# Chitosan/Alginate Nanocomposite with Fe Nanoparticles for the Efficient Removal of Hexavalent Chromium Pollutant

Authors: Mahmoud Kandeel; S. Latha; Kumaran Subramanian; D. Rennita; Rajasekar Thirunavukkarasu; V. Ramesh; Guru Prasad Srinivasan; Abdullah I. Al-Mubarakc
Journal: Journal of Nanomaterials
 (2023)

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## Abstract

Biopolymers and nanomaterials are an excellent choice for removing heavy metals and keeping the environment clean. The hexavalent chromium (Cr6+) (or) chromium-6 is usually produced by various industrial processes, which can be a toxic liquid pollutant. In this study, a nanopolymeric compound supplemented with Fe nanoparticle was used in the extraction (removal) process of Cr6+ present in the aqueous solutions. Two biopolymers were blended and connected (using a microemulsion process) to produce nanoparticles (Cht/Alg NPs), and the nanoparticles have an average size of 311.2 nm with a negative charge of 23 and 2 mV. During synthesis, the red cabbage extract was also used to make iron nanoparticles (Fe-NPs), and these Fe-NPs had semispherical species with a diameter of 21.4 nm. The nanopolymeric compound was loaded and equally distributed with chitosan and alginate (Cht/Alg) NPs and synthesized Fe-NPs. The assessment using batch adsorption assays showed that both nanocomposites exhibited more ability than the Cr6+ adsorbents under various conditions (e.g., pH, initial ion concentration, adsorbent volume, and contact time (CT)). At the start, the initial Cr6+ concentration was 75 ppm, and the most effective adsorption condition was found at 5.0 pH, the adsorbent capacity was 4 g/L, and the CT was 210 min. These documented results show that Cr6+ may be completely removed from bulk testing. Therefore, the use of these composite nanopolymers (Cht/Alg NPs) combined with the synthesized Fe-NPs can be extrapolated for use in the aquatic milieu for the removal of Cr6+.


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## Body

## 1. Introduction

Nanotechnology is a remarkably new and rapidly evolving technology with a wide variety of processes, including the creation and use of objects of one or more sizes ranging from 1 to 100 nm. A series of physicochemical techniques are now used for the synthesis of nanoparticles (NPs) [1]. Nanoparticles (NPs) have a width of 1–100 nm function as a link between masses and atomic or molecular structures. Nanoparticles have a unique and attractive criterion of being small in size making them easy to handle and have larger surface area with free hanging bonds and high performance [2]. Nanotechnology has been described as the scientific art of deciphering atoms and the atomic molecules. As a result, nanotechnology will bring a promising change of new and unique developments in the field of environmental protection. Nanotechnology, by far, has been developed as a very powerful tool in assisting researchers in the diagnosis, treatment, and prevention of life-threatening diseases, such as cancer, etc. However, the consequent potential for toxicity and the application of nanomaterials has been tightly regulated [3]. Nanoparticles (NPs) play a pivotal role in medical, biological, and academic research [4]. Chitosan-based polymeric nanoparticles have been recently the choice of many researchers as they can be used as effective carriers of the drug, bioactive, eco-friendly, and cost-effective. There are certain other beneficial internal characteristics of chitosan NPs, such as biological compatibility, environmental degradation, nontoxicity, bioactivity efficiency, simplification, and targeted specific therapy [5]. The development of nanotechnology in other fields includes automobiles, paints, electronics, energy, agriculture, and food business [6]. In terms of drug applications, NPs can be defined as submicron colloidal drug management systems made of natural or synthetic polymers. The prime functional factors of NPs, like absorption, distribution, targeted domain collection, and specification in the body, are strongly influenced by their size [7]. Iron nanoparticles (Fe-NPs) have attracted much attention in recent years because of their extraordinary physicochemical and biological abilities, along with their chemical structure and characteristics. Iron valent iron, iron oxide-hydroxides, and iron hydroxides are some of the many types of these particles. Because of their unique features and great promise of various applications, iron nanoparticles (Fe-NPs) have gained plenteousness interest. Fe-NPs are commonly synthesized using physiological and chemical processes [8].


## 2. Chromium

Chromium is awfully a very common and hazardous contaminant in the groundwater. Chromium is found locally mainly in two valence regions: trivalent Cr(III) and hexavalent Cr(VI). The trivalent chromium(III) is less harmful than Cr(VI) and comes up commonly in the environment and also, they are extremely sustainable in nature and in anatomical systems [9]. The Cr(VI) is the most dominant in oxidizing conditions, while Cr(III) is particularly dominant in reducing conditions [10]. Traditional therapeutic procedures, such as chemical rainfall, ion exchange, and electrochemical medical technology, can all be used to remove chromium from contaminated living water but they do not ward off the chromium completely. One of the heaviest metals, hexavalent chromium (Cr(VI)), is found mainly in dirty soils and groundwater [11]. To reduce water pollution and make the water nonhazardous requires the elimination of heavy metals (HM) from contaminated water. The efficacy of chitosan and alginate nanocomposites in extracting chromium(VI) from wastewater was studied within study. Recent research focuses and addresses the use of nanoparticles in the modification of hexavalent chromium species. Batch adsorption testing of these NPs was subjected for investigation to monitor the removal process under an assortment of conditions, such as concentration, adsorbent volume, pH, and turbulence time, showed the removal of ions and was pH dependent, with a high pH of 5. From these findings, it was determined that chitosan and alginate nanocomposites are a powerful Cr(VI) bio-sorbents from the wastewater [12]. Natural chromium pollution is responsible for a vast array of factors and conditions that must be carefully selected, including pH, concentration Cr(VI), temperature, humidity species, dehydration in the groundwater, potential pollution hazards, possible removal of time-sensitive pollution, etc. Given this, various waste disposal technologies may be required in an assortment of contexts [13].


## 3. Biopolymers

For industrial applications marine environment has been identified as a valuable source of a variety of bioactive polymers. Some polysaccharide families, such as chitosan and alginate, are hugely renewable biomasses derived from microorganisms, shrimp, clams or algae, etc. These polysaccharides have a wide range of biological activities such as antioxidant, antiinfection, anticoagulant, antiinflammatory and antidiabetic properties. Apart from their logical botanical and structural functions, marine biopolymers can be tailored to create new biomaterials with novel functions [7]. Chitosan (Cht) is an easily appearing amino-polysaccharide, which is one of the most comprehensively essential polymers in biomedical science. Chitosan is the second most sufficient polymer after cellulose. It is synthesized from chitin (established in the exoskeletons of insects, including marine aquatic animals, together with microorganisms such as fungi, yeast, and microalgae) through partial deacetylation in an alkaline environment. Numerous marine microbial strains have chitinase producing capacity [14]. Active Cht groups (e.g., primary/secondary amines and hydroxyl groups) with their distinguishing features (e.g., biological compatibility, toxicity, biodegradability decay, high density, adhesion to mucoadhesion, antioxidant, antimicrobial activity, along with anticancer) allows it to be used in a variety of premises, inclusive of Hg removal and water/soil preparation [15, 16].


## 4. Materials and Methods

### 4.1. Buildup of Biopolymers Nanoparticles

The microemulsion process, as previously reported, was used to make chitosan–alginate nanoparticles (Cht/Alg NPs) [16]. To prepare the watery phases, Cht and Alg were blended in 2% acetic acid solution and hot distilled water (DW) (at 1% w/v), consequently. Paraffin oil was applied in the fuel category. For stable emulsions, these three solutions were made in uniform quantity (equal quantity, 10 mL gradually) within 30 min, followed by cross-linkers (10 mL and tripolyphosphate (1 M) along with 10 mL CaCl2 solutions (1 M) can be stirred with 180 min. Centrifugation was done at 8,000 rpm for 30 min, the NPs pellet were extracted, which was then washed twice with DW and acetone, then freshly reconstituted for lyophilization and taken for further analysis.


### 4.2. Iron Nanoparticle Synthesis

The ethanol (70%) extract was prepared to isolate NPs from prepared red cabbage. For iron nanoparticle (Fe-NPs) biosynthesis, 0.1 M of FeCl3·6H2O solution was marginally lowered (0.5 mL/min) in red cabbage extract at a ratio of 1 : 2 (v/v) FeCl3 solution, diluted at 425 rpm and then moved to another 90 min after the fall. The synthesis of NPs was attained by altering the shade of the solution to black. NPs pellets were suspended in DW, refrigerated (20°C) and was processed after the reaction solution incorporated into 14,000g on 33 min [17].


### 4.3. Manufacture Based on Nanoadsorbents

The liquid solvent (10 mg/mL) was used upon the Cht/Alg NPs and Fe-NP, and composites were made by forcing strong nanomaterials into DW until clear solution was obtained, which were then filtered to extract any undigested particles. The resulting Cht/Alg NPs solvent was stirred at 450 rpm for 120 min, and then Fe-NPs solution was extracted with red cabbage extract (uniform volume). The NPs appeared and were gradually incorporated into the biopolymer solution while stirring. Following that, the combined Cht/Alg/Fe-NPs were centrifuged, cleaned with DW, refrigerated, and lyophilized.


## 4.1. Buildup of Biopolymers Nanoparticles

The microemulsion process, as previously reported, was used to make chitosan–alginate nanoparticles (Cht/Alg NPs) [16]. To prepare the watery phases, Cht and Alg were blended in 2% acetic acid solution and hot distilled water (DW) (at 1% w/v), consequently. Paraffin oil was applied in the fuel category. For stable emulsions, these three solutions were made in uniform quantity (equal quantity, 10 mL gradually) within 30 min, followed by cross-linkers (10 mL and tripolyphosphate (1 M) along with 10 mL CaCl2 solutions (1 M) can be stirred with 180 min. Centrifugation was done at 8,000 rpm for 30 min, the NPs pellet were extracted, which was then washed twice with DW and acetone, then freshly reconstituted for lyophilization and taken for further analysis.


## 4.2. Iron Nanoparticle Synthesis

The ethanol (70%) extract was prepared to isolate NPs from prepared red cabbage. For iron nanoparticle (Fe-NPs) biosynthesis, 0.1 M of FeCl3·6H2O solution was marginally lowered (0.5 mL/min) in red cabbage extract at a ratio of 1 : 2 (v/v) FeCl3 solution, diluted at 425 rpm and then moved to another 90 min after the fall. The synthesis of NPs was attained by altering the shade of the solution to black. NPs pellets were suspended in DW, refrigerated (20°C) and was processed after the reaction solution incorporated into 14,000g on 33 min [17].


## 4.3. Manufacture Based on Nanoadsorbents

The liquid solvent (10 mg/mL) was used upon the Cht/Alg NPs and Fe-NP, and composites were made by forcing strong nanomaterials into DW until clear solution was obtained, which were then filtered to extract any undigested particles. The resulting Cht/Alg NPs solvent was stirred at 450 rpm for 120 min, and then Fe-NPs solution was extracted with red cabbage extract (uniform volume). The NPs appeared and were gradually incorporated into the biopolymer solution while stirring. Following that, the combined Cht/Alg/Fe-NPs were centrifuged, cleaned with DW, refrigerated, and lyophilized.


## 5. Representation of Products Along with Nanomaterials

### 5.1. FTIR Analysis

Fourier transform infrared (FTIR) spectrophotometer was used to analyze biochemical bond production, including red cabbage extract-synthesized Fe-NPs, along with Cht/Alg NPs. Sampling values, later then mingling over potassium bromide, were entered at 25°C at a frequency area of 450–4,000 cm−1 along with 4 cm−1 correction.


### 5.2. Structural Analysis of Nanomaterial

Transmission electron microscope (TEM) magnets (electron microscopy) were used to evaluate the size of structural features, morphology, composition, and distribution [18] of synthesized Fe-NPs from red cabbage.


### 5.3. SEM (Scanner Electron Microscopy) Analysis

Further structural fundamentals of this combined Cht/Alg/Fe-NPs were taken for SEM analysis to ensure the combination of compliance and physiognomy.


### 5.4. Particles Size Analysis

The nanoparticle size was analyzed by particle size (Ps) dispersion, and high cost (zeta capacity) of synthetic nanomaterials/nanocomposites (e.g., Fe-NPs, Cht/Alg NPs, along with Cht/Alg/Fe-NPs) were made using DLS (Dynamic Light Dispersion, Malvern).


### 5.5. Batch Adsorption Around Hexavalent Chromium

Batch adsorption testing was performed to test the capability of Cht/Alg NPs along with Cht/Alg/Fe-NPs facing adsorb hexavalent chromium (Cr6+) from liquefied media under various conditions (e.g., pH-adsorbent, contact time (CT) and ion concentration start) [19]. Other common techniques were used to adjust the Cr(VI) stock solution. An aliquot of 1.41 mg of K2Cr2O7 was dispersed in 500 mL of deionized water to form a stock solution containing 500 mg/L of Cr(VI). Subsequent analysis of this stock solution was employed as per previous reports [20]. The diphenylcarbohydrazide method was used to determine Cr(VI) values in solutions. The Cr6+ residual values were obtained accurately using 1,5-diphenylcarbazide, which produces a red–violet complex containing Cr6+ [21] as an indicator. The absorption of the structure was assessed at 540 nm using a UV–vis spectrophotometer and was compared with standard deviation curves. The following formula was used to calculate the efficiency (%) of the Cr(VI) removal.(1)Removal efficiency%=1−Ci/C0×100%,where Ci is a balance Cr(VI) in filtered resolution solutions, and C0 is the first Cr(VI) primary [22].The diagnosis was made using colorimetric techniques for all tests. Chromium was acidified with phosphoric acid and mixed with a 1,5-diphenyl carbazide (DPC) solution in acetone, followed by a spectrophotometer (UV/visible) analysis at 540 nm, as one of the highest and frequently used water analysis technique to assess polluted water.


### 5.6. Reaction of pH on Chromium Adsorption

The pH of aqueous solution is a vital specification that controls the adsorption procedure. The test for this phase was performed under conditions of constant temperature (25°C), CT (1 hr), adsorbent dose (2 g/100 mL), and basic chromium concentration (5 mg/L). The pH of the solution was adjusted and then the chromium adsorption was investigated.


### 5.7. Reaction of Contact Time on Chromium Adsorption

The CT based on the factors within the batch adsorption process was studied. During the study, all parameters except for CT, including warmth (25°C), adsorbent volume (2 g/100 mL), pH (3), and the basic chromium concentration (5 mg/L), were kept constant.


### 5.8. Effect on Adsorbent Quantity Chromium Adsorption

The reaction of the adsorbent measurement on the powerful discharge of chromium(VI) was investigated at different concentrations of chromium −2, 10 mg, and 15 mg/L at pH-2. At this stage, the vibration speed and reaction time were at 120 rpm and 24 hr, respectively.


### 5.9. Reaction of Basic Chromium Application on Adsorption Procedure

Initial focus is the main and single key factor in effective adsorption process. Tests were performed with the first variable application on chromium (2.5, 5, 7.5, 10, 12.5 mg and 15 mg/L) with even condition (25°C), pH (3), contact interval (1 hr), along with 2 g of adsorbent quantity (2 g/100 mL).


## 5.1. FTIR Analysis

Fourier transform infrared (FTIR) spectrophotometer was used to analyze biochemical bond production, including red cabbage extract-synthesized Fe-NPs, along with Cht/Alg NPs. Sampling values, later then mingling over potassium bromide, were entered at 25°C at a frequency area of 450–4,000 cm−1 along with 4 cm−1 correction.


## 5.2. Structural Analysis of Nanomaterial

Transmission electron microscope (TEM) magnets (electron microscopy) were used to evaluate the size of structural features, morphology, composition, and distribution [18] of synthesized Fe-NPs from red cabbage.


## 5.3. SEM (Scanner Electron Microscopy) Analysis

Further structural fundamentals of this combined Cht/Alg/Fe-NPs were taken for SEM analysis to ensure the combination of compliance and physiognomy.


## 5.4. Particles Size Analysis

The nanoparticle size was analyzed by particle size (Ps) dispersion, and high cost (zeta capacity) of synthetic nanomaterials/nanocomposites (e.g., Fe-NPs, Cht/Alg NPs, along with Cht/Alg/Fe-NPs) were made using DLS (Dynamic Light Dispersion, Malvern).


## 5.5. Batch Adsorption Around Hexavalent Chromium

Batch adsorption testing was performed to test the capability of Cht/Alg NPs along with Cht/Alg/Fe-NPs facing adsorb hexavalent chromium (Cr6+) from liquefied media under various conditions (e.g., pH-adsorbent, contact time (CT) and ion concentration start) [19]. Other common techniques were used to adjust the Cr(VI) stock solution. An aliquot of 1.41 mg of K2Cr2O7 was dispersed in 500 mL of deionized water to form a stock solution containing 500 mg/L of Cr(VI). Subsequent analysis of this stock solution was employed as per previous reports [20]. The diphenylcarbohydrazide method was used to determine Cr(VI) values in solutions. The Cr6+ residual values were obtained accurately using 1,5-diphenylcarbazide, which produces a red–violet complex containing Cr6+ [21] as an indicator. The absorption of the structure was assessed at 540 nm using a UV–vis spectrophotometer and was compared with standard deviation curves. The following formula was used to calculate the efficiency (%) of the Cr(VI) removal.(1)Removal efficiency%=1−Ci/C0×100%,where Ci is a balance Cr(VI) in filtered resolution solutions, and C0 is the first Cr(VI) primary [22].The diagnosis was made using colorimetric techniques for all tests. Chromium was acidified with phosphoric acid and mixed with a 1,5-diphenyl carbazide (DPC) solution in acetone, followed by a spectrophotometer (UV/visible) analysis at 540 nm, as one of the highest and frequently used water analysis technique to assess polluted water.


## 5.6. Reaction of pH on Chromium Adsorption

The pH of aqueous solution is a vital specification that controls the adsorption procedure. The test for this phase was performed under conditions of constant temperature (25°C), CT (1 hr), adsorbent dose (2 g/100 mL), and basic chromium concentration (5 mg/L). The pH of the solution was adjusted and then the chromium adsorption was investigated.


## 5.7. Reaction of Contact Time on Chromium Adsorption

The CT based on the factors within the batch adsorption process was studied. During the study, all parameters except for CT, including warmth (25°C), adsorbent volume (2 g/100 mL), pH (3), and the basic chromium concentration (5 mg/L), were kept constant.


## 5.8. Effect on Adsorbent Quantity Chromium Adsorption

The reaction of the adsorbent measurement on the powerful discharge of chromium(VI) was investigated at different concentrations of chromium −2, 10 mg, and 15 mg/L at pH-2. At this stage, the vibration speed and reaction time were at 120 rpm and 24 hr, respectively.


## 5.9. Reaction of Basic Chromium Application on Adsorption Procedure

Initial focus is the main and single key factor in effective adsorption process. Tests were performed with the first variable application on chromium (2.5, 5, 7.5, 10, 12.5 mg and 15 mg/L) with even condition (25°C), pH (3), contact interval (1 hr), along with 2 g of adsorbent quantity (2 g/100 mL).


## 6. Results and Discussion

In this study, Fe-NPs, Cht/Alg NP, and their nanocomposites were successfully synthesized (Figures1–3). The characteristics of the combined NPs were tested biologically and physically.Figure 1
Chitosan/alginate nanoparticles.Figure 2
Iron nanoparticles (Fe-NPs).Figure 3
Cht/Alg/Fe-NPs.


### 6.1. Depiction on Biopolymers Nanocomposites

#### 6.1.1. FTIR Analysis

The FTIR spectra of the composite (Cht/Alg), along with Fe-NPs synthesized from the red cabbage extract, are given in Figure4. In the Cht/Alg composite blend, the spectral data have taken different collections against any polymer, securing polymers, cross-linking along with biochemical communications. In addition, the conversion of the expandable signal C–O–C (Alg spectrum) at 1,024–1,413 cm−1 showed the Alg and Ca2+ ion and the ionic interactions among Alg carboxyl groups along with calcium ions. As seen after the Cht/Alg cross-link interaction, the extended (CH) Cht and Alg CH vibration points are seen scattered; the additional hydrogen bonds formed between the Cht amino category are converted to NH3+ and produce a polyelectrolyte compound under strong electrostatic contact with Alg carboxyl anions [23].Figure 4
The FTIR spectra of blended chitosan/alginate nanoparticle (Cht/Alg). The merge category/bonds from beginning polymers in Cht/Alg are determined by vertical lines.In the spectrum of red cabbage/Fe-NPs (Figure5—red cabbage-Fe-NPs), the maximum value of O–H changed to 2,920 cm−1 after Fe-NPs synthesis. The dispersal on the reference point at 1,134 cm−1 reveals the embarrassment of these biochemical bonds in Fe-NPs synthesis along with capping. The “Van der Waals” interactions are recommended as the essential explanation of the disruption among O group along with N atoms in the extraction also synthesized Fe-NPs.Figure 5
FTIR spectra of a mixed extract among synthesized Fe-NPs (red cabbage/Fe-NPs).


#### 6.1.2. TEM Imaging

The infrastructure of synthesized Fe-NPs was observed under TEM imaging. The field showed that almost all of the synthesized NPs were in circular/semispherical shapes, with obvious agglomeration between the composite particles—(Ps) for synthesized Fe-NPs in the range of 13.6−72.4 nm. NPs cluster was primarily caused by the distinctive tense aspects of marine vegetation extraction and the presence of strong O–H groups in it. In addition, the tendency of Fe-NPs agglomeration was expected due to its minute size and potentially magnetic characteristics.


#### 6.1.3. SEM Imaging

Ultrasound imaging of Cht/Alg nanocomposite containing red cabbage-synthesized Fe-NPs is illustrated in Figure6. The nanocomposite has a statistically stable shape of Ps at a distance of 0.5 µm. The Fe-NPs embedded in Cht/Alg nanocomposite are very markedly visible up to the location of the nanoparticles, indicating their potential interaction with the environment and its components. Additionally, Fe-NPs appear in nonagglomerated forms, confirming the ability of Cht/Alg nanocomposite to capture and stabilize red cabbage extract-synthesized Fe-NP.Figure 6
Scanning electron microscopy image of assembled chitosan/alginate nanocomposite by synthesized Fe-NPs.


#### 6.1.4. Nanomaterials Capacity Along with Charge

In Ps analysis, along with the charge of NPs constructs, showed a minimum Ps width of Fe-NPs (12.5–83.1 nm), with an average Ps width of 21.4 nm. The Ps ranges from 162.6 to 514.6 for Cht/Alg NPs and against 173.9–568.5 as Cht/Alg/Fe nanocomposite, amidst an average width of 311.2 and 342.6 nm, correspondingly. The distribution of Fe-NPs in nanocomposite polymers led to an increase on Ps along with a significant increase on nanocomposite negative charge from −23.2 to 34.6 mV (Table1).Table 1
Intensity distribution.
d (nm)f (%)f (cum.%)d (nm)f (%)f (cum.%)d (nm)f (%)f (cum.%)d (nm)f (%)f (cum.%)1.00.00.08.00.00.064.31.812.1515.22.381.31.10.00.08.70.00.069.82.014.1559.92.283.51.20.00.09.50.00.075.92.116.2608.52.085.51.30.00.010.30.00.082.52.318.5661.41.987.41.40.00.011.20.00.089.72.420.9718.81.789.11.50.00.012.20.00.097.42.623.5781.21.690.71.60.00.013.20.00.0105.92.726.2849.01.592.11.80.00.014.40.00.0115.12.829.0922.71.393.51.90.00.015.60.00.0125.12.931.91,002.81.294.62.10.00.017.00.00.0136.03.034.91,089.91.195.72.30.00.018.40.00.0147.83.037.91,184.50.996.62.50.00.020.00.00.0160.63.141.01,287.40.897.42.70.00.021.80.00.0174.53.144.21,399.20.798.13.00.00.023.70.00.0189.73.247.31,520.70.698.73.20.00.025.70.30.3206.23.250.51,652.70.599.23.50.00.027.90.40.7224.13.153.61,796.20.499.73.80.00.030.40.51.2243.53.156.81,952.10.3100.04.10.00.033.00.61.9264.73.159.82,121.60.0100.04.50.00.035.90.82.6287.63.062.82,305.80.0100.04.90.00.039.00.93.5312.62.965.82,506.00.0100.05.30.00.042.41.04.6339.82.968.62,723.60.0100.05.70.00.046.11.25.7369.22.871.42,960.10.0100.06.20.00.050.11.37.1401.32.774.13,217.10.0100.06.80.00.054.41.58.6436.22.576.63,496.40.0100.0


#### 6.1.5. Reaction of pH on Chromium Adsorption

The pH test result for adsorption is given in Figure7. The result shows that high adsorption was noted in pH of 3 and with an increase in pH, and later a significant loss in adsorption percentage was observed with the increase of pH. This can be owed to the collapsing of the attractive electrical energy between the opposite charge adsorbate and the adsorbent, ultimately leading to loss at sorption volume [24].Figure 7
Reaction of pH at Cr(VI) removal.


#### 6.1.6. Reaction of Contact Time on Chromium Adsorption

The impact based on CT at the effectiveness based on chromium adsorption is shown in Figure8. The adsorption rate starts at a slow phase along with chromium removal (%) increasing. Discharge ability concluded within about 90% during the 5th day of the study. There was no powerful difference on the concentration balance after 1–4 hr, and after 1 hr, the adsorption phase reached the balance mark [25].Figure 8
Reaction of contact time at adsorption procedure ability.


#### 6.1.7. Effect on Adsorbent Quantity Chromium Adsorption

The reaction on adsorbent volume on chromium release is given in Figure9. The consequences presented that the discharge of chromium on equilibrium state increased with a rising load of adsorbent. So that, when the adsorbent quantity was added on from 0.05 g to 0.2 g/100 mL, the removal efficiency was increased from 88% to 100%, 56.1% to 91.7%, and 45% to 79.2% by application of 0.2, 0.5 mg, and 0.75 mg/L, respectively.Figure 9
Reaction of adsorbent quantity by Cr(VI) discharge.


#### 6.1.8. Reaction of Basic Chromium Application on Adsorption Procedure

The developmental impact of the reaction on the first chromium concentrate on effective removal function is presented in Figure10. The efficiency of chromium release got decreased by raise in basic chromium application. In case of low chromium concentration, the scale of the basic amount of chromium ions to the convenient adsorbent area was vast, and thereafter, partial adsorption developed into separate of its initial concentration (Figures 11 and 12). However, in high applications, the feasible advertising sites are few, and that is why the discharge of the percentage of iron ions reliant on the basic application decreases.Figure 10
Effect of chromium application on Cr(VI) discharge chromium removal (%).Figure 11
A normal solution of chromium.Figure 12
1,5-diphenylcarbazide that forms a reddish–violet complex with Cr6+.


#### 6.1.9. Batch Adsorption of Cr(VI)

The Cr(VI) batch adsorption was strongly noted along with the successful implementation of applying both Cht/Alg NPs and the mixed Cht/Alg/Fe-NPs, with 90% removal of Cr(VI) (Figure13). While testing the factor, the resting conditions were optimized and maintained at normal levels (e.g., pH = 5, adsorbent quantity = 5 g/L, contact interval = 5 days and concentration of the first ion = 100 ppm). Generally, the combined Cht/Alg/Fe-NPs have a higher Cr(VI) adsorption performance than Cht/Alg NPs as per parameter. Due to the high content against OH (hydroxyl groups) along with NH2 (primary amine), which moves as a capable filtration site, the Cht-based NPs were promoted as excellent commercial tool, along with the dispersion of many HM, in addition to Cr(VI), from the solution [22]. The transformation of biopolymers, like Cht and Alg, into a potential nanoforms extremely increases its capability and capacity for the dispersion of HM expected to their improved physiochemical setting, determined by bigger communication facilities, more functional groups, and more filtering space. These limits increase amidst the packing of nanopolymers by metals (e.g., metal nanoparticles) that can define the greater concentration of the Cht/Alg/Fe-NPs compound/absorption.Figure 13
The batch adsorption of Cr(VI) was strongly and adequately accomplished, applying complex Cht/Alg/Fe-NPs, with 90% elimination ratio at 5th day.


## 6.1. Depiction on Biopolymers Nanocomposites

### 6.1.1. FTIR Analysis

The FTIR spectra of the composite (Cht/Alg), along with Fe-NPs synthesized from the red cabbage extract, are given in Figure4. In the Cht/Alg composite blend, the spectral data have taken different collections against any polymer, securing polymers, cross-linking along with biochemical communications. In addition, the conversion of the expandable signal C–O–C (Alg spectrum) at 1,024–1,413 cm−1 showed the Alg and Ca2+ ion and the ionic interactions among Alg carboxyl groups along with calcium ions. As seen after the Cht/Alg cross-link interaction, the extended (CH) Cht and Alg CH vibration points are seen scattered; the additional hydrogen bonds formed between the Cht amino category are converted to NH3+ and produce a polyelectrolyte compound under strong electrostatic contact with Alg carboxyl anions [23].Figure 4
The FTIR spectra of blended chitosan/alginate nanoparticle (Cht/Alg). The merge category/bonds from beginning polymers in Cht/Alg are determined by vertical lines.In the spectrum of red cabbage/Fe-NPs (Figure5—red cabbage-Fe-NPs), the maximum value of O–H changed to 2,920 cm−1 after Fe-NPs synthesis. The dispersal on the reference point at 1,134 cm−1 reveals the embarrassment of these biochemical bonds in Fe-NPs synthesis along with capping. The “Van der Waals” interactions are recommended as the essential explanation of the disruption among O group along with N atoms in the extraction also synthesized Fe-NPs.Figure 5
FTIR spectra of a mixed extract among synthesized Fe-NPs (red cabbage/Fe-NPs).


### 6.1.2. TEM Imaging

The infrastructure of synthesized Fe-NPs was observed under TEM imaging. The field showed that almost all of the synthesized NPs were in circular/semispherical shapes, with obvious agglomeration between the composite particles—(Ps) for synthesized Fe-NPs in the range of 13.6−72.4 nm. NPs cluster was primarily caused by the distinctive tense aspects of marine vegetation extraction and the presence of strong O–H groups in it. In addition, the tendency of Fe-NPs agglomeration was expected due to its minute size and potentially magnetic characteristics.


### 6.1.3. SEM Imaging

Ultrasound imaging of Cht/Alg nanocomposite containing red cabbage-synthesized Fe-NPs is illustrated in Figure6. The nanocomposite has a statistically stable shape of Ps at a distance of 0.5 µm. The Fe-NPs embedded in Cht/Alg nanocomposite are very markedly visible up to the location of the nanoparticles, indicating their potential interaction with the environment and its components. Additionally, Fe-NPs appear in nonagglomerated forms, confirming the ability of Cht/Alg nanocomposite to capture and stabilize red cabbage extract-synthesized Fe-NP.Figure 6
Scanning electron microscopy image of assembled chitosan/alginate nanocomposite by synthesized Fe-NPs.


### 6.1.4. Nanomaterials Capacity Along with Charge

In Ps analysis, along with the charge of NPs constructs, showed a minimum Ps width of Fe-NPs (12.5–83.1 nm), with an average Ps width of 21.4 nm. The Ps ranges from 162.6 to 514.6 for Cht/Alg NPs and against 173.9–568.5 as Cht/Alg/Fe nanocomposite, amidst an average width of 311.2 and 342.6 nm, correspondingly. The distribution of Fe-NPs in nanocomposite polymers led to an increase on Ps along with a significant increase on nanocomposite negative charge from −23.2 to 34.6 mV (Table1).Table 1
Intensity distribution.
d (nm)f (%)f (cum.%)d (nm)f (%)f (cum.%)d (nm)f (%)f (cum.%)d (nm)f (%)f (cum.%)1.00.00.08.00.00.064.31.812.1515.22.381.31.10.00.08.70.00.069.82.014.1559.92.283.51.20.00.09.50.00.075.92.116.2608.52.085.51.30.00.010.30.00.082.52.318.5661.41.987.41.40.00.011.20.00.089.72.420.9718.81.789.11.50.00.012.20.00.097.42.623.5781.21.690.71.60.00.013.20.00.0105.92.726.2849.01.592.11.80.00.014.40.00.0115.12.829.0922.71.393.51.90.00.015.60.00.0125.12.931.91,002.81.294.62.10.00.017.00.00.0136.03.034.91,089.91.195.72.30.00.018.40.00.0147.83.037.91,184.50.996.62.50.00.020.00.00.0160.63.141.01,287.40.897.42.70.00.021.80.00.0174.53.144.21,399.20.798.13.00.00.023.70.00.0189.73.247.31,520.70.698.73.20.00.025.70.30.3206.23.250.51,652.70.599.23.50.00.027.90.40.7224.13.153.61,796.20.499.73.80.00.030.40.51.2243.53.156.81,952.10.3100.04.10.00.033.00.61.9264.73.159.82,121.60.0100.04.50.00.035.90.82.6287.63.062.82,305.80.0100.04.90.00.039.00.93.5312.62.965.82,506.00.0100.05.30.00.042.41.04.6339.82.968.62,723.60.0100.05.70.00.046.11.25.7369.22.871.42,960.10.0100.06.20.00.050.11.37.1401.32.774.13,217.10.0100.06.80.00.054.41.58.6436.22.576.63,496.40.0100.0


### 6.1.5. Reaction of pH on Chromium Adsorption

The pH test result for adsorption is given in Figure7. The result shows that high adsorption was noted in pH of 3 and with an increase in pH, and later a significant loss in adsorption percentage was observed with the increase of pH. This can be owed to the collapsing of the attractive electrical energy between the opposite charge adsorbate and the adsorbent, ultimately leading to loss at sorption volume [24].Figure 7
Reaction of pH at Cr(VI) removal.


### 6.1.6. Reaction of Contact Time on Chromium Adsorption

The impact based on CT at the effectiveness based on chromium adsorption is shown in Figure8. The adsorption rate starts at a slow phase along with chromium removal (%) increasing. Discharge ability concluded within about 90% during the 5th day of the study. There was no powerful difference on the concentration balance after 1–4 hr, and after 1 hr, the adsorption phase reached the balance mark [25].Figure 8
Reaction of contact time at adsorption procedure ability.


### 6.1.7. Effect on Adsorbent Quantity Chromium Adsorption

The reaction on adsorbent volume on chromium release is given in Figure9. The consequences presented that the discharge of chromium on equilibrium state increased with a rising load of adsorbent. So that, when the adsorbent quantity was added on from 0.05 g to 0.2 g/100 mL, the removal efficiency was increased from 88% to 100%, 56.1% to 91.7%, and 45% to 79.2% by application of 0.2, 0.5 mg, and 0.75 mg/L, respectively.Figure 9
Reaction of adsorbent quantity by Cr(VI) discharge.


### 6.1.8. Reaction of Basic Chromium Application on Adsorption Procedure

The developmental impact of the reaction on the first chromium concentrate on effective removal function is presented in Figure10. The efficiency of chromium release got decreased by raise in basic chromium application. In case of low chromium concentration, the scale of the basic amount of chromium ions to the convenient adsorbent area was vast, and thereafter, partial adsorption developed into separate of its initial concentration (Figures 11 and 12). However, in high applications, the feasible advertising sites are few, and that is why the discharge of the percentage of iron ions reliant on the basic application decreases.Figure 10
Effect of chromium application on Cr(VI) discharge chromium removal (%).Figure 11
A normal solution of chromium.Figure 12
1,5-diphenylcarbazide that forms a reddish–violet complex with Cr6+.


### 6.1.9. Batch Adsorption of Cr(VI)

The Cr(VI) batch adsorption was strongly noted along with the successful implementation of applying both Cht/Alg NPs and the mixed Cht/Alg/Fe-NPs, with 90% removal of Cr(VI) (Figure13). While testing the factor, the resting conditions were optimized and maintained at normal levels (e.g., pH = 5, adsorbent quantity = 5 g/L, contact interval = 5 days and concentration of the first ion = 100 ppm). Generally, the combined Cht/Alg/Fe-NPs have a higher Cr(VI) adsorption performance than Cht/Alg NPs as per parameter. Due to the high content against OH (hydroxyl groups) along with NH2 (primary amine), which moves as a capable filtration site, the Cht-based NPs were promoted as excellent commercial tool, along with the dispersion of many HM, in addition to Cr(VI), from the solution [22]. The transformation of biopolymers, like Cht and Alg, into a potential nanoforms extremely increases its capability and capacity for the dispersion of HM expected to their improved physiochemical setting, determined by bigger communication facilities, more functional groups, and more filtering space. These limits increase amidst the packing of nanopolymers by metals (e.g., metal nanoparticles) that can define the greater concentration of the Cht/Alg/Fe-NPs compound/absorption.Figure 13
The batch adsorption of Cr(VI) was strongly and adequately accomplished, applying complex Cht/Alg/Fe-NPs, with 90% elimination ratio at 5th day.


## 6.1.1. FTIR Analysis

The FTIR spectra of the composite (Cht/Alg), along with Fe-NPs synthesized from the red cabbage extract, are given in Figure4. In the Cht/Alg composite blend, the spectral data have taken different collections against any polymer, securing polymers, cross-linking along with biochemical communications. In addition, the conversion of the expandable signal C–O–C (Alg spectrum) at 1,024–1,413 cm−1 showed the Alg and Ca2+ ion and the ionic interactions among Alg carboxyl groups along with calcium ions. As seen after the Cht/Alg cross-link interaction, the extended (CH) Cht and Alg CH vibration points are seen scattered; the additional hydrogen bonds formed between the Cht amino category are converted to NH3+ and produce a polyelectrolyte compound under strong electrostatic contact with Alg carboxyl anions [23].Figure 4
The FTIR spectra of blended chitosan/alginate nanoparticle (Cht/Alg). The merge category/bonds from beginning polymers in Cht/Alg are determined by vertical lines.In the spectrum of red cabbage/Fe-NPs (Figure5—red cabbage-Fe-NPs), the maximum value of O–H changed to 2,920 cm−1 after Fe-NPs synthesis. The dispersal on the reference point at 1,134 cm−1 reveals the embarrassment of these biochemical bonds in Fe-NPs synthesis along with capping. The “Van der Waals” interactions are recommended as the essential explanation of the disruption among O group along with N atoms in the extraction also synthesized Fe-NPs.Figure 5
FTIR spectra of a mixed extract among synthesized Fe-NPs (red cabbage/Fe-NPs).


## 6.1.2. TEM Imaging

The infrastructure of synthesized Fe-NPs was observed under TEM imaging. The field showed that almost all of the synthesized NPs were in circular/semispherical shapes, with obvious agglomeration between the composite particles—(Ps) for synthesized Fe-NPs in the range of 13.6−72.4 nm. NPs cluster was primarily caused by the distinctive tense aspects of marine vegetation extraction and the presence of strong O–H groups in it. In addition, the tendency of Fe-NPs agglomeration was expected due to its minute size and potentially magnetic characteristics.


## 6.1.3. SEM Imaging

Ultrasound imaging of Cht/Alg nanocomposite containing red cabbage-synthesized Fe-NPs is illustrated in Figure6. The nanocomposite has a statistically stable shape of Ps at a distance of 0.5 µm. The Fe-NPs embedded in Cht/Alg nanocomposite are very markedly visible up to the location of the nanoparticles, indicating their potential interaction with the environment and its components. Additionally, Fe-NPs appear in nonagglomerated forms, confirming the ability of Cht/Alg nanocomposite to capture and stabilize red cabbage extract-synthesized Fe-NP.Figure 6
Scanning electron microscopy image of assembled chitosan/alginate nanocomposite by synthesized Fe-NPs.


## 6.1.4. Nanomaterials Capacity Along with Charge

In Ps analysis, along with the charge of NPs constructs, showed a minimum Ps width of Fe-NPs (12.5–83.1 nm), with an average Ps width of 21.4 nm. The Ps ranges from 162.6 to 514.6 for Cht/Alg NPs and against 173.9–568.5 as Cht/Alg/Fe nanocomposite, amidst an average width of 311.2 and 342.6 nm, correspondingly. The distribution of Fe-NPs in nanocomposite polymers led to an increase on Ps along with a significant increase on nanocomposite negative charge from −23.2 to 34.6 mV (Table1).Table 1
Intensity distribution.
d (nm)f (%)f (cum.%)d (nm)f (%)f (cum.%)d (nm)f (%)f (cum.%)d (nm)f (%)f (cum.%)1.00.00.08.00.00.064.31.812.1515.22.381.31.10.00.08.70.00.069.82.014.1559.92.283.51.20.00.09.50.00.075.92.116.2608.52.085.51.30.00.010.30.00.082.52.318.5661.41.987.41.40.00.011.20.00.089.72.420.9718.81.789.11.50.00.012.20.00.097.42.623.5781.21.690.71.60.00.013.20.00.0105.92.726.2849.01.592.11.80.00.014.40.00.0115.12.829.0922.71.393.51.90.00.015.60.00.0125.12.931.91,002.81.294.62.10.00.017.00.00.0136.03.034.91,089.91.195.72.30.00.018.40.00.0147.83.037.91,184.50.996.62.50.00.020.00.00.0160.63.141.01,287.40.897.42.70.00.021.80.00.0174.53.144.21,399.20.798.13.00.00.023.70.00.0189.73.247.31,520.70.698.73.20.00.025.70.30.3206.23.250.51,652.70.599.23.50.00.027.90.40.7224.13.153.61,796.20.499.73.80.00.030.40.51.2243.53.156.81,952.10.3100.04.10.00.033.00.61.9264.73.159.82,121.60.0100.04.50.00.035.90.82.6287.63.062.82,305.80.0100.04.90.00.039.00.93.5312.62.965.82,506.00.0100.05.30.00.042.41.04.6339.82.968.62,723.60.0100.05.70.00.046.11.25.7369.22.871.42,960.10.0100.06.20.00.050.11.37.1401.32.774.13,217.10.0100.06.80.00.054.41.58.6436.22.576.63,496.40.0100.0


## 6.1.5. Reaction of pH on Chromium Adsorption

The pH test result for adsorption is given in Figure7. The result shows that high adsorption was noted in pH of 3 and with an increase in pH, and later a significant loss in adsorption percentage was observed with the increase of pH. This can be owed to the collapsing of the attractive electrical energy between the opposite charge adsorbate and the adsorbent, ultimately leading to loss at sorption volume [24].Figure 7
Reaction of pH at Cr(VI) removal.


## 6.1.6. Reaction of Contact Time on Chromium Adsorption

The impact based on CT at the effectiveness based on chromium adsorption is shown in Figure8. The adsorption rate starts at a slow phase along with chromium removal (%) increasing. Discharge ability concluded within about 90% during the 5th day of the study. There was no powerful difference on the concentration balance after 1–4 hr, and after 1 hr, the adsorption phase reached the balance mark [25].Figure 8
Reaction of contact time at adsorption procedure ability.


## 6.1.7. Effect on Adsorbent Quantity Chromium Adsorption

The reaction on adsorbent volume on chromium release is given in Figure9. The consequences presented that the discharge of chromium on equilibrium state increased with a rising load of adsorbent. So that, when the adsorbent quantity was added on from 0.05 g to 0.2 g/100 mL, the removal efficiency was increased from 88% to 100%, 56.1% to 91.7%, and 45% to 79.2% by application of 0.2, 0.5 mg, and 0.75 mg/L, respectively.Figure 9
Reaction of adsorbent quantity by Cr(VI) discharge.


## 6.1.8. Reaction of Basic Chromium Application on Adsorption Procedure

The developmental impact of the reaction on the first chromium concentrate on effective removal function is presented in Figure10. The efficiency of chromium release got decreased by raise in basic chromium application. In case of low chromium concentration, the scale of the basic amount of chromium ions to the convenient adsorbent area was vast, and thereafter, partial adsorption developed into separate of its initial concentration (Figures 11 and 12). However, in high applications, the feasible advertising sites are few, and that is why the discharge of the percentage of iron ions reliant on the basic application decreases.Figure 10
Effect of chromium application on Cr(VI) discharge chromium removal (%).Figure 11
A normal solution of chromium.Figure 12
1,5-diphenylcarbazide that forms a reddish–violet complex with Cr6+.


## 6.1.9. Batch Adsorption of Cr(VI)

The Cr(VI) batch adsorption was strongly noted along with the successful implementation of applying both Cht/Alg NPs and the mixed Cht/Alg/Fe-NPs, with 90% removal of Cr(VI) (Figure13). While testing the factor, the resting conditions were optimized and maintained at normal levels (e.g., pH = 5, adsorbent quantity = 5 g/L, contact interval = 5 days and concentration of the first ion = 100 ppm). Generally, the combined Cht/Alg/Fe-NPs have a higher Cr(VI) adsorption performance than Cht/Alg NPs as per parameter. Due to the high content against OH (hydroxyl groups) along with NH2 (primary amine), which moves as a capable filtration site, the Cht-based NPs were promoted as excellent commercial tool, along with the dispersion of many HM, in addition to Cr(VI), from the solution [22]. The transformation of biopolymers, like Cht and Alg, into a potential nanoforms extremely increases its capability and capacity for the dispersion of HM expected to their improved physiochemical setting, determined by bigger communication facilities, more functional groups, and more filtering space. These limits increase amidst the packing of nanopolymers by metals (e.g., metal nanoparticles) that can define the greater concentration of the Cht/Alg/Fe-NPs compound/absorption.Figure 13
The batch adsorption of Cr(VI) was strongly and adequately accomplished, applying complex Cht/Alg/Fe-NPs, with 90% elimination ratio at 5th day.


## 7. Conclusion

Pulling biopolymers are assembled and connected to produce Cht/Alg NPs, among an average width of 311.2 nm. The synthesis of Fe-NPs was strongly obtained using red cabbage extract, and Fe-NPs contained semispherical membranes with a width of 214 nm. The combination of Cht/Alg NPs with the synthesized Fe-NPs resulted in a uniform distribution and stability of metal NPs inside the polymer nanocomposites [26]. Both nanocomposites have shown promising and a very high efficiency as Cr6+ adsorbent when checked in various conditions. The most effective adsorption conditions were found to be at pH value of 2, the adsorbent application at 0.75 g/L, the contact interval of 5 days along with basic Cr6+ combination of 0.2 g/100 mL. The optimized features can be applied for use in the complete removal of Cr6+ in a mass scale. One report suggests the real-time use of carbon nanocomposites in wastewater treatment must be addressed economically [27]. Use of these composite nanopolymers (Cht/Alg NPs), formulated in a new way with red cabbage-synthesized Fe-NPs, will be of great significance for integrated discharge of Cr6+ in wetlands. These active nanocomposite sorbents can be used from “lab” to “land” after HM sorption experiments, thus making them a cost-effective approach in wastewater management.



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*Source: 1713690-2023-02-07.xml*