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An Overview on Composite Sorbents Based on Polyelectrolytes Used in Advanced Wastewater Treatment

Advanced wastewater treatment processes are required to implement wastewater reuse in agriculture or industry, the efficient removal of targeted priority and emerging organic & inorganic pollutants being compulsory (due to their eco-toxicological and human health effects, bio-accumulative, and degradation characteristics). Various processes such as membrane separations, adsorption, advanced oxidation, filtration, disinfection may be used in combination with one or more conventional treatment stages, but technical and environmental criteria are important to assess their application. Natural and synthetic polyelectrolytes combined with some inorganic materials or other organic or inorganic polymers create new materials (composites) that are currently used in sorption of toxic pollutants. The recent developments on the synthesis and characterization of composites based on polyelectrolytes, divided according to their macroscopic shape—beads, core-shell, gels, nanofibers, membranes—are discussed, and a correlation of their actual structure and properties with the adsorption mechanisms and removal efficiencies of various pollutants in aqueous media (priority and emerging pollutants or other model pollutants) are presented.


Introduction
Municipal wastewater treatment plants (MWWTPs) face great challenges in optimizing technologies to avoid ecological and human health problems and to ensure environmental sustainability, in direct correlation with the increased pollution due to economic and social growth, wastewater quality discharged into surface waters and climate changes. Industrial activities are responsible for the discharge of effluents with a wide range of inorganic and organic compounds that belong to the priority (PPs) and emerging pollutants (EPs) classes, pharmaceuticals and personal care products, pesticides, heavy metals, detergents, flame-retardants being only few examples of such pollutants. Through their presence, eco-toxicological and human health effects, bio-accumulative and degradation characteristics may influence aquatic biota and the performances and costs of water and wastewater treatment technologies [1]. Moreover, considering the new Circular Economy Action Plan and EU Green Deal there is a huge pressure nowadays on the regional water operators (running water and wastewater treatment plants) to decrease their operational costs and associated environmental impacts and carbon footprints (especially due to energy consumption), while introducing more viable alternatives for wastewater recycling for industries, agriculture/irrigation, aquacultures, trying to recover materials and energy from wastewater sludge [2,3].
MWWTPs collecting wastewater from combined sewers usually remove solids of different sizes, biodegradable organic and inorganic compounds based on conventional processes such as the following: mechanical (bar-screens, grit removal and sedimentation), biological (suspended or attached growth) and tertiary (nitrogen and phosphorous removal) treatment. The implementation of wastewater reuse in agriculture or industry requires the elimination of targeted priority and emerging organic & inorganic pollutants, microorganisms (bacteria, viruses, parasites) by means of advanced wastewater treatment (AWWT) (such as membrane processes, advanced oxidation, adsorption, filtration, disinfection, etc.), that complete the conventional treatment as presented in Figure 1. Although, inorganic and organic pollutants classified as PPs or EPs are detected in wastewater at low concentrations (few micrograms/milligrams per liter), they are toxic, bio-accumulative, low biodegradable and very difficult to remove in terms of technological, energy and environmental efforts. In the European Union, both PPs and EPs are monitored in surface water [4][5][6], but at the moment, in Europe, only Switzerland enforces legal obligations to remove these compounds within MWWTPs [7]. The advanced wastewater treatment for EPs removal (for wastewater recycling and reuse) should consider at least the following criteria: (i) range of treated pollutants, treatment efficiency & removal mechanisms, (ii) environmental reduced impacts, (iii) simplicity of operation & maintenance, (iv) cost-effectiveness, (v) social acceptance [8].
In recent years, numerous classes of inorganic (metal oxides, zeolites, sand), organic (activated carbon, resins, covalent organic frameworks), or composite sorbents have been designed to sorb different classes of organic/inorganic pollutants [9][10][11][12][13][14][15]. Due to some disadvantages (high costs, low sorption capacities, low number of reusing cycles, nondegradable characteristics, secondary pollution) many types of these materials could be difficult to be used in practice at large scale. Recently, natural and synthetic polyelectrolytes were combined with some inorganic materials (SiO 2 , TiO 2 , graphene oxide, Fe 3 O 4 , clays, zeolites etc.) or other organic polymers (cellulose, wood, cyclodextrin, polystyrene (PS), etc.) to create new materials (composite type) as perfect candidates for sorption of toxic pollutants such as pharmaceuticals and heavy metal ions [16,17].
The main objective of this study is to present the recent development on the manufacturing of composite polyelectrolytes with sorption properties of organic and inorganic pollutants from the aqueous effluents. Specifically, this study will provide (a) an overview of the synthesis and characterization of composites based on polyelectrolytes, divided according to their macroscopic shape: beads, core-shell, gels, nanofibers, membranes; (b) correlation of their actual structure and properties with the adsorption mechanisms and removal efficiencies of various pollutants in aqueous media (PPs, Eps, or other model pollutants).

Literature Search and Eligibility Criteria
In this review we exclusively focused on studies that have investigated the composite polyelectrolytes used to remove heavy metal ions and organic compounds from wastewater through sorption processes. The database selected for this research was Scopus and the search was employed from April to September 2021.
For the eligibility criteria [1] we excluded all the studies that: were not written in English (criteria 1); -were not published between 2011-2021 (criteria 2); -did not belong to the subject areas of chemistry, environmental science, chemical engineering, material science, and engineering (criteria 3); -did not contain keywords such as beads OR core-shell OR gels OR nanofiber OR membranes (criteria 4).

Selections of the References
The following keywords have been used in the following combination: composite polyelectrolytes AND wastewater treatment AND sorption AND (heavy metal* OR pharmaceutical*). The search returned 517 publications, but the language of the papers was restricted to English (criteria 1), resulting in 511 documents. We used pharmaceutical compounds as model pollutants for EPs, due to their relevant interest for removal by means of advanced wastewater treatment processes.
We selected the studies published in the period 2011-2021 (criteria 2) ( Figure 2). After the elimination we obtained 457 documents. In this paper we have considered the publications that include research on the following subject areas (criteria 3): chemistry, environmental science, chemical engineering, material science and engineering (425 documents including 253 articles, 121 reviews, 38 book chapters, 11 books, and 2 conference papers).
The next selection includes other keywords related to the type of composite polyelectrolytes presented in this research: beads OR core-shell OR gels OR nanofiber OR membranes (criteria 4), only 395 relevant references were analyzed as full content through manual selection. As the reader will notice in Section 3, our manual selection resulted in the inclusion of articles presenting the adsorptive ability of composite polyelectrolytes concerning dyes. The authors decided so in line with the large use of dyes as model pollutant for the organic pollutants category. In addition, only few articles could be found reporting emerging pollutants elimination using composite polyelectrolytes.

Why Composites Based on Polyelectrolytes?
Polyelectrolytes are charged/chargeable polymers whose repeated ionic/ionizable structural units are higher than 10-15 mol%. Based on their ability to partially/fully dissociate in aqueous environment, polyelectrolytes are usually classified in weak or strong and in anionic and cationic in dependence of charge type. These polymeric compounds have a great potential in water and wastewater treatment (such as coagulation-flocculation process) due to a particular characteristic: the high densities of functional groups bound to a flexible polymeric chain, allowing the intimate interaction at the atomic level with various types of pollutants.
Using polyelectrolyte characteristics, numerous types of composites can be fabricated by covalent bonding or non-covalent bonding (hydrogen bonding, π-π stacking, metal-ligand coordination, ionic, and hydrophobic interactions) between polyelectrolytes and different inorganic/organic partners (Table 1). Composite polyelectrolyte materials, which include mainly polymeric ionic chains, contain a large number and specific stimuli-responsive functional groups with controllable action (detection, immobilization, releasing) toward different classes of pollutants entities found in aqueous environment [18,19]. The main types of polyelectrolytes, polymers, and inorganics entities used in creation of composite sorbents, as well as the main tested pollutants, have been summarized in Table 1. The overview in Table 1 suggests the predominant use of heavy metals and dyes (HM&D) as models for inorganic and organic aqueous pollutants, respectively. From our testing experience, these pollutants present certain advantages as compared to more complex molecules, like emerging pollutants: • chemical structure-HM&D are usually present in solution in ionic form and have smaller molecular weights, allowing them to diffuse more easily through the sorbent's pores and reach the active sites; • range of initial concentration during adsorption tests-HM&D are used up to hundreds of mg/L, while EPs usually are at most in the first few tens of mg/L; • analysis equipment-HM&D can be determined by using more affordable, less time consuming and potentially less sophisticated equipment (e.g., UV-Vis spectrophotometer, atomic absorption spectrometer).
Every sorption process of the active species implies physical (transport, flow, swelling, diffusion etc.) and chemical (interactions, immobilization) aspects. First of all, the pollutant molecules, dissolved in a certain medium, must be transported near to the active site of the composite sorbent. Then, based on physico-chemical interactions between sorbate and sorbent, the sorption process can take place. Therefore, the shape and size of each composite sorbent at macro/nanoscale will dictate the active specific surface available for subsequent chemical interactions. The swelling will influence the diffusion of sorbate through the dynamic pores and the composite particle size will dictate the potential applications at laboratory or industrial scale. For example, composites larger than 10 microns could be used in a column experimental set-up.
Thus, in this study all composites based on polyelectrolytes have been divided according to their macroscopic shape: (1) Beads-high porous materials with high accessibility to the functional moieties; (2) Core-shell, "hard-soft" composites with high surface area; (3) Gels (hydrogels, cryogel monoliths, sponges), stimuli-responsive systems with high surface area; (4) Nanofibers, presenting good mechanical properties with high specific area and (5) Membranes, with sorption and separation in one step ( Figure 3).
The use of inorganic/organic or organic/organic composites with polyelectrolyte(s) as active part of the sorbent proved to be of high interest for immobilization of different pollutant types from aqueous environment, due to the large variety and high numbers of functional groups (carboxylic, sulphonic, amine, imine, hydroxyl) [125]. Immobilization efficiency and selectivity through complexation, ion exchange, electrostatic and hydrophobic interactions were linked to the nature of both functional groups and pollutants. The nature of composite components, the cross-linking density of the synthesized material and the polyelectrolyte architecture significantly influence the sorption properties and kinetics. Thus, after the physical state of composites (shape, size, density, crosslinking degree etc.), the chemical interactions will be the second important parameter that dictates the material capacity for pollutant detection, immobilization, concentration in solid phase and subsequent releasing for a new starting sorption cycle. The sorption process of inorganic (Me 2+ ) or organic pollutants (dyes, pharmaceuticals etc.) are driven mainly by electrostatic interactions, coordinative bonds formation, dipole-dipole or Yoshida Hbonding interactions, and ion exchange interactions. The schematic diagram of all these interactions is presented in Figure 4. This review brings a clear outlook on the benefits of using different moieties types as active sites of composites based polyelectrolytes for the removal by sorption mechanism of a wide range of toxic, undesired pollutants dissolved in water and wastewaters. The following subsections will be in accordance with the physical state of composite materials, such as beads, core-shells, gels, fibers and membranes, where the chemistry behind each pollutant retention is based only on sorptive mechanisms.
Magnetic composites beads based on natural polyelectrolytes have attracted the scientists' attention due to the high sorption/selectivity capacity. Liang and co-workers [31] obtained composite beads with magnetic responsiveness, showing high sorption efficiency toward dyes (MB and CR) and heavy metal ions (Cu 2+ and Cr 3+ ). Gopalakannan and Viswanathan [67] obtained magnetic alginate composites beads by incorporating Fe 3 O 4 into SA network followed by Ce 3+ ionic gelation ( Figure 6). The synthesized beads presented higher sorption capacity for chromate ions (14.29 mg/g) compared with beads without Fe 3 O 4 (9.45 mg/g) and single Fe 3 O 4 particles (9.72 mg/g). In this study it was shown the spontaneous and endothermic nature of chromium sorption. To improve the mechanical stability and porosity/accessibility inside the composite beads, different types of clays (bentonite, kaolinite, montmorillonite), SiO 2 , hydroxyapatite etc., have been included during the beads synthesis [63,65,66,68,76,80], where the inorganic component could act as a cross-linker agent together with small ions, such as Ca 2+ . Pandi and Viswanathan [66] showed that defluorination capacity of hydroxyapatite (1296 mg F − /kg) and SA beads (680 mg F − /kg) increased to 3870 mg F − /kg for SA/hydroxyapatite composite beads. Belhouchat and co-workers [63] used bentonite to obtain SA/bentonite composite beads with high sorption capacity for anionic dyes, such as MB and MO. The authors observed that both anionic and cationic dyes could be immobilized by SA composite beads with bentonite inside. The MO sorption increased with bentonite content of SA composite, while MB sorption decreased.
Uyar and co-workers [82] demonstrated that the drying method of composite beads could have a significant influence onto subsequent sorption of different types of pollutants. Composites that were deep-freezed at −21 • C presented a drastically modified morphology of beads and improved surface area and sorption capacity, compared with beads dried at room temperature. The pollutants sorption capacity and selectivity of synthesized composite beads could be drastically improved by subsequent grafting of different small molecules [98] or polymers (PEI [55], polyaniline [61]) onto the solid beads surface. The PEI beads modified with 3-chloropropanesulfonyl chloride exhibited high removal percentage for Hg 2+ (>87%) and high selectivity in the presence of competing ions (Mn 2+ , Ni 2+ , Fe 2+ , Pb 2+ , Zn 2+ , and Cr 3+ ) [98]. The grafting of PEI onto CS beads, gelated in basic media and sodium dodecylsulphate, increased~3 times the sorption capacity of composite beads toward RB5 [55]. Also, the grafting of polyaniline nanofibers onto SA beads by a sorptionrestricted polymerization method [61] increased the affinity of support for Cu 2+ and Pb 2+ in aqueous media. In the majority of all mentioned studies, the pollutant sorption processes in batch experiments [52,56,63] could be modeled by Langmuir or Freundlich isotherms, pseudo-first or pseudo-second order rate, and intra-particle diffusion model, while Thomas isotherm model was more applicable in column studies [59].

Core-Shell Composites
Many scientists conducted pollutant sorption studies on different types of small inorganic (SiO 2 , TiO 2 , Fe 3 O 4 , clays, minerals, etc.) and organic (active carbon, GO, biochar) solid surfaces [126]. The pollutant immobilization on a certain surface strongly depends on the nature, concentration, distribution and accessibility of material functional groups. Inorganic sorbents present very good kinetics but low pollutant sorption capacity relative to sorbent amount. Polyelectrolytes, with high number of functional groups on unit mass, present very high sorption capacities but low kinetics due to slow diffusion in the collapsed state. Therefore, combination of two categories, inorganic solids and polyelectrolytes, can generate new materials with upgraded properties, mechanical stability, and high sorbate accessibility to a high number of functional groups distributed on a high surface area, fast regeneration, and reusability. These composite materials, with a core-shell design, fulfill the utility in pollutant removal by fast, selective, and high amount immobilization on solid phase.
The core-shell architecture could be achieved by direct deposition of different types of natural/synthetic polyelectrolytes (CS, PEI, humic acid, PAH, PVAm, PAA, PSS etc.) on 2D-cores, such as GO [21][22][23]25,115,116] and Ti 3 C 2 -MXenes [117], or 3D-cores, including Fe 3 O 4 [57,108,122,123,126,127], SiO 2 [24,28,83,90,100,101,103,109], SiO 2 /Fe 3 O 4 [88,128], PS [91], FeS [129], clays [99,111,112], CaCO 3 [102], mesoporous diatomite [89], natural fibers [107] and sand [123]. The direct deposition of the organic or organic/inorganic "shell" onto inorganic or organic "core" could be carried out in (i) one-step, by physisorption [21,89,108,111,112], grafting [23,83,88,100,115,117], ionic or solvent gelation/precipitation [25,27,57,69,128] or (ii) a multi-step procedure, such as layer-by-layer [24,90,[101][102][103]109]. Using a strong polyelectrolyte (PSS), Chong and co-workers [108] obtained a stable magnetite nanoparticles with excellent dye removal efficiency (~94%). By simple PSS sorption onto Fe 3 O 4 , the dynamic light scattering and electrophoretic measurements showed a constant hydrodynamic diameter of 150 nm of the magnetic composites over 5 h measuring. This stable dispersion had 50% higher dye sorption capacity compared with bare magnetite nanoparticles. Also, Yao and co-workers [129] obtained stable core-shell colloids (~65-90 nm) based on FeS and PAA with increased sorption properties for Cr 6+ sorption compared with unmodified FeS. Using direct deposition, by pH inversion precipitation of carboxymethylchitosan onto unmodified and modified silica particles, Aden and collaborators [83] obtained core-shell composites with excellent sorption properties for Ni 2+ (Figure 7). After drying at 100 • C for 24 h, the composite particles were used without further modification steps as Ni 2+ ion sorbent at pH 5 and 7. Sometimes, due to harsh environment conditions (extreme pH, high ionic strength, temperature, etc.), which can delaminate the "shell" of composite, the direct grafting of polymeric chains to the solid "core" or "shell" cross-linking after or during deposition, must be carried out. For more stable composites over wide ranges of environment stim-uli, many authors anchor polyelectrolyte chains covalently to the inorganic core, which contains a linker molecule on surface [88,100,115]. In this way, the new created core-shell composite is more stable in aqueous media and more effective in sorption of different pollutants. The immobilization of "shell" around the "core" could be achieved by chemical cross-linking with bifunctional compounds, such as glutaraldehyde [89,102,103,109,115], epichlorohydrin [23], α,α'-dichloro-p-xylene [24], phtaldialdehyde [91]. Ge and Ma [23] obtained CS/GO composite microparticles by microwave irradiation method using GO, triethylenetetraamine, ECH and CS (Figure 8). Sorption of Cr(VI) onto composite particles showed high values, reaching 219 mg/g at pH 2. The results obtained by batch experiments showed that sorption capacity of synthesized composite increased with temperature and the sorbent material could be recyclable. Bucatariu and co-workers used selective cross-linking to obtain core-shell silica composites based on PEI, PVAm, polylysine, and PAH. This type of composites has been utilized in the removal of dyes [109] and heavy metal ions [90,101,103] from real and simulated waters. The layer-by-layer technique involved in these studies allowed a controlled deposited polyelectrolyte amount onto spherical silica particles. Furthermore, the subsequent glutaraldehyde cross-linking stabilized the polycation layer onto each individual solid particle. To increase the multilayer flexibility and functional groups accessibility toward pollutant molecules, the polyanion has been removed from the cross-linked multilayer in extreme basic medium, as it can be seen in Figure 9. The fast kinetic of Cu 2+ sorption and high sorbed amount of anionic dyes (BCG, CR) after polyanion extraction, confirmed the polyelectrolyte multilayer stability and flexibility after cross-linking and polyanion extraction. Based on distribution parameter and relative atomic concentration of elements on surface, the authors demonstrated that silica/(PEI) 10 composite particles can clean (>95%) a simulated water contaminated with four heavy metal ions (Cu 2+ , Co 2+ , Ni 2+ , Cd 2+ ), if the ratio between number of composite functional groups and number of ions is higher than~9 (non-competitive regime). The competitive sorption between different metal ions showed that the composite had high selectivity for Cu 2+ . Subsequent chemical modification of stable cross-linked core-shell composites with small molecules, i.e., disodium ethylenediamine tetraacetate (EDTA-2Na), increased the sorption capacities by creation of new functional groups onto core-shell surface. Zhang and co-workers [21] obtained GO/CS composites modified with EDTA-2Na, with higher sorption capacity for Cr 6+ than unmodified GO/CS. The authors showed that ion sorption strongly depends on pH and GO/CS composite could be used in 7 multiple sorption/desorption cycles with a loss capacity of 5%. Removing phosphate and arsenate ions from eutrophic waters is, also, of paramount importance, therefore the design of lowcost, high-efficient composite sorbents for anionic charged pollutants removal has remained a huge challenge. Kloster and co-workers [130] and Pincus and co-workers [131] created nano-iron/chitosan composites for arsen removal from aqueous media, while Zong and co-workers [132] modified lignin with PEI to create an excellent composite for phosphate ions removal. These composites showed a fast and high removal capacity toward the anionic species.

Composite Gels (Hydrogels, Monolith Cryogels, Sponges)
Composite gels based on polyelectrolytes represent a class of composite soft materials consisting of hydrophilic charged/uncharged chains that absorb a high content of water (>95%) [133]. These low cost and high efficient 3D-dimensional networks are based on polyelectrolytes of different types: (i) synthetic, such as: PEI [36,92], PAH [93,118], PAA [38], PAMPS [106,118,119], or (ii) natural, like the following: CS [30,[32][33][34]38,39], modified CS [37,84,85], SA [33,70,73], modified SA [72], modified cellulose [104]. Many studies reported the incorporation of organic/inorganic entities into the gel structure, including GO [70,73], Fe 3 O 4 [36,106], SiO 2 [113], zeolites [30,32], clays [72]. In this way, these gel composites gain more structural integrity, useful in the water treatment field. The presence in the gel structure of different types of functional groups (-NH 2 , -NH-, -COOH, -SO 3 H, -OH), confirmed by the solid-state characterization methods, facilitates the pollutant sorption from aqueous environment. The gel composite architectures presenting a high number of functional groups are obtained by different polymerization methods, as presented in Table 2. The synthesis and stability of composite gels depends on the polyelectrolyte chain concentration, pH of medium, ionic strength, temperature, nature of ionic groups, which dictates the subsequent types of interactions between chains and polymer mixing ratios. By simple mixing, Ramakrishnan and collaborators [34] obtained CS/karaya gum composite sponges with removal capacity for both anionic (MO) and cationic (MB) dyes. Table 2. Synthesis methods of gel composites sorbents.

Synthesis Methods
Monomers or Bifunctional Agents References Step 1 Step 2 Free-radical (co)polymerization - Mixing of polymer chains with monomers Free-radical polymerization - [38,39,106] The combination of Karaya gum and CS polymeric chains brings a stable composite sponge with negative and positive functional groups. The authors studied the swelling profiles and optimized the ratio between these two natural polyelectrolytes for better sorption properties toward negative and positive charged dyes. Harris and McNeil [104] studied a dye sorption onto a locally formed hydrogel between quaternized cellulose and sulfated wood pulp. In this study, the sorption process took place during gel formation. Combining high functionalities of polyelectrolytes and high porous structures of composite gels with magnetism (Fe 3 O 4 ) results in a versatile magnetic porous composite gel with superior sorption capability and facile separation [36,106]. Using one-pot synthesis approach, You and co-workers [36] obtained Fe 3 O 4 /CS-PEI composite nanogels with high number of positive charges and magnetic responsiveness ( Figure 10). The synthesized porous sorbent, with good mechanical strength, had a high sorption capacity for CR due to the high surface area resulted from multi-level pore distribution. To remove hydrogel from sorption medium, Ruiz and co-workers [106] synthesized in situ magnetic particles during the free-radical polymerization of modified gelatin in the presence of sodium styrenesulfonate and AMPS.
Magnetic separation is a very promising approach for water treatment due to easy recovery of composite sorbent from contaminated medium by magnetic field. Monoliths with macroporous hydrophilic 3D polymeric matrices could be obtained by free-radical polymerization of different monomeric units at high temperature [124] or subzero temperature of reaction medium [118]. Using an oil/water high internal phase emulsion, Makrygianni and co-workers [124] polymerized the 2-(methacryloxy)ethyl]trimethylammonium chloride in continuous aqueous phase. The authors showed that the gel with 10% cross-linking reached very fast higher water uptake (18 times) and anionic dye subsequent immobilization were characterized by a synergistic of chemisorption and diffusion. 3D monoliths obtained under freezing temperature are denoted cryogels. Also, under freezing temperature of reaction medium, the composite cryogels could be obtained directly from polymers by covalent cross-linking of chains or by monomer polymerization in the presence of other polymer chains or inorganic entities [30,32,84,92,93]. The fast removal and high sorption capacities of cryogels are completed by the modifiability, fast regeneration and high number of reusing cycles of composite cryogels. Baimenov and colaborators [118] obtained macroporous composite cryogels by free-radical polymerization of N,N-dimethylacrylamide, allylamine, N,N-methylenebisacrylamide, AMPS) ( Figure 11). In this case, the porous structure of gel has been obtained due to ice crystals formed inside, and the 3D network strength is due to the monomer cryocentration effect. Figure 11. Schematic representation of composite cryogel synthesis (reprinted with permission from ref. [118]).
The monoliths obtained in pharmaceutical syringes has been sliced in 10 mm diameter pieces, fully characterized, and studied in Hg 2+ removal from contaminated waters. Humelnicu and co-workers [32] studied the heavy metal ions interactions with a composite cryogel obtained from a zeolite (clinoptilolite) and an ion-imprinting CS in a unidirectional ice-templating method ( Figure 12). The CS matrix with zeolite embedded formed an anisotropic composite cryogel where the fast metal ion diffusion has been attributed to the 1D-orientation and interconnectivity of flow channels. The removal efficiency of the synthesized cryogel reached 50% in 30 min. and the equilibrium after 150 min. To study the influence of the imprinting technique, the authors used binary, ternary, and five-component metal ion simulated mixtures. Under competitive conditions, the heavy metal ions followed the sorption order: Cu 2+ > Fe 3+ > Ni 2+ > Zn 2+ > Cr 3+ . Cryogels based on metal-chelates with super macroporous structure could had a high affinity towards pharmaceuticals, such as ciprofloxacin [84]. It was shown that cryogel with Cu 2+ and Al 3+ inside the carboxyethyl CS network improved the ciprofloxacin recovery up to 98%, if 7 < pH < 10. The sorbent affinity for the drug increased with the metal content, reaching 280 mg and 390 mg/g cryogel for Cu 2+ and Al 3+ chelates, respectively.
The composite gels based on polyelectrolytes have been studied by swelling, rheology, morphology, thermal measurements before and after multiple interaction with aqueous pollutants (heavy metals, dyes, pharmaceuticals, pesticides, etc.). Usually, the pollutant molecule immobilization in the gel network is a synergistic process between chemisorption and diffusion, the composite gels being characterized by relative mechanical stability and very high sorbed amounts which make them suitable for using in water treatment technologies.

Nanofibers
Increasing the diversity of pollutants in aqueous media requires development of multifunctional membranes, among already discussed composite materials based on polyelectrolytes. A very interesting and practical approach in this direction is the membrane (polymeric, mixed-matrix, ceramic) modifications with composite electrospun nanofibers. The following subsection describes the principal types of polyelectrolytes and other organic/inorganic entities used in nanofibers synthesis, the factors that influence the composite stability and sorption capacities toward different inorganic/organic pollutants. According to Figure 13, composite nanofibers used in pollutant removal by sorption are fabricated by (i) electrospinning of a charged polymer solution or melt in high electric field [13,40,[43][44][45]48,49,58,71,74,75,134], (ii) subsequent chemical modification of electrospun nanofibers [46,47,134], and (iii) electrospinning combined with electrospraying techniques [41]. The physico-chemical properties of composite nanofibers depend on the nature of polyelectrolyte and the partner involved, the solvent type, the molecular weight, and concentration of polymeric chains, which determines the viscosity and surface tension of solution. If the polymer concentration is low, the fiber appears as beads on string, and if the concentration is high enough the fibers are homogenous under tensile force [94]. The composite nanofibers with controlled morphology are formed after the solvent evaporation. Composite polyelectrolyte nanofibers based on CS [40,41,[43][44][45][46][47][48][49]58], SA [71,74,75], PAA [49,71], and PEI [134] attracted great attention due to high specific surface area, high porosity, superhydrophilicity, and faster sorption rate toward small and large pollutant molecules. To improve solvent resistance and mechanical strength, nanofibers, were annealed at high temperature (150 • C) [49,71], chemically treated with bifunctional agents, e.g., ECH [46], GA [48] etc., or reinforced with organic/inorganic particles, e.g., GO [58], rectorite [41], TiO 2 [40] etc. Moreover, the reinforcing process increased the sorption capacity of the nanofiber support [40,41,58]. Some authors used poly(vinyl alcohol) to increase the spinnability during the electrospinning process [43,47,58]. Wang and coworkers [71] obtained PAA/SA composite nanofibers by electrospinning followed by a thermal cross-linking at 150 • C. The PAA/SA were characterized by high swelling ratio, excellent stability, high sorption capacity toward Cu 2+ ions (~600 mg/g nanofiber) and good reusability. Moreover, the authors converted the sorbed toxic Cu 2+ ions by NaBH 4 reduction into Cu nanoparticles with subsequent application in catalysis.
Chen and collaborators [47] functionalized oxidized CS nanofibers in solid state with an antibacterial agent, polyhexamethylene guanidine. In this study it was shown that this composite, with grafted agent, combined the antibacterial (S. aureus and P. aeruginosa) activity with very good sorption for Cu 2+ (57 mg/g) and CR (183 mg/g). Bai and co-workers [58] used GO to synthesize composite nanofibers based on modified CS with a quaternary amine. The authors showed the double role of GO: first, the particles enhanced the ability of polycation to form nanofibers and second, they increased the removal capacity by sorption of porcine parvovirus, a non-enveloped virus. The hydrophobicity of GO and high charge density of polyelectrolyte created a composite with 95% retention for the virus. Razzaz et al. [40] used two methods for CS/TiO 2 composite nanofibers synthesis: (i) the "coating method", where electrospun CS nanofibers were dipped in a TiO 2 dispersion and (ii) "entrapped method", where composite nanofibers have been obtained by electrospinning of CS and TiO 2 mixture. The chitosan/TiO 2 nanofibers prepared by entrapped method have been reused in five consecutive sorption/desorption cycles of Cu 2+ (710 mg/g) and Pb 2+ (526 mg/g), the support being more selective for Cu 2+ in a binary mixture. Composite nanofibers formed from electrospun PS with electrosprayed CS-rectorite (layered silicate) nanospheres on surface, have been synthesized by Tu and co-workers [41]. Also, (PS/CS-rectorite) n composite nanofibers were obtained in a electrospinning-electrospraying alternately deposition approach (Figure 14). In the sorption experiments, the more hydrophylic PS nanofibers coated with CS-rectorite nanospheres showed very good Cu 2+ sorption (134 mg/g). The authors improved this value by adding Ca 2+ in the composite, due to additive cation exchange mechanism. After three sorption cycles, the nanofibers maintained the sorption ability at~75%. The pollutants removal by the composite nanofibers mentioned above and others, have been carried out in batch experiments [43,47,74] and in dynamic conditions [48]. The adsorption process in batch conditions was successfully modeled by Langmuir [46,74], Freundlich [47,74] or Temkin [47] isotherms, and by pseudo-first or pseudo-second order kinetic models [43,47,75]. The composites nanofibers based on polyelectrolytes have been characterized by modern techniques to obtain information about size and morphology, chemical modifications, distribution of phases, behavior in water etc. The pollutants sorption properties of nanofibers based on polyelectrolytes are strongly related to the nature and ratio of polyelectrolytes and components involved in composite creation, the nanofiber size, which dictates the specific surface area, the swelling of composite, the nature/strength of interactions between support and pollutant and finally, on the characteristic of sorption medium (ionic strength, pH, temperature, solvent, etc.).

Membranes
Composite membranes based on polyelectrolytes are one of the most used materials in removal of unwanted molecules from surface/waste waters, due to sorption and rejection functions of it. In this review we took under consideration principal types of composite based on polyelectrolytes which are capable to remove pollutants only by sorptive mechanisms. Because of the large number of reviews published in the field of membranes used in water cleaning [18,[135][136][137][138][139][140][141], in this review only some pollutant sorptive composite polyelectrolyte membranes will be exemplified. Sorptive membranes have the same sorption capacity as sorbents, therefore they are known as membrane sorbents (chelating, complexation, and ion exchange membranes) with affinity for heavy metal ions and organic molecules [142]. A schematic overview of the principal types of composite membranes is shown in Figure 15. The composite membranes can be fabricated by deposition (coating, grafting, self-assembly) of organic/inorganic components onto an unmodified membrane [28,95,[143][144][145]. Using a covalent bonded polyelectrolyte onto a cellulose membrane, Pei and collaborators synthesized a sorptive composite membrane with high abilities for metal ions (Cu 2+ , Pb 2+ , Cd 2+ ) immobilization. This membrane could be easy regenerated and recovered, reaching a~200 mg/g sorption capacity. The covalent bonding of a reactive polymer [poly(maleic anhydride-co-acrylic acid)] to the cellulose acetate membrane extended the membrane lifetime in water cleaning, and the LbL deposition method increased the polymer amount, therefore increasing the heavy metal sorption capacity [95]. To improve the characteristics of CS membranes, Sahebjamee and co-workers used two methods: (i) a selective dissolution of a porogen [poly(vinyl pyrrolidone)] and (ii) a mixed solvent system with one volatile solvent (acetone) [144]. The authors showed that adding acetone to the composite membrane mixture, the Cu 2+ sorption capacity increased by 50%. The reusability test with EDTA-2Na demonstrated that after four sorption/desorption cycles, the composite membrane maintained the capacity for heavy metal ions sorption with only 8% reduction.
Due to the low manufacture costs and easy chemistry modification, the composite polymer membranes are popular and frequently used in the water treatment technologies. Such composite membranes still lack some properties required in membrane processes, such as high selectivity towards low solutes. In this way, many studies have been carried out for enhancement of sorption/separation performance of composite membranes. The creation of membranes with high permeability and selectivity, rejection and sorption capacities, antifouling properties are the biggest issues among researchers all over the world who work in the development of membrane materials.

Conclusions and Future Research Directions
In summary, this study discussed about the multiple synthesis approaches utilized in creation of different types of composite materials based on polyelectrolytes with subsequent application in pollutants removal from synthetic/waste/surface waters.
In the sorption experiments the physical aspects dictate the pollutant path to the active sorption site from the composite and therefore the first criteria in selection of composite was the composite shape (beads, core-shell, gels, nanofibers, and membranes). Using "soft" polyelectrolytes, with high and diverse number of functional groups, in combination with "hard" inorganic components could results in an "upgraded" composite material with synergic properties in pollutant retention. All pollutants sorption processes could be modeled, mostly by Langmuir and Freundlich isotherms, pseudo-first or pseudo-second order rate. The composites based on polyelectrolytes have been characterized by different solidstate analysis methods, including the following: scanning electron microscopy, Fourier transform infrared spectroscopy, X-ray photoelectron spectrometry, X-ray diffraction, thermogravimetry analysis, dynamic light scattering, transmission electron microscopy, BET analysis. The obtained data provide physico-chemical information about the composite state before and after interaction with different types of pollutants. It can be summarized that composite polyelectrolytes are promising adsorbents for the elimination of inorganic and organic pollutants from wastewater, both in batch and dynamic experimental set-up. There is extensive work done testing these materials using heavy metal ions and dyes as models for the inorganic and organic pollutants, respectively. Only few studies were found to discuss the removal of EPs, such as pharmaceuticals.
The current limitations/challenges of pollutants removal by means of sorption processes using composite polyelectrolytes refer to the following: • the individual removal of EPs or PPs compounds and not their simultaneous removal, in adsorption columns, the latter being a solution for both the complex nature of wastewater matrix and the operational requirements; • usually, a combination of two or three AWWT processes might be needed to remove both inorganic and organic PPs/EPs; • when a combination of sorption is made with processes that are not selective (such as AOPs), intermediates that could be more toxic than the initial compounds could be generated in the final effluent; • phase transfer of pollutants on solid surfaces (membranes, sorbents) and further regeneration might also contribute to supplementary environmental impacts; • the technical assessments are used frequently to evaluate the feasibility of sorption or combined processes; there are only few studies that consider the sustainability assessments (by means of Life Cycle Assessment, Life Cycle Costing, carbon footprint, multi-criteria decision analysis, etc.) to design specific functionalized materials.
Overall, this paper could be a starting point in the identification of old "partners/components", but new by combination methods and different techniques in achieving versatile materials with adaptive behavior for the present demands of wastewater treatment.