Removal of methylene blue from wastewater using hydrogel nanocomposites: A review

Abstract

Water pollution by organic dyes continues to pose a serious health and environmental threat to the ecosystem. Although adsorption using biopolymer-based hydrogels has proven to be an ideal technique for the treatment of these dye contaminants from aqueous solutions, these hydrogels suffer from lack of mechanical stability and recovery as compared to synthetic polymers. Herein, we review the low-cost synthesis of hydrogel incorporated with inorganic components mainly focusing on strategies to improve the mechanical stability and separation of the hydrogel in removing methylene blue (MB) dye from aqueous solution. The literature shows that hydrogel nanocomposites are a class of materials that have flourished significant consideration, especially concerning water treatment. In adsorption technology, hydrogel nanocomposites act as absorbents, prominent to enhance their removal efficiency towards contaminants. This review highlights the preparation and use of hydrogel nanocomposites as efficient adsorbents. In-depth discussions on adsorption and diverse synthetic routes of hydrogels have been devoted to applications of these nanocomposites and are compared in this contribution to the removal efficiency of MB dye from wastewater.

Keywords

Adsorption hydrogel inorganic components methylene blue nanocomposites

Introduction

Water is very important for the survival of living things on earth.¹ Despite the need for this resource, water pollution continues to be a problem in most countries including South Africa, where the mainstream water supplies are underground and surface water.² Water pollution may be defined as any water that is unsafe for drinking by humans and animals.² There are two classes of water contaminants, namely, point sources and non-point sources in which they are defined as a source of pollution at a fixed location (mines, industries, power stations, water treatment station, etc.) and pollution from moving sources (cars, buses and trains), respectively.^3,4 In point source, water pollutants may be classified as either inorganic (fertilizers and toxic metals), organic (dyes) or microbial (viruses and bacteria).⁵ For example, dyes are organic complexes mostly used by textile industries to give colour to fabrics and contribute largely to pollution.⁶ Other applications may include use in medical, pharmaceutical, paper, rubber, plastics, leather, food and cosmetics industries.⁷ Dyes contain aromatic rings in their structure and can be made up of either chromophores or auxochromes.^7,8 Chromophores are responsible for the production of colour (OH, NH₂, NHR, NR₂, Cl, COOH and R =alkyl group), and auxochromes (NO₂, NO and N = N) improve chromophores, make molecules soluble in water and improve their affinity to bind materials.⁸ The discharging of dye effluents into either surface and/or groundwater sources leads to contamination which ultimately results in various health and environmental problems.^8,9 Consumption of contaminated water by humans can lead to vomiting, mutation, cancer, breathing problems, diarrhoea, eyes burn, nausea shock, cyanosis, jaundice and tissue necrosis.^7,8–10 The environmental issues include the death of aquatic organisms, leading to the development of foul smell,^11,12 hence the need to eliminate dyes from waste effluents before discharging them into rivers and other water streams.

Conventional methods used to remove dyes from water include adsorption, membrane filtration, ion-exchange, photochemical method, electrochemical destruction and anaerobic bioremediation systems (Table 1).¹³ The membrane filtration technique separates pollutants using a physical barrier that allows permeability by water only such that contaminants are retained on the membrane surface. Factors influencing the separation behaviour of the membrane filtration may include sieving, size of contaminants, adsorption and electrostatic interactions.¹⁴ Its advantage is that it is fast with low space requirement and it removes all dye types.¹³ However, the disadvantage is its limited lifetime before fouling, high costs of the membrane and sludge production.¹⁵ During ion-exchange for treatment of dye effluents, the concentration of the dye is reduced through the use of anionic or cationic resins whose ions exchange with the dye molecules to form solid particles that are easy to remove.¹⁶ The advantage of ion-exchange is that it has high removal capacity for dyes, but the major disadvantage is its inability to remove all dye types and high costs.^13,16 The photochemical method uses UV light and most use Fenton reagent.¹⁷ It offers the advantage of no sludge production and odour elimination.^13,16 The main advantage of dye degradation using heterogeneous photocatalysts is the ability to use the sunlight in the production of hydroxyl radicals. Its drawback is the formation of by-products.¹⁸ The electrochemical destruction method applies electrical current for the destruction of dye molecules.^19,20 This method does not generate sludge and does not require the addition of any chemical reagent.^13,19 However, it has the disadvantage of high flow rates, which consequently reduce the removal efficiency of dyes, sludge production and causing a secondary pollution problem.^13,21 It is worth mentioning that above-mentioned conventional methods are also applicable for recovery of metals from wastewater. Apart from the aforementioned processes, cementation processes have been well documented in the literature for recovering metals from wastewater. Several researchers have investigated this process in the recovery of copper (Cu), gold (Au), aluminium (Al) and zinc (Zn) from wastewater.²² Anaerobic bioremediation involves degradation of organic contaminants under anaerobic conditions in the presence of anaerobic microorganisms.²³ The advantage of this technique is that water-soluble dyes can be decolourized; however, this method results in the production of sulphide and methane.²⁴ Amongst these techniques, the adsorption technique is most favoured owing to its cheap operation costs, easy design and fast removal of dye.^25,26 During this process, dye molecules are attached on the surface of a solid material (adsorbent) through either physical interactions (hydrogen bonding, weak Van der Waals forces) or chemical bonding.²⁷

Table 1.

Methods of removing dyes from water.

Adsorbent method	Disadvantages	References
Membrane filtration	Membrane fouling and production of concentrated sludge	25
Ion-exchange	Ineffective for all dye types	6,13
Photochemical method	Production of by-products	25
Electrochemical destruction	Moderately high flow rates that decrease the amount of dye removed	25
Anaerobic bioremediation systems	Lead to the production of methane and hydrogen sulphide which are harmful	13,28
Adsorbent using activated carbon	The adsorbent is expensive	28

The most used commercial adsorbent is activated carbon (AC) (powder or granular).^6,25 The application of AC as an adsorbent is possible due to its high adsorption capacity, high removal efficiency, large surface area and high porosity.²⁹ It effectively removes various types of organic micropollutants as well as their secondary oxidation products and inorganic compounds.²⁹ The main disadvantage of this adsorbent, however, is the high cost and its regeneration problems.⁶ To reduce the cost of using commercial AC, agricultural by-products including shells and seeds of fruits have been used for production of AC.^30,31 For example, a study by Geçgel et al. (2012) generated AC from Pea Shells (Pisum sativum) and removed 246.91 mg/g of methylene blue (MB) from water.³² Further, to improve regeneration of AC, a study by Park et al. (2019) regenerated spent AC obtained from wastewater treatment plant through heat treatment and KOH chemical activation.³³ The group reported an increased specific surface area from 680 m²/g (spent AC) to 710 m²/g (regenerated AC). Despite these improvements, AC still suffers the problem of separation from water bodies and that it produces secondary pollution.³³ In an attempt to improve separation of AC from water bodies, many studies have introduced magnetic nanoparticles into the AC material, to enable recovery through exposure to an external magnetic field.^29,34,35 Considering the evidence that biological materials could be used for dyes removal, many researchers were prompted to investigate the use of biological materials such as polysaccharides, agricultural waste and fruit peels as cheap and effective adsorbents for MB removal.⁶ Compared to AC and other materials, polysaccharides (cellulose, chitin, chitosan, sodium alginate, etc.) offer greater advantages for use as adsorbents for removal of MB.⁷ The advantages include non-toxicity, cheap cost, and eco-friendliness, sustainability due to their abundant availability, high chemical reactivity, biodegradability, polyfunctionality and biocompatibility.^36–38 However, due to their lack of stability, most researchers have explored their application as hydrogels.^7,10,39,40 For example, Zhou et al.⁴⁰ prepared cellulose based hydrogels and removed 2197 mg/g of MB.

Hydrogels are a class of three-dimensional (3D) soft polymeric materials, which can imbibe a substantial amount of liquids.⁴¹ In this direction, their innate ability to absorb and hold a high volume of liquid qualifies them as ideal materials for the adsorption of aquatic pollutants.⁴¹ Hydrogels attracted a great deal of attention in various fields (gas sensing,⁴² drug delivery⁴³ and cosmetics⁴⁴) owing to their non-toxicity, low cost, permeability and biocompatibility.¹⁰ However, the applicability of hydrogels has been overshadowed due to their weak mechanical properties and partial adsorption capacity.¹⁰ The yearning for enhancing inherent shortcomings exhibited by hydrogels has instigated tremendous research interest in the development of hydrogel nanocomposite, which is a robust process to improve the disadvantages without losing the advantage of hydrogels. In the past decades, the use of hydrogel nanocomposites for the removal of MB dyes in aqueous environment has increased considerably. In the past 10 years, a developing trend of publications in hydrogel nanocomposites for removal of MB dyes is shown in Figure 1. The literature survey statistics show an exponential increase in the number of publications per year considering hydrogel nanocomposites for the removal of MB dye.

Figure 1.

The total number of publications per year on hydrogel nanocomposites for removal of dyes during the period 2011–2021 (using science direct database). *Data collected in May 2021.

This review summarizes the recent advances and developments of hydrogel nanocomposites as adsorbents for wastewater treatment. This is realized by doing a detailed review of the reactions and mechanisms of adsorption including an overview of the adsorption of MB dye. Then, we introduce hydrogel nanocomposite as an adsorbent for MB removal with great emphasis on the structure and synthetic routes.

Adsorption

Background

The attachment or adherence of molecules on the surface of solid material is known as adsorption. The adsorbent material contains active adsorptive sites on its surface to which molecules (gas or liquid) from the bulk solution (adsorbate solution) bind to.^45,46 Adsorption of molecules may occur either physically or chemically.⁴⁷ The mass transfer process may occur in the form of migration, diffusion or convection, in which liquid or gaseous molecules are transferred to a solid phase.^48,49 Interactions such as Lewis acid-base, van der Waals and Columbic are characteristic of physisorption^50,51 whereas chemisorption is distinguished through the development of new adsorbate–adsorbent bonds.⁵² The adsorptive sites can have the same or different energy, depending on the nature of the material.⁵³ Owing to its principle, adsorption has gained interest for application in hydrogen storage, sensing, drug delivery, gas capture and water treatment.^54–57

The recent interest in applying adsorption for the treatment of dyes from wastewater was attracted by its low operation costs, easy design, efficiency and fast removal of dye.^58,59 Before applying an adsorbent material on an industrial scale (column adsorption), it is first optimized in batch mode experiments; then if it possesses a high removal efficiency, it can be employed for column adsorption studies.^60,61 Factors that affect the adsorption process in wastewater treatment include the following^55,56,60:

1. The adsorbent and adsorbate charges,

2. the solution pH,

3. temperature,

4. dye concentration,

5. adsorbent dose and

6. the surface area of the solid material.

When an adsorption process reaches equilibrium, it means the active sites of the adsorbent are saturated with adsorbate molecules and no further adsorption can take place.⁶¹

Adsorption parameters

Adsorption isotherms

The isotherms of adsorption are significant for describing the adsorbate–adsorbent interactions.⁶² Additionally, they provide information about the mechanisms of adsorption, adsorption capacity and surface properties. This study employs the Langmuir, Freundlich and Temkin isotherm models. Below are their brief descriptions including their linear and non-linear equations.

Langmuir isotherm model

Irving Langmuir⁶³ established the Langmuir isotherm in 1916. The model theory assumes that the active sites on the solid surface have the same energy, leading to homogeneous adsorption of adsorbate molecules (monolayer coverage).⁶⁴ Graphically, adsorption equilibrium is observed by a plateau, which is a point where all active sites are fully occupied and no further adsorption can occur.^65,66 The model is expressed as follows, non-linear (equation (1)) and linear (equation (2)) forms

q_{e} = \frac{q_{m} b C_{e}}{1 + b C_{e}}

(1)

\frac{c_{e}}{q_{e}} = \frac{1}{q_{m} K_{L}} + \frac{c_{e}}{q_{m}}

(2)

where Ce is the equilibrium concentration (mg/L), qe is the amount adsorbed at equilibrium (mg/g), K_L (L/mg) is the adsorption equilibrium constants of Langmuir, the Langmuir constants q_m (mg/g) represent the monolayer adsorption capacity and b relates to the heat of adsorption. The values of qm and K_L can be determined from the linear plot of Ce/qe against Ce. The essential features of the Langmuir isotherm can be employed to predict the affinity between the sorbate and the sorbent using the dimensionless equilibrium constant (R_L).

The R_L is a dimensionless constant denoted as the separation factor. R_L is calculated using the following equation (3)

R_{L} = \frac{1}{1 + b C_{o}}

(3)

If R_L > 1, adsorption is not favoured. If R_L = 1, adsorption is linear. If R_L < 1, adsorption is favoured, and if R_L = 0, the reaction is irreversible.⁶⁶

Freundlich isotherm

The model assumes multilayer coverage of the adsorbent. The model is expressed by the following equations in a non-linear (equation (4)) and linear (equation (5)) form

q_{e} = K_{F} C_{e}^{1 / n}

(4)

l n q_{e} = l n l n K_{F} + \frac{1}{n} l n l n c_{e}

(5)

where q_e (mg/g) and C_e (mg/L) are the amounts adsorbed and the solution concentration, respectively, at equilibrium. K_F is the sorption enthalpy and varies with temperature. K_F and n are the sorption capacity and sorption intensity.⁶⁷ n determines the non-linear relation between adsorption and the concentration of the solution.⁶⁷

Temkin isotherm

The Temkin isotherm theory ignores the concentration values and assumes that the decrease in heat of adsorption concerning the temperature is linear instead of decreasing logarithmically as suggested in the Freundlich equation. The non-linear (equation (6)) and linear (equation (7)) forms of the Temkin model are expressed as follows below

q_{e} = \frac{R T}{b_{T}} l n l n (K_{T} C_{e})

(6)

q_{e} = \frac{R T}{b_{T}} l n A_{T} + \frac{R T}{b_{T}} l n C_{e}

(7)

where A_T is the equilibrium binding constant corresponding to the maximum binding energy (L/g), b_T is the Temkin constant related to the heat of adsorption (kJ/mol), R is the universal gas constant (8.314 J/mol/K) and T is the absolute temperature (K).⁶⁸

Kinetic isotherms

Adsorption is a process that involves the transfer of mass of a solute from the liquid phase to the surface of the adsorbent.⁶⁹ The mechanism of adsorption can be researched using either Lagergren’s pseudo-first-order equation or pseudo-second-order equation. The amount of contaminant adsorbed with time can be analysed provided an appropriate model is used.⁷⁰ To identify which model is appropriate, the correlation coefficient (R²) is measured and must be close or equal to 1. The model with a higher R² is the most suitable model for the adsorption kinetics of contaminants.

The non-linear (equation (8)) and linear (equation (9)) equations for the pseudo-first-order kinetic model are

q_{e} = q_{e} [1 - \exp (K_{1} t)

(8)

\ln (q_{e} - q_{t}) = \ln (q_{e}) - K_{1} t

(9)

where q_e and q_t refer to the amount of dye adsorbed (mg/g) at equilibrium and at any time, t (min). K₁ is the equilibrium rate constant of pseudo-first-order sorption (1/min). K₁ will be determined using the slope and intercept of the plot of ln (q_e −q_t) versus t.⁷¹

The non-linear and linear equations for the pseudo-second-order kinetic model are

q_{e} = \frac{K_{2} q_{e}^{2} t}{1 + K_{2} q_{e} t}

(10)

\frac{t}{q_{e}} = \frac{1}{K_{2} q_{e}^{2}} + \frac{t}{q_{e}}

(11)

where K₂ is the equilibrium rate constant of pseudo-second-order adsorption (g/mmol min). K₂ will be determined using the slope and intercept of the plot of t/qt versus t.

Thermodynamics

During the adsorption process, thermodynamic parameters such as enthalpy (ΔH^o), entropy (ΔS^o) and Gibbs free energy (ΔG^o) are required to determine spontaneity and heat change.⁷² Thermodynamics parameters may be calculated according to the formulas below

K_{D} = \frac{q_{e}}{C_{e}}

(12)

Δ G ° = - R T l n K_{D}

(13)

l n K_{D} = \frac{Δ S}{R} - \frac{Δ H}{R T}

(14)

where

K_{D}

represents the distribution coefficient of the adsorbate,

q_{e}

and

C_{e}

represent the equilibrium concentration (mg/g) and in the solution (mg/L). R represents the universal gas constant (8.314 J/mol K), and T is the temperature (K). ΔH^o and ΔS^o may be calculated from the slope and intercept of the plot

l n K_{D}

versus 1/T. Negative

Δ G

values at different temperatures are an indication of a spontaneous adsorption process.^71,73 If

Δ G

decreases when the temperature is increased, it means there is a more efficient interface during adsorption. A positive

Δ H

value indicates an endothermic adsorption process.⁷⁴

Adsorbent materials for MB

Although the adsorption technique is effective for dye removal, the type of adsorbent used limits its efficiency.⁷⁵ Various materials have been used for MB dye removal. For example, AC is reported to be the most frequently used nano-adsorbent for removing a variety of inorganic and organic contaminants owing to its high surface area, porous structure, thermal stability and amphoteric nature.^76,77 However, AC has some drawbacks such as intraparticle resistance in industrial application, high production costs and regeneration costs.^77–79 Recent research studies have attempted to find ways to improve the regeneration of AC and produce it at a lower cost.⁷⁷ On the other hand, alternative adsorbents such as fly ash, graphene, clay, carbon nanotubes and polysaccharides were reported for removal of MB.^80–87 Among these adsorbents, Mittal et al.⁸⁰ reported that using polysaccharides-based adsorbents is a promising strategy for MB dye removal from aqueous solutions. This is due to their enhanced adsorption capacity amongst other attractive properties.

Polysaccharides

Polysaccharides can be defined as highly hydrophilic and non-toxic natural polymers made up of multiple small units of saccharides that are connected through glycosidic bonds.^83–85 These biopolymers are found and used in plants or animals for structural support and energy storage.⁸⁶ Examples of polysaccharides include carboxymethyl cellulose (CMC), alginate, carrageenan, chitosan, guar gum, starch and locust bean gum.^85–87 These natural polymers offer the advantages of high absorption capacity, biodegradability and cheap synthesis.⁸⁸ However, due to low solubility and other physical drawbacks, synthetic polymers are incorporated into the biopolymeric backbone to improve their properties.⁸⁹ Polysaccharides-based materials have recently attracted use for adsorption of dyes and toxic metals because of their non-toxic nature, biodegradability, easy availability and low-cost synthesis.⁹⁰ Amongst other polysaccharides, CMC and alginate offer more attractive properties for application as dye adsorbents.

Carboxymethyl cellulose

Cellulose is the main component of most plants.⁶ Carboxymethyl cellulose is a highly reactive, hydrophilic, water-dissolving derivative of cellulose with many carboxyl groups on its surface.⁸² Commercially it can be obtained as sodium CMC with different degrees of saturation (DS), which may range from 0.6–0.95 depending on how it was prepared, and the solvent used.^91,92 Carboxymethyl cellulose is mostly used in paper, packaging, textile, food, cosmetics and pharmaceuticals.^85,93 Due to its sensitivity to pH, non-toxic nature, hydrophilicity, low cost and ability to form gels, CMC has been applied on its own or in a composite form as an adsorbent for removing inorganic and organic contaminants.^92,94

Carboxymethyl cellulose (Figure 2) is a cellulose derivative with carboxymethyl groups at carbon 2, 3 and 6.⁹⁵ In a study conducted by Kono,⁹⁶ the resonances of CMC were determined using carbon-13 nuclear magnetic resonance (¹³C NMR) as shown in Figure 3. In the spectrum of CMC, the carbonyl carbon (C1, C4), overlap of C2, C3, C5, the carboxymethyl groups, and C6 were assigned to broad ¹³C resonances at 178, 104, 83, 75 and 63 ppm.⁹⁶ The existence of carboxylic groups (COO⁻) on the polymer chains of CMC allows for interactions with multivalent metal cations (Al³⁺ and Fe³⁺) which results in the formation of stabilized ionotropic hydrogels. Interactions with metal ions through the hydroxyl groups of the CMC may improve the water insolubility and stability of the polymer aggregates.^95,96

Figure 2.

Structure of sodium carboxymethyl cellulose.⁶³

Figure 3.

¹³C NMR of CMC.⁷⁵ CMC: carboxymethyl cellulose.

The reaction of cellulose with monochloroacetic acid (MCA) or its sodium salt in the presence of an organic solvent under basic conditions produces NaCMC.⁹⁷ There are various materials from which CMC can be derived; for example, Petri⁹⁸ prepared CMC from pineapple peels, and in another study, Begum et al.⁹⁹ prepared CMC from sugarcane bagasse. The synthesis of CMC occurs in three steps: (1) alkalization, (2) carboxymethylation and (3) neutralization as outlined in the steps below.

Step 1

Cell-OH + NaOH $\to$ Cell-OH.NaOH

Step 2

Cell-OH.NaOH + ClCH₂COONa $\to$ Cell-O-CH₂COO⁻ Na⁺ + NaCl + H₂O

Step 3

NaOH⁺ Cl⁻CH₂COONa $\to$ HO-CH₂COONa + NaCl

During the synthesis process, carboxymethyl groups replace hydroxyl groups at positions 2, 3 and 6 of cellulose. In the synthesis of CMC, it is important to consider the degree of substitution, which will govern the porosity, and adsorption capacity of CMC.⁹⁹ Degree of Substitution (DS) refers to the number of hydroxyl groups replaced by carboxymethyl groups. Each β-glucopyranose unit of cellulose has three hydroxyl groups; therefore, hypothetically DS value will range between 0 and 3.0.¹⁰⁰ Various factors may affect the DS of CMC such as the solvent, temperature and the NaOH concentration.¹⁰¹ For example, most researchers report that the use of isopropanol as the solvent yields CMC with very high DS.¹⁰¹ Huang et al.¹⁰² synthesized CMC from the pulp of six different plants; the conditions that yielded the best CMC were 20% NaOH concentration, the temperature of 60°C and 3–5 g of MCA. The group reported that CMC yield increased with increasing MCA content. The degree of saturation influences the application of CMC.¹⁰² The hydrophilicity of CMC increases with an increase in DS. When DS > 0.4 (higher), CMC becomes soluble in water, has better viscosity, enhanced cationic exchangeability and improved covalent crosslinking through radiation. Whereas when DS < 0.4 (lower), CMC is insoluble, and it swells in solution.¹⁰² For example, a study reported the degradation of a polymer with irradiation of 10% CMC (0.7 DS), whereas irradiation of CMC of 1.32 DS resulted in outstanding crosslinking and high gel-fraction.¹⁰³ For adsorption, the properties of CMC can be modified by crosslinking to form a gel, which will improve the solubility and hydrophilicity of CMC.

Alginate

Alginate is a sentimental term used in the dietetic, cosmetic, pharmaceutical and biotechnological industries.¹⁰⁴ The alginate can be found in salts of magnesium (Mg), potassium (K), calcium (Ca) and sodium (Na).¹⁰⁴ E.C.C Stanford who was a pharmacist¹⁰⁵ discovered alginates in 1929. SA is found in brown algae, marine algae and produced by some bacteria, hence abundant in nature.^106,107 Applications of sodium alginate include drug delivery, thicker, gel-forming agent, binder during the production of tablets, use as a stabilizer and mixing agent.^105–108 The recent use of polysaccharides as adsorbents for dyes and other pollutants is mostly due to the attractive properties that polysaccharides possess, such as high hydrophilic structures, their non-toxic nature, biodegradability and cheap synthesis.^109–111

Sodium alginate (SA, Figure 4) is made up of poly- $β$ -1, 4-D- mannuronic acid and $α$ -1, 4-L-guluronic acid.¹¹² The structure consists of carboxylic groups and hydroxyl groups, which can react with metal ions or crosslinking agents to form hydrogels.¹¹³ Alginate can be extracted from its salt forms by ion-exchange methods.¹¹⁴ Because of the presence of divalent ions, monovalent, water-soluble salts of alginates can transform into water-insoluble salts. The COO⁻ and -OH functional groups on the alginate backbone will allow adsorption of cationic dye pollutants.¹¹⁵ However, sodium alginate just like other polysaccharides suffers from a lack of stability.¹¹¹ To enhance the stability of SA and its adsorption capacity, the biopolymer may be cross-linked with synthetic polymers into forming a hydrogel.^116,117 This will allow their use as adsorbents without them dissolving in the adsorbate solution. The major disadvantage of polysaccharides as adsorbents is that they dissolve in water and have low mechanical stability.^116,117 To resolve this problem, polysaccharides are cross-linked to form hydrogels, which do not dissolve in water.

Figure 4.

Structure of sodium alginate.⁶²

Hydrogels

Background

Hydrogels are hydrophilic polymer chains that are cross-linked to form gel structures that swell in aqueous solution and trap fluids for a long period without dissolving.^83,84 Hydrogels may contain carboxylic, amine, imide, hydroxyl and sulfonyl groups in their 3D structure that are responsible for the hydrophilicity and swelling capacity.¹¹⁸ Depending on the nature of the hydrogel, it can be classified based on various properties. Classification of hydrogels (Figure 5) can be based on whether they are synthetic (involves the use of synthetic monomers), natural (involves using biopolymers) or a combination of synthetic and natural monomers resulting in a hybrid hydrogel.¹¹⁹ The polymeric composite classification can be based on the method used to synthesize the hydrogel¹¹⁹:

a. Homopolymeric hydrogels: they are hydrogels consisting of the same type of monomer.

b. Copolymeric hydrogels: these hydrogels comprise two or more different kinds of monomers such that the network would have at least one hydrophilic component on the polymer network chain.

c. Multipolymer interpenetrating polymeric hydrogel (IPN): the hydrogel network consists of two components (natural and/or a synthetic polymer) that are independently cross-linked.

Figure 5.

Classification of hydrogels.

It was also demonstrated that hydrogels can be categorized based on whether they are¹²⁰

a. crystalline,

b. amorphous or

c. semi-crystalline: showing properties of both crystalline and amorphous phases.

The other classification is based on whether the crosslinking of hydrogels occurs via chemical or physical means. Briefly,

a. physical crosslinking in hydrogels may be through (1) formation of a hydrogen bond, (2) hydrophobic interactions between chains, in which the dissipation energy of the bond prevents breakage and improves the hydrogel strength, and (3) crystallization where gels are subjected to freeze and thaw process in PVA/PVP solution 10 h at 15°C and then placed at room temperature for 2 h. Lastly (4) between oppositely charged groups.⁸⁴

b. Chemical crosslinking can be achieved by (1) using aldehydes such as acetaldehyde, glutaraldehyde (GA) and formaldehyde and (2) radiation using an electron beam, gamma rays or ultraviolet rays at room temperature in which a free radical is formed, monomers are added to the chain for growth and the gel forms at the critical gelling point. Lastly (3) free-radical polymerization using a cross-linker, for example, MBA. In this method, an initiator such as potassium persulfate (KPS) generates free radicals, the radicals react with other monomers and then MBA is added to the polymer chain to form the hydrogel.^84,121

In addition, the hydrogels may be classified based on the charge on their cross-linked polymer network.^122,123 The charge may be

a. ionic (cationic/anionic),

b. non-ionic (neutral),

c. amphoteric (comprising both basic and acidic groups) and

d. zwitterionic (contains anionic and cationic components on each repeating structural unit). The net charge of the gel is zero.

Lastly, hydrogels can also be categorized according to what stimulates their response. These hydrogels are sometimes called smart hydrogels.^119,121 There are two categories of stimulus, namely, physical stimuli and chemical stimuli as stipulated in Table 2. The swelling or de-swelling of hydrogels caused by changes in the environment can be too much to a point that the hydrogel changes phase (volume collapse).

Table 2.

Physical and chemical stimuli classifications.

Physical stimuli	Chemical stimuli
Light	Composition of solvent
Magnetic field	pH
Temperature	Molecular species
Sound	Ionic strength
Electric field
Pressure	—

Application of hydrogels

Hydrogels have gained much attention for use in various applications owing to their outstanding qualities; these include use in the making of disposable diapers, absorbent pads, use in hydrogen storage, sensing, CO₂ capture, biomedical field (drug and cell delivery systems), immobilization of enzymes, wastewater treatment and agriculture for trapping water.^11,48,49 The ideal properties of a hydrogel depend on its specific application. For application in water treatment, the hydrogel must have the following properties below⁹⁸:

1. High absorption capacity;

2. low residue monomer and soluble content;

3. cost-effective;

4. reusable;

5. high biodegradability and not produce harmful by-products;

6. must retain neutral pH after swelling in water and

7. easy recoverability.

The swelling capacity of hydrogels is indicative of their absorptive capacity which may be affected by factors such as the intermolecular spaces in the 3D network, the existence of hydrophilic groups on the hydrogel polymer backbone and the pore size of the hydrogel surface.¹⁰ Hence, parameters such as the amount of initiator, cross-linker, polymer, monomer and solvent volume are optimized during the preparation of the hydrogel to obtain optimum conditions for preparing an ideal hydrogel.¹²²

Preparation methods

As stated previously, biopolymers suffer poor mechanical, thermal stability and they dissolve in water.⁸⁹ Most researchers have reported that crosslinking, grafting and modification with inorganic constituents such as metal oxides and clay improves solubility and stability problems associated with biopolymers.^3,121 The type of method used to prepare the hydrogel, therefore, affects its structural make-up or physical properties. Amongst several physical and chemical techniques used for hydrogel synthesis, the most widely used methods are discussed below.

Grafting

Grafting is the modification of the polymer backbone using synthetic polymers such as acrylamide, acrylic acid, methacrylamide and vinyl alcohol as support materials.¹²³ During grafting, an initiator creates a free radical site, and then a monomer unit is added to the generated free radical site.¹²⁴ Grafting can occur via either a chemical or radiation. Chemical grafting involves using chemical reagents such as ammonium persulfate, KPS or other chemical initiators.¹²⁵ Radiation grafting involves initiating free radicals using UV visible or microwave radiation.¹²⁶

It was shown in the literature that using a microwave radiation method for synthesizing hydrogels produces sterilized hydrogels.¹²⁶ Naturally, polysaccharides suffer from poor chemical and physical stability.⁸⁹ Grafting has been reported to solve these issues including enhancing the performance of hydrogels through the introduction of new functionalities from grafted monomers.¹²⁷ For example, in a study conducted by Tally and Atassi,⁸⁶ it could be observed from the thermogravimetric analysis (TGA) curves of (a) SA and (b) SA-g-P (AA-co-AM)/PVP semi-IPN SAP (Figure 6) that grafting with synthetic polymers enhanced the thermal stability of hydrogels by more than 20% weight loss at above 200°C.

Figure 6.

Thermogravimetric analysis of (a) SA and (b) SA-g-P (AA-co-AM)/PVP semi-IPN SAP.⁶² SA: sodium alginate; PVP: polyvinylpyrrolidone; SAP: semi-IPN.

A study of the modification of CMC by grafting with poly (3-sulfopropyl methacrylate), P (SPMA), in the presence of KPS initiator for MB removal was carried out.⁹³ The main vibrational peaks at C =O (1718 cm⁻¹), S =O (1085 cm⁻¹) and S-O (626 cm⁻¹) were observed in Figure 7(a) of the Fourier transform infrared (FTIR) of the CMC-g-P (SPMA) hydrogel.⁹³ The scanning electron microscopy (SEM) image showed the well-defined pores and 3D interconnections of CMC-g-P (SPMA) hydrogel, for which the hydrogel could allow easy penetration of dye molecules in solution through its pores as observed in Figure 7(b).⁹³ The adsorption of MB by the hydrogel was characterized by an absorption peak at 664 nm corresponding to the characteristic absorption band of MB (Figure 7(c)). From the X-ray diffraction (XRD) (Figure 7(d)), the partially crystalline structure of CMC was characterized by sharp peaks at 2θ = 9.4 and 20.1° resulting from the intermolecular and intramolecular hydrogen bonding between carboxylic groups and hydroxyl groups of the biopolymer. Upon grafting on the CMC-g-P (SPMA), it could be observed that the peaks were broader, indicating the hydrogen bonds were destructed, allowing grafting to take place.⁹³

Figure 7.

FTIR (a), SEM (b), UV-vis (c) and XRD (d) of CMC-g-P (SPMA).⁶⁸ FTIR: Fourier transform infrared; SEM: scanning electron microscopy; P (SPMA): poly (3-sulfopropyl methacrylate); CMS: carboxymethyl cellulose; XRD: X-ray diffraction.

Crosslinking

The process of crosslinking can occur through physical or chemical interactions. Physical interactions are irreversible and include electrostatic interactions, hydrogen bonding and the van der Waals forces.¹²⁸ Chemical crosslinking involves forming irreversible covalent bonds in the hydrogel polymer chain usually through the reaction of complementary groups.¹²⁹ Chemically cross-linked hydrogels are mostly used in medical applications. For example, Liu et al.¹³⁰ synthesized chitosan-based hydrogels from PEG for application in drug delivery. In another study by Kumar et al.,¹³¹ cross-linked hydrogels were produced from GA as a covalent cross-linker (Scheme 1).

Scheme 1.

Crosslinking using glutaraldehyde to produce hydrogel.¹⁰⁹

The most commonly used chemical cross-linkers include ethylene glycol dimethyl-acrylate, N, N-methylene-bis-acrylamide (MBA), tetra-ethylene glycol dimethyl-acrylate (EGDMA) or tri-propyleneglycol diacrylate (TPGDA).¹³² However, these cross-linkers are usually toxic and result in non-biodegradable hydrogels.¹³³ In addition, because of the lack of internal structural homogeneity and an effective mechanism for energy dissipation, chemically cross-linked hydrogels are very brittle.¹³⁴ This prompted many researchers to consider introducing nanocomposites, ionic interactions, hydrogen bonding and hybrid hydrogel systems to improve the hydrogel properties.^135–137 A hybrid system consists of physical interactions that will aid in energy dissipation and chemical interaction, which will mainly improve structural properties.¹³⁸ Figure 8 illustrates the preparation of hydrogel beads through ionic interactions by Rahmani et al.¹³⁹ Briefly, a mixture containing gum tragacanth (GT), graphene oxide (GO) and calcium carbonate (CaCO₃) was added dropwise into a concentrated solution of Ca²⁺ which interacted with -OH and COO⁻ groups on the GT and GO to form hydrogel beads. Ionic crosslinking offers the advantage of less toxicity.¹³³

Figure 8.

Scheme showing the preparation of gum tragacanth–based hydrogel beads.¹¹⁷

In a study by Eftekhari-sis et al.,¹⁴⁰ hybrid hydrogels constructed from poly (N-isopropyl acrylamide-co-itaconic acid) and non-toxic octa-vinyl polyhedral oligomeric silsesquioxane (OV-POSS) cross-linker were prepared. Their obtained SEM (Figure 9), XRD and TGA (Figure 10) results are discussed. The rough non-homogeneous surface was observed on the SEM image (a) of poly (NIPAM-co-IA). Upon hybridization with 8% POSS (b), 12% POSS (c) and 12% POSS (d), the morphology changed to a honey-comb like structure with homogeneous pores of varying pore sizes as POSS content was increased. The study reported that at 12% POSS the honey-comb pattern was disrupted, indicating that the degree of uniformity in the hydrogel hybrid can be controlled by changing the crosslinking content.¹⁴⁰

Figure 9.

SEM images of poly (NIPAM-co-IA) hydrogel (a) and hybrid poly (NIPAM-co-IA)/OV-POSS (8%, 10% and 12% POSS) (b–d).¹¹⁸ SEM: scanning electron microscopy; OV-POSS: octa-vinyl polyhedral oligomeric silsesquioxane.

Figure 10.

X-ray diffraction and thermogravimetric analysis.¹¹⁸

For example, the XRD patterns in Figure 10(a) showed a successful hybridization and a uniform dispersion of the cross-linker as confirmed by the disappearance of characteristic crystalline diffraction peaks of OV-POSS at 2θ = 9.8, 23.1 and 23.9°.¹⁴⁰ The TGA thermogram (Figure 10(b)) showed that the crosslinking with POSS in the hybrid hydrogels increased the thermal stability, wherein the weight loss at temperatures 340–500°C was less than weight loss obtained for poly (NIPAM-co-IA) at the same temperature.¹⁴⁰ From the obtained literature, it could be observed that the chemical and physical properties of the hydrogels were improved, including creating porous structures that enable penetration of adsorbate molecules.

Free-radical polymerization

Free-radical polymerization is a technique in which polymerization is achieved by generating free radicals to which chain growth occurs in succession.¹⁴¹ This method involves a combination of grafting and crosslinking. The decomposition of the initiator may occur using temperature, light or photon, which then forms a free radical.¹⁴² Decomposition by photon offers advantages such as low costs; it allows better spatial and time-based control of the reaction process and does not use chemical solvent.¹⁴³ Scheme 2 shows a schematic representation of an overview of free-radical polymerization for synthesizing hydrogels. Firstly, there is the generation of free radicals by an initiator (initiation). Secondly, the free radicals react with the monomer to generate vacant active sites (propagation) and lastly, the formation of a polymer network through crosslinking (termination).¹⁴⁴

Scheme 2.

An overview of thermal free-radical polymerization and crosslinking.¹²²

Free-radical polymerization is the most frequently used procedure in the polymer industry.¹ The advantages of using free-radical polymerization are that it is easy to carry out, convenient, it is not easily affected by impurities and it is suitable for designing and preparing polymers that can be used for a variety of applications. Free-radical polymerization allows well-characterized reaction kinetics and achievement of in situ properties.¹⁴⁵

Modification with inorganic materials

Depending on the intended application of the hydrogels, their physical properties can be further enhanced through the incorporation of inorganic materials. For example, for use in removing contaminants from aqueous solutions, the hydrogel must be mechanically and thermally stable for application especially for removing effluents from industries that utilize water for cooling reactions,^146,147 wherein the contaminants may be introduced at that point. In addition, the hydrogels must be easy to recover. Many recent studies have incorporated nanofillers such as clay-based materials, carbon-based materials and metal oxides into the hydrogel matrix during the polymerization process to improve stability and recoverability. The blended product is then called a hydrogel nanocomposite.

Carbon-based

Carbon-based hydrogel nanocomposites are hydrogels synthesized by incorporating materials such as graphene oxide (GO), biochar, AC and carbon nanotubes.^148,149 GO is a carbon material prepared by oxidizing graphene through chemical or thermal reduction processes. It contains highly hydrophilic groups such as hydroxyl, carboxylic and epoxy groups that are essential for adsorbing dyes and toxic metals.¹⁵⁰ GO may interact with contaminants through pi-to-pi interactions, electrostatic interactions or hydrogen bonding.¹⁵¹ Owing to its outstanding mechanical, electrical and thermal properties, GO has attracted its use in the biomedical, energy and environmental field.¹⁵²

Carbon nanotubes are simply graphene sheets rolled up in cylinders of 1 nm in diameter.¹⁵³ As a result of their porous structure, large surface area, high tensile strength (0.15 TPa) and elastic modulus (0.91 TPa), CNTs have attracted interests in use for adsorption of pollutants such as dyes, dichlorobenzene, ethylbenzene and some heavy metals.^154,155 CNTs can be categorized into two forms, namely, single-walled carbon nanotubes (SWCNTs), which are made up of single layers of graphene sheets, and multi-walled carbon nanotubes (MWCNTs), which are made up of multiple layers of concentric cylinders.^153,156 For example, the incorporation of CNTs in gels improves the mechanical properties; however, the rate of degradation decreases. This is because carbon-based materials have high hydrothermal stability, which makes them resistant to harsh environments.¹⁵⁴ Scheme 3 shows various interactions or applications that carbon-based materials can take part in such as surface complexation, physical adsorption through its surfaces and electrostatic interactions.¹⁵⁷ Amongst recent studies that have used carbon-based materials to modify properties of the hydrogel, the incorporation of MWCNTs into XG/PAA hydrogel improved the surface hydrophilicity and specific area of xanthan gum.¹⁰ Makhado et al.¹¹⁹ conducted studies on xanthan gum polymer cross-linked with polyacrylic acid and incorporated with reduced graphene oxide (rGO); the successful synthesis was confirmed by FTIR. Various carbon-based nanocomposite hydrogels and their adsorption properties for removing contaminants from aqueous solutions are listed in Table 3.

Scheme 3.

Showing possible interactions of carbon-based materials.¹³⁵

Table 3.

Carbon-based adsorbent hydrogels and their adsorption properties in removing contaminants from aqueous solution.

Adsorbent	Cross-linker	Dye	Adsorption parameter					Reference
Adsorbent	Cross-linker	Dye	q_e (mg/g)	pH	Dosage (mg)	Isotherm	Kinetics	Reference
CMC-AAm-GO	MBA	Acid black-133	185.45	6	100	—	—	9
XG-cl-pAA/o-MWCNTs	MBA	MB	521	6	30	Langmuir	Pseudo-first-order	10
XG-cl-pAA/rGO	MBA	MVMB	1052.63793.65	5	10	Langmuir	Pseudo-second-order	119
CS/CNTs beads	Alkaline mixture	CR	450.4	5	20	Langmuir	Psedo-first-order	158
p (AAm)-CBp (AAm)-WB	MBA	Phenol	1112	10	50	Langmuir	Pseudo-first-order	159
k-C-g-pAA/CNT	MBA	CV	118	5–8	200	Langmuir	—	160

Clay-based hydrogels

Natural clays and their improved forms have recently been used for removing pollutants from water.¹⁶¹ The most commonly used clays, especially for treating toxic metals and dyes, are modified kaolinite and montmorillonite.¹⁶² However, these clays are difficult to regenerate and reuse because of their colloidal dimensions.¹⁶³ This prompted the functionalization of these clays, for example, the modification of montmorillonite to form Cloisite 30B clay. In a study where C30B clay was incorporated onto polypropylene grafted with maleic anhydride (PP-g-MA) and thermoplastic starch (TPS), it was reported that the biodegradability of the materials was improved.¹⁶⁴ Modification of adsorbents by introducing functionalized clay components may improve both the physical and chemical properties of adsorbents.^163,164 Other modifications with clay results improve the number of adsorbing active sites, enhanced porosity and low levels of mineral impurities.¹⁶⁴ In a recent study, C30B was mixed with a culture obtained from an anaerobic sludge to remove hexavalent chromium, where the removal capacity of nearly 100% was obtained.¹⁶⁵ Peng et al.¹⁶⁶ prepared cellulose-MMT hydrogels for removing MB. The hydrogels had a maximum removal capacity of 1065 mg/g (Table 4). Their viscoelasticity studies from the sweep measurements (Figure 11(a)) showed that when G′ < G″ the cellulose-MMT systems were in a viscous liquid form; however with increasing time when G′ > G″, the materials were in a gel form. Figure 11(b) in this case revealed that increasing clay content decreased the gel formation. Figure 11(c) revealed that the storage moduli (G′) of hydrogels containing clay was higher than that of unmodified hydrogel and was proportional to the clay content from 10 to 15 wt.%. The incorporation of clay, however, increased the gel strength from 0.3 KPa to 4.7 KPa as shown in Figure 11(d) and (e), which was approximately 16 times higher. Furthermore, the study reported that an increase in clay content from 10–15 wt.% reduced the swelling capacity of the hydrogel (Figure 9(f)), reportedly due to a high degree of crosslinking. Increasing the crosslinking density of the hydrogel enhanced mechanical properties.¹⁶⁶

Table 4.

Clay-based adsorbent hydrogels and their adsorption properties in removing contaminants from aqueous solution.

Adsorbent	Cross-linker	Dye	Adsorption parameter					Reference
Adsorbent	Cross-linker	Dye	q_e (mg/g)	pH	Dosage (mg)	Isotherm	Kinetics	Reference
CMC-MMT	ECH	MB	1065	1–10	500	Langmuir	Pseudo-second-order	166
K-Carra-AAm-MMT	APS	MB	49.52	7	50	Langmuir	Pseudo-second-order	167
P (AA-co-AMPS)/MMT	MBA	MB	192	10	—	Redlich–Peterson	Pseudo-second-order	168
CS-g-IA/BT	MBA	MB	500	6	30	Langmuir	Pseudo-second-order	169

Figure 11.

‘Properties of cellulose−clay nanocomposite hydrogels. (a) Time dependence of storage modulus (G′) and loss modulus (G″) for different gelation systems at 60°C. The data are shifted along the y-axis to avoid overlapping. (b) Gelation time. (c) Storage modulus at 1 h. (d) Compressive-strain curves. (e) Photographs of M-5. (f) The swelling ratio in distilled water’.¹⁴⁴

Metal oxide–based hydrogels

Metal oxide–based nanoparticles have been reported to have a high density and restricted size, which are responsible for their very interesting and unique chemical and physical properties.^170,171 Examples of metal oxides include titanium dioxide (TiO₂), iron oxide (Fe₃O₄), magnesium oxide (MgO) and aluminium oxide (Al₂O₃). Owing to their non-toxic nature, high surface area, high chemical stability and economical friendliness, Fe₃O₄ nanoparticles are widely used for the removal of toxic metals and organic pollutants from water.^{170,171,172,173} Ion-oxide and zinc oxide nanoparticles are some of the most frequently used metal oxides in treating dyes from aqueous solutions.¹⁷⁴

Magnetic (Fe₃O₄) nanocomposite hydrogels

Magnetite (Fe₃O₄) also known as black iron oxide amongst other transition metals has the strongest magnetism and is stable at ambient temperatures.¹⁷⁵ Magnetite is prepared from the co-precipitation of iron oxide salts that result in an inverse spinel crystal structure consisting of half of the Fe³⁺ in tetrahedral coordination and the other half Fe²⁺ ions in octahedral coordination (Figure 12).^176,177 The co-precipitation method is the most useful and suitable technique in preparing magnetite at both lab-scale and industrial scale.¹⁷⁸

Figure 12.

The inverse spinel structure of magnetite Fe₃O₄.¹⁵⁵

Due to their cheap synthesis costs, susceptibility, stability, high porosity, magnetic properties, biocompatibility and easy chemical modification, MNPs have attracted much use in the wastewater treatment field.^173–177 The introduction of MNPs into polymer structures to produce nanocomposite hydrogels leads to a hybrid hydrogel with advantages of both components, thus improving chemical and physical properties. An example of such hybridized hydrogel is Fe₃O₄-g-pAA hydrogel synthesized via radical polymerization in the presence of MBA cross-linker, which resulted in a highly adsorptive hydrogel of 507.7 mg/g removal capacity for MB¹⁷⁹ as shown in Table 5. However, according to Flory’s theory, the swelling degree of a hydrogel depends on the density of crosslinking, the ionic osmotic pressure and the attraction of the gel for the liquid.¹⁸⁰ When the crosslinking density is high, the space between the polymer chains decreases making the gel to be stiff due to small nonexpendable pores.¹⁸⁰ Additionally, an increase for MNPs increases the thermal properties but consequently reduces the swelling capacity as the Fe³⁺ from the incorporated MNPs may act as a physical crosslinking agent.¹⁷⁹ The greatest advantage of incorporating MNPs into the hydrogel matrix is the improved stability and easy recovery of the material after application.¹⁸¹

Table 5.

Metal oxide–based adsorbents for organic dyes removal.

Adsorbent	Cross-linker	Dye	Adsorption parameter					References
Adsorbent	Cross-linker	Dye	q_e (mg/g)	pH	Dosage (mg)	Isotherm	Kinetics	References
PAA-grafted MNPs	MBA	MB	507.7	4	20	Langmuir	Pseudo-second-order	179
Fe₃O₄-CS-Clay	Clay	MB	82	9–12	500	—	—	181
SA-PAAc/ZnO	MBA	MB	1530	6–9	10	Langmuir	Pseudo-second-order	182
Fe₃O₄/p (Am-co-Na Ac)	MBA	MB	641	7	50	Langmuir	Pseudo-second-order	170
CMC coated Fe₃O₄@SiO₂ nanocomposite	—	MB	22.7	11	30	Langmuir	Pseudo-second-order	183
Fe₃O₄/CA gel beads	CaCl₂	MV	713	—	20–40	modified Langmuir–Freundlich	Pseudo-second-order	184
ZnO–clay–alginate hydrogel beads	Clay	CR	546.89	5–7	200	Temkin	Pseudo-first-order	185
ZnO-PPy nanocomposite	—	BG	140.8	—	50–200	Langmuir	Pseudo-second-order	186
chitosan/silica/ZnO NC	—	MB	293.3	—	—	Langmuir	Pseudo-second-order	187

Zinc oxide–based hydrogels

Zinc oxide (ZnO) can be found in nature as a zincite mineral; however, the majority of it is prepared synthetically. Its crystal structure can be found in a hexagonal wurtzite form or cubic zinc blende form (Figure 13). The form that is most stable and commonly found at ambient temperature is the wurtzite structure.¹⁸⁸ ZnO is commonly used for treating skin-related problems such as nappy rash, dandruff and incorporation in ointments used in wound dressing.¹⁸⁸ Other applications of ZnO include use in catalysis, batteries, sensors and adsorption of contaminants.^189–192 Khan et al.¹⁹³ reported their application as adsorbent material in a study, where a guar gum adsorbent hydrogel incorporated with ZnO nanoparticles was used for removing chromium (VI) from water. The group reported that incorporating ZnO nanoparticles improved the recovery of the adsorbent from the aqueous solution after the removal of Cr (VI). In another study, CMC hydrogel was modified with ZnO for antimicrobial activity, which was influenced by their inexpensiveness and lacks colour.¹⁹⁴ Therefore, looking at these properties, the ZnO would be ideal for preparing hydrogels for adsorbing dyes.

Figure 13.

Crystal structure of zinc oxide.¹⁶²

Titanium dioxide–based hydrogels

Titanium dioxide is a naturally occurring oxide of titanium. It exists in three crystalline phases, namely, brookite, anatase and rutile.¹⁹⁵ The rutile phase is thermodynamically stable compared to the anatase and brookite phases, which are metastable.¹⁹⁵ The advantages of TiO₂ are that it is non-toxic, chemically stable, highly reactive, biocompatible, cost-effective, contains electrochemical properties and is safe to produce.^195,196 In addition, TiO₂ possesses antimicrobial and UV-protection properties.¹⁹⁶ Applications of titanium dioxide include the use of a photocatalyst for water-dye degradation, in food and pharmaceuticals as a white colourant, in sensors, ceramic industries, inorganic membranes and biological implants.^195,196 For example in a study by Kangwansupamonkon et al.,¹⁹⁷ TiO₂/poly [acrylamide-co-(acrylic acid)] hydrogel was reported to have 91.6% removal for MB using 5% TiO₂ as an inorganic initiator. Another study by Ari et al.¹⁹⁵ used P (AMPS)-TiO₂ composite hydrogel for photocatalytic degradation of MB and reported high catalytic performance and high thermal stability due to the incorporated TiO₂ nanoparticles. The group also reported over 80% removal capacity for MB after repeated cycles of more than five, hence improved reusability and regeneration. Another study by Han et al.¹⁹⁸ also reported excellent performance in terms of regeneration, self-cleaning and recovery of the prepared hydroxyethyl-titanium dioxide-CMC (HEC-TiO₂-CMC) hydrogel cage for the removal of MB.¹⁹⁸ Adsorption of MB onto polyacrylamide-grafted gum ghatti (PAAm-g-Gg)/TiO₂ hydrogel nanocomposite prepared by Mittal and Ray was reported to be greatly dependent on the adsorbent dose, the ionic strength, pH and temperature of the solution.¹⁹⁹ The pair reported a removal capacity of 1305.5 mg g⁻¹ dominated by pseudo-second-order rate model and Langmuir adsorption isotherm.¹⁹⁹ The incorporation of TiO₂ NPs onto sodium alginate cross-linked polyacrylic acid (SA-cl-poly (AA) hydrogel) was reported to have improved removal capacity from 80% using hydrogel with no TiO₂ to 94.1% and 99.4% for nanocomposites containing 0.05 and 0.2 g of TiO₂ NPs, respectively.²⁰⁰ XRD patterns from this study showed the disappearance of some TiO₂ peaks after MB absorption indicating a reduction in the crystallinity of the nanocomposite that is said to be caused by the trapping of dye molecules within the micropores and macropores of the absorbent.²⁰⁰

In recent years, efforts have been made to confirm the effectiveness of using NCHs as adsorbent for wastewater treatment. In this context, Malatji and co-workers fabricated clay/magnetic hydrogel nanocomposites via free-radical polymerization method; their material exhibited improved thermal stability and mechanical strength in comparison to the pure hydrogel. However, their adsorption studies showed that the incorporation of Fe₃O₄ and Cloisite 30B in the polymeric hydrogel networks reduced the adsorption capacity. The prepared clay/magnetic hydrogel nanocomposites exhibited an adsorption capacity of 1081.60 mg/g, which is low when compared to the adsorption capacity (1109.55 mg/g) of pure hydrogel.²⁰¹ Surprisingly, Zhang et al.²⁰² prepared PAAm/CS/Fe₃O₄ composite hydrogel via in situ polymerization for the removal of MB dye from aqueous solution, and the obtained results demonstrated that the incorporation of Fe₃O₄ magnetic nanoparticles in the hydrogel matrices improved both swelling and adsorption capacity.²⁰² Another study by Makhado et al.,¹⁸² synthesized sodium alginate/ZnO hydrogel nanocomposites by the in situ free-radical polymerization method. They applied the as-prepared material as an adsorbent for MB dye removal from the aqueous phase. According to their results, sodium alginate/ZnO hydrogel nanocomposites showed high adsorption capacity (1529.6 mg/g) for MB in contrast to adsorption capacity (1129.0 mg/g) exhibited by the pure hydrogel. In addition, sodium alginate/ZnO hydrogel nanocomposites displayed relatively high thermal stability and excellent recycling performance than pure hydrogel. Nonetheless, the incorporation of ZnO NPs in the SA-poly (AA) hydrogel matrix increased the swelling capacity, which sequentially led to a decrease in the mechanical strength.¹⁸² Table 6 shows the advantages and disadvantages of variously reported hydrogel nanocomposites in the removal of MB from wastewater.^199–205

Table 6.

Advantages and disadvantages of several hydrogel nanocomposites for the removal of methylene blue from aqueous solution.

Adsorbent	Filler	Advantages	Disadvantages	References
(PAAm-g-Gg)/TiO₂ hydrogels nanocomposite	TiO₂ NPs	Recyclability, adsorption capacity	—	199
SA-cl-poly (AA)-TiO₂ O/I-hydrogels nanocomposite	TiO₂ NPs	Mechanical properties and adsorption capacity	Swelling capacity	200
CMC-p (AA)/Fe₃O₄ hydrogels nanocomposite	Fe₃O₄ NPs	Mechanical properties and thermal stability	Swelling and adsorption capacity	201
Poly (acrylamide-chitosan)/Fe₃O₄ hydrogels	Fe₃O₄ NPs	Adsorption capacity, low cost and swelling capacity	—	202
Sodium alginate/ZnO hydrogel nanocomposite	ZnO NPs	Thermal stability, swelling and adsorption capacity	Mechanical properties	182
SA/p (AAc)/o-MWCNTs hydrogels nanocomposite	o-MWCNTs	Thermal stability, swelling and adsorption capacity	Mechanical properties	203
GK-cl-P (AA-cl-AAM)/SiO₂ nanocomposite	SiO₂ NPs	Surface area, adsorption capacity	Pore size	204
GumT-cl-HEMA/TiO₂ hydrogel	TiO₂ NPs	Adsorption capacity, surface area, thermal stability and regeneration	Swelling capacity	205

Conclusions

This review discusses recent studies applied for removing MB from aqueous solution using biopolymer-based hydrogel nanocomposites. Owing to various advantages such as low cost and easy design, the adsorption method is recognized as the most promising treatment technique for the removal of MB dye. This work discussed the principle behind the adsorption method, common adsorbent materials used and its advantages. We also briefly explained the hydrogels and methods to improve their properties. Three isothermal models: Langmuir, Freundlich and Temkin models have been thoroughly explained with their respective principles. From this review, it was observed that the preparation of hydrogels can be affected by various factors and its removal capacity is affected by pH, temperature and dye concentration. This contribution emphasized the importance of incorporating metal oxide nanoparticles in hydrogels for the removal of dyes and also their advantages and disadvantages towards the gel structure and properties. Concerning the research up to date, it has been observed that the realization of hydrogels for practical purposes needs more research, especially the preparation of hydrogel nanocomposites with the ability to remove organic contaminants such as dyes. It was seen that both magnetic nanoparticles and ZnO nanoparticles have contributed greatly to improving stability and enabling easy separation of adsorbent materials after application. Although the actual wastewaters are complex to be treated because they possess various ions and pollutants, it is more pivotal to conduct analysis on wastewater for adsorption studies using the actual industrial water samples. This is mainly because the adsorbent performance may be noticeably different from the one carried out in batch mode in the laboratory.

Footnotes

Declaration of conflicting interests

The author(s) declared no potential conflicts of interest with respect to the research, authorship, and/or publication of this article.

Funding

The author(s) disclosed receipt of the following financial support for the research, authorship, and/or publication of this article: The authors immensely acknowledge the financial support from the National Research Foundation (NRF) (Grant Nos. 116679, 117727, and 118113), Sasol Foundation and University of Limpopo, South Africa.

ORCID iD

Kwena D Modibane

References

Gupta

Ali

Saleh

, et al. Chemical treatment technologies for waste-water recycling-an overview. RSC Adv 2012; 2: 6380–6388.

Muller

. Understanding the origins of Cape Town’s water crisis. Civil Eng 2017; 2017(5): 11–16.

Park

Ayoko

Frost

. Application of organoclays for the adsorption of recalcitrant organic molecules from aqueous media. J Colloid Interf Sci 2011; 354(1): 292–305.

Abu Shmeis

. Water chemistry and microbiology. Compr Anal Chem 2018; 81: 1–56.

Bodzek

. Membrane technologies for the removal of micropollutants in water treatment. Advances in Membrane Technologies for Water Treatment: Materials, Processes and Applications. Woodhead Publishing Series in Energy, 2015, pp. 465–517.

Yagub

Sen

Afroze

, et al. Dye and its removal from aqueous solution by adsorption: a review. Adv Colloid Interf Sci 2014; 209: 172–184.

Liu

Omer

Ouyang

X-k

. Adsorptive removal of cationic methylene blue dye using carboxymethyl cellulose/k-carrageenan/activated montmorillonite composite beads: isotherm and kinetic studies. Int J Biol Macromol 2018; 106: 823–833.

Dawood

Sen

. Review on dye removal from its aqueous solution into alternative cost effective and non-conventional adsorbents. J Chem Process Eng 2014; 1(1): 1–11.

Varaprasad

Jayaramudu

Sadiku

. Removal of dye by carboxymethyl cellulose, acrylamide and graphene oxide via a free radical polymerization process. Carbohydr Polym 2017; 164: 186–194.

10.

Makhado

Pandey

Nomngongo

, et al. Preparation and characterization of xanthan gum-cl-poly(acrylic acid)/o-MWCNTs hydrogel nanocomposite as highly effective re-usable adsorbent for removal of methylene blue from aqueous solutions. J Colloid Interf Sci 2018; 513: 700–714.

11.

Arami

Limaee

Mahmoodi

, et al. Equilibrium and kinetics studies for the adsorption of direct and acid dyes from aqueous solution by soy meal hull. J Hazard Mater 2006; 135(1–3): 171–179.

12.

Ukaogo

Ewuzie

Onwuka

. Environmental pollution: causes, effects, and the remedies. In: Microorganisms for sustainable environment and health. 2020, pp. 419–429.

13.

Adegoke

Bello

. Dye sequestration using agricultural wastes as adsorbents. Water Resour Industry 2015; 12: 8–24.

14.

Nascimben

László

Hodúr

, et al. Photocatalytic membrane filtration and its advantages over conventional approaches in the treatment of oily wastewater: a review. Asia‐Pac J Chem Eng 2020; 15(5): e2533.

15.

Thamaraiselvan

Noel

. Membrane processes for dye wastewater treatment: recent progress in fouling control. Crit Rev Environ Sci Technol 2015; 45(10): 1007–1040.

16.

Wawrzkiewicz

Hubicki

. Anion exchange resins as effective sorbents for removal of acid, reactive, and direct dyes from textile wastewaters. In: Ion Exchange-Studies and Applications. 2015, pp. 37–72.

17.

Priya

Stanly

Kavitharani

, et al. Highly effective photocatalytic degradation of methylene blue using PrO2-MgO nanocomposites under UV light. Optik 2020; 206: 164318.

18.

Shaban

Abukhadra

Ibrahim

, et al. Photocatalytic degradation and photo-Fenton oxidation of Congo red dye pollutants in water using natural chromite-response surface optimization. Appl Water Sci 2017; 7(8): 4743–4756.

19.

Riera-Torres

Gutiérrez

M-C

. Colour removal of three reactive dyes by UV light exposure after electrochemical treatment. Chem Eng J 2010; 156(1): 114–120.

20.

Laghrib

Bakasse

Lahrich

et al. Advanced oxidation processes: photo-electro-Fenton remediation process for wastewater contaminated by organic azo dyes. Int J Environ Anal Chem 2020; 1–16, doi:10.1080/03067319.2020.1711892.

21.

Ashraf

Abid

Shahid

, et al. Methods for the treatment of wastewaters containing dyes and pigments. In: Water Pollution and Remediation: Organic Pollutants. 2021, pp. 597–661.

22.

Crane

Sapsford

. Tunable formation of copper metal, oxide, chloride and hydroxyl chloride nanoparticles from aqueous copper solutions using nanoscale zerovalent iron particles. Nanomater Nanotechnology 2019; 9: 1–16.

23.

Nzila

. Biodegradation of high-molecular-weight polycyclic aromatic hydrocarbons under anaerobic conditions: overview of studies, proposed pathways and future perspectives. Environ Pollut 2018; 239: 788–802.

24.

Okoniewska

. Removal of selected dyes on activated carbons. Sustainability 2021; 13(8): 4300.

25.

Salleh

MAM

Mahmoud

Karim

WAWA

, et al. Cationic and anionic dye adsorption by agricultural solid wastes: a comprehensive review. Desalination 2011; 280(1–3): 1–13.

26.

Katheresan

Kansedo

Lau

. Efficiency of various recent wastewater dye removal methods: a review. J Environ Chem Eng 2018; 6: 4676–4697.

27.

Rathi

Kumar

. Application of adsorption process for effective removal of emerging contaminants from water and wastewater. Environ Pollut 2021; 280: 116995.

28.

Mohammadzadeh Pakdel

Peighambardoust

. A review on acrylic based hydrogels and their applications in wastewater treatment. J Environ Manage 2018; 217: 123–143.

29.

Moosavi

Lai

Gan

, et al. Application of efficient magnetic particles and activated carbon for dye removal from wastewater. ACS Omega 2020; 5(33): 20684–20697.

30.

Amaya

Medero

Tancredi

, et al. Activated carbon briquettes from biomass materials. Bioresour Technol 2007; 98(8): 1635–1641.

31.

Ioannidou

Zabaniotou

. Agricultural residues as precursors for activated carbon production-A review. Renew Sustain Energ Rev 2007; 11(9): 1966–2005.

32.

Geçgel

Özcan

Gürpınar

GÇ

. Removal of methylene blue from aqueous solution by activated carbon prepared from pea shells (Pisum sativum). J Chem 2013; 2013: 1–9.

33.

Park

Lee

Hong

, et al. Regeneration of activated carbons spent by waste water treatment using KOH chemical activation. Appl Sci 2019; 9(23): 5132.

34.

Zhang

Wang

Zhang

, et al. Adsorption of Pb(II) and Cd(II) by magnetic activated carbon and its mechanism. Sci The Total Environ 2021; 757: 143910.

35.

Yang

Zhao

Yang

, et al. Xanthate modified magnetic activated carbon for efficient removal of cationic dyes and tetracycline hydrochloride from aqueous solutions. Colloids Surf A: Physicochem Eng Aspects 2021; 615: 126273.

36.

Nasrollahzadeh

Sajjadi

Iravani

, et al. Starch, cellulose, pectin, gum, alginate, chitin and chitosan derived (nano)materials for sustainable water treatment: a review. Carbohydr Polym 2020; 251: 116986.

37.

Bealer

Onissema-Karimu

Rivera-Galletti

, et al. Protein-polysaccharide composite materials: fabrication and applications. Polymers 2020; 12(2): 464.

38.

Russo

Fucile

Giacometti

, et al. Sustainable removal of contaminants by biopolymers: a novel approach for wastewater treatment. Current state and future perspectives. Processes 2021; 9(4): 719.

39.

Crini

Torri

Lichtfouse

, et al. Cross-Linked Chitosan-based hydrogels for dye removal. In: Sustainable Agriculture Reviews. Cham: Springer, 2019, Vol. 36, pp. 381–425.

40.

Zhou

Liu

, et al. Removal of methylene blue dyes from wastewater using cellulose-based superadsorbent hydrogels. Polym Eng Sci 2011; 51(12): 2417–2424.

41.

Makhado

Pandey

Nomngongo

, et al. Xanthan gum-cl-poly (acrylic acid)/reduced graphene oxide hydrogel nanocomposite as adsorbent for dye removal. In: 9th Int’l conference on advances in science, engineering, technology and waste management (ASETWM-17), Parys, South Africa, 27–28 November 2017, 2017, pp. 159–164.

42.

Zhi

Gao

Feng

. Hydrogel-based gas sensors for NO2 and NH3. ACS Sensors 2020; 5(3): 772–780.

43.

Alvarez-Lorenzo

Grinberg

Burova

, et al. Stimuli-sensitive cross-linked hydrogels as drug delivery systems: impact of the drug on the responsiveness. Int J Pharmaceutics 2020; 579: 119157.

44.

Mitura

Sionkowska

Jaiswal

. Biopolymers for hydrogels in cosmetics: review. J Mater Sci Mater Med 2020; 31(6): 50.

45.

Crini

Lichtfouse

Wilson

, et al. Adsorption-oriented processes using conventional and non-conventional adsorbents for wastewater treatment. Environ Chem Sustainable World 2019; 18: 23–71.

46.

Crini

Morcellet

. Synthesis and applications of adsorbents containing cyclodextrins. J Sep Sci 2002; 25: 789–813.

47.

Lavrenko

Podchernyaeva

Shchur

. Nanostructured materials features of physical and chemical adsorption during interaction polycrystalline nanocrystalline mater gases 2018; 56(517): 504–511.

48.

Yan

Chu

Zhang

, et al. Determination of adsorption isotherm parameters with correlated errors by measurement error models. Chem Eng J 2015; 281: 921–930.

49.

Foo

Hameed

. Insights into the modeling of adsorption isotherm systems. Chem Eng J 2010; 156(1): 2–10.

50.

Milonjic

. A consideration of the correct calculation of thermodynamic parameters of adsorption. J Serbian Chem Soc 2007; 72: 1363–1367.

51.

Hintermeyer

Lacour

Padilla

, et al. Separation of the chromium (iii) present in a tanning wastewater by means of precipitation, reverse osmosis, and adsorption. Latin Am Appl Res 2008; 71: 63–71.

52.

Hibbitts

Iglesia

. Hydrogen chemisorption isotherms on platinum particles at catalytic temperatures: Langmuir and two-dimensional gas models revisited. J Phys Chem 2019; 123: 8447–8462.

53.

Balis

Zaky

Perganti

, et al. Dye sensitization of Titania compact layer for efficient and stable perovskite solar cells. ACS Appl Energy Mater 2018; 1: 6161–6171.

54.

Worch

55.

Monama

Mdluli

Mashao

, et al. Palladium deposition on copper(II) phthalocyanine/metal organic framework composite and electrocatalytic activity of the modified electrode towards the hydrogen evolution reaction. Renew Energ 2018; 119: 62–72.

56.

Xia

Wei

Wan

. Conducting polymer nanostructures and their application in biosensors. J Colloid Interf Sci 2010; 341: 1–11.

57.

Padash

Nasab

Nasrabadi

, et al. Is it possible to use X 12 Y 12 (X = Al, B, and Y = N, P) nanocages for drug-delivery systems? A DFT study on the adsorption property of 4-aminopyridine drug. Appl Phys A 2018; 124(9): 1–11.

58.

Song

Shi

, et al. Reinforced-concrete structured hydrogel microspheres with ultrahigh mechanical strength, restricted water uptake, and superior adsorption capacity. ACS Sustainable Chem Eng 2018; 6: 5950–5958.

59.

Cheng

Show

P-L

Lau

, et al. New prospects for modified algae in heavy metal adsorption. Trends Biotechnol 2019; 37(11): 1255–1268.

60.

Sham

AYW

Notley

. Adsorption of organic dyes from aqueous solutions using surfactant exfoliated graphene. J Environ Chem Eng 2018; 6(1): 495–504.

61.

Jawad

Norrahma

SSA

Hameed

, et al. Chitosan-glyoxal film as a superior adsorbent for two structurally different reactive and acid dyes: adsorption and mechanism study. Int J Biol Macromol 2019; 135: 569–581.

62.

Sun

C-J

Sun

L-Z

Sun

X-X

. Graphical evaluation of the favorability of adsorption processes by using conditional langmuir constant. Ind Eng Chem Res 2013; 52: 14251–14260.

63.

Boutahala

Sahnoun

Gomri

. Adsorption characteristics, isotherm, kinetics, and diffusion of modified natural bentonite for removing the 2, 4, 5-trichloropheno. Appl Clay Sci 2014; 90: 81–87.

64.

D-q

Wang

Guo

Z-g

, et al. Pectin gels cross-linked by Ca 2+: An efficient material for methylene blue removal. J Mol Liquids 2017; 238: 36–42.

65.

State

. Langmuir, Freundlich, Temkin and Dubinin – Radushkevich isotherms studies of equilibrium sorption of Zn²⁺ unto phosphoric acid modified rice husk. J Appl Chem 2012; 3(1): 38–45.

66.

Seidel-morgenstern

. Experimental determination of single solute and competitive adsorption isotherms. J Chromatogr A 2004; 1037: 255–272.

67.

Oguz Erdogan

. Freundlich, Langmuir, Temkin and Harkins-Jura Isotherms Studies of H2 adsorption on porous adsorbents. Chem Chem Technol 2019; 13(2): 129–135.

68.

Losso

Marshall

, et al. Freundlich adsorption isotherms of agricultural by-product-based powdered activated carbons in a geosmin-water system. Bioresour Technol 2002; 85: 131–135.

69.

Azizian

. Kinetic models of sorption: a theoretical analysis. J Colloid Interf Sci 2004; 276: 47–52.

70.

Mckay

. Pseudo-second order model for sorption processes. Process Biochem 1999; 34: 451–465.

71.

Salvestrini

. Analysis of the Langmuir rate equation in its differential and integrated form for adsorption processes and a comparison with the pseudo first and pseudo second order models. React Kinet, Mech Catal 2018; 123(2): 455–472.

72.

Yusuff

Khim

Zin

, et al. Isotherms and thermodynamics of CO₂ adsorption on thermally treated alum sludge. Nat Environ Pollut Technol 2019; 18(1): 247–250.

73.

Cai

Jin

, et al. Adsorption mechanisms of five bisphenol analogues on PVC microplastics. Sci Total Environ 2019; 650: 671–678.

74.

Zhao

Bai

, et al. The reaction thermodynamics during plating Al on graphene process. Materials (Basel) 2019; 12(2): 330.

75.

Gómez

Larrechi

Callao

. Kinetic and adsorption study of acid dye removal using activated carbon. Chemosphere 2007; 69: 1151–1158.

76.

Malik

Ramteke

Wate

. Adsorption of malachite green on groundnut shell waste based powdered activated carbon. Waste Manage 2007; 27: 1129–1138.

77.

Ismadji

Sudaryanto

Hartono

, et al. Activated carbon from char obtained from vacuum pyrolysis of teak sawdust: pore structure development and characterization. Bioresour Technol 2005; 96: 1364–1369.

78.

Lillo-Rodensas

Carzrola-Ameros

Linares-Solano

. Chemical reactions between carbons and NaOH and KOH – an insight into chemical activation mechanisms. Carbon 2003; 41: 265–267.

79.

Kyzas

Bomis

Kosheleva

, et al. Nanobubbles effect on heavy metal ions adsorption by activated carbon. Chem Eng J 2019; 356: 91–97.

80.

Mittal

Ray

Okamoto

. Recent progress on the design and applications of polysaccharide-based graft copolymer hydrogels as adsorbents for wastewater purification. Macromol Mater Eng 2016; 301: 496–522.

81.

Moreno-López

González-López

Manríquez-González

, et al. Evaluation of the Cr(VI) adsorption performance of xanthate polysaccharides supported onto agave fiber-LDPE foamed composites. Water Air Soil Pollut 2019; 230: 133.

82.

Largitte

Pasquier

. A review of the kinetics adsorption models and their application to the adsorption of lead by an activated carbon. Chem Eng Res Des 2016; 109: 495–504.

83.

Gupta

Suhas . Application of low-cost adsorbents for dye removal - A review. J Environ Manage 2009; 90(8): 2313–2342.

84.

Guilherme

Aouada

Fajardo

, et al. Superabsorbent hydrogels based on polysaccharides for application in agriculture as soil conditioner and nutrient carrier: a review. Eur Polym J 2015; 72: 365–385.

85.

Zheng

Monty

Linhardt

. Polysaccharide-based nanocomposites and their applications. Carbohydr Res 2015; 405: 23–32.

86.

Tally

Atassi

. Optimized synthesis and swelling properties of a pH-sensitive semi-IPN superabsorbent polymer based on sodium alginate-g-poly (acrylic acid-co-acrylamide) and polyvinylpyrrolidone and obtained via microwave irradiation. J Polym Res 2015; 22: 181.

87.

Mohammadzadeh Pakdel

Peighambardoust

. A review on acrylic based hydrogels and their applications in wastewater treatment. J Environ Manage 2018; 217: 123–143.

88.

Essawy

Ghazy

MBM

El-Hai

, et al. Superabsorbent hydrogels via graft polymerization of acrylic acid from chitosan-cellulose hybrid and their potential in controlled release of soil nutrients. Int J Biol Macromol 2016; 89: 144–151.

89.

Chen

Liu

Jin

, et al. Dye adsorption and photo-induced recycling of hydroxypropyl cellulose/molybdenum disulfide composite hydrogels. Carbohydr Polym 2017; 167: 36–43.

90.

Benhalima

Ferfera-Harrar

Lerari

. Optimization of carboxymethyl cellulose hydrogels beads generated by an anionic surfactant micelle templating for cationic dye uptake: Swelling, sorption and reusability studies. Int J Biol Macromol 2017; 105: 1025–1042.

91.

Song

, et al. Control of gypsum-dominated scaling in reverse osmosis system using carboxymethyl cellulose. J Membr Sci 2019; 577: 20–30.

92.

Shi

Tao

Cui

. Evaluation of nitriloacetic acid modified cellulose film on adsorption of methylene blue. Int J Biol Macromol 2018; 114: 400–407.

93.

Salama

. Preparation of CMC-g-P(SPMA) super adsorbent hydrogels: Exploring their capacity for MB removal from waste water. Int J Biol Macromol 2018; 106: 940–946.

94.

Colombo

Bettini

Santi

, et al. Swellable matrices for controlled drug delivery: gel-layer behaviour, mechanisms and optimal performance. Pharm Sci Technol Today 2000; 3: 198–204.

95.

Son

Y-R

Rhee

Park

S-J

. Influence of reduced graphene oxide on mechanical behaviors of sodium carboxymethyl cellulose. Composites Part B: Eng 2015; 83: 36–42.

96.

Kono

. Characterization and properties of carboxymethyl cellulose hydrogels crosslinked by polyethylene glycol. Carbohydr Polym 2014; 106: 84–93.

97.

Zhu

Bao

Wei

, et al. Removal of toxic indigo blue with integrated biomaterials of sodium carboxymethyl cellulose and chitosan. Int J Biol Macromol 2016; 91: 409–415.

98.

Petri

DFS

. Carboxymethyl cellulose/poly (acrylic acid) interpenetrating polymer network hydrogels as multifunctional adsorbents. Cellulose 2019; 26(1): 597–615.

99.

Begum

Mahbub

MKB

. Effectiveness of carboxymethyl cellulose for the removal of methylene blue from aqueous solution. Dhaka Univ J Sci 2013; 61(2): 193–198.

100.

Lee

Park

Roh

, et al. Preparation and characterization of superabsorbent polymers based on starch aldehydes and carboxymethyl cellulose. Polymers 2018; 10(605): 1–16.

101.

Saputra

Qadhayna

Pitaloka

. Synthesis and characterization of carboxymethyl cellulose (cmc) from water hyacinth using ethanol-isobutyl alcohol mixture as the solvents. Int J Chem Eng Appl 2014; 5(1): 36–40.

102.

Huang

CMY

Chia

Lim

CSS

, et al. Cellulose chemistry and technology synthesis and characterisation of carboxymethyl cellulose from various agricultural wastes. Cellul Chem Technol 2017; 51: 665–672.

103.

Nizam El-Din

Abd Alla

El-naggar

AWM

. Swelling and drug release properties of acrylamide/carboxymethyl cellulose networks formed by gamma irradiation. Radiat Phys Chem 2010; 79(6): 725–730.

104.

Tønnesen

Karlsen

. Alginate in drug delivery systems. Drug Deve Ind Pharm 2002; 28(6): 621–630.

105.

Ertesvag

Valla

. Biosynthesis and applications of alginates. Polym Degrad Stab 1998; 59(1–3): 85–91.

106.

Cade

Rizvi

Peters

. Feasibility studies for the removal of heavy metals from solution using tailored bentonite. Hazardous and industrial wastes, Proceedings of the twenty-second mid-Atlantic industrial waste conference. Drexel University, 1990, pp. 77–79.

107.

Gupta

Abu-Ghannam

. Bioactive potential and possible health effects of edible brown seaweeds. Trends Food Sci Technol 2011; 22(6): 315–326.

108.

Liu

. Enhanced stability and mechanical strength of sodium alginate composite films. Carbohydr Polym 2017; 160: 62–70.

109.

Liu

Y-g

X-j

Wang

, et al. Photoreduction of Cr(VI) from acidic aqueous solution using TiO2-impregnated glutaraldehyde-crosslinked alginate beads and the effects of Fe(III) ions. Chem Eng J 2013; 226: 131–138.

110.

Chen

, et al. Adsorption of lysozyme by alginate/graphene oxide composite beads with enhanced stability and mechanical property. Mater Sci Eng C 2018; 89: 25–32.

111.

Wang

Meng

, et al. Facile synthesis of low-cost magnetic biosorbent from peach gum polysaccharide for selective and efficient removal of cationic dyes. Int J Biol Macromol 2018; 107: 1871–1878.

112.

Wang

. Synthesis and swelling properties of pH-sensitive semi-IPN superabsorbent hydrogels based on sodium alginate-g-poly (sodium acrylate) and polyvinylpyrrolidone. Carbohydr Polym 2010; 80(4): 1028–1036.

113.

Rashidzadeh

Olad

Salari

. The effective removal of methylene blue dye from aqueous solutions by NaAlg-g-poly(acrylic acid-co-acryl amide)/clinoptilolite hydrogel nanocomposite. Fibers Polym 2015; 16: 354–362.

114.

Sterner

Ribeiro

Gröndahl

, et al. Cyclic fractionation process for Saccharina latissima using aqueous chelator and ion exchange resin. J Appl Phycol 2017; 29(6): 3175–3189.

115.

Hefnawy

Ali

Allah

MMD

. Preparation and properties of a novel eco-friendly carboxymethylcellulose/k- carrageenan/graphene oxide gel beads for the removal of heavy metals from water. Chem Process Eng Res 2018; 58: 6–16.

116.

Ren

Gao

, et al. Efficient Pb(II) removal using sodium alginate-carboxymethyl cellulose gel beads: preparation, characterization, and adsorption mechanism. Carbohydr Polym 2016; 137: 402–409.

117.

Lan

Liu

. Preparation and properties of sodium carboxymethyl cellulose/sodium alginate/chitosan composite film. Coatings 2018; 8(8): 291.

118.

Shirsath

Patil

, et al. Removal of brilliant green from wastewater using conventional and ultrasonically prepared poly(acrylic acid) hydrogel loaded with kaolin clay: a comparative study. Ultrason Sonochem 2014; 20(3): 914–923.

119.

Makhado

Pandey

Ramontja

. Microwave assisted synthesis of xanthan gum-cl-poly (acrylic acid) based-reduced graphene oxide hydrogel composite for adsorption of methylene blue and methyl violet from aqueous solution. Int J Biol Macromol 2018; 119: 255–269.

120.

Garg

. Hydrogel: classification, properties, preparation and technical features. Asian J Biomater Res 2016; 2(6): 163–170.

121.

Çankaya

. Synthesis of graft copolymers onto starch and its semiconducting properties. Results Phys 2016; 6: 538–542.

122.

Ahmed

. Hydrogel: preparation, characterization, and applications: a review. J Adv Res 2015; 6(2): 105–121.

123.

Liang

Zhao

, et al. pH-responsive injectable hydrogels with mucosal adhesiveness based on chitosan-grafted-dihydrocaffeic acid and oxidized pullulan for localized drug delivery. J Colloid Interf Sci 2019; 536: 224–234.

124.

Singh

Kumar

Sanghi

. Use of microwave irradiation in the grafting modification of the polysaccharides - A review. Prog Polym Sci 2012; 37(2): 340–364.

125.

Makhado

Pandey

Nomngongo

, et al. Fast microwave-assisted green synthesis of xanthan gum grafted acrylic acid for enhanced methylene blue dye removal from aqueous solution. Carbohydr Polym 2017; 176: 315–326. DOI: 10.1016/j.carbpol.2017.08.093.

126.

Cook

Goodall

Khutoryanskaya

, et al. Microwave-assisted hydrogel synthesis: a new method for crosslinking polymers in aqueous solutions. Macromol Rapid Commun 2012; 33(4): 332–336.

127.

Anah

Astrini

. Influence of pH on Cr (VI) ions removal from aqueous solutions using carboxymethyl cellulose-based hydrogel as adsorbent. IOP Conf Ser Earth Environ Sci 2017; 60: 012010.

128.

Ismail

Irani

Ahmad

. Starch-based hydrogels: present status and applications. Int J Polym Mater Polyme Biomater 2013; 62(7): 411–420.

129.

Shen

Wen

, et al. Fast and highly efficient removal of dyes under alkaline conditions using magnetic chitosan-Fe (III) hydrogel. Water Res 2011; 45(16): 5200–5210.

130.

Liu

Gao

, et al. In situ forming hydrogels based on chitosan for drug delivery and tissue regeneration. Asian J Pharm Sci 2016; 11(6): 673–683.

131.

Kumar

Thakur

Alexander

, et al. Modified chitosan hydrogels as drug delivery and tissue engineering systems: present status and applications. Acta Pharm Sin B 2012; 2(5): 439–449.

132.

Song

Zhu

Chen

, et al. Temperature- and pH-sensitive nanocomposite gels with semi-interpenetrating organic/inorganic networks. Macromol Chem Phys 2008; 209(15): 1564–1575.

133.

Zhu

Xiong

Wang

, et al. High tensibility and pH-responsive swelling of nanocomposite hydrogels containing the positively chargeable 2-(dimethylamino) ethyl methacrylate monomer. Reactive Funct Polym 2010; 70(5): 267–271.

134.

Liu

Ren

, et al. The role of chemical and physical crosslinking in different deformation stages of hybrid hydrogels. Eur Polym J 2018; 100: 86–95.

135.

Shen

, et al. Self-healing pH-sensitive cytosine- and guanosine-modified hyaluronic acid hydrogels via hydrogen bonding. Polymer 2017; 108: 348–360.

136.

Huang

Jiao

, et al. A novel hydrogel with high mechanical strength: a macromolecular microsphere composite hydrogel. Adv Mater 2007; 19: 1622–1626.

137.

Sun

J-Y

Zhao

Illeperuma

WRK

, et al. Highly stretchable and tough hydrogels. Nature 2012; 489: 133–136.

138.

, et al. Low chemically cross-linked pam/c-dot hydrogel with robustness and superstretchability in both as-prepared and swelling equilibrium states. Macromolecules 2016; 49: 3174–3183.

139.

Rahmani

Sahraei

Ghaemy

. Preparation of spherical porous hydrogel beads based on ion-crosslinked gum tragacanth and graphene oxide: study of drug delivery behavior. Carbohydr Polym 2018; 194: 34–42.

140.

Eftekhari-sis

Rahimkhoei

Akbari

, et al. Cubic polyhedral oligomeric silsesquioxane nano-cross-linked hybrid hydrogels: synthesis, characterization, swelling and dye adsorption properties. Reactive Funct Polym 2018; 128: 47–57.

141.

Braun

. Origins and development of initiation of free radical polymerization processes. Int J Polym Sci 2009; 2009: 1–10.

142.

Chen

Zhong

Johnson

. Light-controlled radical polymerization: mechanisms, methods, and applications. Chem Rev 2016; 116: 10167–10211.

143.

Kamoun

Omer

Khattab

, et al. In-situ UV-photopolymerized PVA-g-GMA hydrogels for biomedical applications: I. Synthesis, Characterizations and Grafting Optimization. J Appl Pharm Sci 2018; 8(01): 034–042.

144.

Jung

Riahinezhad

Duever

, et al. Case studies with mathematical modeling of free-radical multi-component bulk/solution polymerizations: part 1. J Macromol Sci Part A 2015; 52(9): 659–698.

145.

Ranganathan

Joseph Bensingh

Abdul Kader

, et al. Synthesis and properties of hydrogels prepared by various polymerization reaction systems. In: Mondal M (ed) Cellulose-based superabsorbent hydrogels. polymers and polymeric composites: a reference series. Cham: Springer; 2018, 1–25.

146.

Dannert

Stokke

Dias

. nanoparticle-hydrogel composites: from molecular interactions to macroscopic behavior. Polymers 2019; 11(2): 275.

147.

Guanghui

Wang

, et al. Recent progress on study of hybrid hydrogels for water treatment. Colloids Surf A: Physicochem Eng Aspects 2013; 416: 86–94.

148.

Smith

Rodrigues

. Carbon-based nanomaterials for removal of chemical and biological contaminants from water: a review of mechanisms and applications. Carbon 2015; 91: 122–143.

149.

Biswas

Sen

Yeneneh

, et al. Synthesis and characterization of a novel Ca-alginate-biochar composite as efficient zinc (Zn2+) adsorbent: thermodynamics, process design, mass transfer and isotherm modeling. Sep Sci Technol 2019; 54(7): 1106–1124.

150.

Bai

Wang

, et al. A pH-sensitive graphene oxide composite hydrogel. Chem Commun 2010; 46: 2376–2378.

151.

Wang

Liu

Yuan

, et al. Non-covalently functionalized graphene strengthened poly (vinyl alcohol). Mater Des 2018; 139: 372–379.

152.

Fazil

Bangesh

Rehman

et al. Mechanical, thermal, and dielectric properties of functionalized graphene oxide/polyimide nanocomposite films. Nanomater Nanotechnology 2019; 9: 1–8.

153.

Elhissi

AMA

Ahmed

Hassan

, et al. Carbon nanotubes in cancer therapy and drug delivery. J Drug Deliv 2012; 2012: 1–10.

154.

Zhou

Tang

Zeng

, et al. Mesoporous carbon nitride based biosensor for highly sensitive and selective analysis of phenol and catechol in compost bioremediation. Biosens Bioelectron 2014; 61: 519–525.

155.

Demczyk

Wang

Cumings

, et al. Direct mechanical measurement of the tensile strength and elastic modulus of multiwalled carbon nanotubes. Mater Sci Eng A 2002; 334: 173–178.

156.

Aqel

El-nour

KMMA

Ammar

RAA

, et al. Carbon nanotubes, science and technology part (I) structure, synthesis and characterisation. Arabian J Chem 2012; 5(1): 1–23.

157.

Yang

Wan

Zheng

, et al. Surface functional groups of carbon-based adsorbents and their roles in the removal of heavy metals from aqueous solutions: a critical review. Chem Eng J 2019; 366: 608–621.

158.

Chatterjee

Lee

Woo

. Adsorption of Congo red by chitosan hydrogel beads impregnated with carbon nanotubes. Bioresour Technol 2010; 101(6): 1800–1806.

159.

Karakoyun

Kubilay

Aktas

, et al. Hydrogel-biochar composites for effective organic contaminant removal from aqueous media. Desalination 2011; 280: 319–325.

160.

Hosseinzadeh

. Synthesis of carrageenan/multi-walled carbon nanotube hybrid hydrogel nanocomposite for adsorption of crystal violet from aqueous solution. Polish J Chem Technol 2015; 17(2): 70–76.

161.

Cadena

Rizvi

Peters

162.

Gopal

Sen

. Adsorption of a few heavy metals on natural and modified kaolinite and montmorillonite: a review. Adv Colloid Interf Sci 2008; 140: 114–131.

163.

Yuan

Theng

BKG

North

, et al. Clays and clay minerals for pollution control. Dev Clay Sci 2013; 1: 624–675.

164.

Abreu

Oliveira

Machado

. Effect of clay mineral addition on properties of bio-based polymer blends. Appl Clay Sci 2015; 104: 277–285.

165.

Lytras

Argyropoulou

, et al. A novel two-phase bioreactor for microbial hexavalent chromium removal from wastewater. J Hazard Mater 2017; 336: 41–51.

166.

Peng

Zeng

, et al.. Superabsorbent cellulose-clay nanocomposite hydrogels for highly efficient removal of dye in water. ACS Sustainable Chem Eng 2016; 4: 7217–7224.

167.

Mahdavinia

Baghban

Zorofi

, et al. Kappa-carrageenan biopolymer-based nanocomposite hydrogel and adsorption of methylene blue cationic dye from water. J Mater Environ Sci 2014; 5(2): 330–337.

168.

Hosseinzadeh

Khoshnood

. Removal of cationic dyes by poly(AA-co-AMPS)/montmorillonite nanocomposite hydrogel. Desalin Water Treat 2016; 57(14): 6372–6383.

169.

Shakib

Dadvand Koohi

Kamran Pirzaman

. Adsorption of methylene blue by using novel chitosan-g-itaconic acid/bentonite nanocomposite - equilibrium and kinetic study. Water Sci Technol 2017; 75(8): 1932–1943.

170.

Atta

Akl

Youssef

, et al. Superparamagnetic core-shell polymeric nanocomposites for efficient removal of methylene blue from aqueous solutions. Adsorpt Sci Technol 2013; 31(5): 397–419.

171.

Pasqui

Atrei

Giani

, et al. Metal oxide nanoparticles as cross-linkers in polymeric hybrid hydrogels. Mater Lett 2011; 65(2): 392–395.

172.

Stankic

Suman

Haque

, et al. Pure and multi metal oxide nanoparticles: synthesis, antibacterial and cytotoxic properties. J Nanobiotechnol 2016; 14(1): 73.

173.

Rao

Ashok

Rao

, et al. Structural properties of MgO nanoparticles: synthesized by co-precipitation technique. Int J Sci Res 2014: 2319–7064.

174.

Markides

Rotherham

El Haj

. Biocompatibility and toxicity of magnetic nanoparticles in regenerative medicine. J Nanomater 2012; 2012: 1–11.

175.

Majewski

Thierry

. Functionalized magnetite nanoparticles—synthesis, properties, and bio-applications. Crit Rev Solid State Mater Sci 2007; 32(3–4): 203–215.

176.

Rivani

Retnosari

Kusumandari

, et al. Influence of TiO2 addition on the magnetic properties of carbon-based iron oxide nanocomposites synthesized using submerged arc-dischargeInfluence of TiO₂ addition on the magnetic properties of carbon-based iron oxide nanocomposites synthesized using submerged arc-discharge. IOP Conf Ser Mater Sci Eng 2019; 509(1): 012034.

177.

Frimpong

Hilt

. Poly(n-isopropylacrylamide)-based hydrogel coatings on magnetite nanoparticles via atom transfer radical polymerization. Nanotechnology 2008; 19(17): 175101.

178.

Leslie-Pelecky

Rieke

. Magnetic properties of nanostructured materials. Chem Mater 1996; 8(8): 1770–1783.

179.

Pooresmaeil

Mansoori

Mirzaeinejad

, et al. Efficient removal of methylene blue by novel magnetic hydrogel nanocomposites of poly (acrylic acid). Adv Polym Technol 2018; 37(1): 262–274.

180.

Koetting

Peters

Steichen

, et al. Stimulus-responsive hydrogels: theory, modern advances, and applications. Mater Sci Eng R: Rep 2016; 93: 1–49.

181.

Bée

Obeid

Mbolantenaina

, et al. Magnetic chitosan/clay beads: a magsorbent for the removal of cationic dye from water. J Magn Magn Mater 2017; 421: 59–64.

182.

Makhado

Pandey

Modibane

, et al. Sequestration of methylene blue dye using sodium alginate poly(acrylic acid)@ZnO hydrogel nanocomposite: kinetic, Isotherm, and thermodynamic investigations. Int J Biol Macromol 2020; 162: 60–73.

183.

Zirak

Abdollahiyan

Eftekhari-Sis

, et al. Carboxymethyl cellulose coated Fe3O4@SiO2 core-shell magnetic nanoparticles for methylene blue removal: equilibrium, kinetic, and thermodynamic studies. Cellulose 2018; 25(1): 503–515.

184.

Asadi

Eris

Azizian

. Alginate-based hydrogel beads as a biocompatible and efficient adsorbent for dye removal from aqueous solutions. ACS Omega 2018; 3(11): 15140–15148.

185.

Vahidhabanu

Karuppasamy

Adeogun

, et al. Impregnation of zinc oxide modified clay over alginate beads: a novel material for the effective removal of Congo red from wastewater. RSC Adv 2017; 7(10): 5669–5678.

186.

Zhang

Chang

Zhao

, et al. Fabrication of Zinc Oxide/Polypyrrole Nanocomposites for brilliant green removal from aqueous phase. Arabian J Sci Eng 2019; 44(1): 111–121.

187.

Hosseini

Mashaykhi

. New chitosan/silica/zinc oxide nanocomposite as adsorbent for dye removal. Int J Biol Macromol 2019; 131: 520–526.

188.

Stefaniuk

Cieniek

Rogalska

, et al. Magnetic properties of ZnO:Co layers obtained by pulsed laser deposition method. Mater Sci-Pol 2018; 36(3): 439–444.

189.

Ahmad

Yingying

Nisar

, et al. Synthesis of hierarchical flower-like ZnO nanostructures and their functionalization by Au nanoparticles for improved photocatalytic and high performance Li-ion battery anodes. J Mater Chem 2011; 21(21): 7723–7729.

190.

Nassar

Ali

Amin

. A facile Pechini sol-gel synthesis of TiO2/Zn2TiO2/ZnO/C nanocomposite: an efficient catalyst for the photocatalytic degradation of Orange G textile dye. RSC Adv 2017; 7(48): 30411–30421.

191.

Young

S-J

Tang

W-L

. Wireless zinc oxide based pH sensor system. J Electrochem Soc 2019; 166(9): B3047–B3050.

192.

Farrokhi

Hosseini

Yang

, et al. Application of ZnO–Fe 3 O 4 nanocomposite on the removal of azo dye from aqueous solutions: kinetics and equilibrium studies. Water Air Soil Pollut 2014; 225(9): 1–12.

193.

Khan

Nazir

Ali

, et al. Removal of Chromium (VI) from aqueous solution using guar gum-nano zinc oxide biocomposite adsorbent. Arabian J Chem 2017; 10: S2388–S2398.

194.

Fang

Tait

, et al. Preparation of conductive composite hydrogels from carboxymethyl cellulose and polyaniline with a nontoxic crosslinking agent. Rsc Adv 2017; 7(86): 54823–54828.

195.

Ari

Sengel

Sahiner

. The use of titanium dioxide particles embedded in anionic hydrogel composite for photocatalytic degradation of methylene blue. SPE Polym 2021; 2(2): 97–109.

196.

Anaya-Esparza

Villagrán-de la Mora

Ruvalcaba-Gómez

, et al. Use of Titanium Dioxide (TiO2) Nanoparticles as reinforcement agent of polysaccharide-based materials. Processes 2020; 8(11): 1395.

197.

Kangwansupamonkon

Klaikaew

Kiatkamjornwong

. Green synthesis of titanium dioxide/acrylamide-based hydrogel composite, self degradation and environmental applications. Eur Polym J 2018; 107: 118–131.

198.

Han

Wang

. Preparation of a hydroxyethyl-titanium dioxide-carboxymethyl cellulose hydrogel cage and its effect on the removal of methylene blue. J Appl Polym Sci 2017; 134(23): 44925.

199.

Mittal

Ray

. A study on the adsorption of methylene blue onto gum ghatti/TiO2 nanoparticles-based hydrogel nanocomposite. Int J Biol Macromol 2016; 88: 66–80.

200.

Thakur

Pandey

Arotiba

. Development of a sodium alginate-based organic/inorganic superabsorbent composite hydrogel for adsorption of methylene blue. Carbohydr Polym 2016; 153: 34–46.

201.

Malatji

Makhado

Ramohlola

, et al. Synthesis and characterization of magnetic clay-based carboxymethyl cellulose-acrylic acid hydrogel nanocomposite for methylene blue dye removal from aqueous solution. Environ Sci Pollut Res 2020; 27(35): 44089–44105.

202.

Zhang

Dai

, et al. Facile preparation of polyacrylamide/chitosan/Fe3O4 composite hydrogels for effective removal of methylene blue from aqueous solution. Carbohydr Polym 2020; 234: 115882.

203.

Makhado

Hato

. Preparation and characterization of sodium alginate-based oxidized multi-walled carbon nanotubes hydrogel nanocomposite and its adsorption behaviour for methylene blue dye. Front Chem 2021; 9: 576913.

204.

Mittal

Maity

Ray

. Synthesis of co-polymer-grafted gum karaya and silica hybrid organic-inorganic hydrogel nanocomposite for the highly effective removal of methylene blue. Chem Eng J 2015; 279: 166–179.

205.

Sharma

Thakur

Mamba

, et al. Titania modified gum tragacanth based hydrogel nanocomposite for water remediation. J Environ Chem Eng 2021; 9(1): 104608.

Removal of methylene blue from wastewater using hydrogel nanocomposites: A review

Abstract

Keywords

Introduction

Adsorption

Background

Adsorption parameters

Adsorption isotherms

Langmuir isotherm model

Freundlich isotherm

Temkin isotherm

Kinetic isotherms

Thermodynamics

Adsorbent materials for MB

Polysaccharides

Carboxymethyl cellulose

Alginate

Hydrogels

Background

Application of hydrogels

Preparation methods

Grafting

Crosslinking

Free-radical polymerization

Modification with inorganic materials

Carbon-based

Clay-based hydrogels

Metal oxide–based hydrogels

Magnetic (Fe3O4) nanocomposite hydrogels

Zinc oxide–based hydrogels

Titanium dioxide–based hydrogels

Conclusions

Footnotes

Declaration of conflicting interests

Funding

ORCID iD

References

Magnetic (Fe₃O₄) nanocomposite hydrogels