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Cellulose polymers with β-amino ester pendant group: design, synthesis, molecular docking and application in adsorption of toxic metals from wastewater



Cellulose polymers with multidentate chelating functionalities that have high efficiency for toxic metal ions present in water were designed, synthesized, and analyzed. The synthesis was carried out by reacting microcrystalline cellulose extracted from the solid waste of the olive industry with tert-Butyl acetoacetate (Cell-AA), produced cellulose with β-ketoester functionality was then reacted with aniline and the amino acid glycine to produce Cell-β-AN and Cell-β-GL, respectively.


The adsorption efficiency of the three polymers toward Pb(II) and various toxic metal ions present in sewage was evaluated as a function of adsorbent dose, time, temperature, pH value, and initial ion concentration to determine optimum adsorption conditions. The three polymers showed excellent efficiency toward about 20 metal ions present in a sewage sample collected from the sewer. The adsorption process follows the Langmuir adsorption isotherm model with a second-order of adsorption rate, the calculated qe values (2.675, 15.252, 20.856 mg/g) were close to the experimental qe values (2.133, 13.91, 18.786 mg/g) for the three polymers Cell-AA, Cell-β-AG and Cell-β-AN, respectively. Molecular Dynamic (MD) and Monte Carlo (MC) simulations were performed on the three polymers complexed with Pb(II).


The waste material of the olive industry was used as a precursor for making the target cellulose polymers with β-Amino Ester Pendant Group. The polymer was characterized by SEM, proton NMR, TGA, and FT-IR spectroscopy. The efficacy of adsorption was quantitative for metal ions present in a real sample of wastewater and the efficiency didn’t drop even after 7 cycles of use. The results indicate the existence of strong complexation. The thermodynamic study results showed a spontaneous bonding between of Pb(II) and the polymers pendant groups expressed by the negative value of the Gibbs free energy.

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Water contamination has become a critical global problem and a major health issue for living organisms and ecosystems. The issue was related to [1,2,3] industrial waste, agricultural waste, and the household cleaning items that release toxic heavy metals, organic material, dyes and other to the sewage system [4,5,6]. Other sources of toxic contaminants include medical, agricultural, plumbing, body care products. Among the toxic heavy metal ions that pose a risk and required immediate attention are Cd(II), Cu(II), Mn(II), Mg(II), Sr(II), Al(II), Co(II), Ni(II), Cr(III), Zn(II) and Pb(II) ions [7, 8]. Recycling of wastewater released from industrial and human activities has become a necessity. Among the most effective technologies used in wastewater purification and recycling wastewater from toxic heavy metals and other contaminants are precipitation, membrane filtration, electrodialysis, electrochemical treatment, coagulation [9], flotation [10], cementation [11], solvent-solvent extraction [12], ion exchange [13], chemical oxidation [14], reverse osmosis [15], and adsorption [16]. Amon these methods, adsorption received the highest attention due to its simplicity, availability, profitability, practicality, ecofriendly, recyclability, relatively low cost, less sludge production, high efficiency, and high selectivity [17,18,19]. The adsorption method mainly focuses on activated carbon as the adsorbents. However, some withdraw backs such as processing costs have led the scientist to search for other means [20]. More desirable adsorbents are those made from renewable, low-cost materials, especially those derived from agricultural waste materials [21] and biological adsorbent [22, 23]. Natural based adsorbents made from cellulose [24], lignin, chitosan and hemicellulose received the most attention. They are economically feasible, environmentally friendly, and highly efficient for removal of heavy metal ions from wastewater [25]. Cellulosic based adsorbents and related obtained from waste materials such as Kenaf [26, 27], cotton linters [28], wheat straw [29], wood sawdust [30], rice husk [31] were prepared and investigated for the adsorption of several metals such as those mentioned above. Nanoparticle adsorbents made from natural materials such as cellulose nanocrystalline (CNC) were the most promising, especially. Despite all the rapid progress in the nanocellulose adsorbents still many celluloses-based materials and derivatives have not been explored in wastewater purification. In this work, new cellulose-based adsorbents were prepared and used in wastewater purification. The new adsorbents were prepared by functionalizing microcrystalline cellulose with β-ketoester to form cellulose with 1,3-dicarbonyl pendant group, which then converted to a Schiff base by reacting it with aniline and the amino acid glycine. Microcrystalline cellulose used in this work was extracted from olive industry solid waste (OISW) [32, 33]. The prepared polymer showed an excellent affinity for various heavy metals since the functional groups are considered multidentate chelating agents. The adsorption efficiency of the three cellulose-based polymers was evaluated toward Pb(II) and other metal ions from real wastewater samples.



All chemicals and reagents used in this work were purchased from Sigma-Aldrich chemical company (Jerusalem) and used as received. The chemicals include tert-Butyl acetoacetate (t-BAA), lithium chloride anhydrous (LiCl), N,N-dimethylacetamide anhydrous (DMAc), aniline, glycine, lead(II) nitrate, acetic acid, methanol and nitrogen gas (purity 99.9%). All reagents used were of analytical grade. Deionized water was used to prepare all solutions. Cellulose used in this work was extracted from olive industry solid waste (Jeft) by a chemical process that was developed at the laboratories of An-Najah National University-Nablus/Palestine.



Nicolet 6700 Fourier Transform Infrared (FT-IR) spectrometer equipped with the Smart Split Pea micro-ATR accessory (Thermo Fisher Scientific, Waltham, MA, USA) was used in this work. The following IR parameters were used: resolution 4 cm-1, spectral range 400–4000 cm-1, number of scans 128. Thermo-gravimetric analysis (TGA) and differential scanning calorimetry (DSC) measurements were performed using a TG/DSC Star System (Mettler-Toledo) coupled with a MS-Thermostar GSD320 (Pfeiffer Vacuum) Mass Spectrometer. TG/DSC analysis was performed with Pt crucibles, in N2 flow (20 mLmin−1) at a heating rate of 5 ºC min−1 in the range 25–1100 ºC by a HT1100 oven connected to a MX5 microbalance (thermostatic at 22 ºC). The STARE software v.10.0 (Mettler Toledo) controlled the process.

Metal ions concentrations were determined using Flame Atomic Absorption Spectrometer (FAAS, ICE3500 AA System, Thermo scientific, United Kingdom) and the inductively coupled plasma mass spectrometry (ICP-MS) via an iCAPTM RQ ICP-MS (Thermo Fisher Scientific, Waltham, MA, USA). All analysis studies were performed in triplicate and the mean of the three runs was reported. The error range in the experimental data was analyzed using Excel Microsoft software, a certainty interval of 95% was used. The data analysis was performed using the t-test. All variations were considered statistically when p ˂ 0.05 for the analysis of t-test. The flame type was air-C2H2.

Preparation of cellulose acetoacetate (Cell-AA)

A sample of microcrystalline cellulose (5.0 g, 0.15 mol/anhydrous glucose repeat unit) was added to a 0.5 L one necked round bottomed flask containing 200.0 ml distilled water and stirred magnetically for 2 h at room temperature. The cellulose was collected from water by suction filtration then suspended in 200 ml methanol for one hour. This process was repeated three times to activate the cellulose and remove water. The activated cellulose was collected by suction filtration then suspended in a 130.0 ml anhydrous DMAc two times, the first time was done for an hour, while the second time was carried out overnight. The activated cellulose was then collected by suction filtration and transferred to was added to a solution of LiCl in DMAc (8.0%, 150 mL) prepared by dissolving a 9.75 g of anhydrous LiCl in a 150 ml DMAc (2.697 mol) in a 500 ml round bottomed flask equipped with a magnetic stir bar and condenser, the flask was connected to a trap via the condenser and kept under nitrogen gas. The mixture was stirred at room temperature until a clear solution was obtained (about two hours). Then, a 33.5 ml of a t-butyl acetoacetate (t-BAA) (9.6 g, 61.5 mmol) was added dropwise to the solution under a blanket of nitrogen and heated to 120 ºC using oil bath in a 2 h period and stirred overnight. The reaction was transferred to a 1 L beaker, then 500 ml of distilled water was added dropwise to the reaction and then placed in the refrigerator overnight.

The resulted gel was filtered by suction filtration then transferred to a 1000 ml beaker containing 500 ml of methanol for washing. This step was repeated twice, the first stirring was done for 15 min, while the second one was carried out for 30 min. Product was collected by suction filtration and dried at 100 ºC, yield was about 86.7%.

Preparation of cellulose β-aniline ester (Cell-β-AN)

A 2.0 g sample of cell-AA polymer was suspending in a 100 ml methanol, then 2.0 ml (2.04 g, 21.9 mmol) of aniline was added in one portion, followed with a 2.0 ml (2.1 g, 34.96 mmol) of acetic acid, added at once as a catalyst. The mixture was refluxed for 8 h. The resulting polymer was filtered, washed with water (3 x 20 mL) and dried in an oven at 110 ºC.

Preparation of cellulose β-glycine ester (Cell-β-GL)

A 2.0 g of cell-AA polymer was suspended in acetic acid (40 ml), then 2.0 g (1.587 ml, 26.6 mmol) of glycine was added at once. Reflux was done for 6 h at 70 ºC. The resulting polymer was washed two times with water, diluted solution of sodium bicarbonate (1.0%), water and finally two times with methanol, and dried at 90 ºC.

Adsorption study

All experiments were performed in plastic vials (50 ml each) that were held in a shaker and placed in a water bath equipped with a thermostat. The effect of various variable such as metal ion concentration (C0), adsorption time, pH value, adsorbent dosage, and temperature on adsorption efficiency was evaluated. The adsorption study was performed on the Pb(II) metal ion. A sample of each mixture was withdrawn using a 5.0 ml plastic syringe, then filtered through a 0.45 µm syringe filter. The collected filtrate was analyzed by FAAS at 217.0 nm for determining the residual metal ion concentration and thus to determine the adsorption efficiency according to Eq. 1 and 2, respectively.

$$ R\,\left( {\text{\% }} \right)\, = \,\frac{{C_{o} - C_{e} }}{{C_{o} }}100 $$
$$ Q_{e} = \frac{{C_{o} - C_{e} }}{m}V $$

C0 and Ce are the initial and equilibrium concentration in ppm of metal ion in solution respectively, Qe (ppm) is the equilibrium adsorption capacity of the adsorbent (mg/g), m is the weight of the adsorbent (g), and V is the volume of the solution (L).

Wastewater purification

A sample of sewage water collected from the Beit Dajan wastewater purification planet (Nablus-Palestine) was used in this study. The sample was first analyzed by ICP-AES (Water Center, An-Najah National University, Nablus, Palestine) to determine the metals content and their concentrations. Then three 10 ml samples of the wastewater were placed in two Erlenmeyer flasks, a 100 mg of each cellulose-based polymer (Cell-AA, Cell-β-AN, Cell-β-GL) was added to each flask. The pH of the solution was adjusted to 8.0. The mixtures were shaken at room temperature for 30 min using a thermostat shaker. A 5.0 mL sample of each mixture was withdrawn and filtered through a 0.45 µm syringe filter and analyzed by ICP-AES for residual metal ions concentrations.

DFT calculations

DFT was performed using the Dmol3 software. Geometry optimization (spin unrestricted) using the double numerical plus polarization basis set (DNP) along with the PBE functional within the m-GGA approximation is used. Grimee DFT-D was used to provide dispersion correction effects. The COSMO method is used to include water as a solvent [34,35,36,37]. For the ELF—analysis, a single point geometry calculation (using geometry coordinates generated by the Dmol3 software in the previous step) was performed using the Orca software [38] at the density functional theory level with the M06 exchange-correlation functional and the def2-TZVP basis set [39]. The van der Waals interactions were accounted for by an atom-pair dispersion correction using the zero-damping scheme (D30) [40]. The adsorption energy is evaluated using the well-known method [41,42,43,44]. The non-covalent interaction (NCI) was calculated using Multiwfn software [45]. The NCI surface is plotted using software the Visual Molecular Dynamics [46].

Molecular Dynamic simulations were with the universal force field [47] to obtain detailed molecular details to elucidate the adsorption process of the between lead ions and the Cell-β-AN or Cell-β-GL surface. The adsorption is modelled using an 8 monomeric cellulose unit with a side chain modified by 8 GL or AN moiety, containing an upper layer composed of 400 water molecules and 3 Pb(II) ions. The MD is performed under NVT ensemble at 298.15 K, with 1 fs time step and a total simulation time of 2500 ps [37, 48,49,50,51,52,53,54,55,56,57]. A Nose thermostat is used for temperature control [58].

Result and discussion

Synthesis of cellulose-acetoacetate polymers (Cell-AA)

Cellulose functionalized with acetoacetate group was prepared according to a procedure reported in the literature with major modification [59]. Cellulose was dissolved in 8.0 wt% LiCl/DMAc solution at room temperature then reacted with tert-butyl β-ketoester at about 110 °C for 6 h (Fig. 1). The yield after product purification was about 86.7%.

Fig. 1
figure 1

Preparation of cellulose acetoacetate from Cellulose and t-BAA

The prepared Cell-AA was characterized by FT-IR, obtained spectrum is shown in Fig. 2. The most significant peaks for Cell-AA were observed at 1742 and 1709 cm-1 assigned to the carbonyls of ester and ketone, respectively. The IR spectrum also shows three bands at about 1152, 1057 and 1033 cm-1 corresponding to the vibration of C–O–C of ester, pyranose ring skeletal and to β-glycosidic linkage respectively. The broad peak at 3439 cm-1 attributed to the O-H bond stretching.

Fig. 2
figure 2

FT-IR spectrum for Cell-AA

Cell-AA was reacted with aniline, which undergoes a condensation reaction with the Ketone carbonyl to form Cell-β-AN functionality. The reaction is summarized in Fig 1. The FT-IR spectrum of the Schiff base Cell-β-AN (Fig. 3). The disappearance of the ketone domain at 1709 and the presence of an amine group C-N at about 1271 cm-1 is an indication that the amine linkage is formed. The peak at 3473 cm-1 is due to N-H vibration of the secondary amine groups. The peak at 1740 cm-1 could be attributed to C=O of the ester group. The broad peak at 3430 cm-1 could be attributed to the stretching of the hydrogen bonded hydroxyl group (O–H). The amine peak is not sharp, because it overlaps with the OH group peak which has almost the same wavenumber. The carbonyl of the ester group appears at 1740 cm-1, IR spectrum shows two bands at about 1157 and 1033 cm-1 of C–O–C ring of pyranose ring skeletal and to β-glycosidic linkage vibration, respectively. The adsorption peak at 2922 cm−1 is corresponding to symmetric and asymmetric stretching vibration of the C–H bond. The two peaks at about 3010 and 1582 cm-1 could be attributed to =C-H and C=C stretching vibrations in an aromatic part of Cell-β-AN as shown in Fig. 3.

Fig. 3
figure 3

FT-IR spectrum for Cell-β-AN

The cellulose β-glycinocetoester (Cell-β-GL) was produced from reacting cellulose acetoacetate with the amino acid glycine, acetic acid was used as a solvent and a catalyst as proposed in Fig. 4. The FT-IR spectrum of the Cell-β-GL is shown in Fig. 5. The broad strong peak at 1713 cm-1 composed of several overlapped peaks that could be attributed to C=O of ester and carboxyl groups. The broad peak at about 3300 cm-1 is attributed to the stretching hydrogen bonded hydroxyl group of alcohol and carboxyl.

Fig. 4
figure 4

Preparation of cellulose β-aminoacetonate using glycine

Fig. 5
figure 5

FT-IR spectrum for Cell-β-GL

The IR spectrum also shows three bands at about 1152, 1050 and 1030 cm-1 for C-O–C of ester, pyranose ring skeletal and to β-glycosidic linkage vibration respectively. The adsorption peak at 2963 cm−1 is corresponding to symmetric and asymmetric stretching vibration of the C-H bond.

The cellulose-based Schiff bases were designed to have a high affinity for various metals. As shown in Fig. 6, the coordination sites bi and tridentate ligand with binding sites contain amines, carbonyl and hydroxyl.

Fig. 6
figure 6

Representative structures show the interaction between Cell-β-GL and Cell-β-AN and the metal ion Pb(II)

SEM analysis

The SEM images of the two polymers Cell-β-GL and Cell-β-AN are shown in Fig. 7, the images show the surface morphology that appears as a spongy. This explains the high affinity of the polymers for the metal ions.

Fig. 7
figure 7

The SEM images of a Cell-β-AN and b Cell-β-GL at a magnification of 250x 500x, respectively

Polymer solubility in water

The solubilities of the three polymers in water was determined by suspending 0.5 g of each of the polymers in 50 ml water and stirring for about 6 h. Then collected by suction filtration, dried in an oven at 100 °C, and weighed. Negligible reduction in the weight was noticed.

TGA analysis and thermal stability

TGA was performed on the three polymers, results are shown in Fig. 8. All polymers show about the same trend, a major drop in the mass appears at 200 °C that could be related to the loss of the pendant group. Complete decomposition started at about 400 °C. The polymers are considered thermally stable since it synthesized mainly for wastewater purification.

Fig. 8
figure 8

TGA and DTG analysis results of A Cell-AA, B Cell-β-AN C Cell-β-GL polymers

Adsorption of Pb(II)

pH effect on adsorption

The effect of the pH value on adsorption efficiency for the three polymers was studied, the other parameters were kept constant (adsorbent dose 40.0 mg, time 30 min, solution volume 10 mL and temperature at 30 °C). The results are shown in Fig 9d. At low pH value (about 3.0) the amine presents in ammonium form (-NR2H2+), also the carboxyl and hydroxyl groups are in protonated form (COOH and OH), so the adsorption efficiency was low. As the pH value increased the amines, carbonyl and hydroxyl groups start to shift to the Lewis base form, causing the hydroxyl, carbonyl and amine to behave as a stronger chelating agent due to the availability of O and N lone pairs of electrons. The highest efficiency was observed at pH 9. At pH value higher than 9, the adsorption efficiency started to decline, this decrease could be related to formation of soluble metal oxide complex which reduced the adsorption efficiency of Pb(II) from the aqueous solution. So, the optimum pH value was selected to be 9.0.

Fig. 9
figure 9

The effect of a: adsorbent dose, b adsorption time, c temperature, d pH, and e initial ion concentration on the metal removal by the three adsorbents

Concentration effect on adsorption

The effect of the initial lead ions concentration on adsorption efficiency was also investigated, the other variables being kept constant (pH 4.3, time 30 min, solution volume 10 mL and temperature at 30 °C). The maximum percentage of lead ions removal was about 44.4% by cell-AA, 57.29% by Cell-β-AN and 63.7 % by Cell-β-GL at 10 ppm initial concentration of Pb(II) (Fig. 9e). At concentration higher than 10 ppm the rate of adsorption decreases with increasing the concentration of lead ions. The results show that, at a concentration of 10.0 ppm or lower, there are sufficient binding sites, and the adsorption process is controlled by ion diffusion [60]. As the concentration increases, the availability of the binding sites decreases until the binding site are almost saturated, and the adsorption process is controlled by the adsorbent dosage.

Contact time effect on adsorption

The effect of the contact time on %removal was evaluated under conditions of pH 4.3, initial ion concentration 10 ppm, volume of adsorbate 10 ml, adsorption temperature 30 °C and adsorbent dose 50.0 mg. Results are shown in Fig. 9b, the figure shows a sharp increase in the adsorption of Pb(II) after 30 min for all three polymers, which could have related to the availability of plenty of binding sites on the outer surface of the adsorbent. Then a slow increase was observed, the adsorption rate reached equilibrium after about 120 min, so at this period almost all adsorption sites are occupied [60]. A contact time of 30 min was chosen as an equilibrium time for the three polymers.

Temperature effect on adsorption

The effect of temperature on the adsorption rate of Pb(II) ions was studied under the conditions shown above at 15, 22, 30, 40 and 60 oC. The highest adsorption rate was found to be at 30 °C. At temperature higher than 30 °C, the percentage of removal tends to decrease as the temperature rises as shown in Fig. 9c. This result is an indication that the adsorption process is spontaneous at low temperature. At high temperature values, over 30 °C, the percentage of metal removal decrease could be related to the kinetic energy of the adsorbed particle on the adsorbent surface increase, which leads to an increase in the possibility of de-complexing from the adsorbent surface.

Adsorbent dose effect on adsorption

The effect of adsorbent dosage on %removal is summarized in Fig. 9a. The experiment was performed using various amounts of adsorbents ranging from 5.0 mg to 50.0 mg and 10 ml solutions of Pb(II) with a concentration of 10.0 ppm and a pH value of 4.3. The adsorption time was performed for 30 min at room temperature. The results show that the amount of metal extracted increased by increasing the polymer dosage. The highest removal of about 60.5% was achieved using a 40.0 mg of Cell-β-GL polymers.

Desorption studies

The regeneration experiment was repeated seven times using the same adsorbent to determine the efficiency of the polymers and the result are shown in Fig. 10. The adsorption efficiency decreases slightly as the number of regeneration cycles increases. In the seventh time, the Cell-AA, Cell-β-GL and Cell-β-AN polymers absorption of lead metals were 99%, 98.5% and 98.7% respectively.

Fig. 10
figure 10

Adsorption efficiency, effect of adsorbent recycling

Wastewater purification from metals

Samples of sewage water were taken from the Beit Dajan wastewater treatment plant in Palestine. Three samples of this water were prepared to be treated with the prepared polymers according to the optimum conditions. The concentrations of the metal ions in each of the sewage samples prior and after using the polymers are summarized in Table 1. Metal ions concentrations were measured using ICP-MS. Excellent efficiency was achieved against some metal ions present in the wastewater samples because polymers contain several coordination sites including hydroxyl, amine, and aromatics groups.

Table 1 Percent removal of metal ions present in sewer using the three adsorbents.


Adsorption analysis


Langmuir (Eq. 3) and Freundlich isotherm (Eq. 5) models were applied to investigate the adsorption equilibrium between Pb(II) ion solution and the three adsorbents [20]. Both models were used to assess the metal ion dispersion on the adsorbent surface at the equilibrium stage. The value of the correlation coefficients, R2 (Eq. 4) can lead to the type of isotherm model of the adsorption process. The RL ratio was defined as a dimensionless quantity indicating that sorption is favorable or not, since if the value of RL is higher than 1, this indicates that the adsorption is unfavorable. However, when the RL value is between 1 and 0, this indicates favorable adsorption, whereas when RL = 1 indicates the presence of linear adsorption [20].

$$ \frac{{C_{e} }}{{Q_{e} }} = \frac{1}{{q_{\max } }}\,C_{e} + \frac{1}{{q_{\max } K_{L} }} $$

Where Ce represents the equilibrium concentration of the adsorbate (mg/L), Qe is the amount of the adsorbate adsorbed per unit mass of cellulose-based polymers at equilibrium (mg/g), qmax is the adsorption capacity equilibrium (mg/g), and KL is usually, the Langmuir affinity constant (L/mg).

$$ R_{L} = \frac{1}{{1 + K_{{L C_{0} }} }} $$

Co is the initial adsorbate concentration.

$$ {\text{In}}\,\left( {q_{e} } \right) = {\text{In}}\,k_{F} + \frac{1}{n}{\text{In }}C_{e} $$

KF is the Freundlich constant that deals with adsorption capacity (mg/g) and n is the heterogeneity coefficient which leads to how favorable the adsorption process (g/L).

Figure 11 summarizes all adjustment parameters. The correlation coefficients of the Freundlich isotherm model is lower for Cell-AA while it is higher for Cell-β-AG and Cell-β-AN than those of the Langmuir isotherm model (Table 2), reflecting that the adsorption of Pb(II) ions obey the Freundlich isotherm model for Cell-β-AG and Cell-β-AN and Langmuir isothermal model for Cell-AA. The results indicate a single-layer adsorption behavior with a heterogeneous energy distribution of the active sites along with the interactions between adsorbent and adsorbate. However, in the case of Cell-AA polymer the Pb(II) cation are distributed equally and homogeneously across the porous surfaces of the cellulose based polymers [61].

Fig. 11
figure 11

A Langmuir adsorption model and B Freundlich adsorption model of Pb(II) ions on three adsorbents

Table 2 Langmuir and Freundlich parameters for the adsorption of Pb(II) ions by cellulose-based polymers

The separation factor RL, which has been calculated for different quantities of adsorbent, ranges from 0< RL<1 (Table 2). This reflects the high degree of affinity of the three adsorbents for the studied metal ions.

Adsorption kinetics

The kinetic of the adsorption of metal ion Pb(II) by the three adsorbents was evaluated using the kinetic models: pseudo-first order (Eq. 6) and pseudo-second order models (Eq. 7) [62]. Weber and Morris developed Eq. 8 describing the intraparticle diffusion [62].

$$ {\text{ ln}}(q_{e} - q_{t} ) = \ln q_{e} - {\text{K}}_{{1}} {\text{t}} $$
$$ \frac{1}{{{\text{q}}_{{\text{t}}} }} = \frac{1}{{{\text{K}}_{{2{\text{q}}_{e}^{2} }} }} + \frac{{\text{t}}}{{{\text{q}}_{e} }} $$
$$ {\text{Q}}_{{\text{t}}} = {\text{ K}}_{{{\text{id}}}} {\text{t}}^{{{1}/{2}}} + {\text{ Z}} $$

where Qt (mg g-1) is adsorption capacity at any time t, kid (mg/g min1/2) is the intraparticle diffusion rate constant, and Z (mg/g) is a constant proportional to the thickness of the boundary layer.

Table 3 and Fig. 12 summarize the values of all parameters obtained using the above equations. The plots of Ln (qe-qt) versus t (Fig. 12A) provide the value of K1, whereas the values of K2 and the adsorption capacity qe were derived from the slope and intercept of the plot of t/Qt versus t (Fig. 12B), while Kid and Z were deduced by tracing Qt vs t1/2 (Fig. 12C).

Table 3 The pseudo-second-order model for adsorption of Pb(II) ions onto cell-AA, cell-β-AN, and cell-β-AG
Fig. 12
figure 12

A Pseudo first-order model B Pseudo-second order model and C Intra-particle diffusion model for the adsorption of Pb(II) ions onto cell-AA, cell-β-AN, and cell-β-AG at various concentrations

The experimental results show that the correlation coefficient (R2) for the pseudo-second order kinetics model (0.91 to 0.973) was greater than the value obtained by pseudo-first order (0.891). Also, the qe values (2.675, 15.252, 20.856 mg/g) which are close to the experimental qe values (2.133, 13.91, 18.786 mg/g) for the three polymers Cell-AA, Cell-β-AG and Cell-β-AN, respectively, indicating that the adsorption process follows the pseudo-second order model for adsorption of Pb on the surfaces of the three polymers obey the pseudo-second order (Table 3 and Fig. 12B).

From (Fig. 12C) (Qt vs. t1/2) Kid and Z were calculated and reported in Table 3. All graphs plotted in Fig. 16 didn’t cross the origin, indicating the occurrence of more than one rate-limiting process.

Based on initial graphs linearity presented in Fig. 12B it can be conclude that, at the outset of the adsorption process, the adsorption of Pb(II) on the three polymers takes place initially by an instantaneous adsorption step (on the external surface), which caused a chemical complexation between the metal ions and functional groups, COOH, NR2 and the OH [21, 24, 63,64,65,66,67,68,69,70]. The other steps were also linear, showing a progressive adsorption of Pb(II) ions and the step of limiting intraparticle diffusion rate.

The results presented in Table 3 reveal that the Z values reflect an expansion in the upper layer of the adsorbent and a decrease in the outer mass transfer although the inner mass transfer potential was increasing. The energy of activation of the adsorption process was computed at 298 and 323 K according to Eq. 8.

These findings are important for understanding how temperature influences adsorption performance of three polymers. The activation energy computed was nearly zero, suggesting a spontaneous adsorption process.

Thermodynamics study

The thermodynamic parameters free energy, standard enthalpy, and standard entropy for adsorption of Pb(II) by the three polymers were calculated using the following equations [52]. The aim of this study is to understand the spontaneity and the nature of adsorption.

$$ {\text{K}}_{{\text{c}}} = {\text{ C}}_{{{\text{ads}}}} /{\text{C}}_{{\text{e}}} $$
$$ \Delta {\text{G}}^{0} = \, - {\text{RTlnK}}_{{\text{c}}} $$
$$ {\text{In}}\,K_{S} \frac{\Delta S}{R} - \frac{\Delta H}{{RT}} $$

where Kc is an apparent constant of the thermodynamics; and Cads and Ce are respectively the amount adsorbed at equilibrium (mg/L) and concentration of metal ion in the solution (mg/L), R is the universal gas constant (8.314 J/mol K); T is the solution temperature [54]. The (ΔG0) (J mol-1) value was determined according to Eq. 10. The ln Ks vs. 1/T was mapped as illustrated in Fig. 13, the slopes and crossings were utilized to determine various thermodynamics parameters as shown in Table 4.

Fig. 13
figure 13

Adsorption thermodynamics of Pb(II) ions onto cell-AA, cell-β-AN, and cell-β-AG

Table 4 Thermodynamic parameters for the adsorption of Pb(II) ions onto cell-AA, cell-β-AN, and cell-β-AG

The value obtained for ΔS0 and ΔH0 are positive, whereas the entropy raised at the solid/solution interface induced as a result of the adsorption process. The findings further indicate that, the free energies for the three polymers were negative reflecting a spontaneous process of adsorption at various temperatures.

The results indicate that the metal removal occurs at various stages. In the first stage, metal ions migrate from the solution to the outer surface of the adsorbent, then diffuse across the boundary-layer to the outer surface of the adsorbents, followed by coordination of metals ions at the binding sites on the adsorbent surface, and lastly, intra-particle diffusion and adsorption of ions across the adsorbent particles.

Monte Carlo and molecular dynamic simulations

Recognizing the adsorbate molecules' preferred adsorption arrangement on the Cell-β-AN or GL surface is crucial for determining the various energy outputs.

The interaction of the adsorbate ions Pb2+with the modified cellulose surface enables the calculation of this method's adsorption energetics. This is performed quantitatively by use the equation below to determine the adsorption energy (Eads) [71,72,73,74,75,76,77] :

$$ E_{{adsorption}} = \,E_{{Pb\left( {II} \right)/Cell - \beta - GLorAN}} - \left( {Cell - \beta - GLor{\mkern 1mu} AL + Pb\left( {II} \right)} \right) $$

where \({E}_{Pb(II)/Cell-\beta -GL orAL}\) is the total energy of the simulated adsorption system, \(Cell-\beta -GL orAN\) and \(Pb(II)\) is the total energy of the adsorbate ions.

Figure 14 shows the energy terms and the energy evolution during MC for the most sable or low energy adsorption sites of adsorbates in the vicinity of the modified cellulose surface obtained through an excessive number of randomly generated Monte Carlo calculations.

Fig. 14
figure 14

A Different energy terms during the exploration of random MC configurations (3 000 000) and B Probability of the adsorption energy distributions during MC for the adsorbate ions onto modified cellulose surface

The experimental findings are supported by a strikingly superior negative value of Eads of the adsorbate ions onto the both modified cellulose surface.

The method for measuring and imaging the dynamics of inhibitor adsorption on the materials surface is used in MD simulation. Fig. 15 shows the adsorbate ions final structure on the modified cellulose surfaces.

Fig. 15
figure 15

Lowest energy configurations of Pb Pb2+ ions onto the corresponding modified cellulose surfaces as obtained from MD

As can be seen in Fig. 16, where the adsorption energy of the lead ions is calculated over the course of the entire trajectory, the adsorption of the lead ions occurs spontaneously (as indicated by the relatively high adsorption energy values), and the results are consistent with those obtained experimentally [77, 78]. The mean of the adsorption energy is calculated after the system equilibration (last 2000 ps of the MD trajectory). The interaction is based mostly on the electrostatic one with a contribution through van der Waals forces.

Fig. 16
figure 16

The change of the adsorption energy (and corresponding energy terms) for the Pb2+ions onto the modified cellulose surfaces obtained during the MD

The relatively small changes of the adsorption energy (black line) energy as observed in Fig. 16, indicate that the system has reached the lowest energy.

To better understand this interaction DFT calculations involving a monomeric system of modified cellulose were performed.

The assessment of the interaction nature amid the Pb2+ions and the modified cellulose structures is performed via the NCI surface plot and the reduced density gradient (RDG) vs. sign (λ) (Fig. 17) [79, 80]. The greenish-blueish colored surface and the spikes with negative sign (λ) values in the 2D NCI plot support that the van der Waals interactions are presented in the formed structures.

Fig. 17
figure 17

Noncovalent interaction surfaces and the plot of RDG vs sign(λ)ρ for the van der Waals interactions among the Pb2+ions and the modified cellulose moieties

The ‘bonding’ interaction among the Pb(II) ions and the side groups of the modified cellulose is discernible via the ELF analysis, where the low values of ELF indicate the low degree of covalence of these formed bonds [79]. This "binding" is also evident when Mayer's binding order analysis is applied as shown in Fig. 18 and Table 5.

Fig. 18
figure 18

Electron localization function (ELF) analysis of the “bonding” between Pb2+ions and the side groups of the modified cellulose

Table 5 Mayer bond order for selected bonding atoms in the Pb2+/ modified cellulose structures.

The Mayer bond order ruptures the electron density in such a mode that the degree of bonding is calculated in a modest way, where a perfectly fulfilled double bond has a value of 2, a triple bond has a value of 3, and so on as shown in Table 5 [80]. The bond order values point to that the interaction of the Pb2+ions is moderately strong paralleled to other types of coordinative binding [81].


Cellulose used in this study was extracted from olive industry solid waste, it was successfully functionalized with the pendant group β-amino ester by first introducing 1,3-dicarbonyl to the cellulose repeat unit then reacting it with aniline and the amino acid glycine. The structures of the target polymers were identified by FT-IR spectroscopy and other techniques. The prepared three polymers showed excellent efficiency toward removal of toxic metal ions from wastewater. The optimum value of various parameters (contact time, pH value, adsorbent dose, temperature, and initial concentration of lead ion) that lead to highest adsorption efficiency were determined. The adsorption mechanism follows the Langmuir isotherm model. Kinetic data revealed that the adsorption of Pb(II) obeys the pseudo second order. Thermodynamic study showed negative Gibbs free energies, indicating a spontaneous adsorption process of Pb(II) by the three polymers. Theoretical calculation using Monte Carlo (MC) and Molecular Dynamic (MD) simulation models were conducted to confirm the experimental results of strong interaction and spontaneous adsorption between Pb(II) and the functional groups on the cellulose polymers. The polymers quantitatively removed metal ions present in a real sample of sewage and showed good desorption properties.

Data availability

Adequate and clear descriptions of the applied materials and tools are provided in the materials and method section of manuscript. In addition, the obtained data is clearly justified by mentioning the figures and tables in the manuscript.


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The authors would like to thank the Palestinian Water Authority and the Midle East Desalination Research Center (MEDRC) for the financial support of this work.


This research received some funding from Middle East Desalination Research Center (MEDRC) and Palestine Water Authority (PWA)” grant number MEDRC- 20-2022

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Nairat, N., Hamed, O., Berisha, A. et al. Cellulose polymers with β-amino ester pendant group: design, synthesis, molecular docking and application in adsorption of toxic metals from wastewater. BMC Chemistry 16, 43 (2022).

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  • Water treatment
  • Persistent pesticides
  • Difenoconazole
  • Cellulose nanocrystalline
  • 2-furan carbonyl chloride
  • Cellulose
  • Monte Carlo
  • Glycine
  • Molecular dynamic
  • Adsorption
  • Wastewater