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Review

Polysaccharides as Economic and Sustainable Raw Materials for the Preparation of Adsorbents for Water Treatment

by
Gema Díaz Bukvic
1,2,
Ezequiel Rossi
1,2 and
María Inés Errea
1,2,*
1
Instituto Tecnológico de Buenos Aires (ITBA), Lavardén 315, Ciudad Autónoma de Buenos Aires C1437FBG, Argentina
2
Consejo Nacional de Investigaciones Científicas y Técnicas (CONICET) Godoy Cruz 2290, Ciudad Autónoma de Buenos Aires C1425FQB, Argentina
*
Author to whom correspondence should be addressed.
Polysaccharides 2023, 4(3), 219-255; https://doi.org/10.3390/polysaccharides4030016
Submission received: 3 July 2023 / Revised: 8 August 2023 / Accepted: 16 August 2023 / Published: 20 August 2023
(This article belongs to the Special Issue New Insights into the Production of Polysaccharides and Their Derivatives for Challenging Sustainable Development)
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Abstract

:
Adsorption processes, due to their technical simplicity and cost-effectiveness, have arisen as one of the most well-known, straightforward solutions to water pollution. In this context, polysaccharides, due to their abundance, biodegradability, and biocompatibility, are appealing raw materials for the design of adsorbents. Moreover, some of them, such as chitosan, can be obtained from organic waste products, and their use additionally contributes to solving another concerning problem: organic waste accumulation. Unfortunately, due to their low adsorption capacities and/or physicochemical properties, native polysaccharides are not suitable for this purpose. However, there are alternatives that can overcome these physical or chemical limitations, often taking advantage of the versatility of their polyhydroxylated structure. In this context, this review aims to present an overview of the advances from 2019 onwards in the design of new adsorbents for water treatment from cellulose, alginate, chitosan, and starch, addressing the two main strategies reported in the literature: the preparation of either polysaccharide-based composites or polysaccharide derivatives. It is important to point out that, herein, special emphasis is placed on the relationship between the chemical structure and the efficiency as adsorbents of the analyzed materials, in an attempt to contribute to the rational design of adsorbents obtained from polysaccharides.

1. Introduction

Water is a scarce natural resource globally, not only due to its limited physical access but also to the progressive deterioration in its quality caused by pollution [1]. Over the last century, freshwater use has increased by a factor of six and has been growing at a rate of one per cent per year since 1980, which is a result of population growth, economic development, and consumption habits. Some concerning facts reported by the United Nations are that eight out of ten people lack drinking water access in rural areas, and by 2030, only 81% of the need for clean water will be met, which means that 1.6 billion people would not manage to have safe water by then [2]. Thus, one of the greatest challenges of the XXI century is guaranteeing access to safe drinking water. Hence, technologies aiming to pursue this goal intend to make water affordable and accessible for all by developing efficient systems for polluted water remediation [3,4].
Depending on the target pollutant and its concentration, contaminated water can be treated via biological, physical, and chemical processes. These approaches include several technologies such as aeration [5], filtration [6,7,8], flotation [9,10,11], coagulation [12,13,14], flocculation [15], skimming [16,17], chlorination [18,19], membrane technologies [20,21,22], ozonation [23], oxidation and advanced oxidation processes [24,25], neutralization [26], and adsorption [27,28,29], among others.
Moreover, adsorption processes have famously provoked interest among the scientific community since they provide a simple, feasible, cost-effective, and straightforward solution to water pollution [30,31].
Adsorption is a superficial phenomenon in which one or more fluid phase components interact with a solid surface, adhering to it. Based on interaction forces between the adsorbate (the substance attached to the surface) and the adsorbent (which provides the surface where adsorbate adheres), adsorption can be either physical (physisorption) or chemical (chemisorption) [32].
One of the main differences between physisorption and chemisorption lies in enthalpy values of 40 kJ mol−1 or lower for physical adsorption and higher values for chemically governed adsorption processes [33,34]. Adsorbents’ capacity, selectivity, and adsorption rate is determined by their structure and properties [34,35,36,37,38,39]. It is therefore crucial to study the materials to select the most adequate material according to the pollutants found.
There is a wide variety of adsorbents, which include conventional materials such as inorganic materials (e.g., zeolites, aluminas, silica gel, iron oxides, and clays), activated carbons, ion-exchange resins; and non-conventional adsorbents such as polysaccharides and their derivatives (e.g., chitosan, cellulose, starch, alginate, or cyclodextrin), biosorbents (e.g., algae, fungi, or yeasts) and either by-products or waste from agricultural and industrial activities (e.g., sawdust, corn cob, sugar bagasse, wheat straw, or sewage sludges) [40].
In this context, polysaccharides are materials that are remarkable for their low cost and environmentally friendliness. Unfortunately, as it will be discussed throughout this manuscript, due to either their low adsorption capacities, physicochemical properties or both, polysaccharides are not suitable for water treatment in their native form. However, their polyhydroxylated structure provides them enough versatility to be subjected to chemical modifications in order to impart specific physicochemical properties depending on the products’ final application.
Taking into account the above discussion, this review aims to present an overview of the advances from 2019 onwards in the design of new adsorbents suitable for water treatment, made from cellulose, alginate, chitosan, and starch, addressing the two main strategies reported in literature: the preparation of either polysaccharide-based composites or polysaccharide derivatives. Moreover, it is important to point out that, herein, special emphasis is placed on the relationship between the chemical structure and the efficiency as adsorbents of the analyzed materials, in an attempt to contribute to the rational design of adsorbents from polysaccharides.

2. Polysaccharides Involved in Water Remediation

Among naturally existing polysaccharides, cellulose, alginate, chitosan, and starch are the most studied in this field because of their remarkable relative abundance and availability.

2.1. Cellulose

It is well known that cellulose, one of the most abundant organic compounds on Earth, is composed of D-glucopyranose units linked by β-(1→4) bonds (Figure 1).
Although traditionally cellulose has been mainly obtained from wood, over the past few decades, alternative vegetable sources have been increasingly researched to relieve the demand on wood-based biomass and improve process sustainability [41]. In this context, grasses such as bamboo as well as agricultural residues and agro-industrial crop by-products are among the most explored sources due to their low initial cost and fast regeneration. In the case of waste, their use also contributes to their valorisation [41], but they have as a drawback a lower content of cellulose than wood due to the higher content of lignin and hemicellulose [42].
The search for alternatives beyond vegetable sources has led to the study of bacterial cellulose. Bacterial cellulose is produced via fermentation with specific bacteria under suitable conditions and is obtained as a highly hydrated gelatinous pellicle that grows on the aerated surface of the fermentation vessel [43]. Bacterial cellulose is recognized for its high crystallinity, polymerization degree, and chemical purity, as well as for its unique intrinsic nanofibrillar structure. Furthermore, while the isolation of cellulose from plant sources implies the use of reagents that can have a negative environmental impact, bacterial cellulose is produced free of lignin, hemicelluloses, and pectin, thus, avoiding the need for aggressive chemical treatments for the removal of these compounds [38].
The production of bacterial cellulose has the disadvantage of being more expensive than plant cellulose since until now, it has mainly been produced using specific bacteria, typically Komagataeibacter xylinus (formerly called Gluconacetobacter xylinus and Acetobacter xylinum), which require axenic conditions and strict control of fermentation variables [44]. However, for certain applications, it could be alternatively obtained from the floating pellicle developed during kombucha tea production, in a much simpler process which does not require laboratory conditions, complex growth media, or sophisticated cultivation and processing equipment [44,45]. Given the proliferation in recent years of not only classical home-scale breweries, but also larger-scale kombucha enterprises, this production method offers an attractive alternative to obtain pure cellulose by valorising this by-product of kombucha tea.
As far as cellulose tridimensional structure is concerned, the D-glucopyranose units of its chains have a linear arrangement that allows for the formation of numerous intercatenary hydrogen bonds, which result in the polymer’s water insolubility [46] (Figure 2). Additionally, this cellulose arrangement is responsible for its low surface area and consequent low adsorption efficiency of pollutants when employed unmodified, necessitating the functionalization of cellulose [47,48].
In fact, He et al. illustrated the enhanced adsorption capacity when native cellulose was modified. In this case, native cellulose achieved maximum capacity values of 9.8 and 14.3 mg g−1 for Cr (III) and Fe (III), while 377.2 and 84.0 mg g−1 were attained by preparing a porous spherical polyethyleneimine-cellulose (PEI-cell) absorbent [49].
In that context, intensive work has been carried out on the design of efficient adsorbents from cellulose. The strategies are based either on the preparation of composite materials or on chemical modifications to this polymer.
Approaches to composite materials reported in literature include the preparation of cellulose-based materials using alginate [50,51,52,53,54], chitosan [55,56,57,58,59], hydroxyapatite [60,61,62], crown ethers [63], graphene oxide (GO) [64,65], magnetite (Fe3O4) [66,67], montmorillonite [68,69,70,71,72,73], titanium dioxide [74], collagen [75], bentonite [76,77], and activated carbon [78,79], among others. Some of them are shown in the table below (Table 1).
Nonetheless, in most of the mentioned cases, the main role of cellulose was just to provide mechanical resistance, a porous matrix insoluble in water, or both, while the metal adsorption capacity was provided by the other materials chosen for the adsorbents’ preparation.
Regarding chemical modifications of cellulose, strategies are based on the chemical reactivity of the hydroxyl groups. These reactions are intended to confer cellulose-specific features according to the target pollutant and can be divided into two groups:
  • Polymerization in the presence of adequate monomers (grafting).
  • Reactions of the hydroxyl groups with compounds possessing the functionalization needed according to the final application.
Among the different monomers grafted onto cellulose aiming to enhance its adsorption capacity, acrylic acid [80,81,82,83], acrylamide [84], methacrylic acid [85], acrylonitrile [86,87,88], vinyl acetate [89], and 2-hydroxyethyl methacrylate [90] can be mentioned. In all cases, after grafting the monomers onto cellulose, grafted polymers can be subjected to crosslinking reactions or subsequent modifications [91].
In the case of hydroxyl groups’ chemical modifications, some only aim to disrupt hydrogen bonds interactions to increase the exposure of the internal chains’ hydroxyl groups to the adsorbates. An example of such modifications is the preparation of cellulose crosslinked with crown ethers, such as dibenzo-18-crown 6, using ceric ammonium nitrate as the initiator, which was found to be suitable for Cd (II), Zn (II), Ni (II), Pb(II) and Cu(II) as described by A. Fakhre et al. [92]. Moreover, the crown ether-immobilized cellulose acetate membranes presented by Oana Steluta Serbanescu et al. were efficient in Gd (III) retention [93]. Other modifications include cellulose subdued to esterification and oxidation processes for Cu(II) removal as described by Dutta Gupta et al., using octenyl succinic anhydride and sodium hypochlorite, respectively [94].
Other experiments aim to improve cellulose adsorption of ionic pollutants by introducing charged groups into the cellulose’s structure. Cationic and anionic exchangers were produced by introducing carboxyl or amino groups, respectively. Furthermore, the preparation of amphoteric materials was also studied.
Among cationic exchangers, carboxylic groups are mainly introduced in cellulose via carboxymethylation (Figure 3). For instance, the preparation of carboxymethyl cellulose (CMC) with the highest substitution degree that still guarantees its water insolubility was reported in [38,95].
Further modifications of CMC have led to the production of hydrogels by crosslinking CMC with epichloridrine [96], polyacrylamide [97], and polyvinyl alcohol [98]. Furthermore, Lin et al. carried out a systematic study to obtain cellulose sponges from CMC via treatment of the cellulose derivative with different concentrations of sulphuric acid and a further freeze–thawing treatment, without the need for an organic crosslinker [99].
Over the above-mentioned cellulose derivatives, adsorption studies have been carried out with Pb (II), Cd (II), Cu (II), Ag (I), Hg (II), and Ni (II), and results showed a wide range of adsorption capacity values (Table 2).
Regarding the material obtained by Chen et al., not only was it the one with the highest lead adsorption capacity value, but it also exhibited a remarkable adsorption capacity towards the cationic dye MB (1611.4 mg g−1) [97].
In addition to carboxymethylation, other sources of carboxylic groups used to obtain cation exchangers found in the literature include the incorporation of succinic or citric acid via ester bonds into cellulose chains (Figure 4).
In the case of succinic derivatives, the one obtained by Gurgel et al. [100] achieved maximum capacity values of 185.2, 256.4,and 500.0 mg g−1 for Cu(II), Cd (II) and Pb(II), respectively. On the other hand, Olivito et al. reported the introduction of citric acid into cellulose structure, observing some measure of crosslinking [101]. This adsorbent was efficient for MB removal, obtaining a maximum capacity value of 96.2 mg g−1. Another cellulose citrate, reported by Tursi et al., exhibited a high affinity and a remarkable maximum adsorption uptake for Hg (II) (1600.0 mg g−1) [102].
On the other hand, the production of anion exchangers can be achieved by introducing amino groups into the cellulose structure, as mentioned above. Under acidic conditions, the amino groups are easily protonated, increasing the affinity of these derivatives to anionic pollutants via electrostatic interactions, compared to native cellulose [103].
In this context, Chen et al. reported on a hyperbranched polyethyleneimine cellulose derivative (Figure 5I) with a high maximum adsorption capacity value for reactive yellow X-RG dye (970.9 mg g−1) [104].
Jin et al. also reported on the preparation of an amino-functionalized nanocrystalline cellulose as an adsorbent for anionic dyes [105]. This work describes the partial oxidative rupture of the cellulose glucopyranose units that led to the formation of aldehyde groups, which were further converted into amino groups via amination-reductive reactions (Figure 5II). The product described by Jin et al. was assayed as adsorbent for the removal of anionic dyes and showed the maximum adsorption capacity value for acid red (555.6 mg g−1).
Moreover, anion exchanger cellulose hydrogels were prepared by modifying cellulose with 2,3-epoxypropyl trimethyl ammonium chloride and crosslinked with poly(ethylene glycol) diglycidyl ether (Figure 5III). The maximum adsorption capacity values of the samples for anionic dyes were found to be between 240.0 and 447.0 mg g−1 [106].
Anirudhan et al. reported a cellulose-based anion exchanger synthesized by a graft polymerization reaction between cellulose and glycidyl methacrylate using N,N-methylene-bis-acrylamide as a crosslinker, followed by amination with dimethylamine (Figure 5IV) [107]. The authors studied the effectiveness of the exchanger for As (V) removal, reporting a maximum adsorption capacity value of 200.3 mg g−1.
Pereira et al. described an adsorbent for As (V) and Cu (II) removal, prepared by tosylation of microcrystalline cellulose and further nucleophilic substitution of the tosyl group with ethylenediamine (Figure 5V) [108], achieving maximum adsorption capacity values of 121.4 and 69.2 mg g−1, respectively.
Moreover, in recent years, the number of published articles reporting cellulose-based ion liquid as ionic adsorbents for water treatment has increased significantly. For instance, Dong et al. reported the production of imidazolium-based ionic liquid glycidyl methacrylate grafted cellulose microspheres using 1-aminopropyl-3-methyl imidazolium salts as ionic liquids, with a high adsorption capacity value of 735.3 mg g−1 for Au(III) [109]. Guo et al. also reported gold recovery via another cellulose-based ionic liquid. In their study, carboxymethyl-diethylammoniumethyl cellulose was prepared, but the resulting material had remarkably poor adsorption properties, with maximum capacity value of 15 mg g−1 for Au (III) [110].
Zhang et al. reported the use of cellulose nanocrystals grafted with poly(ionic liquid) prepared via gamma-ray-initiated polymerization of cellulose. The material was assayed via CR and yielded a higher capacity value for the modified composite (195.8 mg g−1), compared to the 59.7 mg g−1 removed using cellulose unmodified nanocrystals [111].
In particular, a highly effective novel magnetic cellulose-based ionic liquid was described by Ling et al. as functionalized by Fe3O4 nanoparticles grafted with imidazole ionic liquid followed by the formation of cellulose microspheres modified by polyethyleneimine. The material was efficient for CR and MB, obtaining maximum capacity values of 1299.3 and 1068.1 mg g−1, respectively [112]. Likewise, as reported by Li et al., a functionalized magnetic cellulose was prepared by dissolving microcrystalline cellulose in an ionic liquid, which was further modified with glutaric anhydride [113]. In this case, the adsorbent achieved maximum adsorption capacity values of 1186.8 and 151.8 mg g−1 for MB and Rhodamine B, respectively. In both cases, in addition to their reusability, the fact that adsorbents possess magnetic properties allows them to be separated from aqueous solutions via the use of an external magnetic field, which is an interesting advantage for green wastewater treatment.
Wan et al. modified cellulose with ionic liquid 4-methylimidazole, obtaining 3D porous microspheres with large surface areas [114], achieving a maximum adsorption capacity value of 218.6 mg g−1 for Acid Orange 7 dye.
Zhang et al. prepared a cellulose-base adsorbent via modification with imidazolium ionic liquid, which was assayed for the removal of other anionic dyes. In this work, the maximum adsorption capacity values obtained were 1169.0 and 563.0 mg g−1 for xylenol orange and CR, respectively. In this case, these adsorption capacity values were 3.5 times higher than those obtained with native cellulose [115].
On the other hand, there are also reports of amphoteric adsorbents obtained from cellulose. For instance, Zhou et al. reported the preparation of a material with a high density of amino and carboxyl groups from microcrystalline cellulose for the simultaneous removal of anionic and cationic heavy metal ions. Herein, the complete removal of Cr (VI), Cd (II), Cu (II), Zn (II), and Pb (II) from an aqueous solution was reported [116].
Zhong et al. synthesized an adsorbent from wheat straw, first introducing quaternary amine groups onto cellulose by reaction with epichlorohydrin, ethylenediamide, and triethylamine. Then, carboxylic groups were introduced via reaction with sodium hydroxide and monochloroacetic acid. Hence, the maximum adsorption capacity values obtained for Cu (II) and Cr (VI) removal with unmodified wheat (16.0 and 30.9 mg g−1, respectively) and the modified amphoteric adsorbent (90.9 and 270.1 mg g−1, respectively) were compared [117].
Kono reported on cellulose polyampholyte hydrogels prepared with a cationization reaction of sodium carboxymethylcellulose with 2,3-epoxypropyltrimethylammonium chloride, crosslinked with ethyleneglycoldiglycidylether. The adsorbent was assayed with Acid Red 9, Acid Red 13, and Acid Blue 92 dyes, obtaining maximum adsorption capacity values of 866, 911, and 816 mg g−1, respectively [118].
In addition, a several-times reusable amphoteric adsorbent was prepared by Zhu et al. from cellulose-grafted calcium hydroxide and assayed for CR and MB dyes. The respective maximum adsorption capacity values were 2552.7 and 756.5 mg g−1 [119].

2.2. Alginate

Alginate is a polysaccharide which naturally exists as its sodium salt and is constituted of (1→4)-linked β-D-mannuronate (M) and α-L-guluronate (G) residues (Figure 6). Alginate does not have regular repetitive units, since it is a block copolymer composed of homopolymeric regions of M or G and interspersed with regions with MG blocks [120].
Its abundance is mainly due to its presence in marine brown algae Phaeophyceae, Ascophyllum nodosum, Laminaria hyperborea, and Macrocystis pyrifera as a structure-forming component and in soil bacteria as a capsular polysaccharide. Several bacteria can produce alginate, such as Azotobacter sp. and Pseudomonas sp. However, commercial alginates are mainly obtained from algal sources, since industrial bacterial production is not economically feasible at present despite being technically possible [121].
The distribution and sequence of M and G blocks of alginate varies according to its source and affects the polysaccharides’ properties, such as viscosity. In fact, for example, alginate obtained from brown algae of the specie Sargassum is considered to be of “borderline” quality due to its low G content [122]. It is important to note that both the environmental conditions during the growth of algae and the extraction techniques used are also two variables that have a high impact on the final structure of the alginate [123].
The interaction between sodium alginate and divalent or trivalent metal cations produces ionic gelation [124], which is related to the length of G blocks in alginate. The formation of coordinate sites is generated by G chains looping, known as the egg-box model (Figure 7).
In the presence of monovalent metal cations such as sodium, alginate acts as semiflexible chains instead of the stiff aggregated rigid chains obtained via egg-box formation with Ca (II) [125].
Calcium alginate beads are well known for their ability to adsorb cationic pollutants. In particular, there is some evidence that relates metal cation size to the adsorption efficacy of alginate beads. Both He et al. and Papageorgiou et al. observed higher adsorption capacity values when cation size increases: Pb (II) > Cu (II)> Cd (II), suggesting that larger ions fit better in binding sites [126,127].
Alginate capsules have been proven to have a high lead-binding capacity, with maximum adsorption capacity values of 1540.0 mg g−1 reported by Gyu Park et al. In this case, capsules were prepared by dropping CaCl2 solution and xanthan gum into sodium alginate [128].
Vijaya et al. also obtained insoluble calcium alginate beads which were assayed for Ni (II) adsorption, obtaining 310.4 mg g−1 for calcium alginate. Ni (II) uptake was attributed to both pore volume and large surface area [129].
Nevertheless, the mentioned alginate adsorbents still face two main drawbacks: alginate calcium complex instability and low porosity. Additionally, many of the alginate beads tried in packed column operation exhibited pressure drops that were too high to flow and were not rigid enough. Therefore, intensive work has been done to improve their adsorption performance. To this end, Jeon et al. reported an alginic acid immobilized with PVA-boric acid and crosslinked with glutaraldehyde, designed to reduce the hydration of the bead, obtaining a mechanically strong adsorbent, stable at pH levels under 1.0 and temperatures above 170 °C, with a maximum adsorption capacity value of 390 mg g−1 for Pb (II) [130].
Considering the issues mentioned before, another alternative to the use of calcium alginate on its own is the preparation of composite materials as reported in the literature. Some examples are described next.
Wang et al. obtained satisfactory results for heavy metal removal with granular alginate-based hydrogels, prepared via grafting and crosslinking reactions between sodium alginate, acrylic acid, polyvinylpyrrolidone, and gelatine. The maximum adsorption capacity values obtained for Ni (II), Cu (II), Zn (II) and Cd (II) were: 177.7, 199.9, 190.4 and 321.7, mg g−1, respectively. Competitive studies suggested that Cu (II) has a stronger affinity for the hydrogel [131].
Mahji et al. reported the preparation of a polyaniline/sodium alginate composite for the removal of both cationic and anionic dyes. In particular, the adsorption of MB, rhodamine B, orange II, and methyl orange was assessed, reporting maximum adsorption capacity values of 555.5, 434.8, 476.2, and 416.7 mg g−1, respectively [132].
Pashaei-Fakhri et al. were able to graft polyacrylamide onto alginate chains with free radical polymerization, obtaining a hydrogel whose adsorption affinity towards the cationic dye crystal violet was compared with an acrylamide/GO bonded sodium alginate, also prepared by these authors [133]. Results showed that increasing the amount of GO improved the efficiency of the hydrogel in removing the dye studied, but a GO concentration above 5 wt.%, began to decrease in efficiency. This was attributed to the reduction of dye penetration into the hydrogel as a consequence of the agglomeration of the GO nanoparticles [134].
Jiang et al. also reported on the preparation of a sodium alginate-grafted polyacrylamide/GO hydrogel produced via free radical polymerization. In this case, adsorption of Cu (II) and Pb (II) was studied, and maximum adsorption capacity values of 68.8 and 240.7 mg g−1, respectively, were obtained. It is important to highlight that the concentration of GO in the hydrogel was not informed by the authors and, considering the results of Pashaei-Fakhri [133], this data would have been extremely relevant for result comparison.
Zhang et al. prepared alginate-based hydrogels by incorporating polyaniline-polypyrrole-modified GO as reinforced fillers into the alginate matrix [135]. In this paper, the authors reported a GO concentration of 0.5 % w/v. The materials were assayed for the removal of cationic and anionic heavy metals, achieving maximum adsorption capacity values of 87.2 and 133.7 mg g−1 for Cu (II) and Cr (VI), respectively.
Majdoub et al. also used GO to improve the adsorption capacity of alginate towards cationic heavy metals [136]. In this case, the carboxyl and epoxy groups of GO were used to covalently bond hexamethylenediamine (HDMA) to the GO’s surface (GO-HDMA). Further, GO-HDMA was encapsulated in alginate hydrogel beads with different loading (5, 10, 15, and 20 wt.%) yielding alginate/GO-HDMA hybrid adsorbents. Adsorption studies towards Pb (II), Cu (II), and Cd (II) showed almost complete removal of these metals even when a complex matrix, such as tap water was assayed.
Moreover, a modification including both the incorporation of sulphur atoms and GO into the alginate structure was described by Zhang et al., who reported the synthesis of a biocomposite hydrogel in which L-cysteine-modified alginate (TA) was combined with GO for the removal of heavy metal ions from water (Figure 8). TA/GO hydrogel microspheres were prepared by dropping GO, dispersed in water, into a TA water solution. The mixture was then dropped into a CaCl2 solution, leading to the formation of TA/GO microspheres. TA/GO was assessed as adsorbent towards Pb (II) and Cu (II), and the calculated maximum adsorption capacity values were 369.6 and 124.1 mg g−1, respectively [137].
On the other hand, aerogels have emerged as remarkable adsorbent materials in water treatment for its beneficial characteristics such as adjustable surface chemistry, low density, high specific surface area, and highly porous three-dimensional structure [138,139,140,141].
In this context, there is a report of a three-dimensional sodium alginate/gelatine/GO triple network composite aerogel with a 3 wt.% of GO incorporated into its structure. This material was assayed as adsorbent of both anionic and cationic dyes, such as CR and MB [142], with maximum adsorption capacity values of 196.8 and 322.6 mg g−1, respectively.
Wang et al. described the preparation of a calcium alginate disodium ethylendiaminetetraacetate dihydrate hybrid aerogel (aerogel-EDTA) for the removal of heavy metals from wastewater. Results showed high affinity of the adsorbent for Pb (II), Cd (II), Cu (II), Cr (III), and Co (II), exhibiting the highest selectivity towards Cd (II) with a maximum adsorption capacity value of 177.3 mg g−1 [143].
As far as adsorbents with magnetic properties are concerned, a new alginate derivative capable of removing heavy metal ions from an aqueous multicomponent solution containing Pb (II), Cu (II), Cd (II), and Ni (II) was reported [144]. Intrinsically mesoporous halloysite (HNTs) nanoclays, β-cyclodextrin (β-CD), and iron nanoparticles were incorporated into the alginate beads. HNTs, due to their ordered tubular and nano-sized structure, enhance the thermal and chemical stability of the adsorbent [145]. β-CD is a cyclic non-toxic oligosaccharide whose ability to form metal ion complexes is well known [146]. Moreover, the iron nanoparticles confer magnetic properties to the material. Unfortunately, adsorption studies of the alginate derivative showed low maximum adsorption capacity values of 21.1, 15.5, 2.5, and 2.7 mg g−1 for Pb (II), Cu (II), Cd (II), and Ni (II), respectively.
Another magnetic alginate-based composite was described by Alver et al. In this case, a magnetic alginate/rice husk composite was prepared via the ionotropic gelation method [147]. Magnetic properties were achieved by incorporating FeCl2 into the alginate/rice husk beads. Adsorption studies were carried out towards MB, and results showed a maximum adsorption capacity value of 274.9 mg g−1 [148].
Moreover, it is well known that clay minerals and their modified derivatives have high efficacy in removing most of the common chemical contaminants from aqueous solutions. Shi et al. reported aydrazide-modified sodium alginate as an efficient adsorbent of heavy metals [149]. In this case, alginate chains were crosslinked using adipic acid hydracid as a crosslinker (Figure 9). The ability of the new material to remove Hg (II), Pb (II), Cd (II), and Cu (II) was assayed, yielding maximum adsorption capacity values of 7.8, 2.0, 4.8, and 3.9 mg g−1, respectively.
Among this family of adsorbents, those based on montmorillonite, a typical 2:1 type clay mineral, have been the most extensively studied [150]. Thus, the inclusion of this mineral in an alginate composite is expected to enhance the adsorption capacity of the polysaccharide. In fact, Wang et al. reported the synthesis of a porous montmorillonite nanosheet/poly (acrylamide-co-acrylic acid)/sodium alginate hydrogel beads which could reach a maximum adsorption MB capacity of 530.7 mg g−1 [151].
The maximum adsorption capacity for MB reported by Wang was similar to the ones obtained from other alginate composite materials also containing montmorillonite, as stated by Sezen et al. [152].
The use of alginate-based composite materials that include minerals with the aim of enhancing their efficiency for water treatment is also exemplified by the work of Isawi, who reported on the preparation of zeolite/polyvinyl alcohol/sodium alginate nanocomposite beads for the removal of heavy metals from wastewater [153]. The maximum adsorption capacity of this new material at the optimal pH (6) for Pb (II), Cd (II), Sr (II), Cu (II), Zn (II), Ni (II), and Mn (II) were 47.6, 46.3, 47.2, 48.5, 48.3, 47.6 and 46.3 mg g−1, respectively.
Moreover, there is also a report in which waste, in this case, sugar bagasse [154], was chemically modified via ester bonds with succinic acid, leading to sugar bagasse succinate (SBS), which was further used to make an alginate composite material. The new SBS/alginate composite yielded maximum adsorption capacity values of 176.4 and 354.6 mg g−1 for Cd (II) and Pb (II), respectively [155].
Furthermore, there are reports of alginate/chitosan composites that are described in the following section.

2.3. Chitosan

Chitosan is a polysaccharide obtained via partial deacetylation of naturally existing chitin, the second most abundant polysaccharide on Earth after cellulose, which can be found in the shells of insects and crustaceans [156,157]. Industrialization and commercialization of shrimps and prawns are relevant to the economy of many countries but, at the same time, crustacean shells accumulate when discarded, with a significant negative environmental impact. Therefore, the utilization of this waste contributes to solving environmental problems associated with its accumulation [37,158].
Chemical structure of chitosan (poly (β (1→4)-2-amino-2-deoxy-D-glucopyranose) is shown in Figure 10 [159].
Considering that the amino groups of the D-glucosamine residues of chitosan (Figure 9) have a pKa value of 6.5 [34], at pH values below 6.5 they are predominantly positively charged, making chitosan a polycation [37]. Nevertheless, despite the polycation’s capacity to form ionic complexes with a wide variety of anionic pollutants [160], its complete solubility in aqueous media at pH values lower than 5 limits its use as adsorbent [34,37].
On the other hand, regarding cationic pollutants such as lead, mercury, copper, cobalt, and cadmium, among others, chitosan chains must be predominantly deprotonated to avoid electrostatic repulsion and, therefore, pH values above 6.5 are required. In this case, the main mechanism involved in metal retention is chelation, in which the amino groups play a key role, serving as coordination sites for metal-binding [160,161]. Additionally, it is important to highlight that cation diffusion into chitosan’s structure could affect its adsorption capacity, depending on the physical nature of chitosan (i.e., flakes, beads, or membranes) and its crystallinity [160,161].
From an economic point of view, the use of an adsorbent on an industrial scale is only feasible if it is reusable, so regeneration of the materials is critical. Hence, the fact that chitosan is soluble in the acidic aqueous mediums required for heavy metal desorption prevents it from regenerating and consequently from being used on a large scale.
Therefore, efforts are focused towards producing insoluble chitosan materials in an acidic environment and enhancing the materials’ adsorption capacity. In this context, the main strategies reported include: substitutions involving either the C-6 hydroxyl group, the C-2 amino group, or both; crosslinking reactions; and grafting of polymeric chains.
For instance, Zhao et al. reported an amphoteric crosslinked chitosan with citric acid esterified β-cyclodextrin (Figure 11) [162]. The material was reported as effective for the removal of many common dyes, including reactive blue 49, reactive yellow 176, reactive blue 14, reactive black 5, and reactive red 141, which vary in size and structure, showing the versatility of the materials for pollutant removal. The authors used reactive blue 49 as the model adsorbate, and under the optimum adsorption conditions, up to 500 mg g−1 was adsorbed.
A synthetic strategy similar to the one employed by Zhao [162] was carried out by Usman et al. [163], who also used a β-cyclodextrin as a modifying chitosan agent to prepare an adsorbent for dye removal from wastewater. In this case, nitrilotriacetic acid was used instead of citric acid and glutaraldehyde was chosen as a crosslinker. The maximum MB adsorption capacity of the material was 162.6 mg g−1, which is lower than that reported by Zhao.
Karimi-Maleh et al. reported the preparation of 1-butyl-3-methylimidazolium bromide impregnated chitosan beads and the product was assayed as adsorbent for the removal of the cationic dye MB [164]. However, a maximum adsorption capacity value of just 7 mg g−1 was reported.
Fan et al. reported the synthesis of a CO2-responsive chitosan aerogel, and the results achieved for adsorption and desorption of Cu (II) were reported. The authors synthesized a polyacrylic acid 2-(dimethylamino)ethyl methacrylate (P(AA-co-DMAEMA)), which was combined with chitosan via physical crosslinking via electrostatic interactions between the carboxyl and amino groups in chitosan. Then, porous chitosan/P(AA-co-DMAEMA) aerogels (CPA) were obtained by freeze-drying. The calculated Cu (II) maximum adsorption capacity value of the material was 163.7 mg g−1. In this work the most remarkable feature was that the heavy metal could be desorbed by CO2 bubbling under mild conditions, avoiding the use of strong acids usually involved in metal desorption processes. The desorption rate reported by the authors surpassed 80%. It is important to note that after 6 cycles, the adsorption capacity of CPA for Cu (II) still reached 70% of the initial adsorption capacity [165].
There are also reports of lignosulphonate/chitosan adsorbents for the removal of heavy metals from wastewater [166,167]. Lignins are important resources found in large amounts as waste products in paper industry effluents. They are highly branched phenolic polymers with a vast number of aromatic monomers derived from three monolignols (p–coumaryl, coniferyl and sinapyl alcohols; Figure 12) [168,169,170].
Within this kind of chitosan-based material, Mu et al. reported a free radical polymerization method for the synthesis of a porous lignosulphonate/chitosan material, which was assayed as adsorbent towards Co (II) and Cu (II), finding maximum adsorption capacity values of 386.0 and 283.0 mg g−1, respectively. In the case of Zhang et al., the chitosan derivative was obtained in a similar way to the one reported by Mu, and the authors reported a high efficiency of this material as a Pb (II) adsorbent (maximum adsorption capacity value: 525.0 mg g−1) [166,167].
Rossi et al. described the preparation and characterization of water insoluble chitosan derivatives using mucic and adipic acid (a polyhydroxylated and a non-functionalized diacid of the same length chain, respectively) as a crosslinkers. In highly regioselective reactions, N-substituted crosslinked chitosan derivatives were achieved and their efficiency as lead adsorbent was assessed. Maximum adsorption capacity values of 76.3 and 69.7 mg g−1 were reported for chitosan crosslinked with mucic and adipic acid, respectively, evidencing the role of the crosslinker hydroxyl groups in the lead adsorption mechanism on the chitosan derivative [34].
Besides, as stated in the previous Section, there are recent reports of chitosan/alginate composites described as adsorbents of heavy metals or dyes.
For instance, Zhao et al. prepared a fibrous chitosan/sodium alginate composite foam by freeze-drying with ternary acetic acid/water/tetrahydrofuran solvents and compared its maximum adsorption capacity against selected dyes to the ones obtained preparing the same composite but using the classic binary mixture of solvents (acetic acid/water) instead. The hypothesis of the authors was that solvents play a key role in the transformation of the microstructure of the composite into finer scale structure, increasing the adsorption capacity of the material. The composite material prepared with the ternary mixture of solvents showed a significantly higher maximum adsorption capacity values towards the cationic dye MB than the ones observed for the composite obtained using the binary mixture of solvents (1488.1 and 560.2 mg g−1, respectively) [171].
In the case of Tang et al., a physically crosslinked hydrogel of chitosan/sodium alginate/calcium ion was prepared. The adsorbent was assayed as a heavy metals adsorbent. The maximum adsorption capacity values towards Pb (II), Cu (II) and Cd (II), reached 176.5, 70.8 and 81.2 mg g−1, respectively [172].
Ablouh et al. reported the obtention of chitosan microspheres/sodium alginate hybrid bead for heavy metals removal from aqueous solutions. In this work, maximum adsorption capacity values of 180 and 16 mg g−1 for Pb (II) and Cr (VI), respectively, were achieved. These results clearly show the higher efficiency of this material for the removal of cationic pollutants [173].
Among this kind of composite materials, Khapre et al. proposed a chitosan crosslinked with glutaraldehyde/alginate composite as adsorbent of dyes from water solutions. Adsorption studies towards methyl orange, brilliant green and patent blue V were carried out, achieving between moderate and low maximum adsorption capacity values of 198.1, 235.8, and 117.3 mg g−1, respectively [174].
A similar composite was prepared by Hamza et al. (Figure 13) but, in this case, adsorption of Cd (II) and Pb (II) was assessed [175]. The sorbent was first studied as adsorbent of each heavy metal, obtaining maximum adsorption capacity values of 220.5 and 258.6 mg g−1 for Cd (II) and Pb (II), respectively. Furthermore, the new material was assayed for its use on water samples collected from an industrial area with a high concentration of various heavy metals, showing a drastically decrease in the pollutants’ concentration in the effluents.

2.4. Starch

Researchers have been also focused on other abundant polysaccharide: starch. It is constituted by two homopolysaccharides, amylose and amylopectin [176]. The former is a water-soluble linear polymer, consisting in D-glucopyranose units linked by α-(1→4) bonds. Amylopectin has a branched structure with mostly short chains of α-(1→4) linked D-glucopyranose units with 5–6% branches linked by α-(1→6) glycosidic bonds to the main chain (Figure 14) [177].
Depending on the source from which starch is obtained, the proportion of amylose and amylopectin varies, and so does its average molecular weight [178]. Some of the most common sources include maize, potato, wheat and rice. Nevertheless, there are promising unconventional sources under study, such as fruits and vegetables waste. Kringel et al. conducted studies on amylose and amylopectin content of waste from fruits and vegetables with the aim of analysing its suitability as valorised residues from natural sources. The reported starch content of outer pericarp and core tissues of kiwi, mango kernels, pineapple stems, apple pulp, banana peels and avocado seeds was in a 20–50% range [179].
Regarding water treatment, native starch has been reported to have a poor adsorption capacity [180], which can mainly be attributed to its low surface area, limited thermal stability and absence of highly-absorptive functional groups, such as carboxyl, xanthate, acrylate, acetyl, hydroxypropyl, amine or amide [181,182]. Analogously to cellulose, alginate and chitosan, there are reports describing starch’s chemical modifications as well as the preparation of starch composites.
For instance, Guo et al. compared the efficiency for MB removal attained by native starch and a modified porous derivative, prepared by crosslinking native starch with epichlorohydrin and further hydrolysis with α-amylase, obtaining a maximum adsorption capacity value for MB almost three times higher than native starch [183]. In accordance with the results reported by Guo et al., Alvarado et al. also observed an enhancement of the adsorption capacity for the MB of starch after being modified by esterification with malonic, glutaric and valeric acids [184].
Soto et al. also compared modified and native starch. In this case, maleic acid and itaconic acids were used for esterification of starch, achieving maximum adsorption capacity values for Pb (II) and Zn (II) of 25.2 and 7.9 mg g−1, respectively for itaconate starch, while 5.2 and 3.2 mg g−1 were the corresponding values for native starch [185]. Soto et al. also reported oxidized starch adsorbents that achieved higher heavy metal removal capacity values compared to native starch; for Cd (II): 11.1 and 8.0 mg g−1; for Ni (II): 22.6 and 8.3 mg g−1; for Pb (II): 18.0 and 5.2 mg g−1; and for Zn (II): 10.3 and 3.2 mg g−1, respectively [186].
Sancey et al. reported the crosslinking of starch with 1,4-butanediol diglycidylether in presence of ammonium hydroxide and 2,3-epoxy-propyltrimethylammonium chloride, with further carboxymethylation. Herein, metal adsorption studies were conducted, achieving almost complete removal of Cu (II) and Fe (III) [187]. Copper removal was also assayed by Zheng et al. using starch hydrogels prepared with poly(acrylic acid), achieving an uptake of 179.9 mg g−1 Cu(II) in aqueous medium [188].
Chaudhari et al. prepared a starch xanthate that achieved almost complete removal of Hg (II), Cu (II), Cd (II) and Ni (II), and attributed the heavy metals uptake to the complexation of metals with xanthate groups [189].
As far as starch composites are concerned, composites with layer double hydroxide for methyl orange and fluoride removal from wastewater were reported. These materials were prepared by co-precipitation and different metals were used for the hydroxide layers, such as Mg (II), Al (III), Zn (II), Fe (III) and Ni (II). In particular, Zubair et al. reported a Starch-Ni/Fe-layered double hydroxide composite that achieved a maximum methyl orange (MO) adsorption capacity value of 387.6 mg g−1 [190]. However, Tao et al. achieved a higher maximum adsorption capacity value towards MO of 1555.0 mg g−1 [191] for the Zn/Mg/Al- Layered double hydroxide starch. On the other hand, a Mg/Al layered double hydroxides reported by Liu et al. achieved almost complete removal of fluoride [192].
Besides, iron nanoparticles are well-known to contribute to arsenic removal due to electrostatic attraction, ion exchange, and surface complexation [193]. It is therefore interesting to analyze iron nanoparticles’ effect when used in materials prepared with starch, such as composite materials with magnetite, maghemite and ferromanganese binary oxide. Next, some of the reported materials are described, in which starch acted only as a support or stabilizer of the mentioned inorganic particles.
Adsorption studies towards As (III) on iron-starch materials were carried out in aqueous solutions, achieving a maximum adsorption capacity value of 161.3 mg g−1 with the material reported by Xu et al. [194], while Siddiqui et al., obtained a maximum capacity value of 8.9 mg g−1 for a functionalized maghemite [195] and Robinson et al., 55.9 mg g−1 for a starch/maghemite nano-adsorbent [196].
On the other hand, as in the case of the other polysaccharides mentioned in previous sections, the preparation of ion exchangers from starch is a widely used strategy for ionic pollutants removal. For instance, Ma et al. [197] chemically modified starch attaching either xanthate or citrate groups to their structure (Figure 15I,II). In this work, adsorption assays towards Pb (II) were carried out, and the maximum adsorption capacity values were 109.1 and 57.6 mg g−1 for starch xanthate and starch citrate, respectively.
Another strategy for introducing negative charges in the starch structure is the oxidation of C-6 to a carboxyl group (Figure 15III). In this context, Liu et al. [198] modified starch nanoparticles through oxidization, using sodium hypochlorite. The new materials were preliminarily explored as adsorbents of heavy metals, using Pb (II) and Cu (II) as adsorbate models. Compared to the unmodified nanoparticles, the modified ones had remarkably higher adsorption capacity values (94.5 and 81.0 mg g−1 for Pb (II) and Cu (II), respectively).
Chen et al. [199] also used starch nanoparticles, but in this case the incorporation of negative charges in their surface was achieved by esterification with succinyl anhydride (Figure 15IV). The maximum degree of substitution was 0.1, which resulted in an increase on the surface Z-potential. The modified nanoparticles were assayed for the adsorption of Cu (II) and MB, showing that the adsorption process was greatly influenced by the pH value, as expected in presence of carboxyl groups. At low pH values, carboxyl groups are highly protonated, and the adsorption could be neglected (less than 3.0 mg g−1). At pH values above 4.0, the degree of protonation decreases and the surface charge of the adsorbents becomes negative, exerting electrostatic attraction to the adsorbate [34,38], which enhances the adsorption capacity of Cu (II) and MB (8.4 and 24.4 mg g−1, respectively).
Another example of modifications to obtain negatively charged starch was performed by Hashem et al. [200], who reported starch hydrogels prepared via graft polymerization of acrylonitrile, followed by nitrile groups hydrolysis to generate carboxylic acids and amides (Figure 15V). In this work, adsorption of Hg (II) on the starch hydrogels were carried out and a maximum adsorption capacity value of 1250 mg g−1 was reported by the authors. Subsequently, the same author reported adsorption studies against Pb (II) carried out on a similar material. In this last case, the value of the maximum adsorption capacity value reported was 264.4 mg g−1 [201].
Haroon et al. [202] also obtained cation exchangers by grafting carboxymethylated starch with N-vinylpyrrolidone (Figure 15VI). The new material was assayed as adsorbent towards rhodamine 6G from wastewater with a maximum adsorption capacity value of 363.9 mg g−1.
There are also reports of materials prepared using acrylic acid as the grafting monomer. For instance, Bahadoran et al. [82] reported a starch-g-poly(acrylic acid) hydrogel, achieving 736.0 mg g−1 of Cu (II) removal. Additionally, cellulose nanofibers were incorporated into the hydrogel, which enhanced its adsorption capacity, obtaining a value of 957.0 mg g−1 of Cu (II).
Ma et al., also prepared a composite material from starch, obtaining a starch-graft-poly(acrylic acid)/organo-modified zeolite, which was assayed for Cr (III) adsorption. The adsorbent’s removal of the mentioned metal was 651.4 mg g−1 [203].
Moreover, Chen et al. [204] prepared a starch-based high-performance adsorptive hydrogel by grafting polyacrylic acid onto starch, and then crosslinking it with N,N’-methylene-bisacrylamide (Figure 15VII). This adsorbent was employed to remove the organic cationic dye MB from effluents in which its concentration was high, yielding a maximum adsorption capacity value of 2967.7 mg g−1.
Additionally, Shoaib et al. prepared a composite material using starch, acrylic acid, and activated carbon from the red alga Pterocladia capillacea with N,N′-methylenebisacrylamide as a crosslinker and ammonium persulphate as an initiator. The adsorbent was assayed for MB dye removal, achieving 1428.6 mg g−1 as the maximum adsorption capacity value [205].
On the other hand, anion exchangers have been obtained by incorporating positive charges into the starch structure by introducing amino groups, as discussed for the other polysaccharides included in this review.
In this context, Zhang et al. [206] obtained a guanidine-containing starch-based resin via chemical modification of starch’s structure with arginine (Figure 16). The material was assayed for the adsorption of dyes. In particular, acid fuchsin, acid orange G, and acid blue 80 were studied, and maximum adsorption capacity values of 21.6, 21.5 and 33.4 mg g−1, respectively, were obtained.

3. Discussion

Results presented along the review clearly show that polysaccharides are not suitable adsorbents in their native form due to low adsorption capacity and gel instability, among other traits. However, when polysaccharides are properly modified, the drawbacks mentioned can be overcome.
On the other hand, it is well known that polysaccharides’ structure is variable and depends not only on the source from which each one is extracted, but also on environmental conditions. For instance, the content of G and M residues in alginates or starch composition (i.e., amylose and amylopectin proportions) are variable according to the season when sources are collected. Consequently, reproducibility of results could be affected considering such variations.
It is important to point out that reactivity to chemical modifications of polysaccharides can be enhanced by subjecting them to processes that increase the accessibility of reagents in their hydroxyl groups. For example, in the work of Gurgel et al. [100], the esterification degree of cellulose was significantly enhanced by carrying out a mercerization process, which reduced packing efficiency and increased the number of hydroxyl groups available for esterification.
It is noteworthy that the use of polysaccharides as support for highly adsorptive materials such as carbon nanotubes, GO, or other nanoparticles has a remarkable advantage: micro-sized water pollution is prevented.
Table 3 summarizes the materials addressed in this review that reached maximum adsorption capacity values that surpassed 200 mg g−1; these are grouped by the type of pollutant (i.e., heavy metals or dyes) and the raw material involved in each case, pH, adsorption kinetic and isotherm models are detailed. It is important to highlight that pH has a critical role in the adsorption process when either the adsorbents or pollutants are sensitive to it. For instance, when the adsorbent structure contains carboxylic groups, its adsorption capacity for cationic pollutants is highly increased at pH levels over 6, at which point this group, in their anionic form, can establish ionic interaction with cations. Conversely, in the case of adsorbents containing amino groups, the adsorption towards anionic pollutants is higher at pH levels below 5, at which point the protonation of the amino groups confers them a positive charge. In the case of pollutants, most dyes have acidic or basic properties, and therefore their structure and charge are pH-dependent, while heavy metals can form insoluble hydroxides at pH above 7 (e.g., Pb (II), Cu (II)).
Nevertheless, since adsorbents’ efficiency could be related not only to the chemical structure of the adsorbent, but also to experimental conditions (such as temperature, adsorbent dose, contact time, initial concentration of the contaminant, among others), comparison between the results given for different authors should be carefully analysed.
Moreover, it is important to point out that, since heavy metals and dyes may have significantly different molecular weights, their adsorption capacity values are not worth comparing.

4. Conclusions

From the analyses of the results presented along the manuscript, it can be concluded that higher maximum adsorption capacity values are related to the final products’ chemical structure and not to the structure of the native polysaccharides.
Moreover, it is important to point out that most of the works summarized herein evaluate the adsorption capacity of the materials regarding certain pollutants in model aqueous systems, while complex matrixes such as wastewater samples have not been analysed so far. Therefore, as far as pollutant analysis is concerned, there is still a long way ahead for the industrial application of the adsorbents reported until now.
Furthermore, it is relevant to highlight that in all the analysed cases, materials were developed in laboratory scales and there is no economic analysis reported at all. Furthermore, most of the studies were only conducted in batches, and continuous column system analyses are still pending in many of the works included here. In this context, it is difficult to determine whether the materials could be scaled up or not to a pilot or industrial level, regarding both technical and economic feasibility. Nevertheless, it is important not to lose sight of the fact that, despite the need for column studies prior to scaling up, batch studies are the first step in the selection of novel materials that are worth submitting to deeper analyses as a means to the industrial scale.
All in all, researchers should continue to put in efforts towards scalability of the materials designed until now. In fact, a useful complementary tool for this feasibility analysis could be the use of computational modelling to predict the potential application of the designed materials in the adsorption process.

Author Contributions

G.D.B.: Investigation, Data curation, Visualization, Writing—original draft, Writing—review and editing. E.R.: Investigation, Data curation, Visualization, Writing—original draft, Writing—review and editing. M.I.E.: Conceptualization, Investigation, Data curation, Funding acquisition, Visualization, Writing—original draft, Writing—review and editing, Supervision. All authors have read and agreed to the published version of the manuscript.

Funding

This research was funded by the Agencia Nacional de Promoción Científica y Tecnológica (PICT2020-00221) and Instituto Tecnológico de Buenos Aires (ITBA).

Acknowledgments

Gema Díaz Bukvic has a fellowship from Consejo Nacional de Investigaciones Científicas y Técnicas (CONICET).

Conflicts of Interest

The authors declare no conflict of interest.

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Polysaccharides 04 00016 g001
Figure 1. Chemical structure of cellulose.
Figure 1. Chemical structure of cellulose.
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Figure 2. Rearrangement of cellulose chains.
Figure 2. Rearrangement of cellulose chains.
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Figure 3. Chemical structure of carboxymethylcellulose.
Figure 3. Chemical structure of carboxymethylcellulose.
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Figure 4. Modification of cellulose with (a) citric acid; (b) succinic acid.
Figure 4. Modification of cellulose with (a) citric acid; (b) succinic acid.
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Figure 5. Chemical structures of anion exchangers derived from cellulose.
Figure 5. Chemical structures of anion exchangers derived from cellulose.
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Figure 6. Chemical structure of mannuronate (M), guluronate (G) and alginate.
Figure 6. Chemical structure of mannuronate (M), guluronate (G) and alginate.
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Figure 7. Egg-box model for G alginate residues and Ca (II).
Figure 7. Egg-box model for G alginate residues and Ca (II).
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Figure 8. Alginate chemical modification described by Zhang et al. [137].
Figure 8. Alginate chemical modification described by Zhang et al. [137].
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Figure 9. Alginate chemical modifications described by Shi et al. [149].
Figure 9. Alginate chemical modifications described by Shi et al. [149].
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Figure 10. Chemical structure of partially acetylated chitosan.
Figure 10. Chemical structure of partially acetylated chitosan.
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Figure 11. Chitosan-modified chemical structure reported by Zhao et al. [162].
Figure 11. Chitosan-modified chemical structure reported by Zhao et al. [162].
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Figure 12. Lignin precursors (monolignols).
Figure 12. Lignin precursors (monolignols).
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Figure 13. Hydrogel of chitosan/sodium alginate/calcium ion reported by Tang et al. [172].
Figure 13. Hydrogel of chitosan/sodium alginate/calcium ion reported by Tang et al. [172].
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Figure 14. Chemical structures of amylose and amylopectin.
Figure 14. Chemical structures of amylose and amylopectin.
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Figure 15. Chemical structures of cation exchangers derived from starch.
Figure 15. Chemical structures of cation exchangers derived from starch.
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Figure 16. Starch chemical modifications described by Zhang et al. [206].
Figure 16. Starch chemical modifications described by Zhang et al. [206].
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Table 1. Adsorption studies carried out over cellulose composite materials (N/R: not reported).
Table 1. Adsorption studies carried out over cellulose composite materials (N/R: not reported).
Composite MaterialAdsorbateOptimum pHIsotherm ModelKinetic ModelMaximum Adsorption Capacity (mg g−1)Reference
Cellulose-based modified citrus peels/calcium alginate compositeMethylene blue (MB)
Crystal violet		6.5LangmuirPseudo-second order923.1
882.0		[50]
Nanocrystalline cellulose/sodium alginate/K-carrageenan composite hydrogelPb (II)N/RLangmuirPseudo-second order351.0[51]
Glutaraldehyde crosslinked calcium alginate/cellulose beadPb (II)5.0FreundlichPseudo-second order206.8[52]
Calcium alginate hydrogels reinforced with cellulose nanocrystalsMB7.0LangmuirPseudo-first
order		676.7[53]
Coffee ground cellulose/sodium alginate double-network hydrogel beads MB
Congo red (CR)		N/RLangmuir-FreundlichPseudo-second order400.5
411.5		[54]
Chitosan/cellulose nanofibril composite membrane MB7.0LangmuirPseudo-first
order		14.7[55]
Zeolitic imidazolate framework-67 modified bacterial cellulose/chitosan composite aerogel Cu (II)
Cr (VI)		6.0N/RPseudo-second order200.6
152.1		[56]
Cellulose/chitosan composite aerogel CR7.0LangmuirPseudo-second order381.7[57]
Ethylenediamine-modified nanofibrillated cellulose/chitosan compositesMB4.0N/RN/R19.5
96.7		[58]
New Coccine2.0
Cellulose microfibril-grafted-hydroxyapatite Pb (II)
Cu (II)		N/RLangmuirPseudo-second order143.8
83.1		[60]
Cellulose-graft-polyacrylamide/hydroxyapatite composite hydrogelCu (II)7.0N/RPseudo-second order175.0[61]
Cellulose/hydroxyapatite nanocompositesChlortetracycline hydrochloride7.0FreundlichPseudo-second order139.4[62]
Supramolecular polysaccharide composite materials from cellulose, chitosan, and crown etherCd (II)
Zn (II)
2,4,5-trichlorophenol		6.0N/RPseudo-second order49.1
15.2
6.4		[63]
Graphene oxide incorporated into cellulose acetate beadsMB7.0LangmuirPseudo-second order369.9[64]
Crystalline nanocellulose anchored to reduced graphene oxide Aspirin
Acetaminophen		4.0N/RPseudo-second order99.0
76.3		[65]
Acrylic acid grafting and amino-functionalized magnetized TEMPO-oxidized cellulose nanofiber Pb (II)5.3FreundlichPseudo-second order122.0[66]
Microcrystalline cellulose/Fe3O4 composite Malachite green7.0FreundlichPseudo-second order2.9[67]
Cellulose/montmorillonite mesoporous composite beads Auramine O dye7.0Redlich-PetersonPseudo-second order1336.2[68]
Directional cellulose nanofiber/chitosan/montmorillonite aerogel Cu (II)
Pb (II)
Cd (II)		2.0LangmuirPseudo-second order181.9
170.2
163.9		[69]
Crosslinked cellulose nanofibrils/alkali lignin/montmorillonite/polyvinyl alcohol network hydrogel MB10.5N/RPseudo-second order67.2[70]
Bamboo nanocellulose/montmorillonite nanosheet/polyethyleneimine gel adsorbent MB10.0SipsFractal-like pseudo-second order361.9
254.6		[71]
Cu (II)5.0
Na-montmorillonite/cellulose nanocomposite Cr (VI)4.0LangmuirSecond order22.3[72]
Electrospun composite nanofiber mats of cellulose/organically modified montmorilloniteCr (VI)3.0N/RN/R18.5[73]
Titanium oxide-bacterial cellulose bioadsorbent Pb (II)7.0N/RN/R200.0[74]
Waste collagen, polyethyleneimine, and carbon dots cross-linked by aldehyde cellulose nanofibersCr (VI)2.0LangmuirPseudo-second order103.3[75]
Cellulose/bentonite-zeolite compositeBrilliant green5.6LangmuirPseudo-second order99.1[76]
Microcrystalline cellulose/bentonite-grafted polyacrylic acid hydrogelCd (II)6.0FreundlichPseudo-second order242.5[77]
3D porous structured cellulose nanofibril-based hydrogel with carbon dotsCr (VI)2.0LangmuirPseudo-second order116.0[78]
Activated carbon/carborundum/microcrystalline cellulose core shell nano-compositeAs (III)
Cu (II)		6.0FreundlichPseudo-second order422.9
423.6		[79]
Table 2. Adsorption studies carried out over carboxymethylated cellulose *.
Table 2. Adsorption studies carried out over carboxymethylated cellulose *.
CMC Substitution Degree (Carboxymethyl Groups/Anhydroglucose Units)ModificationAdsorbatepHIsotherm
Model		Kinetic
Model		Maximum
Adsorption
Capacity
(mg g−1)		Reference
0.17NonePb (II)7.0LangmuirPseudo-second order59.5[38]
0.35NonePb (II)7.0LangmuirPseudo-second order127.0[95]
0.65–0.85Crosslinking in presence of epichloridrineCd (II)6.0LangmuirBoth pseudo-first and pseudo-second order~150.0[96]
N/RCrosslinking in presence of polyacrylamidePb (II)5.0LangmuirPseudo-second order~850.0[97]
N/RCrosslinking in presence of PVACu (II) 5.0N/RN/R~2.3[98]
Cd (II)~0.3
Ni (II)~0.3
Hg (II)~0.1
0.7Crosslinking by heating in presence of sulphuric acid and a further freeze-thawing treatmentAg (I)
Cu (II)
Ni (II)		6.6
5.5
6.4		N/RN/R7.7
6.8
7.2		[99]
* In all cases the best results obtained are shown.
Table 3. Summary table including the materials described that in this review that have at least a maximum adsorption capacity value of 200 mg g−1.
Table 3. Summary table including the materials described that in this review that have at least a maximum adsorption capacity value of 200 mg g−1.
PollutantsRaw MaterialProductMaximum Adsorption Capacity (mg g−1)pHIsotherm
Model		Kinetic
Model		Reference
Heavy metals
As (III)CelluloseActivated carbon/carborundum/microcrystalline cellulose core shell nano-composite422.96.0FreundlichPseudo-second order[79]
As (V)CelluloseCellulose anion exchanger (graft polymerization of cellulose and glycidyl methacrylate)200.36.0Langmuir-FreundlichPseudo-second order[107]
Cd (II)Alginate and chitosanGlutaraldehyde-crosslinked chitosan/alginate composite220.55.8LangmuirPseudo-first order[175]
CelluloseMicrocrystalline cellulose/bentonite grafted polyacrylic acid hydrogel242.56.0FreundlichPseudo-second order[77]
Co (II)ChitosanPorous lignosulphonate/chitosan composite386.06.0LangmuirPseudo-second order[166]
Cu (II)CelluloseBamboo nanocellulose/montmorillonite nanosheets/polyethyleneimine gel adsorbent254.65.0SipsFractal-like pseudo-second order[71]
Activated carbon/carborundum/microcrystalline cellulose core shell nano-composite423.66.0FreundlichPseudo-second order[79]
ChitosanPorous lignosulphonate/chitosan composite283.06.0LangmuirPseudo-second order[166]
Chitosan and celluloseZeolitic imidazolate framework-67 modified bacterial cellulose/chitosan composite aerogel200.66.0N/RPseudo-second order[56]
StarchStarch-g-poly(acrylic acid) hydrogel736.05.0LangmuirN/R[82]
Starch and celluloseStarch-g-poly(acrylic acid) hydrogel with cellulose nanofibers incorporated957.0
Cr (III)StarchStarch-graft-poly(acrylic acid)/organo-modified zeolite651.44.0N/RN/R[203]
Hg (II)CelluloseCitrate cellulose derivative1600.06.5LangmuirPseudo-second order[102]
StarchStarch hydrogels prepared via graft polymerization of acrylonitrile, followed by nitrile groups hydrolysis1250.04.0LangmuirSecond order[200]
Pb (II)AlginatePolyacrylamide/GO/sodium alginate composite240.75.5LangmuirPseudo-second order[207]
Thiol and amido-modified alginate/GO/composite369.65.5LangmuirPseudo-second order[137]
Sugarcane bagasse succinate/alginate composite354.66.0LangmuirPseudo-second order[155]
CelluloseCellulose crosslinked in presence of polyacrilamide840.15.0LangmuirPseudo-second order[97]
Titanium oxide-bacterial cellulose bioadsorbent200.07.0N/RN/R[74]
Cellulose and alginateNanocrystalline cellulose/sodium alginate/K-carrageenan composite hydrogel351.0N/RLangmuirPseudo-second order[51]
Glutaraldehyde crosslinked calcium alginate/cellulose bead206.85.0FreundlichPseudo-second order[52]
Chitosan and alginateGlutaraldehyde-crosslinked chitosan/alginate composite258.65.8SipsPseudo-first order[175]
ChitosanPorous lignosulphonate/chitosan composite525.07.0LangmuirPseudo-second order[167]
StarchStarch hydrogels prepared via graft polymerization of acrylonitrile, followed by nitrile groups hydrolysis264.45.0LangmuirPseudo-first order[201]
Dyes
Acid redCelluloseAmino-functionalized nanocrystalline cellulose555.64.7LangmuirPseudo-second order[105]
AR13, AB92, AR112Cationic cellulose hydrogels crosslinked with poly(ethylene glycol)322.0–447.07.0LangmuirPseudo-second order[106]
Auramine OCellulose/montmorillonite mesoporous composite beads1336.27.0Redlich-PetersonPseudo-second order[68]
Reactive yellowHyperbranched polyethyleneimine cellulose970.875.0LangmuirPseudo-second order[104]
Crystal violetCellulose and alginateCellulose-based modified citrus peels/calcium alginate composite882.06.5LangmuirPseudo-second order[50]
CRCoffee ground cellulose/sodium alginate double-network hydrogel beads411.5N/RLangmuir-FreundlichPseudo-second order[54]
Cellulose and chitosanCellulose/chitosan composite aerogel381.77.0LangmuirPseudo-second order[57]
MB, rhodamine B, orange II, mehyl orangeAlginatePolyaniline-sodium alginate nanocomposite416.7–555.57.0LangmuirPseudo-second order[132]
MBAlginateAlginate/rice husk composite274.96.0FreundlichFractal Brouers-Sotolongo[148]
Porous montmorillonite nanosheet/poly (acrylamide-co-acrylic acid)/sodium alginate hydrogel530.76.8FreundlichPseudo-second order[151]
Alginate and celluloseCellulose-based modified citrus peels/calcium alginate composite923.16.5LangmuirPseudo-second order[50]
Calcium alginate hydrogels reinforced with cellulose nanocrystals676.77.0LangmuirPseudo-first
order		[53]
Coffee ground cellulose/sodium alginate double-network hydrogel beads400.5N/RLangmuir-FreundlichPseudo-second order[54]
CelluloseCellulose crosslinked in presence of polyacrylamide1611.45.0LangmuirPseudo-second order[97]
Bamboo nanocellulose/montmorillonite nanosheets/polyethyleneimine gel adsorbent361.910.0SipsFractal-like pseudo-second order[71]
Graphene oxide incorporated into cellulose acetate beads369.97.0LangmuirPseudo-second order[64]
Chitosan and alginateChitosan/sodium alginate composite foam1488.15.8LangmuirPseudo-second order[171]
StarchStarch, acrylic acid, and activated carbon from red alga Pterocladia capillacea with N,N′-methylenebisacrylamide/ammonium persulphate1428.68.0LangmuirPseudo-first
order		[205]
Starch-graft-polyacrylic acid, crosslinked with N,N’-methylene-bisacrylamide2967.75.8LangmuirPseudo-first
order		[204]
Starch-Ni/Fe-layered double hydroxide composite387.63.0LangmuirPseudo-second order[190]
Methyl orangeStarch-modified ZnMgAl-layered doubled hydroxides1555.07.0LangmuirPseudo-second order[191]
Rhodamine 6GCarboxymethyl starch grafting with N-vinylpyrrolidone363.95.0N/RN/R[202]
Reactive blue 49ChitosanChitosan crosslinked with citric acid esterified β-cyclodextrin498.02.0LangmuirPseudo-second order[162]
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Díaz Bukvic, G.; Rossi, E.; Errea, M.I. Polysaccharides as Economic and Sustainable Raw Materials for the Preparation of Adsorbents for Water Treatment. Polysaccharides 2023, 4, 219-255. https://doi.org/10.3390/polysaccharides4030016

AMA Style

Díaz Bukvic G, Rossi E, Errea MI. Polysaccharides as Economic and Sustainable Raw Materials for the Preparation of Adsorbents for Water Treatment. Polysaccharides. 2023; 4(3):219-255. https://doi.org/10.3390/polysaccharides4030016

Chicago/Turabian Style

Díaz Bukvic, Gema, Ezequiel Rossi, and María Inés Errea. 2023. "Polysaccharides as Economic and Sustainable Raw Materials for the Preparation of Adsorbents for Water Treatment" Polysaccharides 4, no. 3: 219-255. https://doi.org/10.3390/polysaccharides4030016

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