Core–shell polymer nanocomposite based on free radical copolymerization of anthranilic acid and o-amino phenol in the presence of copper hexacyanoferrates nanoparticles and its adsorption properties

Core–shell polymer nanocomposite (CSNC) of copper hexacyanoferrate-copolymer of anthranilic acid with o-aminophenol (CHCF-poly(AA-co-OAP)) was synthesized and used as ion exchanger for the sorption of cesium ions from aqueous solution. The nanocomposite was prepared by implantation of CHCF nanoparticles into copolymer of poly(AA-co-OAP) during the polymerization process. The surface morphology and the porous structure were investigated through transmission electron microscope (TEM), scanning electron microscope (SEM) and Brunauer–Emmett–Teller (BET). The characterization of the prepared (CSNC) was carried out by Fourier transform infrared spectroscopy (FT-IR), X-ray diffraction (XRD) and Thermogravimetric (TGA). Which SEM and TEM images confirmed the nano-size of the prepared CSNC. The values of adsorption capacity of CSNC towards cesium ions and the factors influence on the removal of cesium from solutions were investigated as function in pH, metal ion concentration, temperature and contact time. The results illustrated that the highest value of sorption capacity of the prepared CSNC towards Cs+ ions was 2.1 mmol g−1 at pH 11, 10 mmol L−1 Cs+ and 25 °C. Four modeling include on Langmuir, Freundlich, Temkin and Dubinin-Radushkevich (D-R) isotherms models were studied. According to the obtained data, Langmuir model considered the most suitable model, which suggest that the uptake of Cs+ was monolayer and homogeneous. Also, the adsorption kinetics data was fitted well to pseudo-second-order model. Thermodynamic parameters were calculated in the temperature from 25 to 60 °C and the data revealed that Cs+ sorption was endothermic, spontaneous, and more favorable at higher temperature. Up to 92% desorption of Cs+ was completed with 2 M KCl.


Introduction
Since twenty years in research area, the core-shell nanomaterials have great attention due to their uses in different applications like catalysts, industrial and "the study of how life and medicine work together" applications [1][2][3][4][5][6][7][8][9][10][11][12][13][14]. The core-shell nanocomposites may be with different sizes and shapes of core and shell thickness with different surface "the study of the shapes of things". They may be spherical, centric, weird, star-like, or tubular in shape. The properties of core-shell depended on the size and shape, which varies from material to another. In different fields like medical biotechnology, molecular bioimaging, drug delivery and cancer therapy, core-shell nanoparticles are used. The surface of the nanoparticles is changed through functional groups or molecules or coated with a thin layer of other materials (with different voters/parts), they show improved properties compared to the non-functionalized uncoated particles [15][16][17][18].
One of the fission (things produced along with something else) of most current nuclear power plants is cesium. The release of these radioactive isotopes like 134 Cs + and 137 Cs + can show significant poison with the long-lived radionuclides (half-life ῀ 30 years) accumulating in the environment [19]. The high solubility of cesium can cause its moving through underground water that supplies wells to the locations on the Earth that support life, which has possibly dangerous to human health and also to the environment. Also, cesium is chemically almost the same as potassium so it can be easily presented in terrestrial and aquatic organisms [20]. Cs metal can be adsorbed to the body and can be easily dispersed inside the soft tissues of body. The main problems of 137 Cs adsorption through the contaminated food and water is thyroid cancer [21].
Different technologies have been studied to remove cesium from aqueous solutions such as extraction, ion exchange, chemical precipitation, adsorption, and electrochemistry [22]. One of these methods is ion exchange process, which showed a lot of attracted views for removal of cesium from waste streams because of its convenience, efficiency and selectivity [23].
Excellent ion exchangers for cesium ions removal from aquatic solution are known as transition metals of hexacyanoferrates (Fe, Cu, Zn, Ni, Co) [24]. Copper hexacyanoferrate (CuHCF) is among MHCFs, which characterized by the high value of adsorption capacity, chemical stability and selectivity over a range of pH [25]. The disadvantage of using the CuHCF to remove cesium radionuclides from the contaminated aquatic environment is unfeasibly separated from aquatic solution after the adsorption. To overcome this drawback, the CuHCF powders are usually planted on various supporting or binding materials to fabricate composite adsorbents. By implantation of inorganic into the organic materials during the preparation process, the composite ion exchangers are generally obtained [26]. The active components in ion exchangers nanocomposite is the inorganic materials and organic materials are simply inactive binders.
In our previous work, nanoparticles of copolymer of anthranilic acid with o-aminophenol poly(AA-co-OAP) was synthesized and used as chelating resin for the sorption of copper ions from aqueous solution [33]. In this work, we prepared core-shell nanocomposite (CSNC) of copper hexacyanoferrate-copolymer of anthranilic acid with o-aminophenol poly(AA-co-OAP) and used as nanocomposite ion exchanger for the separation of cesium ions. The CHCF nanoparticles implanted in poly(AA-co-OAP) during the copolymerization process. The synthesized CSNC was characterized by Fourier transform infrared spectroscopy (FT-IR), X-ray powder diffraction (XRD) and Thermogravimetric (TGA). The study of the surface shapes was also investigated by transmission electron microscope (TEM), scanning electron microscope (SEM). As function in pH of cesium solution, cesium ion concentration, temperature and contact time, the removal of cesium from aqueous solutions was reported. Also, the regeneration of cesium was studied.  6 ]0.3H 2 O) and polyvinyl alcohol (PVA) were obtained from Sigma Aldrich Co., USA. Non-radioactive cesium chloride (CsCl) was purchased from Alfa Aesar (China). Hydrochloric acid from Merck, India. All chemicals were used without further purification.

Synthesis of the nanoparticles of copper hexacyanoferrate (CHCF)
CHCF was prepared through the addition of CuSO 4 .5H 2 O solution (10 wt % was mixed in 50 ml distilled water until completely dissolve) drop by drop to potassium hexacyanoferrate solution (10 wt % was dispersed in 50 ml of distilled water) with stirring. Then, PVA (6 wt %) was dissolved in 100 ml distilled water and added drop by drop to the above mentioned mixture of solutions. The reaction was left on magnetic stirrer for 24 h at room temperature. The reddish brown precipitate was filtered off next day, washed with distilled water for several times. Finally, the obtained reddish brown powder product was dried in air at room temperature and it was referred as CHCF.
Synthesis of core-shell nanocomposite (CSNC) of copper hexacyanoferrate-copolymer of anthranilic acid with o-aminophenol (poly(AA-co-OAP)) CSNC was synthesized by plantation of nanoparticles of CHCF through free radical copolymerization of AA with OAP in the presence of APS as redox initiator. A mixture of anthranilic acid (40 mmol)  The reaction was left on magnetic stirrer for 24 h. The black precipitate was filtered off next day, washed with 0.1 M of HCl followed by deionized water several times, and dried in air at room temperature to give the black precipitate of CSNC.

Characterization techniques
Morphology and particle size of core-shell nanocomposite was determined using transmission electron microscopy (TEM) (JEOL [JEM-1230 electron microscopy]), the sample was obtained as follows: the fine powder was dispersed in water under ultra-sonication, and then one drop of the suspension was suspended and evaporated on a carbon coated copper grid and placed in the Phillips (CM/TEM). Also scanning electron microscope (SEM, FEI Inspect S, Oxford USA) with increasing speed beam (25)(26)(27)(28)(29)(30) k.v with vacuum pressure 60 Pa and spot size (5-6) using back scattering detector for Z-imaging and an X-ray diffractometer was used to determine the morphology and particle size of core-shell nanocomposite. The IR spectra for the prepared CHCF nanoparticles and the core-shell nanocomposite were measured using Thermofisher Nicolete IS10, USA in the range of 400-4000 cm −1 Spectrophotometer. Thermal analysis experiments including Thermogravimetric (TGA) for the core-shell nanocomposite was carried out using SDT Q600 V20.9 Build 20, USA thermogravimetric analyzer. The experiment was performed in a dynamic atmosphere of nitrogen from room temperature to 1000 °C at heating rate of 10 °C/min. Porous structure parameters of the core-shell nanocomposite was described by Brunauer-Emmett-Teller (BET) and BJH methods through N 2 adsorption-desorption methods to inspect the porous properties of the nano-sized copolymers using nitrogen as the adsorbent at 77.35 K. The measurements were executed using a model NOVA 3200 automated gas sorption system (Quantachrome, USA). The X-ray diffraction of the prepared CHCF nanoparticles and the core-shell nanocomposite were obtained from Rigaku Oxford XtaLAB pro.

Adsorption of cesium ions using CSNC by batch technique
By batch technique, the adsorption properties of CSNC to Cs + ions were studied. The experiment was carried out as following, 0.1 g of the prepared core-shell nanocomposite was shaken with 100 ml of cesium solution (3 mmol/L) at 25 °C. At the end of time, the solution was filtered for phase separation and the concentration of supernatant solutions was measured by using Agilent Technologies 700 Series ICP-OES. For the evaluations of adsorption capacity (q e ) of the prepared core-shell nanocomposite, Eq. (1) was applied.
where C o (mmol L −1 ) and C e (mmol L −1 ) are the initial and the equilibrium cesium concentrations, respectively; V (L) is the volume of the aqueous solution and W is the weight of dry CSNC in grams.
To study the influence of pH on the adsorption process of Cs + ions through CSNC, 100 ml of Cs + solution (3 mmol L −1 ) was mixed with 0.1 g of CSNC at different pH values in the range from 3 to 11. The pH of cesium solutions were adjusted by 0.1 M HCl and 0.1 M NaOH. To study the effect of concentration on Cs + adsorption, adsorption experiments with different initial concentration of Cs + in the range of 2-10 mmol L −1 were performed at optimum pH. To investigate the effect of shaking time on adsorption of Cs + , the experiments were performed at different times (0.5-3.5 h) at optimum pH and optimum concentration of Cs + . The influence of temperature on the cesium uptake was performed at different temperatures 25, 40 and 60 °C, at optimum pH and 10 mmol L −1 of Cs + .

Desorption
The regeneration of the loaded CSNC by Cs was achieved using 2 M KCl at 25 0 C. To study the reusability of CSNC, five adsorption-desorption cycles were performed.

Synthesis of core-shell nanocomposite (CSNC) of CHCFpoly(AA-co-OAP)
A new CSNC was synthesized by the plantation of nanoparticles of CHCF during the free radical copolymerization of anthranilic acid with o-aminophenol. The synthesized CSNC used for sorption of cesium ions from aqueous solutions by ion-exchange process, which the potassium ions in CSNC replaced by cesium ions as shown in Scheme 1. Figure 1 showed the surface properties of synthesized CHCF by SEM and TEM, which was confirmed the cuboid structure with the nanometer size of 25-50 nm of the prepared nanoparticles CHCF. The core-shell structure of the

Morphology properties of CHCF and CSNC of CHCF-copolymer of anthranilic acid with o-aminophenol poly(AA-co-OAP)
nanocomposite was confirmed by TEM techniques as shown in Fig. 2. The SEM-EDX and mapping spectra of CSNC samples before and after cesium adsorption were studied and shown in Figs. 3 and 4. The SEM images in Fig. 3a were studied to determine the distribution of the CHCF nanoparticles through poly(AA-co-OAP). These images indicated that the CHCF nanoparticles were uniformly distributed throughout the sample. Following cesium adsorption, it was shown that cesium was uniformly adsorbed with more bright which indicates that the cesium adsorption was emerged at after adsorption of cesium ions Fig. 4a, as compared with Fig. 3a.
To prove whether adsorption of cesium ions by CSNC, EDX elemental mapping spectra analysis were studied with SEM images. The cesium ion peaks were clearly appeared onto the surface of immobilized CSNC in Fig. 4b in compared with Fig. 3b. Also, the distribution of K + in composite before and after cesium adsorption was shown  Figs. 3b and 4b, which showed that the concentration of K + was decreased slightly after cesium adsorption. To observe the distribution of cesium and potassium ions before and after adsorption process (Figs. 3c and 4c), elemental mapping for CSNC samples before and after cesium adsorption was also studied. The images showed that homogeneous distribution of cesium ions with decreased in distribution of K + due to adsorption process occurs with good efficiency. Figure 5 showed the spectra of the synthesized CHCF nanoparticles and CSNC. In Fig. 5a, the spectrum of CHCF exhibit sharp peak at 2095 cm −1 due to the stretching vibration of cyanide group (C≡N) and the bands in the 480-592 cm −1 region are due to the (Fe-C) stretching. Figure 5b showed the spectrum of CSNC, which exhibit absorption peak at 3421 cm −1 attributed to OH group. The strong peak at 1684 cm −1 for the C = O stretching. The peak in range 3315-3200 cm −1 is due to NH group. The spectrum showed peaks at 1630-1637 cm −1 and 1500-1571 cm −1 due to the C = C of benzenoid and quinoid rings, respectively. Also, peaks at 1204-1244 cm −1 are attributed to the C-N stretching of secondary aromatic amine. Also, Fig. 5b showed sharp peak at 2095 cm −1 due to the stretching vibration of cyanide group (C≡N) similar to that found in Fig. 5a for CHCF. This band indicated the plantation of CHCF nanoparticles in poly(AA-co-OAP).

Surface area
The BET surface area, BJH pore volume and average pore diameter for CSNC were determined by Brunauer-Emmett-Teller (BET) and BJH methods through N 2 adsorption-desorption methods at 77.35 K. The data illustrated that the CSNC has surface area 12.430 m 2 /g, this leads to an efficient transfer of the metal ions to the internal adsorption sites [34].

X-Ray diffraction (XRD)
The X-ray diffraction (XRD) patterns of CHCF nanoparticles and CSNC were shown in Fig. 6. In Fig. 6a showed the diffraction patterns of CHCF nanoparticles, which showed a characteristic peaks at 2Ө values of 17.5, 24.9, 35.9, 40.1, 44.2, and 51.1° which are due to Miller indexes of (200), (220), (400), (420), (424), and (440), respectively [35] of the cubic crystal structure of CHCF (with a cell constant of 9.99 A; JCPDS card no. 02-0383). Figure 6b showed the X-ray diffraction patterns of CSNC, which exhibited peaks at at 2θ = 25° was characteristic of the van der Waals distances between stacks of phenylene rings (polyanthranilic and poly o-aminophenol rings) [33] and additional peaks similar to diffraction peaks of CHCF (Fig. 6a). Thus, the XRD data confirms the presence of CHCF in the copolymer matrix.

Thermogravimetric analysis
The thermal stability of the prepared CSNC was evaluated and shown in Fig. 7. Four stages decomposition pattern were recorded. The first weight loss step started from range 27.89 to 159.18 °C which corresponds to the loss of water molecules, free acids, and volatile molecules in the CSNC. The second step at temperature range 159.64-327.6 °C which represents loss of dopant bound to the copolymer chain and evolution of CO 2 . The third step was temperature range 328.6-502.73 °C, which because of loss of sublimation and removal of low molecular weight polymer from the CSNC matrix [33]. The fourth step at temperature range 503.77-799.06 °C which is due to the complete degradation and decomposition of the polymer backbone. Above 799.06 °C, the results obtained were associated with the residues only.

Adsorption of cesium ions on core-shell nanocomposite (CSNC)
Effect of pH The pH of the aquatic solutions is one of the important factors which affecting the adsorption performance of CSNC towards cesium ion. The sorption behavior of CSNC was studied at pH in range of 3-11 to optimum the best pH, which recorded the maximum adsorption capacity of Cs on CSNC. Figure 8 showed the adsorption capacity  Fig. 8, we concluded that the increasing in pH of aquatic solutions showed increasing in adsorption capacity of Cs ions onto CSNC. The maximum adsorption capacity was 1.26 mmol g −1 at pH 11, thus all further experiments in the present study were performed at pH 11. Also, we observed that the relative low adsorption at pH 3,4 and 5 may be due to one of two reasons or both of them. The first reason is the competitive adsorption between Cs + and the H + ions from carboxyl groups [36]. The second reason is the dissolution of a fraction of CuHCF/ poly(AA-co-OAP) surface under acidic conditions [37]. It is assumed that in acidic condition, H + ions occupy the active sites of the adsorbent. For this reason, Cs ions have to face a repulsive force with the higher concentrated H + ions during the adsorption process. However, when the surface of the adsorbents was deprotonated in alkali conditions then the electrostatic interaction between adsorbents surface and Cs ions increased. Therefore, the Cs adsorption enhanced at higher pH [35][36][37][38][39].

Effect of initial Cs + concentration and equilibrium isotherm models
To study the effect of concentration of cesium on sorption process, experiments were carried out using different initial concentrations of Cs + from 2 to10 mmol L −1 Fig. 3 SEM-EDX and mapping spectra of CSNC sample before cesium adsorption at 25 °C and pH = 11. The obtained results showed that the uptake of Cs + increased with the increasing the initial concentration of Cs + to reach maximum capacity at initial concentration equal to 10 mmol L −1 of 2.1 mmol g −1 (Fig. 9).

Adsorption isotherm models
To understand the mechanism of the adsorption process of cesium using CSNC four isotherm models were applied. The four isotherm models include Langmuir, Freundlich, Temkin and Dubinin-Radushkevich (D-R), which were examined for studying the distribution of Cs + between the aqueous solution and the prepared composite. After applying four isotherm models, the Cs + affinity, surface properties, sorption capacity, and sorption mechanism can be expalined. The Langmuir isotherm (Eq. 2) [40] was applied by plotting C e /q versa. C e to give straight line, Q max and K are calculated from slope and intercept, respectively (Fig. 10).
where C e (mmolL −1 ) is the concentration of Cs + after equilibrium; q and Q max (mmolg −1 ) are amount of Cs + adsorbed at equilibrium and maximum adsorption, respectively. K (Lmmol −1 ) is the Langmuir affinity constant.
The Freundlich isotherm (Eq. 3) [41] was applied by plotting log q versa. Log C e to give straight line, the freundlich constants are calculated from slope and intercept (Fig. 10). The Freundlich isotherm can be explained that the adsorption of cesium ions onto CSNC is heterogeneous.
(2) C e q = C e Q max + 1 KQ max where K F (mmolg −1 ) and N are the Freundlich constants related to the adsorption capacity and sorption intensity, respectively. The third isotherm model is Temkin isotherm model which assumes that the heat of adsorption of cesium ions decreases linearly with coverage due to indirect adsorbate-adsorbate interactions. The Temkin isotherm (Eq. 4) [42] was applied by plotting q versa. ln C e to give straight line, the Temkin constants can be calculated from slope and intercept (Fig. 10).
where K T (Lg −1 ) and B (Jmol −1 ) are constants related to equilibrium binding and heat of adsorption, respectively. The fourth isotherm model is (D-R) model which applied to express the adsorption mechanism with a Gaussian energy distribution onto a heterogeneous surface. Dubinin-Radushkevich (D-R) (Eq. 5) [43] was applied by plotting lnq e versa. ε 2 to give straight line, the (3) log q = N log C e + log K F (4) q = B ln K T + B ln C e Temkin constants can be calculated from slope and intercept (Fig. 10).
where K DR (mol 2 kJ −2 ) is a constant which is related to mean free energy of adsorption, ε (J mol −1 ) represents the Polanyi potential which is related to the equilibrium concentration (C e ) as indicated in the following equation: The mean sorption energy E (kJ/mol), defined as the free energy change when one mole of ion is adsorbed to the surface of the solid from infinity in the solution, is calculated according to the following equation [44]: By studying the Langmuir sorption model, if the data fitted with this model, the sorption of cesium is homogeneous adsorption, which the solute molecules are adsorbed onto a homogenous and flat surface of adsorbent. Langmuir adsorption model can be explained in terms of dimensionless constant (R L ), which is used to predict the affinity between the adsorbent and adsorbate. The R L value was given by the following equation: The R L values indicate the mechanism of the isotherm. Since the isotherm is unfavorable when R L > 1, linear when R L = 1, favorable when 0 < R L < 1 and irreversible when R L = 0 [45].
The four isotherm models were listed in Table 1. From Table 1, we concluded that the highest value of linear correlation coefficient, (R 2 = 0.9975) was obtained from Langmuir model which fitted with the collected results better than other three isotherm models. So we concluded that the sorption of Cs + occurs largely on homogenous surface by monolayer adsorption process. Since the obtained R L values lie between 0.14 and 0.45 (Table. 1), which proved that the equilibrium adsorption is favorable at higher initial concentration. As shown in Table 1, the lowest value of R 2 = 0.9583 for Dubinin-Radushkevich (D-R) isotherm indicated that this model not fitted with adsorption process in this work.
In Table 2, the commonly other adsorbents used to the adsorption of cesium (adsorption capacity) are listed and compared with the synthesized CSNC of this work. Also, the highest capacity was recorded for the synthesized CSNC of this work. These collected data reveals that the CHCF/poly(AA-co-OAP) nanocomposite is an effective adsorbent for the separation of cesium from aqueous solution and it can be used for treatment of large volumes

Effect of contact time and equilibrium kinetic models
To examine the kinetics of adsorption process, a series of experiments was carried out to determine the optimal shaking time for uptake of Cs + onto CSNC in the shaking time range of 0.5-3.5 h. As shown in Fig. 11 it was observed that the adsorption of Cs + ions from aqueous solution using the nanocomposite adsorbent is continuously increased with time increase until reaching equilibrium between two phases after 3 h. Therefore, this obtained equilibrium time was selected for the next adsorption experiments. At the beginning of adsorption process, the rate of uptake was rapid, and the equilibration was achieved in 3 h. This high initial adsorption rate towards Cs + indicates that the adsorption process occurs mainly on the nanocomposite surface and the regular distribution of CHCF inside poly(AA-co-OAP), making the rapid Cs + uptake at the beginning of the experiment. The fast removal process decreased the time needed for the adsorption of Cs + from wastewater which reduced the costs for the operation. The kinetic process of adsorption of Cs + by CSNC can be investigated by using four kinetic models, including the pseudo-first-order (Eq. 9) [51], pseudo second order (Eq. 10) [52], intra-particle diffusion model (Eq. 12) [53], and Elovich equation (Eq. 13) [54] (Fig. 12).  where q and q t are capacities of Cs + adsorbed per unit mass of CSNC (mmolg −1 ) at equilibrium and at any time t (min), respectively; K ads (min −1 ), K 2 (g mmol −1 min −1 ) and K id (mmolg −1 min −0.5 ) are the rate constants of the first-order, second order and intraparticle diffusion models, respectively; h (mmol g −1 min −1 ) is the initial sorption rate constant. α (mmol g −1 min −1 ) is the initial adsorption rate and β (g mmol −1 ) is the constant of the degree of the surface coverage and activation energy for chemisorptions. Pseudo-first-order (Eq. 9), Pseudo second order (Eq. 10), Intra-particle diffusion model (Eq. 12), and Elovich equation (Eq. 13) are four models, which applied in this work in order to evaluate the mechanism of the kinetics of Cs + onto the CSNC. The kinetic parameters and correlation factor (R 2 ) were estimated and are listed in Table 3. The results reveal that the pseudo-second-order model (R 2 = 0.9587) is more suitable than other models. The fitness of pseudo-second-order kinetic model may mean that Cs + adsorbed on CSNC involving chemical (12) reaction, which including ion exchange, substitution, or complexation [22,55].

Influence of temperature and thermodynamic parameters
The temperature plays an important role in the adsorption efficiency of Cs + on the CSNC so, the uptake of Cs + was studied with a temperature range of 25-60 °C. The data in Fig. 13 showed the adsorption efficiency increased as the temperature was raised, indicating the endothermic nature of the process. Increasing the temperature is beneficial to bind of Cs + to adsorption sites. To better evaluate the adsorption process, three thermodynamic parameters were carried out including Gibbs free energy (ΔG), enthalpy change (ΔH) and entropy change (ΔS).
The change of the standard Gibbs free energy ΔG • ads (kJ mol −1 ), the change of the standard enthalpy ΔH • ads (kJ mol −1 ), the change of the standard entropy ΔS • ads (J mol −1 ) are thermodynamic parameters, which can be obtained using Eqs. (14) and (15): where T is the absolute temperature (K), R is the universal gas constant (8.314 Jmol −1 K −1 ) and K d is the equilibrium distribution constant (ml g −1 ). K d was given by Eq. (16).
where C o (mmolL −1 ) is the initial Cs + concentration, C e (mmolL −1 ) is the equilibrium Cs + concentration (mmolL −1 ), V is the total volume of the solution in (L) and W is the weight of the dry composite in gram.
The thermodynamic parameters are collected in Table 4. The calculated value of ΔH is 0.708 kJ/mol > 0 indicated that the adsorption process of Cs + on CSNC is endothermic reaction process. That is, increasing the temperature of the (14)   system can promote the adsorption of Cs + . Also, the values of (ΔG • ads ) were negative, which indicates the spontaneity and feasibility of Cs + adsorption. The positive value of standard entropy (ΔS°a ds ) indicates the affinity of the prepared nanocomposite for Cs + and the increasing randomness at the (nanocomposite / Cs + solution) interface during the uptake process. It can be observed that the removal efficiency was not significantly influenced due to the change of temperature. The marginal drop in Cs removal performance with increasing temperature may be resulted in the thermal destabilization which increased the mobility of Cs ions and inaugurated the desorption steps [35,39,56].

Fig. 13
The effect of temperature on the distribution coefficient of cesium ions on CSNC ion exchanger

Desorption
From the uptake-elution process, the regeneration efficiency can be calculated from the following Eq. (17): From the uptake-elution, we observed that the adsorption capacity of newly synthesized CSNC was hardly affected even after five regeneration cycles. The results showed that adsorption capacity decreased from 100 to 98%, 97%, 95%, 93% and 92%

Conclusion
For the first time, a low cost and facile route has been developed for the synthesis of core shell nanocomposite derived from CHCF and poly(AA-co-OAP). The synthesis route included (i) synthesis of nanoparticles of CHCF (ii) plantation the nanoparticles in polymer matrix of poly(AAco-OAP) during the copolymerization process. The structure of the prepared CSNC via FT-IR, X-ray powder diffraction (XRD) and Thermogravimetric (TGA), TEM and SEM-EDX mapping. The SEM and TEM confirmed the nano structure of the prepared CHCF and CSNC. Also, XRD analysis confirmed the expansion of the CHCF into poly(AA-co-OAP) and The synthesized CSNC used for sorption of cesium ions from aqueous solutions by ionexchange process between the potassium ions in CSNC replaced by cesium ions. FTIR analysis confirmed the presence of CN bonds in the CSNC adsorbents implying the successful plantation of CHCF on the copolymer, which was further supported by EDX mapping.
The sorption process of the synthesized CSNC towards cesium ions and the factors affecting on the cesium sorption from aqueous solutions were reported at the difference in pH, metal ion concentration, shaking time and temperature. The results showed that the maximum capacity of the CSNC towards Cs + ions was 2.1 mmol g −1 at pH 11, 10 mmol L −1 Cs + and 25 °C. Four modeling include on Langmuir, Freundlich, Temkin and Dubinin-Radushkevich (D-R) isotherms models were studied, which the data were well fitted with Langmuir model suggesting that the uptake of Cs + was monolayer and homogeneous. Also, the adsorption kinetics results were fitted well to pseudo-second-order model. Thermodynamic parameters were calculated in the temperature range of 25-60 °C and the data revealed that Cs + sorption was endothermic, spontaneous, and more favorable at higher temperature. Up to 92% desorption of Cs + was completed with 2 M KCl.
Funding Open access funding provided by The Science, Technology & Innovation Funding Authority (STDF) in cooperation with The Egyptian Knowledge Bank (EKB).

Declarations
Conflict of interest All authors declare that they have no conflict of interest.
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