]. The adsorption of solute from a solution into a sorbent involves the mass transfer of adsorbate (film diffusion), surface diffusion, and pore diffusion. Film diffusion is an independent step, whereas surface and pore diffusion may occur simultaneously. The intraparticle diffusion equation (Equation (1)) represented in Figure 6A, as described by Weber and Morris [37], may be applied in the determination of the intraparticle diffusion rate constant, kd, and the boundary resistance, C:
qt = kd (t0.5) + C,
where qt is the amount of adsorbate adsorbed onto the adsorbent at time t (mg/g), kd is the rate constant (mg/g)min0.5, and C determines the boundary layer effect (i.e., the higher the value, the larger the film diffusion resistance) and is linked to external mass transfer [38]. Using the plot of qt versus t0.5, it is possible to determine kd and C. When intraparticle diffusion alone is the rate-limiting step, then the plot of qt versus t0.5 passes through the origin (C = 0). When film diffusion also takes place then the intercept is C > 0, which gives an idea of the thickness of the boundary layer [38]: The larger the intercept, the greater the boundary layer effect, i.e., the film resistance to mass transfer surrounding the adsorbent is greater [39]. The value of the rate constant for the intraparticle diffusion, kd, was evaluated as 10.6 (g/g·min−1) and 11.1 for the CR and BG dyes, respectively, giving an indication of the mobility of the dyes toward the composite.
Generally speaking, the faster the adsorption of ions, the higher the probability of a layer of ions being formed on the adsorbent surface (boundary layer on the membrane surface) [40]. Kinetic models are divided into two main categories, according to the rate-limiting step in the adsorption process: Some models are based on the fact that the sorption is the rate-limiting step (adsorption reaction models) and these are usually suitable to explain chemisorption; others suppose that the diffusion is the rate-limiting step (adsorption diffusion models) and these are well suited to physisorption processes [33]. Pseudo-first-order (PFO) or pseudo-second-order (PSO) and intraparticle (IP) models are some examples of adsorption reaction models and diffusion reaction models, respectively. In order to study adsorption kinetics, the linear forms are applied and the suitability of any model depends on the degree of linear correlation between the experimental and the predicted values (R2) [36]. The PFO and PSO models rest on the main assumption that adsorption only occurs at localized sites and involves no interaction between the adsorbed ions [40]. According to these models, the process rate depends on the availability of adsorption sites on the surface of the adsorbent rather than on the adsorbate concentration in the bulk solution [41]. Also known as the Lagergren model [42], PFO describes the adsorption of solute onto the adsorbent following the first order mechanism. The linear expression of PFO is reported in Equation (2) and represented in Figure 6B:
Log (qe − q) − log qe = −Kads·t/2.303,
where qe is the amount of dye adsorbed at equilibrium (mg·g−1) and Kads is the first-order rate constant for dye adsorption onto the sorbent (min−1). In recent years, the pseudo-second-order rate expression has been widely applied to the adsorption of pollutants from aqueous solutions in order to describe chemisorption involving covalent forces and ion exchange between the adsorbent and the adsorbate [41].
The linear expression of PSO is reported in Equation (2) and represented in Figure 5C. The value of k is determined by plotting:
t/qt = 1/k2qe2 + t/qe,
where k2 is the rate constant of the second-order adsorption (g mg−1 min−1). Similarly, the slope of the plot of t/qt as a function of t was used to determine the second-order rate constant k2.
In order to understand the adsorption kinetics, the order of the adsorption process was ascertained by fitting the experimental data into the pseudo-first-order and pseudo-second-order equations. The equilibrium adsorption capacity (qt) toward the CR and BG dyes was calculated by UV–Vis spectroscopy at different time intervals (t) taking 260 and 140 mg·L−1 of CR and BG dye, respectively, as well as 0.1 g·L−1 of NLS/Cs/Alg. nanocomposite. With increasing times (t = 2, 6, 8, 15, and 70 min), the obtained values of qt are plotted in Table 1. The best fitting was obtained for CR (R2 = 0.968) and BG (R2 = 0.993) for pseudo-second-order adsorption.
The Bangham equation was used to investigate the amount of BG dye that can be introduced into the pores of the nanocomposite [42]:
Log log [Ci/(Ci − q m)] = log (Ko m/2.303 V) + α log t,
where Ko is the proportionality constant and α is the Bangham equation constant. Kinetics parameters for the sorption of CR and BG dyes on the NLS/Cs/Alg. nanocomposite are shown in Table 1. These results showed that the diffusion of dye into composite pores played a role in the adsorption process [43]. The value of α constant indicated that the sorption of dye was favored to be less than 1.

2.5. Isotherm Models

2.5.1. Langmuir Isotherm

In order to model the equilibrium data of the composite and different concentrations of CR and BG dyes, a concentration of 0.1 g/L was applied for the application of the isotherm and thermodynamic models. The Langmuir model was proposed for describing the surface of the composite material, as seen in the following equation [44]:
Ce/qe = 1/b Qmax + (1/Qmax) Ce,
where b is the monolayer adsorption capacity related to the sorption heat (L·mg−1) and Qmax is the maximum adsorption capacity (mg·g−1).

2.5.2. Freundlich Isotherm

The Freundlich expression is an empirical equation describing sorption to a heterogeneous surface [45]. The Freundlich adsorption is presented in Equation (6):
ln qe = ln Kf + 1/n ln Ce,
where Kf (mol1−n Ln g−1) represents the sorption capacity when the dye equilibrium concentration is equal to 1 and n represents the degree of dependence of sorption on the equilibrium concentration. Favorable adsorption was demonstrated by the fact that the value of n was greater than unity.

2.5.3. Dubinin–Radushkevich–Kanager Isotherm

The Dubinin–Radushkevich (D–R) isotherm is more general than the Langmuir isotherm. The model was successfully fit with the cohesive model of adsorption, which deals with the Gaussian energy of distribution. The D–R equation is expressed as follows [45]:
ln q = ln q(DR) − βε2 and
ε = RT ln (1 + 1/Ce),
where q(D-R) is the theoretical adsorption capacity (mg g−1), β is the activity coefficient related to mean sorption energy (mol2 kJ−2), ε is the Polanyi potential, R is the ideal gas constant (0.008314 KJ K−1 mol−1), and T is the absolute temperature (K). E (kJ mol−1) is defined as the free energy change required for transferring 1 mole of ions from solution to the solid surfaces, which equals:
E = 1/(2ß)1/2.
It is useful to analyze the kind of sorption reaction. Sorption is governed by chemical ion exchange if the value of E is in the range of 8–16 kJ mol−1. In this case, physical forces may affect sorption. Otherwise, molecular diffusion may be at the forefront as E > 16 kJ mol−1 [46].
Based on the D–R model simulation in Table 2, the E values were 7.9 and 7.4 kJ mol−1 for CR and BG, respectively, in the range of 8–16 kJ mol−1, which implies that adsorption can be either physical–chemical or physical.

2.6. Thermodynamic Parameters

The thermodynamic adsorption data of CR and BG dyes on the NLS/Cs/Alg. nanocomposite are represented in Table 3. In order to investigate the effect of temperature on the adsorption of CR and BG dyes on the NLS/Cs/Alg. nanocomposite, the distribution coefficient, Kd, (L·g−1) was calculated at temperatures of 288, 298, 313, and 333 K using Equation (10). The enthalpy and entropy change were calculated from the intercept and slope of the plot of log Kd against 1/T, respectively [47,48]:
ln Kd = −∆Ho/RT + ∆So/R.
The other thermodynamic parameter, Gibbs free energy (∆Go), was calculated by:
∆Go = −RT ln Kd,
where R is the universal gas constant (8.314 J mol−1 K−1) and T is the temperature (K).
The Kd value increased with increasing temperature. The heat of adsorption decreased with increasing temperature. From the dataset of the heat transfer, the enthalpy change (∆Ho) and the entropy change (∆So) can be calculated. The other thermodynamic parameter as ∆Go, can be evaluated by Equation (11). ∆Ho indicates that the adsorption of CR and BG dyes on the NLS/Cs/Alg. nanocomposite is endothermic. It showed that the adsorption of chromogenic dyes on the nanocomposite is a random reaction. Going forward, a negative value of ∆Go was displayed, which signified that the adsorption of dye is possible and thermodynamically spontaneous. These results are also in good agreement with the domain-reduction reaction of the D–R isotherm. The adsorption performance of CR and BG dyes onto different adsorbents is described in Table 4.

3. Experimental Methods

3.1. Primary Materials

The primary materials were crushed limestone, which was collected from stones in Mokkatam, Egypt, sodium alginate powder (C6H9NaO7), chitosan low molecular weight (LMW) (C6H11NO4)n (99% A.R grade), hydrochloric acid (HCl; 32%), sodium hydroxide (NaOH) pallets (98.5% A.R grade), and Congo red (C32H22N6Na2O6S2) and brilliant green (C27H34N2O4S) dyes (95% A.R grade). All chemicals were obtained from commercial sources (El-Gomhouria Co. For Trading Drugs, Chemicals & Medical Supplies, Egypt). No further purification was used.

3.2. Synthesis of Nanolimestone

The nanolimestone was made by mixing the crushed limestone with HCl acid. The aqueous solution of BaCl2 was mixed with 1.5 gm of chitosan LMW, which was dissolved in 3% acetic acid and then treated with triphenyl phosphate (TPP) and distilled. The mixture was heated to 90 °C and mixed with 70 g of sodium carbonate. The mixture was kept for 12 h; then it was filtered, washed with water, and finally calcined at 650 °C for 2 h [56].

3.3. Synthesis of Nanolimestone/Alginate Composite

Figure 6 shows a flowchart of the synthesis process for the NLS/Cs/Alg. nanocomposite. The triple nanocomposite was prepared by mixing 2% of w/v of alginate powder and 7% of the nanolimestone in 500 mL deionized water with stirring for 30 min at 80 °C for a homogenous solution. The mixture was then extruded from a prefabricated injector by controlling the opening of the control valve. Finally, the composite beads were immersed in CaCl2 solution for 12 h in order to achieve hardened beads. Distilled water was used for washing the beads many times to remove the excess unbounded CaCl2 from the adsorbent surface [12].

3.4. Structural and Surface Characterization of the NLS/Cs/Alg. Nanocomposite

3.4.1. Analytical Instruments

The final dried powder was crushed for characterization with a scanning electron microscope (SEM). The surface morphology of our adsorbent was analyzed using a electron probe microanalyzer (JXA-840A, JEOL, Tokoy, Japan) attached to an EDAX unit, with an accelerating voltage of 30 kV and a magnification of 10–400,000×. Transmission electron microscopy (JEM 2100, HRTEM, JEOL, Tokoy, Japan) was also used. The functional groups in the NLS/Cs/Alg. nanocomposite and the interfacial modification were analyzed by Fourier transform infrared spectroscopy (FTIR). The FTIR spectrometer was used at frequencies in the 4000–400 cm–1 range. The surface area was determined using BEL SORB-max (MICROTRAC, Tokoy, Japan,). To determine the parameters that had an influence on the adsorption process, measurements of the amounts of CR and BG remaining in the solution after adsorption at a wavelength 497 nm for CR and625 nm for BG were taken using an Visible Spectrophotometer (OPTIMA SP-300, Tokoy, Japan).

3.4.2. Dye Adsorption Studies

All batch experiments were carried out at room temperature (25 °C). The dye solutions with concentrations ranging from 10 to 500 mg L−1 were dropped by pipette into quick-fit-top bottles containing 0.01 g of NLS/Cs/Alg. nanocomposite sorbent in 100 mL of aqueous solution. The solution pH was measured at 6.5 for CR and 8 for BG—appropriate for most cases of adsorption. The authors tried to examine how long the adsorption process took to complete and so varied the time at fixed periods (1.0, 5.0, 10, 20, 30, 60, and 90 min). Hence, the present data showed that the CR and BG dyes adsorbed on the NLS/Cs/Alg. nanocomposite within a time of 30 to 60 min. The samples were filtered before being analyzed using a spectrophotometer. In the industrial sector, the filtrated adsorbent may be dried to examine its properties and be weighed again to identify whether some of it is lost during the filtration process and it can also be re-used. Changing the pH of the media would affect the attraction force between the charge of the nanocomposite surface and the dye, so the dye could easily be removed from the nanocomposite and the nanocomposite could be used again [57].

3.4.3. Experimental Data Analysis

The percentage adsorption of CR and BG dyes from the solution was calculated from the relationship as follows:
% R = (Ci − Cf )/Ci × 100 and
q = [(Ci − Cf)/m]·V.
The adsorption capacity, q, in mg/g and the removal percentage, %R, of the composite toward CR and BG were evaluated by Equations (1) and (2), where Ci and Cf are the initial and final concentrations of CR and BG in the solution in mg/L, (v) is the volume of the solution in ml, and m is the mass of the NLS/Cs/Alg. in g.

4. Conclusions

In this work, an experimental study on the utilization of an NLS/Cs/Alg. nanocomposite for the removal of Congo red and brilliant green dyes from an aqueous solution was carried out. The following conclusions were made based on the experimental results of the present study. The nanocomposite was characterized by Fourier transform infrared spectroscopy (FTIR), TEM, SEM, energy dispersive X-ray analysis (EDX), and Brunauer–Emmett–Teller BET methods. The potential of this adsorbent was studied for the decolonization of CR and BG; the influence of the initial pH, dye concentration, contact time, adsorbent dose, and temperature on the adsorption of CR and BG was investigated. The adsorption capacity of CR and BG increased with increasing initial dye concentration, while the optimized pH was found to be 7.2 for both. The kinetics of CR and BG removal indicated an optimum contact time of 60 min via a two-stage adsorption kinetic profile (initial fast and subsequent slow equilibrium). The CR and BG adsorption onto NLS/Cs/Alg. follows a pseudo-second-order kinetic model with a determination coefficient (R2) very close to unity (~0.983). This relies on the assumption that the chemisorption may be the rate-limiting step, as well as where the CR and BG ions are attached to the adsorbent surface by forming chemical bonds, tending to find sites that maximize their coordination number with the surface. The equilibrium adsorption data for BG on NLS/Cs/Alg. were analyzed by various models. The results indicate that the Langmuir isotherm provides the best correlation (Qmax ~3890 mg/g at 299 K for CR and ~3080 mg/g for BG). The negative free enthalpy, ΔG, and positive enthalpy, ΔH, indicated that the adsorption of CR and BG onto NLS/Cs/Alg. was spontaneous and endothermic over the studied temperature range. CR and BG were strongly bonded to the adsorbent surface, while the positive entropy, ΔS, stated clearly that the randomness increased at the solid–solution interface during dye adsorption, and that there was some structural exchange between the active sites and the dye ions. The comparison of the adsorption capacity of our adsorbent with others showed its attractive properties from both industrial and economic perspectives. This study produced encouraging results.

Author Contributions

I.A.A., A.H.R., M.A.H. and T.S.A. contributed to the methodology and writing of the paper. A.H.R. and E.H.A. were involved in the preparation of the reagents and materials and were responsible for handling the analysis tools. All authors have read and agreed to the published version of the manuscript.

Funding

The authors are grateful to the Deanship of Scientific Research at Princess Nourah bint Abdulrahman University through the Fast-track Research Funding Program.

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Data Availability Statement

Date of the compounds are available from the authors.

Acknowledgments

The authors are grateful to the Dean of Science and Research at King Khalid University for making financial support available. The authors are grateful to the Deanship of Scientific Research, King Saud University for funding through Vice Deanship of Scientific Research Chairs and funded by the Deanship of Scientific Research at Princess Nourah bint Abdulrahman University through the Fast-track Research Funding Program.

Conflicts of Interest

There is no conflict of interest for the authors to declare.

Sample Availability

Samples of the compounds are available from the authors.

References

  1. Islam, A.; Awual, R.; Angove, M.J. A Review on Nickel(II) Adsorption in Single and Binary Component Systems and Future Path; Science Publishing: New York, NY, USA, 2019; pp. 1–6. [Google Scholar]
  2. Almeida, E.J.R.; Corso, C.R. Decolorization and removal of toxicity of textile azo dyes using fungal biomass pelletized. Int. J. Environ. Sci. Technol. 2019, 16, 1319–1328. [Google Scholar] [CrossRef] [Green Version]
  3. Edison, T.N.J.I.; Atchudan, R.; Sethuraman, M.G.; Lee, Y.R. Reductive-degradation of carcinogenic azo dyes using Anacardium occidentale testa derived silver nanoparticles. J. Photochem. Photobiol. B 2016, 162, 604–610. [Google Scholar] [CrossRef]
  4. World Health Organization (Ed.) Global Water Supply and Sanitation Assessment; Report; World Health Organization: Geneva, Switzerland; UNICEF: New York, NY, USA, 2000. [Google Scholar]
  5. Saratale, R.G.; Saratale, G.D.; Chang, J.S.; Govindwar, S.P. Bacterial decolorization and degradation of azo dyes: A review. J. Taiwan Inst. Chem. Eng. 2011, 42, 138–157. [Google Scholar] [CrossRef]
  6. Yang, S.S.; Kang, J.H.; Xie, T.R.; He, L.; Xing, D.F.; Ren, N.Q.; Wu, W.M. Generation of high-efficient biochar for dye adsorption using frass of yellow mealworms (larvae of Tenebrio molitor Linnaeus) fed with wheat straw for insect biomass production. J. Clean. Prod. 2019, 227, 33–47. [Google Scholar] [CrossRef]
  7. De Campos Ventura-Camargo, B.; Marin-Morales, M.A. Azo dyes: Characterization and toxicity—A review. Text. Light Ind. Sci. Technol. 2013, 2, 85–103. [Google Scholar]
  8. Zhuang, M.; Sanganyado, E.; Xu, L.; Zhu, J.; Li, P.; Liu, W. High Throughput Sediment DNA Sequencing Reveals Azo Dye Degrading Bacteria Inhabit Nearshore Sediments. Microorganisms 2020, 8, 233. [Google Scholar] [CrossRef] [Green Version]
  9. Mishra, S.; Nayak, J.K.; Maiti, A. Bacteria-mediated bio-degradation of reactive azo dyes coupled with bio-energy generation from model wastewater. Clean Technol. Environ. Policy 2020, 22, 651–667. [Google Scholar] [CrossRef]
  10. Al-Tohamy, R.; Sun, J.; Fareed, M.F.; Kenawy, E.R.; Ali, S.S. Ecofriendly biodegradation of Reactive Black 5 by newly isolated Sterigmatomyces halophilus SSA1575, valued for textile azo dye wastewater processing and detoxification. Sci. Rep. 2020, 10, 1–16. [Google Scholar]
  11. Behera, S.S.; Das, S.; Parhi, P.K.; Tripathy, S.K.; Mohapatra, R.K.; Debata, M. Kinetics, thermodynamics and isotherm studies on adsorption of methyl orange from aqueous solution using ion exchange resin Amberlite IRA400. Desalination Water Treat. 2017, 60, 249–260. [Google Scholar] [CrossRef]
  12. Kumar, R.; Ansari, M.O.; Barakat, M.A. Adsorption of brilliant green by surfactant doped polyaniline/MWCNTs composite: Evaluation of the kinetic, thermodynamic, and isotherm. Ind. Eng. Chem. Res. 2014, 53, 7167–7175. [Google Scholar] [CrossRef]
  13. Ghaedi, M.; Zeinali, N.; Ghaedi, A.M.; Teimuori, M.; Tashkhourian, J. Artificial neural network-genetic algorithm based optimization for the adsorption of methylene blue and brilliant green from aqueous solution by graphite oxide nanoparticle. Spectrochimica Acta Part A Mol. Biomol. Spectrosc. 2014, 125, 264–277. [Google Scholar] [CrossRef]
  14. Zhang, L.; Liu, X.; Guo, X.; Su, M.; Xu, T.; Song, X. Investigation on the degradation of brilliant green induced oxidation by NiFe2O4 under microwave irradiation. Chem. Eng. J. 2011, 173, 737–742. [Google Scholar] [CrossRef]
  15. Kismir, Y.; Aroguz, A.Z. Adsorption characteristics of the hazardous dye Brilliant Green on Saklıkent mud. Chem. Eng. J. 2011, 172, 199–206. [Google Scholar] [CrossRef]
  16. Rehman, R.; Muhammad, S.J.; Arshad, M. Brilliant green and acid orange 74 dyes removal from water by Pinus roxburghii leaves in naturally benign way: An application of green chemistry. J. Chem. 2019, 2019. [Google Scholar] [CrossRef] [Green Version]
  17. Zabłocka-Godlewska, E.; Przystaś, W. Fed-Batch Decolourization of Mixture of Brilliant Green and Evans Blue by Bacteria Species Applied as Pure and Mixed Cultures: Influence of Growth Conditions. WaterAirSoil Pollut. 2020, 231, 1–23. [Google Scholar] [CrossRef] [Green Version]
  18. Allen, S.J.; Mckay, G.; Porter, J.F. Adsorption isotherm models for basic dye adsorption by peat in single and binary component systems. J. Colloid Interface Sci. 2004, 280, 322–333. [Google Scholar] [CrossRef]
  19. Saeed, A.; Sharif, M.; Iqbal, M. Application potential of grapefruit peel as dye sorbent: Kinetics, equilibrium and mechanism of crystal violet adsorption. J. Hazard. Mater. 2010, 179, 564–572. [Google Scholar] [CrossRef]
  20. Han, R.; Ding, D.; Xu, Y.; Zou, W.; Wang, Y.; Li, Y.; Zou, L. Use of rice husk for the adsorption of Congo red from aqueous solution in column mode. Bioresour Technol. 2008, 99, 2938–2946. [Google Scholar] [CrossRef]
  21. Sadaf, S.; Bhatti, H.N. Batch and fxed bed column studies for the removal of Indosol Yellow BG dye by peanut husk. J. Taiwan Inst. Chem. Eng. 2008, 45, 541–553. [Google Scholar] [CrossRef]
  22. Munagapati, V.S.; Yarramuthi, V.; Kim, Y.; Lee, K.M.; Kim, D.S. Removal of anionic dyes (Reactive Black 5 and Congo Red) from aqueous solutions using Banana Peel Powder as an adsorbent. Ecotoxicol. Environ. Saf. 2018, 148, 601–607. [Google Scholar] [CrossRef]
  23. Jain, R.; Sikarwar, S. Removal of hazardous dye Congo red from waste material. J. Hazard. Mater. 2008, 152, 942–948. [Google Scholar] [CrossRef]
  24. Arami, M.; Limaee, N.Y.; Mahmoodi, N.M.; Tabrizi, N.S. Removal of dyes from colored textile wastewater by orange peel adsorbent: Equilibrium and kinetic studies. J. Colloid Interface Sci. 2005, 288, 371–376. [Google Scholar] [CrossRef] [PubMed]
  25. Alhujaily, A.; Yu, H.; Zhang, X.; Ma, F. Adsorptive removal of anionic dyes from aqueous solutions using spent mushroom waste. Appl. Water Sci. 2020, 10, 1–12. [Google Scholar] [CrossRef]
  26. Filice, S.; D’Angelo, D.; Scarangella, A.; Iannazzo, D.; Compagnini, G.; Scalese, S. Highly effective and reusable sulfonated pentablock copolymer nanocomposites for water purification applications. RSC Adv. 2017, 7, 45521–45534. [Google Scholar] [CrossRef] [Green Version]
  27. Scalese, S.; Nicotera, I.; D’Angelo, D.; Filice, S.; Libertino, S.; Simari, C.; Privitera, V. Cationic and anionic azo-dye removal from water by sulfonated graphene oxide nanosheets in Nafion membranes. New J. Chem. 2016, 40, 3654–3663. [Google Scholar] [CrossRef]
  28. Ragab, A.H.; Ahmed, I. Sorption of Cd (II) and Pb (II) ions by nanolimestone from underground water samples from Tehama region of Saudi Arabia. Indian J. Chem. Sect. A (IJCA) 2020, 59, 333–340. [Google Scholar]
  29. Pathania, D.; Sharma, A.; Siddiqi, Z.M. Removal of Congo red dye from aqueous system using Phoenix dactylifera seeds. J. Mol. Liq. 2016, 219, 359–367. [Google Scholar] [CrossRef]
  30. Popoola, L.T.; Aderibigbe, T.A.; Yusuff, A.S.; Munir, M.M. Brilliant green dye adsorption onto composite snail shell–rice husk: Adsorption isotherm, kinetic, mechanistic, and thermodynamics analysis. Environ. Qual. Manag. 2018, 28, 63–78. [Google Scholar] [CrossRef]
  31. Nallathambi, G.; Ramachandran, T.; Rajendran, V.; Palanivelu, R. Effect of silica nanoparticles and BTCA on physical properties of cotton fabrics. Mater. Res. 2011, 14, 552–559. [Google Scholar] [CrossRef] [Green Version]
  32. Wang, F.; Jiang, J.; Sun, F.; Sun, L.; Wang, T.; Liu, Y.; Li, M. Flexible wearable graphene/alginate composite non-woven fabric temperature sensor with high sensitivity and anti-interference. Cellulose 2020, 27, 2369–2380. [Google Scholar] [CrossRef]
  33. Chen, L.; Zhang, G.; Wang, L.; Wu, W.; Ge, J. Zeta potential of limestone in a large range of salinity. Colloids Surf. A Physicochem. Eng. Asp. 2014, 450, 1–8. [Google Scholar] [CrossRef]
  34. Nkutha, C.S.; Shooto, N.D.; Naidoo, E.B. Adsorption studies of methylene blue and lead ions from aqueous solution by using mesoporous coral limestones. South Afr. J. Chem. Eng. 2020, 34, 151–157. [Google Scholar] [CrossRef]
  35. Tan, K.L.; Hameed, B.H. Insight into the adsorption kinetics models for the removal of contaminants from aqueous solutions. J. Taiwan Inst. Chem. Eng. 2017, 74, 25–48. [Google Scholar] [CrossRef]
  36. Largittea, L.; Pasquierb, R. A review of the kinetics adsorption models and their application to the adsorption of Pb by an activated carbon. Chem. Eng. Res. Des. 2016, 109, 495–504. [Google Scholar] [CrossRef]
  37. Weber, W.J.; Morris, J.C. Kinetics of Adsorption on Carbon from Solutions. J. Sanit. Eng. Division Am. Soc. Civ. Eng. 1963, 89, 31–60. [Google Scholar]
  38. McKay, G.; Otterburn, M.S.; Sweeney, A.G. The removal of colour from effluent using various adsorbents—III. Silica: Rate processes. Water Res. 1980, 14, 15–20. [Google Scholar] [CrossRef]
  39. Filice, S.; Mazurkiewicz-Pawlicka, M.; Malolepszy, A.; Stobinski, L.; Kwiatkowski, R.; Boczkowska, A.; Scalese, S. Sulfonated pentablock copolymer membranes and graphene oxide addition for efficient removal of metal ions from water. Nanomaterials 2020, 10, 1157. [Google Scholar] [CrossRef]
  40. Qiu, H.; Lu, L.V.; Pan, B.; Zhang, Q.; Zhang, W.; Zhang, Q. Critical review in adsorption kinetic models. J. Zhejiang Univ. Sci. A 2009, 10, 716–724. [Google Scholar] [CrossRef]
  41. Kajjumba, G.W.; Emik, S.; Öngen, A.; Özcan, H.K.; Aydın, S. Modelling of adsorption kinetic processes—errors, theory and application. In Advanced Sorption Process Applications; BoD–Books on Demand: Norderstedt, Germany, 2018; pp. 1–19. [Google Scholar]
  42. Mishra, V. Modeling of batch sorber system: Kinetic, mechanistic, and thermodynamic modelling. Appl. Water Sci. 2017, 7, 3173. [Google Scholar] [CrossRef] [Green Version]
  43. Özcan, A.; Öncü, M.; Özcan, S. Kinetics, isotherm and thermodynamic studies of adsorption of Acid Blue 193 from aqueous solutions onto natural sepiolite. Colloid Surf. A. 2006, 277, 90–97. [Google Scholar] [CrossRef]
  44. Al-Jlil, A. Adsorption of cobalt ions from waste water on activated Saudi clays. Appl. Water Sci. 2017, 7, 383. [Google Scholar] [CrossRef] [Green Version]
  45. Tan, X.; Chen, C.; Yu, S.; Wang, X. Sorption of Ni2+ on Na–rectorite studied by batch and spectroscopy methods. Appl. Geochem. 2008, 23, 2767. [Google Scholar] [CrossRef]
  46. Sari, A.; Tuzen, M.; Soylak, M. Adsorption of Pb(II) and Cr(III) from aqueous solution on Celtek clay. Hazard. Mater. 2007, 144, 41. [Google Scholar] [CrossRef]
  47. Tahir, S.S.; Rauf, N. Thermodynamics studies of Nickel(II) adsorptions onto bentonite from aqueous solution. J. Chem. Thermodyn. 2003, 35, 2203. [Google Scholar] [CrossRef]
  48. Ho, S. Selection of Optimum Sorption Isotherm. Carbon 2004, 42, 2115. [Google Scholar] [CrossRef]
  49. Chatterjee, S.; Guha, N.; Krishnan, S.; Singh, A.K.; Mathur, P.; Rai, D.K. Selective and Recyclable Congo Red Dye Adsorption by Spherical Fe3O4 Nanoparticles Functionalized with 1, 2, 4, 5-Benzenetetracarboxylic Acid. Sci. Rep. 2020, 10, 1–11. [Google Scholar] [CrossRef]
  50. Alshammari, M.; Al Juboury, M.F.; Naji, L.A.; Faisal, A.A.; Zhu, H.; Al-Ansari, N.; Naushad, M. Synthesis of a novel composite sorbent coated with siderite nanoparticles and its application for remediation of water contaminated with Congo red dye. Inter. J. Env. Res. 2020, 14, 177–191. [Google Scholar] [CrossRef] [Green Version]
  51. Kim, S.H.; Choi, P.P. Enhanced Congo red dye removal from aqueous solutions using iron nanoparticles: Adsorption, kinetics, and equilibrium studies. Dalton Trans. 2017, 46, 15470–15479. [Google Scholar] [CrossRef] [PubMed]
  52. Yang, K.; Li, Y.; Zheng, H.; Luan, X.; Li, H.; Wang, Y.; Xia, Y. Adsorption of Congo red with hydrothermal treated shiitake mushroom. Mater. Res. Express 2019, 7, 015103. [Google Scholar] [CrossRef] [Green Version]
  53. Mansour, R.A.; El Shahawy, A.; Attia, A.; Beheary, M.S. Brilliant Green Dye Biosorption Using Activated Carbon Derived from Guava Tree Wood. Int. J. Chem. Eng. 2020, 2020. [Google Scholar] [CrossRef]
  54. Abbas, M. Removal of brilliant green (BG) by activated carbon derived from medlar nucleus (ACMN)–Kinetic, isotherms and thermodynamic aspects of adsorption. Adsorpt. Sci. Technol. 2020, 38, 464–482. [Google Scholar] [CrossRef]
  55. Pathak, P.; Gedam, V.V.; Deokar, S.; Bhagat, S.; Chahande, A.; Raut, P. Studies on the removal of Brilliant Green dye using low cost agricultural waste. Indian J. Chem. Techn. 2020, 27, 333–339. [Google Scholar]
  56. Hariharan, M.; Varghese, N.; Cherian, A.B.; Paul, J. Synthesis and characterisation of CaCO3 (Calcite) nano particles from cockle shells using chitosan as precursor. Int. J. Sci. Res. Publ. 2014, 4, 1–5. [Google Scholar]
  57. Ashish, D.K.; Verma, S.K.; Kumar, R.; Sharma, N. Properties of concrete incorporating sand and cement with waste marble powder. Adv. Concr. Constr. 2016, 4, 145. [Google Scholar] [CrossRef]
Molecules 26 02586 g001 550
Figure 1. FTIR for (a) limestone–chitosan–alginate (NLS/Cs/Alg.), (b) NLS/Cs/Alg. brilliant green (BG) dye, and (c) NLS/Cs/Alg. Congo red (CR) dye.
Figure 1. FTIR for (a) limestone–chitosan–alginate (NLS/Cs/Alg.), (b) NLS/Cs/Alg. brilliant green (BG) dye, and (c) NLS/Cs/Alg. Congo red (CR) dye.
Molecules 26 02586 g001
Molecules 26 02586 g002 550
Figure 2. SEM of (A) NLS/Cs/Alg., (B) NLS/Cs/Alg.–CR dye, and (C) NLS/Cs/Alg.–BG dye.
Figure 2. SEM of (A) NLS/Cs/Alg., (B) NLS/Cs/Alg.–CR dye, and (C) NLS/Cs/Alg.–BG dye.
Molecules 26 02586 g002
Molecules 26 02586 g003 550
Figure 3. TEM micrographs of the synthesized NLS/Cs/Alg. composite.
Figure 3. TEM micrographs of the synthesized NLS/Cs/Alg. composite.
Molecules 26 02586 g003
Molecules 26 02586 g004 550
Figure 4. Influence of (A) pH and (B) time on the adsorption of 12 mg/L CR or BG dye by 0.02 g/100 mL NLS/Cs/Alg. nanocomposite.
Figure 4. Influence of (A) pH and (B) time on the adsorption of 12 mg/L CR or BG dye by 0.02 g/100 mL NLS/Cs/Alg. nanocomposite.
Molecules 26 02586 g004
Molecules 26 02586 g005 550
Figure 5. Nanocomposite: (A) Morris–Weber equation, (B) pseudo–first–order (PFO), (C) pseudo–second–order (PSO), and (D) Bangham.
Figure 5. Nanocomposite: (A) Morris–Weber equation, (B) pseudo–first–order (PFO), (C) pseudo–second–order (PSO), and (D) Bangham.
Molecules 26 02586 g005
Molecules 26 02586 g006 550
Figure 6. Flowchart of the NLS/Cs/Alg. formation.
Figure 6. Flowchart of the NLS/Cs/Alg. formation.
Molecules 26 02586 g006
Table
Table 1. Kinetics parameters for the sorption of CR and BG dyes on the NLS/Cs/Alg. nanocomposite.
Table 1. Kinetics parameters for the sorption of CR and BG dyes on the NLS/Cs/Alg. nanocomposite.
Lagrange
(Pseudo-First-Order)		Kads (min−1)qe, cal (mg g−1)R2
CR dye0.01294.90.719
BG dye0.01831.70.791
(Pseudo-Second-Order)K2 (g mg−1 min−1)qe, cal (mg g−1)R2
CR dye2.0794.90.968
BG dye1.9931.70.993
BanghamAKoR2
CR dye0.0487.70.982
BG dye0.7128.90.955
Morris–WeberKd (mg g−1 min0.5)C (mg·g−1)R2
CR dye10.7 510 0.911
BG dye11.14300.906
Table
Table 2. Calculated parameters of the Langmuir, Freundlich, and Dubinin–Radushkevich (D–R) models for the adsorption of CR and BG dyes on the NLS/Cs/Alg. nanocomposite.
Table 2. Calculated parameters of the Langmuir, Freundlich, and Dubinin–Radushkevich (D–R) models for the adsorption of CR and BG dyes on the NLS/Cs/Alg. nanocomposite.
Langmuir
Dyeb (L·mg−1)Qmax (mg·g−1)R2
CR5.3 × 10−322500.998
BG6.6 × 10−320100.988
Freundlich
Dye Kf (moln−1 Ln g−1)nR2
CR3123.30.998
BG1782.10.979
D–R model
DyeE (kJ mol−1)q(DR) (mg·g−1)R2
CR7.938900.995
BG7.43080 0.968
Table
Table 3. Thermodynamic data for the adsorption of CR and BG dyes on the NLS/Cs/Alg. nanocomposite.
Table 3. Thermodynamic data for the adsorption of CR and BG dyes on the NLS/Cs/Alg. nanocomposite.
∆So (J·mol−1·K−1)∆Ho (kJ·mol−1)∆Go (kJ·mol−1)ln KdT(K)Dye
89.137.7−5.110.49 288 CR
−27.110.82 298
−29.911.41 313
−32.411.72 323
79.18.71−21.59.02 288 BG
−22.59.14 298
−24.89.44 313
−27.49.70 323
Table
Table 4. Adsorption performance of CR and BG dyes onto different adsorbents.
Table 4. Adsorption performance of CR and BG dyes onto different adsorbents.
DyeAdsorbentqe (mg/g)References
CRSpherical Fe3O4 nanoparticles functionalized with 1, 2, 4, 5-benzenetetracarboxylic acid192[49]
Synthesis of siderite9416[50]
Iron nanoparticles887[51]
Shiitake mushroom217.8[52]
BGActivated carbon90[53]
Activated carbon derived from medlar nucleus (ACMN)833.33[54]
Nanohydroxyapatite49.1[18]
Low cost agricultural waste24.23[55]
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Ahmed, I.A.; H. Ragab, A.; Habila, M.A.; Alomar, T.S.; Aljuhani, E.H. Equilibrium and Kinetic Study of Anionic and Cationic Pollutants Remediation by Limestone–Chitosan–Alginate Nanocomposite from Aqueous Solution. Molecules 2021, 26, 2586. https://doi.org/10.3390/molecules26092586

AMA Style

Ahmed IA, H. Ragab A, Habila MA, Alomar TS, Aljuhani EH. Equilibrium and Kinetic Study of Anionic and Cationic Pollutants Remediation by Limestone–Chitosan–Alginate Nanocomposite from Aqueous Solution. Molecules. 2021; 26(9):2586. https://doi.org/10.3390/molecules26092586

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Ahmed, Inas A., Ahmed H. Ragab, Mohamed A. Habila, Taghrid S. Alomar, and Enas H. Aljuhani. 2021. "Equilibrium and Kinetic Study of Anionic and Cationic Pollutants Remediation by Limestone–Chitosan–Alginate Nanocomposite from Aqueous Solution" Molecules 26, no. 9: 2586. https://doi.org/10.3390/molecules26092586

APA Style

Ahmed, I. A., H. Ragab, A., Habila, M. A., Alomar, T. S., & Aljuhani, E. H. (2021). Equilibrium and Kinetic Study of Anionic and Cationic Pollutants Remediation by Limestone–Chitosan–Alginate Nanocomposite from Aqueous Solution. Molecules, 26(9), 2586. https://doi.org/10.3390/molecules26092586

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