Innovative Magnetite Based Polymeric Nanocomposite for Simultaneous Removal of Methyl Orange and Hexavalent Chromium from Water

: One of the most important directions for environmental remediation is the effective removal of dyes and toxic heavy metals from water using newly fabricated nanoadsorbents. Here, magnetic Fe 3 O 4 nanoparticles were combined with nitrogen-containing functional group polymers chitosan (CS) and polypyrrole (ppy) to synthesize a nanocomposite (polypyrrole@magnetic chitosan) useful for removing methyl orange (MO) and hexavalent chromium (Cr (VI)) from water. The physicochemical properties of the nanocomposite were determined using SEM, TEM, XRD, FT–IR, and TGA techniques. The effect of different factors on the adsorption system was studied including the contact time, pH, and the effect of co-existed ions. The kinetic study illustrated that the adsorption ﬁt well with Langmuir isotherm. The maximum adsorption capacity of MO and Cr (VI) was found to be 95 and 105 mg/g, respectively. The reusability of the nanocomposite was studied for up to ﬁve cycles using 0.1 M NaOH as eluent with a slight decrease of adsorbent efﬁciency. Furthermore, the removal mechanism studied suggested the removal of MO via adsorption and Cr (VI) via chemical reduction and adsorption. This study suggests that a ppy@magnetic chitosan nanocomposite is a promising nanoadsorbent for removing MO and Cr (VI) from water. interaction and coating of chitosan and polypyrrole over the magnetite nanoparticles. The appearance of the new band at 571 cm − 1 indicates the presence of magnetite as this band is characteristic of magnetite. The strong electrostatic interaction between NH 4+ groups in both polymers (chitosan and ppy) and the negatively charged magnetite surface was indicated from the shift of the Fe–O bond peak at 581 and 585 cm − 1 , which is characteristic of magnetite (571 cm − 1 ). FT–IR results indicate the good integration of chitosan, ppy, and Fe 3 O 4 nanoparticles in the fabricated ppy@magnetic chitosan nanocomposite.


Introduction
Environmental degradation and the lack of clean water have become universal problems associated with the fast increase in industrial activity and social economy and should be solved to maintain a high-quality life [1][2][3]. Recently, great attention has been paid to water treatment for heavy metals [4,5] resulting from steel fabrication, leather tanning, and metal processing and from toxic dyes from the paper, cosmetics, plastics, textile, and food industries. Among these pollutants, the organic dye methyl orange (MO) can cause severe health problems like jaundice, tissue necrosis, tachycardia, vomiting, and cyanosis. Furthermore, as a conventional toxic heavy metal, chromium not only causes significant damage to human health, but also generates extreme environmental contamination that is hard to remediate [6]. Trivalent chromium Cr (III) and hexavalent chromium Cr (VI) are the two oxidation states of chromium [7]. Cr (VI) is carcinogenic and known to be a very dangerous contaminant, while Cr (III) is less toxic to humans and other organisms and is less movable in environmental systems [8]. According to the World Health Organization (WHO), the allowable level of Cr (VI) in water must not exceed 0.05 mg/L [9]. However, in wastewater from chromium electroplating, the Cr (VI) levels were found to reach 100 to 500 mg/L. Thus, the transformation of Cr (VI) to Cr (III) via an efficient reduction concept and the efficient adsorption of MO can greatly decrease the possible hazard of Cr (VI) and MO dye to animals, humans, and the environment [10,11]. Water contamination from chromium and dye has been widely remediated over the past years. In this context, Cr (VI) and MO have been efficiently removed using various techniques including adsorption, electrochemical methods, reduction, biological remediation, ion exchange, and chemical precipitation [12][13][14][15]. Due to its low cost, great efficiency, and simple processing procedures, adsorption is considered the most promising method. Several adsorbents have been proposed for the effective removal of MO and Cr (VI): carbon nanomaterials [16,17], layered double hydroxides [18,19], agricultural waste [16], chitosan [20], metal oxides [21], zeolites [22], and clay minerals [23]. The biocompatibility, nontoxicity, and biodegradability of chitosan make it attractive among other materials for removing of pollutants from water. Chitosan is a polysaccharide with a linear structure resulting from the alkaline treatment of the second-most abundant biopolymer in nature (chitin), which is present in the shells of lobsters, crabs and shrimp [24]. Chitosan is bio-attracted to negatively charged moieties and is water soluble because of an amino group that has a pKa of 6.5, causing it to be easily protonated in a neutral medium and acidic solution. Its molecular structure has large numbers of hydroxyl and amino groups that provide chelation power toward different metal ions [25]. Although adsorption is the most efficient method for Cr (VI) and MO removal, it is considered to be nondestructive, and the regeneration of the adsorbed materials limits the application of chitosan to treat real wastewater. Additionally, only the phase transition of contaminants can be realized by adsorption alone although their intrinsic essence (physicochemical property and toxicity) remains unchanged. Therefore, the best solution is to fabricate a material that can provide in situ chemical reduction of Cr (VI) to Cr (III) (considered less toxic with useful characteristics for organisms) and the simultaneous adsorption of both MO and Cr (VI); however, the association of reduction removal with adsorption has rarely been studied. Moreover, the common recovery techniques used for adsorption-centrifugation, sedimentation, and filtration-have several problems, including cost, high energy consumption, and low potency. The continued recycling of chitosan powder may not be easy due to its biodegradability; however, its adsorption ability has been improved using nanotechnology, which allows the incorporation of nanomaterials in the adsorbent materiel providing very small particle size and large surface area. However, these types of nanoadsorbents still suffer from decreased recycling performance and a complex separation process. Lately, as an adsorbent and adsorbent carrier, magnetic nanoparticles have shown exceptional properties such as simple chemical modification, a large specific surface area, and excellent magnetic characteristics and have attracted the attention of environmental engineers [26,27]. However, the lack of functional groups and the agglomeration of magnetic nanoparticles reduce their adsorption of pollutants. Accordingly, the development of a novel recyclable material having a high adsorption ability necessitates combining the benefits of polymer materials and magnetic nanoparticles (NPs). In recent years great attention has definitely been paid to magnetic chitosan nanocomposites constructed with a magnetic core of hematite (Fe 3 O 4 ) NPs and a chitosan shell [28]. The fast and easy separation of an adsorbent by a commercial magnet as well as excellent mechanical features were provided via the combination of both magnetic NPs and a chitosan biopolymer. Furthermore, the adsorption capacity of magnetic chitosan can be increased by surface modification through the existing amino and hydroxyl groups on its surface. As previously reported, the modification of chitosan with different organic functional moieties (xanthate, α-ketoglutaric acid, thiourea, and ethylenediamine) could enhance its adsorption capacity toward different pollutants [29]. The low synthesis cost, biocompatibility, and better environmental stability enhanced the application of a polypyrrole (Ppy)-conducting polymer for heavy metal removal from water [30]. Polypyrrole is a polymer with a molecular structure containing high numbers of imine groups that provide adsorption sites toward different dyes and metals. In addition to that, the imine groups provide a reduction capacity to convert Cr (VI) to Cr (III). Thus, Ppy can remove hexavalent chromium ions from water via both reduction and adsorption, and remove MO via adsorption. Based on this information, the in situ chemical reduction of Cr (VI) and the simultaneous adsorption of both Cr (VI) and MO could enhance the adsorption capacity. Interestingly, excellent separation ability could be obtained by fabricating a novel nanocomposite containing the three parts to exploit the advantages offered by each component: (i) reductant and adsorbent ability of polypyrrole; (ii) large number of hydroxyl and amino groups of chitosan; and (iii) magnetic characteristics of hematite nanoparticles (Fe 3 O 4 ). As far as we know, there is no similar study. In particular, this novel nanocomposite detoxified water of both hexavalent chromium Cr (VI) and MO. Herein, the novel nanocomposite was synthesized via the combination of CS, Fe 3 O 4 NPs, and polypyrrole. First, a one-step co-precipitation method was used to synthesize magnetic chitosan by mixing two oxidation states of iron with chitosan followed by the modification of magnetic chitosan with polypyrrole using oxidative polymerization to produce the nanocomposite ppy@CS/Fe 3 O 4 . This nanocomposite was tested to remove MO and Cr (VI) from water. The chemical composition, surface structure, and morphology of synthesized ppy@CS/Fe 3 O 4 were characterized via XRD, FT-IR, SEM, and TEM. In order to understand the removal mechanism, the effect of different factors on adsorption behavior (contact time, initial concentration, and pH) was studied. Lastly, the ppy@CS/Fe 3 O 4 nanocomposite was found to remove Cr (VI) via in situ chemical reduction and adsorption while MO was also adsorbed. This nanocomposite was found to be very promising for removing metals and dyes from water as shown by its recyclability and the stability of the obtained data.

Polypyrrole Magnetic Chitosan Synthesis
Firstly, the magnetic chitosan was prepared via the co-precipitation method as described in our previous work [31]. Briefly, two oxidation states of iron (FeCl 3 and FeSO 4 solutions) were mixed in a conical flask in 2:1 molar ratios, respectively, followed by the dropwise addition of aqueous ammonia (33%, v/v) accompanied by vigorous stirring under a nitrogen atmosphere for 30 min. After that, the nanoparticles were washed four times with distilled H 2 O and collected with a permanent magnet. Then, a reverse-phase suspension method was used for the synthesis of magnetic chitosan in which a mixture of 0.6 mL of tween 80, 54 mL of mineral oil, and 200 mg of synthesized Fe 3 O 4 NPs) was supplemented with 1% (w/v) of chitosan dissolved in an acetic acid solution. For 40 min, the resulting magnetic chitosan was stirred and sonicated followed by the addition of (4 mL, 25% w/v) glutaraldehyde. Stirring continued up to 5 h. Then, a permanent magnet was used to separate the synthesized magnetic chitosan, which was washed several times with acetone followed by drying at 45 • C in a vacuum. Secondly, the synthesized magnetic chitosan was modified using pyrrole monomers according the oxidative polymerization method, and 0.6 g of magnetic chitosan was added to 100 mL of water. Then, 2.5 mL of pyrrole was added to the previous mixture followed by the addition of (5.0 mL, 1M) HCl solution. For 30 min, this mixture was stirred in an ice bath. An aqueous solution of ammonium persulfate (4 g in 20 mL) as initiator, was added to the mixture and stirred vigorously for four hours in an ice bath. Then, to 100 mL aqueous ammonia (33%, v/v) the recovered nanoparticles were added under continuous stirring for 13 h. Then, the product was washed several times with distilled water and ethyl alcohol followed by separation with a magnet and dried for 13 h at 75 • C.

Nanocomposite Characterization
The synthesized ppy@magnetic chitosan nanocomposite was characterized using different instruments including a UV/vis spectrometer, Raman spectrometer, magnetometer, thermogravimetric analysis (TGA) measurement, Fourier transform infrared (FT-IR) spectrophotometer, X-ray diffraction (XRD), scanning electron microscope (SEM), and transmission electron microscope (TEM). A UV spectrometer (UVD-2960, Labomed Inc., Los Angeles, CA, USA) was used to measure UV-visible absorption spectra. A triple Raman spectrometer (Horiba, Horiba Inc., Ann Arbor, MI, USA) was used to measure Raman spectra. A vibrating sample magnetometer (Lake Shore 7410, Lake Shore Cryotronics Inc., Westerville, OH, USA) was used to measure the magnetization of the nanocomposite. A Perkin Elmer, STA 6000 (PerkinElmer Inc., Shelton, CT, USA) was used to perform the thermogravimetric analysis in the temperature range of 30-800 • C with 30 • C min −1 of heating rate under a nitrogen atmosphere. A Bruker, Tensor 27 FT-IR (Karlsruhe, Germany) spectrophotometer was used to perform FT-IR spectra in the range of 400-4000 cm −1 at room temperature and collected at a resolution of 4 cm −1 . A GNR APD-2000 PRO (GNR, Cairo, Egypt) diffractometer was used to measure XRD using Cu Ka radiation (λ = 1.5406 Å) operated at 45 kV. The diffraction intensities were recorded over the 2θ ranging from 5 to 90 • with the constant scanning rate of 1 • ·min −1 . A TEM (JEM-2100F, Hillsboro, OR, USA) operating at 200 kV and a SEM (Hitachi S4800, Hitachi, Tokyo, Japan) were used, respectively, to study the size and morphology of the nanocomposite.

Adsorption Batch Experiments
A stock solution (1.0 g/L) of MO and dichromate salt (K 2 Cr 2 O 7 ) were prepared in distilled water and used for further dilution. For the study of the effectiveness of ppy@magnetic chitosan for removing MO and Cr (VI), adsorbent experiments were conducted in batch mode using 100 mL bottles. In each batch, 100 mg of the adsorbent (ppy@magnetic chitosan) was added to 50 mL of the pollutant solution (100 mg/L). The pH was adjusted using 1.0 M of HCl and 1.0 M of NaOH. Then, the samples were incubated under shaking (200 rpm at 25 • C) using a thermostated shaker. A permanent magnet was used to recover the adsorbent at certain intervals. The remaining supernatant was analyzed for MO and Cr (VI) residual concentrations using a UV-Vis spectrophotometer at λ max of 465 and 541 nm, respectively. The effect of different parameters on adsorption performance (pH, contact times, and competing ions Cl − , HCO 3 − , and SO 4 2− ) was studied. The recyclability of the adsorbent was also studied by immersing it after the experiment in 1.0 M NaOH as eluent (for one hour) then shaking it for 13 h. To examine the ppy@magnetic chitosan stability, the recovered adsorbent (with a magnet) was washed with water and ethyl alcohol four times, and then vacuum dried at 75 • C for 1 day. All adsorption experiments were performed in triplicate. The removal percentage (%) and adsorption capacity (mg/g) were determined according to the following equation: Each symbol of the above two equations has a well-known meaning. V denotes the volume of solution, m denotes the mass of ppy@magnetic chitosan, and C i and C t represent the initial and final concentration of MO and Cr (VI) pollutants, respectively.

Nanocomposite Characterization
The morphology, size, and shape of synthesized magnetic chitosan and ppy@magnetic chitosan were characterized using SEM and TEM images as shown in Figure 1. According to Figure  Each symbol of the above two equations has a well-known meaning. V denotes the volume of solution, m denotes the mass of ppy@magnetic chitosan, and Ci and Ct represent the initial and final concentration of MO and Cr (VI) pollutants, respectively.

Nanocomposite Characterization
The morphology, size, and shape of synthesized magnetic chitosan and ppy@magnetic chitosan were characterized using SEM and TEM images as shown in Figure 1. According to Figure 1a, the SEM image of magnetic chitosan indicated the presence of abundant pores with rough surfaces. The surfaces of the material showed the presence of several spherical particles of about 26 nm that represent the magnetite nanoparticles (Fe3O4), thus signifying their effective construction in the fabricated composite. As observed, there was no clear aggregation phenomenon to indicate the excellent distribution of magnetite nanoparticles over the surface of composite. According to Figure  1b, the ppy loading over magnetic chitosan for the synthesis of the ppy@magnetic chitosan nanocomposite provided a smoother surface compared to that of magnetic chitosan. Polypyrrole was successfully loaded over the magnetic chitosan, which clearly indicated the presence of coated Fe3O4 nanoparticles, which were mainly implanted between the chitosan and polypyrrole (in the interior of the formed ppy@magnetic chitosan nanocomposite). According to Figure 1c and Figure 1d, the ppy@magnetic chitosan nanocomposite As observed, there was no clear aggregation phenomenon to indicate the excellent distribution of magnetite nanoparticles over the surface of composite. According to Figure 1b, the ppy loading over magnetic chitosan for the synthesis of the ppy@magnetic chitosan nanocomposite provided a smoother surface compared to that of magnetic chitosan. Polypyrrole was successfully loaded over the magnetic chitosan, which clearly indicated the presence of coated Fe 3 O 4 nanoparticles, which were mainly implanted between the chitosan and polypyrrole (in the interior of the formed ppy@magnetic chitosan nanocomposite). According to Figure 1c,d, the ppy@magnetic chitosan nanocomposite and magnetic chitosan showed granular and irregular particles, respectively, with a size of 1.00-10.00 µm. Polypyrrole, chitosan, and polypyrrole @magnetic chitosan nanocomposite XRD are shown in Figure 2a. Data for chitosan and polypyrrole were used for comparison. The amorphous structure of ppy was indicated from the wide peak observed at 2θ = 22.85 [32]. The two peaks of chitosan at 2θ = 20.35 and 9.95 are characteristic of the biopolymer chitosan. The definite regularity in the chitosan structure was attributed to the strong intrainter-molecular hydrogen bonds formed by the plentiful amount of amino and hydroxyl groups in the chitosan structure [33]. Many diffraction peaks were present in the XRD of ppy@magnetic chitosan nanocomposite (as shown in Figure 2a) representing the planes (533), (620), (440), (511), (422), (400), (311), (220), and (111) of crystalline magnetite [34][35][36]. The small crystalline size of magnetite nanoparticles is indicated by very wide peaks compared to the bulk one. Using the Scherrer equation, the average crystalline size of the magnetite nanoparticles was found to be 10 nm by selecting the highest peaks for calculation. FT-IR spectroscopy was further used to characterize the synthesized ppy@magnetic chitosan nanocomposite as shown in Figure 2b. The broad peak of ppy@magnetic chitosan nanocomposite at 3357 cm −1 corresponds to the chitosan O-H axial stretching vibration band (3435 cm −1 ) and ppy N-H stretching vibration band (3450 cm −1 ), which are shifted in the spectrum of the nanocomposite. Also, the shift of the ppy peak at 1548 cm −1 to 1559 cm −1 in the synthesized nanocomposite as well as the disappearance of the chitosan peak at 1645 cm −1 indicated the strong interaction of both chitosan and ppy with the magnetite nanoparticles. The peaks at 1465 and 1559 cm −1 indicated the strong interaction and coating of chitosan and polypyrrole over the magnetite nanoparticles. The appearance of the new band at 571 cm −1 indicates the presence of magnetite as this band is characteristic of magnetite. The strong electrostatic interaction between NH 4 + groups in both polymers (chitosan and ppy) and the negatively charged magnetite surface was indicated from the shift of the Fe-O bond peak at 581 and 585 cm −1 , which is characteristic of magnetite (571 cm −1 ). FT-IR results indicate the good integration of chitosan, ppy, and Fe 3 O 4 nanoparticles in the fabricated ppy@magnetic chitosan nanocomposite. and magnetic chitosan showed granular and irregular particles, respectively, with a size of 1.00-10.00 μm.
Polypyrrole, chitosan, and polypyrrole @magnetic chitosan nanocomposite XRD are shown in Figure 2a. Data for chitosan and polypyrrole were used for comparison. The amorphous structure of ppy was indicated from the wide peak observed at 2θ = 22.85 [32]. The two peaks of chitosan at 2θ = 20.35 and 9.95 are characteristic of the biopolymer chitosan. The definite regularity in the chitosan structure was attributed to the strong intrainter-molecular hydrogen bonds formed by the plentiful amount of amino and hydroxyl groups in the chitosan structure [33]. Many diffraction peaks were present in the XRD of ppy@magnetic chitosan nanocomposite (as shown in Figure 2a) representing the planes (533), (620), (440), (511), (422), (400), (311), (220), and (111) of crystalline magnetite [34][35][36]. The small crystalline size of magnetite nanoparticles is indicated by very wide peaks compared to the bulk one. Using the Scherrer equation, the average crystalline size of the magnetite nanoparticles was found to be 10 nm by selecting the highest peaks for calculation. FT-IR spectroscopy was further used to characterize the synthesized ppy@magnetic chitosan nanocomposite as shown in Figure 2b. The broad peak of ppy@magnetic chitosan nanocomposite at 3357 cm −1 corresponds to the chitosan O-H axial stretching vibration band (3435 cm −1 ) and ppy N-H stretching vibration band (3450 cm −1 ), which are shifted in the spectrum of the nanocomposite. Also, the shift of the ppy peak at 1548 cm −1 to 1559 cm −1 in the synthesized nanocomposite as well as the disappearance of the chitosan peak at 1645 cm −1 indicated the strong interaction of both chitosan and ppy with the magnetite nanoparticles. The peaks at 1465 and 1559 cm −1 indicated the strong interaction and coating of chitosan and polypyrrole over the magnetite nanoparticles. The appearance of the new band at 571 cm −1 indicates the presence of magnetite as this band is characteristic of magnetite. The strong electrostatic interaction between NH4 + groups in both polymers (chitosan and ppy) and the negatively charged magnetite surface was indicated from the shift of the Fe-O bond peak at 581 and 585 cm −1 , which is characteristic of magnetite (571 cm −1 ). FT-IR results indicate the good integration of chitosan, ppy, and Fe3O4 nanoparticles in the fabricated ppy@magnetic chitosan nanocomposite. Raman spectroscopy was used to confirm integration among the three components of the nanocomposite as shown in Figure 3a. The observed two bands at 450 and 625 cm −1 are characteristic of Fe3O4 and were shifted from 533 and 669 cm −1 , respectively. For further data about the synthesized nanocomposite, the TGA investigation was achieved under N2 atmosphere to obtain the thermal properties of the polypyrrole@magnetic chitosan nanocomposite as shown in Figure 3b, which shows three weight loss steps. Firstly, the weight loss between 41 and 166 °C corresponds to moisture loss from the polymer ppy. Secondly, the weight loss between 166 and 318 °C corresponds to the chitosan degradation. The last weight loss, between 318 and 489 °C, corresponds to the ppy mainchain degradation. One of the main advantages of the synthesized polypyrrole@magnetic chitosan nanocomposite is its simple separation from the medium by using a magnet. The magnetic properties of the nanocomposite were studied and provided in Figure 3c, which shows the relation between the applied field at room temperature and the magnetization of the studied nanocomposite. According to the magnetization curve, the lack of a hysteresis loop (Hc equal 0) indicates a superparamagnetic nature with no permanent magnetic For further data about the synthesized nanocomposite, the TGA investigation was achieved under N 2 atmosphere to obtain the thermal properties of the polypyrrole@magnetic chitosan nanocomposite as shown in Figure 3b, which shows three weight loss steps. Firstly, the weight loss between 41 and 166 • C corresponds to moisture loss from the polymer ppy. Secondly, the weight loss between 166 and 318 • C corresponds to the chitosan degradation. The last weight loss, between 318 and 489 • C, corresponds to the ppy main-chain degradation. One of the main advantages of the synthesized polypyrrole@magnetic chitosan nanocomposite is its simple separation from the medium by using a magnet. The magnetic properties of the nanocomposite were studied and provided in Figure 3c, which shows the relation between the applied field at room temperature and the magnetization of the studied nanocomposite. According to the magnetization curve, the lack of a hysteresis loop (H c equal 0) indicates a superparamagnetic nature with no permanent magnetic moment. The high magnetic saturation moment (M s ) of polypyrrole@magnetic chitosan nanocomposite (equal to 28.99 emu/g) was attributed to the magnetic Fe 3 O 4 great loading. Due to its simple separation from medium solutions using external magnet, the superparamagnetic nanocomposite has attracted great attention for its application in water treatment All the above characterization results approved the good integration and construction among the three parts of the polypyrrole@magnetic chitosan nanocomposite.

pH Effect on the Adsorption
The adsorbent active binding sites and surface chemistry are greatly influenced by the pH, which affects adsorption efficiency. Herein, we study the pH effect on MO, and Cr (VI) adsorption using polypyrrole@magnetic chitosan nanocomposite over a wide pH range from 2 to 12. Figure 4a illustrates the results. %clearpage Processes 2021, 9, x FOR PEER REVIEW 8 of 16 moment. The high magnetic saturation moment (Ms) of polypyrrole@magnetic chitosan nanocomposite (equal to 28.99 emu/g) was attributed to the magnetic Fe3O4 great loading. Due to its simple separation from medium solutions using external magnet, the superparamagnetic nanocomposite has attracted great attention for its application in water treatment All the above characterization results approved the good integration and construction among the three parts of the polypyrrole@magnetic chitosan nanocomposite.

pH Effect on the Adsorption
The adsorbent active binding sites and surface chemistry are greatly influenced by the pH, which affects adsorption efficiency. Herein, we study the pH effect on MO, and Cr (VI) adsorption using polypyrrole@magnetic chitosan nanocomposite over a wide pH range from 2 to 12. Figure 4a illustrates the results.  The adsorption investigations to study the pH effect were performed at 25 °C with a contact time of 40 min, adsorbent dosage of 100 mg, initial concentration of both pollutants of 100 mg/L, and shaking rate of 200 rpm. The results showed that the removal of both Cr (VI) and MO are pH dependent. The pH increase led to a decrease in MO and Cr (VI) removal capacity due to the strong electrostatic interaction between the adsorbent positive charge at low pH and pollutants negative charge [37]. Additionally, at pH below 4.5, a high MO concentration could precipitate [38]. For Cr (VI), HCrO4 − is the dominant anion at pH lower than 6 while at pH higher than 6 the dominant form is CrO2 4− that cause electrostatic repulsion between different ions. Thus, at high pH the major reason for the decreased adsorption efficiency of MO and Cr (VI) was electrostatic repulsion. Consequently, the removal of MO and Cr (VI) over a polypyrrole@magnetic chitosan nanocomposite is very suitable in a neutral or acidic medium at an optimal pH value between 2 and 4.5. This behavior concerning the removal of both pollutants at different pH values is similar to another study reported in the literature [39].

Contact Time Effect on the Adsorption
The adsorption of MO and Cr (VI) over polypyrrole@magnetic chitosan nanocomposite was performed at different reaction times ranging from 0 to 300 m as shown in Figure  4b. The adsorption investigations to study the contact-time effect were performed at 25 °C, pH 4.5, agitation speed 200 rpm, and adsorbent dosage 100 mg with initial pollutant concentrations of 100 mg/L. During the initial stage as shown in Figure 4b, there was rapid The adsorption investigations to study the pH effect were performed at 25 • C with a contact time of 40 min, adsorbent dosage of 100 mg, initial concentration of both pollutants of 100 mg/L, and shaking rate of 200 rpm. The results showed that the removal of both Cr (VI) and MO are pH dependent. The pH increase led to a decrease in MO and Cr (VI) removal capacity due to the strong electrostatic interaction between the adsorbent positive charge at low pH and pollutants negative charge [37]. Additionally, at pH below 4.5, a high MO concentration could precipitate [38]. For Cr (VI), HCrO 4 − is the dominant anion at pH lower than 6 while at pH higher than 6 the dominant form is CrO 2 4− that cause electrostatic repulsion between different ions. Thus, at high pH the major reason for the decreased adsorption efficiency of MO and Cr (VI) was electrostatic repulsion. Consequently, the removal of MO and Cr (VI) over a polypyrrole@magnetic chitosan nanocomposite is very suitable in a neutral or acidic medium at an optimal pH value between 2 and 4.5. This behavior concerning the removal of both pollutants at different pH values is similar to another study reported in the literature [39].

Contact Time Effect on the Adsorption
The adsorption of MO and Cr (VI) over polypyrrole@magnetic chitosan nanocomposite was performed at different reaction times ranging from 0 to 300 m as shown in Figure 4b. The adsorption investigations to study the contact-time effect were performed at 25 • C, pH 4.5, agitation speed 200 rpm, and adsorbent dosage 100 mg with initial pollutant concentrations of 100 mg/L. During the initial stage as shown in Figure 4b, there was rapid adsorption efficiency of MO and Cr (VI). The synergistic effects between adsorbate and adsorbent in the aqueous solution were responsible for a clear high adsorption efficiency. This stage is the saturation phase in which all possible adsorption sites are saturated with the pollutants. In the case of the present adsorbent, saturation was achieved after 40 min due the interaction between adsorbent surface sites and the adsorbate ions. After the saturation phase, there was no substantial change. Thus, the adsorption of MO and Cr (VI) over the nanoadsorbent polypyrrole@magnetic chitosan is related to the physicochemical interactions between the adsorbate and adsorbent in water. Particle diffusion and mass transfer indicate that this system is chemically rate controlled.

Competitive Ions Effect
The selectivity of any promising adsorbent must be studied for different competing co-ions. Therefore, we studied the adsorption efficiency of polypyrrole@magnetic chitosan nanocomposite toward Cr (VI) and MO in the presence of bicarbonate, sulfate, and chloride co-ions, which may be present in drinking water (Figure 5a). These co-existing ions usually competed with the pollutants on the adsorption active sites over the polypyrrole@magnetic chitosan nanocomposite surface. To study the effect of co-ions, the adsorption experiment was performed at 25 • C, pH 4.5, agitation speed 200 rpm, contact time 40 m, and adsorbent dose 100 mg, with co-ion concentrations of 200 mg/L. Processes 2021, 9, x FOR PEER REVIEW 9 of 16 adsorption efficiency of MO and Cr (VI). The synergistic effects between adsorbate and adsorbent in the aqueous solution were responsible for a clear high adsorption efficiency. This stage is the saturation phase in which all possible adsorption sites are saturated with the pollutants. In the case of the present adsorbent, saturation was achieved after 40 min due the interaction between adsorbent surface sites and the adsorbate ions. After the saturation phase, there was no substantial change. Thus, the adsorption of MO and Cr (VI) over the nanoadsorbent polypyrrole@magnetic chitosan is related to the physicochemical interactions between the adsorbate and adsorbent in water. Particle diffusion and mass transfer indicate that this system is chemically rate controlled.

Competitive Ions Effect
The selectivity of any promising adsorbent must be studied for different competing co-ions. Therefore, we studied the adsorption efficiency of polypyrrole@magnetic chitosan nanocomposite toward Cr (VI) and MO in the presence of bicarbonate, sulfate, and chloride co-ions, which may be present in drinking water (Figure 5a). These co-existing ions usually competed with the pollutants on the adsorption active sites over the polypyr-role@magnetic chitosan nanocomposite surface. To study the effect of co-ions, the adsorption experiment was performed at 25 °C, pH 4.  According to Figure 5a, among the tested ions, sulphate showed the greatest effect for adsorption efficiency. This may be related to the higher affinity of the adsorbent amino group for SO4 2− , which has higher electronic charge. On the other hand, chloride allowed an important reduction in the removal efficiency of both MO and Cr (VI). This may be attributed to their greater negative density charge compared to other negative ions. The similarity of ionic charge between Cr (VI) and bicarbonate ions had a greatly competitive effect on Cr(VI) adsorption [40]. In contrast, MO adsorption was not significantly affected by the bicarbonate ions.

Reusability of the Adsorbent
Reusability of any adsorbent is the main factor determining its economic feasibility for application in real water treatment. In order to study the reusability of polypyr-role@magnetic chitosan nanocomposite for the removal of both MO and Cr (VI), 5 successive cycles were performed using adsorbent dose of 100 mg in an adsorption-desorption experiment as shown in Figure 5b. During the desorption process, we applied 0.1 M so- According to Figure 5a, among the tested ions, sulphate showed the greatest effect for adsorption efficiency. This may be related to the higher affinity of the adsorbent amino group for SO 4 2− , which has higher electronic charge. On the other hand, chloride allowed an important reduction in the removal efficiency of both MO and Cr (VI). This may be attributed to their greater negative density charge compared to other negative ions. The similarity of ionic charge between Cr (VI) and bicarbonate ions had a greatly competitive effect on Cr(VI) adsorption [40]. In contrast, MO adsorption was not significantly affected by the bicarbonate ions.

Reusability of the Adsorbent
Reusability of any adsorbent is the main factor determining its economic feasibility for application in real water treatment. In order to study the reusability of polypyr-role@magnetic chitosan nanocomposite for the removal of both MO and Cr (VI), 5 successive cycles were performed using adsorbent dose of 100 mg in an adsorption-desorption experiment as shown in Figure 5b. During the desorption process, we applied 0.1 M sodium hydroxide as eluent. According to the Figure 5b, there was a little decrease in removal efficacy after each cycle. This decrease was attributed to the damage of the polypyr-role@magnetic chitosan nanocomposite reactive groups on the surface as well as to the loss of its integrity. Consequently, the excellent polypyrrole@magnetic chitosan nanocomposite performance and reusability was approved for water treatment of MO and Cr (VI) after 5 regeneration cycles.

Adsorption Isotherm
The adsorption isotherm experiments were done to calculate the maximum adsorption efficiency of a polypyrrole@magnetic chitosan nanocomposite on MO and Cr (VI). The experiments were performed at 25 • C, pH 5.4, agitation speed 200 rpm, and adsorbent dosage 100 mg with initial MO and Cr (VI) concentrations ranging from 20 to 200 mg/L. Freundlich and Langmuir isotherms were used to study the relation between the initial concentration and the adsorption isotherm according to the following two equations, respectively. C e /q e = (1/q m b ) + (C e /q m ), log q e = logK F + 1/n(logC e ), where n and K F are isotherm constants of the adsorption efficacy; b is the equilibrium constant; and q m denotes maximum MO and Cr (VI) adsorption. Isotherm parameters here were calculated using Langmuir and Freundlich isotherms and tabulated in Table 1. The results are shown in Figure 6. dium hydroxide as eluent. According to the Figure 5b, there was a little decrease in removal efficacy after each cycle. This decrease was attributed to the damage of the polypyr-role@magnetic chitosan nanocomposite reactive groups on the surface as well as to the loss of its integrity. Consequently, the excellent polypyrrole@magnetic chitosan nanocomposite performance and reusability was approved for water treatment of MO and Cr (VI) after 5 regeneration cycles.

Adsorption Isotherm
The adsorption isotherm experiments were done to calculate the maximum adsorption efficiency of a polypyrrole@magnetic chitosan nanocomposite on MO and Cr (VI). The experiments were performed at 25 °C, pH 5.4, agitation speed 200 rpm, and adsorbent dosage 100 mg with initial MO and Cr (VI) concentrations ranging from 20 to 200 mg/L. Freundlich and Langmuir isotherms were used to study the relation between the initial concentration and the adsorption isotherm according to the following two equations, respectively.
log qe = logKF + 1/n(logCe), where n and KF are isotherm constants of the adsorption efficacy; b is the equilibrium constant; and qm denotes maximum MO and Cr (VI) adsorption. Isotherm parameters here were calculated using Langmuir and Freundlich isotherms and tabulated in Table 1. The results are shown in Figure 6.  Homogeneous adsorption sites and monolayer interaction between the nanocomposite surface and adsorbates (MO, Cr (VI)) were confirmed from the regression coefficient (R 2 ), which indicated that the Langmuir isotherm was more fit than the Freundlich isotherm as shown in Table 1. This was an indication of the behavior of the nanocomposite adsorption monolayer besides active sites homogeneity. Also, it showed that the different active sites on the nanocomposite surface have energetically equivalent properties. According to this, the chemical bonds between the adsorbent and adsorbates primarily showed monolayer adsorption over the studied nanoadsorbent with no additional interaction between the adsorbed pollutant molecules and other pollutants. Interestingly, the MO and Cr (VI) maximum removal capacity over the polypyrrole@magnetic chitosan nanocomposite was found to be 95 and 105 mg/g, respectively, which is higher than previous reported studies as tabulated in Table 2.

Adsorption Mechanism
FT-IR and XPS investigations were used to study the composition of ppy@magnetic chitosan before and after the adsorption of MO and Cr (VI) to determine the mechanisms of pollutant removal. FT-IR of ppy@magnetic chitosan nanocomposite before and after adsorption of MO and Cr (VI) is shown in Figure 7a. The MO characteristic stretching bands corresponding to C-C, C-N, S=O, and C-H appear at 1607, 1369, 1121, and 826 cm −1 [50] in FT-IR results of ppy@magnetic chitosan adsorbed MO. The slight displacement of bands from their locations was likely observed in FT-IR of ppy@magnetic chitosan adsorbed Cr (VI). In order to approve these results, full range XPS before and after the adsorption of target pollutants was used to identify the adsorbed species over the adsorbent as shown in Figure 7b. The MO and Cr (VI) characteristic peaks appeared as shown in Figure 7b, indicating the effective accumulation of Cr (VI) and MO over the adsorbent surface through the adsorption process.
Furthermore, the XPS spectrum was used to identify the adsorbed species of chromium ions (Figure 8a). XPS analysis showed two satellite bands of Cr (VI) and Cr (III) that appear at 577 and 587 eV, respectively. bands from their locations was likely observed in FT-IR of ppy@magnetic chitosan adsorbed Cr (VI). In order to approve these results, full range XPS before and after the adsorption of target pollutants was used to identify the adsorbed species over the adsorbent as shown in Figure 7b. The MO and Cr (VI) characteristic peaks appeared as shown in Figure 7b, indicating the effective accumulation of Cr (VI) and MO over the adsorbent surface through the adsorption process. Furthermore, the XPS spectrum was used to identify the adsorbed species of chromium ions (Figure 8a). XPS analysis showed two satellite bands of Cr (VI) and Cr (III) that appear at 577 and 587 eV, respectively.
These results suggested that Cr (III) ions are present as chromium species over the surface of the adsorbent. Additionally, the existence of satellite bands of both Cr (VI) and Cr (III) confirmed the adsorption of Cr (VI) over ppy@magnetic chitosan besides the chemical reduction of Cr (VI) to Cr (III) during the adsorption. Subsequently, the chromium removing mechanism can be explained as follows: under acidic conditions, the NH-functional groups were protonated followed by the adsorption of Cr (VI) species (HCrO4 − ) over the adsorbent via bonding with nitrogen species and via electrostatic interactions. This chemical bonding associated with the oxidation of -NH-to =N-was subsequently accompanied by the reduction of hexavalent chromium to Cr (III). The redox activity of =N-/-NH-pairs is responsible for the reduction of Cr (VI) in addition to their minor oxidation potential compared to the Cr (III)/Cr (VI) redox pair. In addition, few Cr (III) species may be dissolved in water, and others could be removed via complexation with ppy@magnetic chitosan nitrogen functional groups. On the other hand, the XPS spectrum of ppy@magnetic chitosan after the adsorption of MO showed a satellite peak at 169 eV, which indicated the adsorption of MO over the binding sites of the nanocomposite. In general, the redox activity of ppy@magnetic chitosan, besides the existence of different functional groups over its surface, gave the adsorbent amazing in situ chemical reduction properties and adsorption toward Cr (VI) and MO removal from aqueous solution. Consequently, this innovative adsorbent could be used for water detoxification from pollutants.

Conclusions
In this study, a novel ppy@magnetic chitosan nanocomposite was synthesized. This novel adsorbent contained magnetic Fe3O4 nanoparticles and several N-containing functional groups giving it an effective application for water detoxification from both MO and Cr (VI). This nanocomposite was successfully characterized using different techniques including SEM, TEM, TGA XRD, and FT-IR. The effect of different factors on the adsorption of MO and Cr (VI) over the synthesized nanocomposite was studied, including contact These results suggested that Cr (III) ions are present as chromium species over the surface of the adsorbent. Additionally, the existence of satellite bands of both Cr (VI) and Cr (III) confirmed the adsorption of Cr (VI) over ppy@magnetic chitosan besides the chemical reduction of Cr (VI) to Cr (III) during the adsorption. Subsequently, the chromium removing mechanism can be explained as follows: under acidic conditions, the NH-functional groups were protonated followed by the adsorption of Cr (VI) species (HCrO 4 − ) over the adsorbent via bonding with nitrogen species and via electrostatic interactions.
This chemical bonding associated with the oxidation of -NH-to =N-was subsequently accompanied by the reduction of hexavalent chromium to Cr (III). The redox activity of =N-/-NH-pairs is responsible for the reduction of Cr (VI) in addition to their minor oxidation potential compared to the Cr (III)/Cr (VI) redox pair. In addition, few Cr (III) species may be dissolved in water, and others could be removed via complexation with ppy@magnetic chitosan nitrogen functional groups. On the other hand, the XPS spectrum of ppy@magnetic chitosan after the adsorption of MO showed a satellite peak at 169 eV, which indicated the adsorption of MO over the binding sites of the nanocomposite. In general, the redox activity of ppy@magnetic chitosan, besides the existence of different functional groups over its surface, gave the adsorbent amazing in situ chemical reduction properties and adsorption toward Cr (VI) and MO removal from aqueous solution. Consequently, this innovative adsorbent could be used for water detoxification from pollutants.

Conclusions
In this study, a novel ppy@magnetic chitosan nanocomposite was synthesized. This novel adsorbent contained magnetic Fe 3 O 4 nanoparticles and several N-containing functional groups giving it an effective application for water detoxification from both MO and Cr (VI). This nanocomposite was successfully characterized using different techniques including SEM, TEM, TGA XRD, and FT-IR. The effect of different factors on the adsorption of MO and Cr (VI) over the synthesized nanocomposite was studied, including contact time, pH, and co-existed ions. The study of the contact time effect indicated that the adsorption system was chemically rate-controlled. The pH effect study revealed that MO and Cr (VI) adsorption over the studied adsorbent was pH dependent and more suitable for an acidic environment at pH between 2 and 4.5. The study of the co-existing ions effect revealed that the most affected co-ion on adsorption efficiency was sulfate, while bicarbonate had the lowest effect. The adsorption isotherm suggested monolayer adsorption of MO and Cr (VI) over a polymeric-inorganic nanocomposite due to its good fit with the Langmuir isotherm. MO and Cr (VI) maximal removal efficiencies over this magnetic polymer nanocomposite reached 95 and 105 mg/g, respectively. The reusability study using 0.1 M NaOH as eluent also indicated an excellent reusability of the nanocomposite up to 5 successive cycles with a slight reduction in the removal efficiency toward MO and Cr (VI), which was attributed to the loss of functional group activity. FT-IR and XPS studies approved the successful adsorption of both MO and Cr (VI) over the adsorbent surface in addition to the reduction of Cr (VI) to Cr (III). Finally, we can conclude that ppy@magnetic chitosan nanocomposite is a promising adsorbent for removing MO and Cr (VI) from water.