SN Applied Sciences

, 1:1180 | Cite as

Chromium (VI) removal from neutral aqueous media using banana trunk fibers (BTF)-reinforced chitosan-based film, in comparison with BTF, chitosan, chitin and activated carbon

  • Muhammad RahimEmail author
  • Mas Rosemal Hakim Mas Haris
Research Article
Part of the following topical collections:
  1. Earth and Environmental Sciences: Membranes and Advanced Materials for Wastewater Treatment


Banana trunk fibers (BTF)‐reinforced chitosan (BTF-i-CTS) biocomposite film was prepared and characterized by means of Fourier‐transform infrared spectroscopy, thermogravimetric analysis and scanning electron microscopy. Characterization of the starting materials and the biocomposite indicated that BTF are widely immobilized in chitosan (CTS) by physical means. The water uptake results of BTF-i-CTS indicated a maximum water uptake of 338.23% with an equilibrium time of 72 h. The starting materials and BTF-i-CTS in comparison with chitin and activated carbon (AC) were used for the removal of Cr6+. The effect of pH, contact time and initial concentration was investigated. Contact time of 120 min and pH of ~ 7.00 were selected for the removal of Cr6+, at ambient temperature (27 ± 1 °C). The percentage removal of Cr6+ at pH ~ 7.00 and initial concentration of 50 mg/L using BTF-i-CTS, CTS, BTF, chitin and AC was observed 97.79, 97.78, 25.79, 36.80 and 23.78%, respectively. The data best-fitted pseudo-second-order kinetic and Freundlich isotherm model indicated that chemisorption is the likely factor for the removal of Cr6+.


Banana trunk fibers Chitosan Biocomposite Chromium (VI) Sorption 

1 Introduction

Industrial wastes are the main sources of surface and ground water contamination [1]. Aqueous wastes of metal plating, tanneries, smelting, batteries, mining operation, pesticide and fertilizer industries contain high level of heavy metal ions [2]. Heavy metal ions attracted the attention of researchers in view of their toxicity [3, 4], bioaccumulation, bio-magnification, persistence and non-biodegradability [5]. Several technologies have been used to remove metal ions from industrial aqueous wastes, and sorption is one of the widely practiced processes [6]. Therefore, the removal of metal ions to an optimum level by a cost‐effective and eco-friendly manner is of great interest [7].

Chitosan (CTS) is a linear polymer of β(1–4)‐linked N-acetyl-D-glucosamine and D-glucosamine units. It is the second most abundant naturally occurring polymer after cellulose [8]. CTS is the excellent chelating agent with several metal ions [9]. The synthetic derivatives of CTS have been investigated for the removal of several metal ions from aqueous medium. The literature survey indicated that CTS and its derivatives have been reported widely for the sorption of Cr(VI) [10, 11, 12, 13, 14, 15, 16]. However, derivatization of CTS requires equipments, chemicals and sometimes toxic by-products and the use of organic solvents discourage the technique. The literature study also indicates that inorganic sorbents and AC have been used extensively for the removal of various metal ions [17, 18, 19, 20, 21, 22, 23], but the removal of these sorbents from the sorption media is very difficult. Furthermore, the removal of these materials requires either filtration or centrifugation, which are time‐consuming and energy‐intensive processes. These materials block pores of the filter paper which needs vacuum filtration, leading to high cost, whereas CTS and BTF are the cost‐effective, eco-friendly and naturally abundant polymers having great potential toward sorption of several metal ions. Therefore, in this study, a green biocomposite film comprising of BTF‐reinforced CTS was prepared and successfully investigated for the removal of Cr6+ from neutral aqueous media.

2 Materials and methods

CTS with degree of N-deacetylation 95% and relative average molecular weight of 1.05 × 105 was supplied by Advanced Materials Research Centre, Kedah, Malaysia. 1000 ± 2 mg/L standard solutions of Cr6+ were purchased from Fluka, Switzerland. Water was freshly distilled prior to use.

2.1 Preparation of BTF‐reinforced CTS biocomposite film

CTS gel was prepared by adding 2.000 ± 0.005 g of CTS powder to 100 mL of 2% (v/v) acetic acid aqueous solution. The mixture was stirred using mechanical stirrer for 1 h. Then, 0.200 g of BTF was added and dispersed by means of a glass rod. The resulting slurry was transferred into a plastic-layered glass petri dish and dried in a convection oven at 60 °C for 48 h.

2.2 Activation of charcoal

Charcoal was placed in a muffle furnace, and the carbonization was carried out at 200 °C for 24 h. The carbonized material was ground to fine powder. The resulting material was placed in an air‐tight container for further studies [24].

2.3 Characterization

Brunauer–Emmett–Teller (BET) surface area and pore size of the materials were determined by a quantachrome NOVA-2200e instrument. The materials were degassed at 110 °C and exposed to constant cryogenic liquid nitrogen (− 197.3 °C) at a series of precisely controlled pressures. The gas adsorption isotherms were obtained by plotting the volume of gas (cm3/g) against P/Po (relative pressure). Surface area and the types of pores were predicted from the shape of the isotherms.

The FT-IR spectra of the starting materials (CTS and BTF) and BTF-i-CTS were obtained by PerkinElmer Spotlight-200 spectrophotometer. Attenuated total reflection (ATR) technique was used to scan the samples at room temperature (27 + 1 °C). The background spectrum was obtained before running the sample. The scanning resolution and the number of scans were adjusted 4 cm−1 and 16, respectively. The samples were scanned in the range of 650–4000 cm−1.

Thermal stability of the starting materials and biocomposite film was determined using PerkinElmer TGA–7 thermogravimetric analyzer. The samples were run under nitrogen atmosphere in the temperature range of 30–900 °C. The temperature was increased slowly with a heating rate of 10 °C/min. The thermograms were obtained by plotted weight loss (%) against temperature (°C).

The surface morphology of the biocomposite film was determined using Leo Supra 50Vp Field Emission Scanning Electron Microscope (FESEM). The biocomposite film was dried in oven at 60 °C for 24 h, coated onto gold foil and observed in the microscope under vacuum using Turbopump: Varian VT-300-HT.

2.4 Batch sorption experiments

2.4.1 Sorption kinetics

Cr6+ solution (50 mg/L) was prepared by dilution technique using standard solution of 1000 ± 2 mg/L. Batch sorption kinetics tests were conducted by mixing 0.200 ± 0.009 g of the sorbent with 50 mL of Cr6+ ion solutions (pH ~ 2.00, 4.00, 6.00 and 7.00) in an Erlenmeyer flask. The flasks were agitated using orbital shaker (KS 130 Basic) with a speed of 300 rpm. The pH was adjusted using either 0.1 M solution of NaOH or HCl. After predetermined time intervals, the solution was pipette out and concentration was determined using atomic absorption spectrometer (PerkinElmer AAnalyst 400). The experiments were conducted in triplicate at 27 ± 1 °C. For the comparison, CTS, BTF, chitin and AC were also investigated for the removal of Cr6+ at the same conditions. The percentage removal and sorption capacity (mg/g) were determined using the following Eqs. 1 and 2, respectively [25].
$$\% \;{\text{removal}} = \frac{{C_{0} - C_{\text{t}} }}{{C_{0} }} \times 100$$
$${\text{Sorption}}\;{\text{Capacity}} = \frac{{(C_{0} - C_{\text{e}} )}}{M} \times V$$
where C0 is the initial concentration (mg/L), Ct is the concentration (mg/L) in the solution at time ‘t’ and Ce is the concentration (mg/L) at equilibrium. V is the volume of solution in liter, and M is the mass of adsorbent in grams.
Pseudo-first- and second-order kinetic models were applied to find out the possible kinetic of the adsorption process, as shown in Eqs. 3 and 4, respectively [26].
$$\log (q_{\text{e}} - q_{\text{t}} ) = \log q_{\text{e}} - \left( {\frac{{k_{1} }}{2.303}} \right)t$$
$$\frac{t}{{q_{\text{t}} }} = \frac{1}{{k_{2} q_{\text{e}}^{2} }} + \left( {\frac{1}{{q_{\text{e}} }}} \right)t$$
where qe and qt are the concentrations of metal ions at equilibrium and time ‘t’, respectively.

2.4.2 Adsorption isotherm

In order to find out the possible sorption isotherm, Cr6+ solutions (1, 5, 10, 20 and 50 mg/L) were prepared and the pH was adjusted ~ 7.00. Batch isotherm experiments were conducted by mixing 0.2 g of either biocomposite film, CTS, BTF, chitin or AC with different concentration solutions (1–50 mg/L). The mixture was agitated, and the supernatant was analyzed for the residual metal ion concentrations. Freundlich and Langmuir isotherm models were applied to the experimental data to find out the sorption isotherm, as shown in Eqs. 5 and 6, respectively [27].
$$\frac{{C_{\text{e}} }}{{q_{\text{e}} }} = \frac{{C_{\text{e}} }}{{q_{\text{m}} }} + \frac{1}{{q_{\text{m}} b}}$$
$$q_{\text{e}} = k_{\text{F}} C_{\text{e}}^{{\frac{1}{n}}}$$
where qe (mg/g) and Ce (mg/L) are the amounts of adsorbed metal ions and remaining concentration, respectively. qm is the maximum amount of the metal ion sorbed, and b is a constant related to the affinity of the binding sites (L/mg). kF and n are the Freundlich constants, which indicate adsorption capacity and intensity, respectively.

2.4.3 Point of zero charge (PZC)

Point of zero charge (PZC) was determined using solid addition method [28]. The initial pH (pHi) of the solutions was adjusted between 2 and 10 by adding either 0.5 M HCl or NaOH. pHi of the solutions were accurately noted, and 0.1 g of the sorbent was added to the series of different pHi solutions. The solutions were kept for 24 h. Then, final pH (pHf) was determined. The difference between pHi and pHf was calculated. The difference was plotted against pH, and the required PZC was obtained [29].

3 Results and discussion

3.1 FT-IR analysis

The FT-IR spectra of CTS, BTF and biocomposite film are shown in Fig. 1. The spectra are assigned as reported in the literature [30, 31]. The spectrum of biocomposite film (curves b) showed that there is no alteration of bands, and neither appearance of new bands nor disappearance of the existing bands. These results indicated that BTF are not grafted but widely immobilized within CTS by physical means which was further supported by TGA analysis.
Fig. 1

FT-IR spectra of: CTS (a), BTF-i-CTS (b) and BTF(c)

3.2 Thermal stability analysis

The thermogravimetric (TG) and derivative thermogravimetric (DTG) thermograms of starting materials and biocomposite film are shown in Fig. 2. CTS indicated two-step decomposition process. The first‐step decomposition in the temperature of 40–115 °C indicated the liberation of volatile compounds and absorbed water molecules. The second‐step rapid decomposition with a weight loss of 58.1% occurred in the temperature range of 257–465 °C. The second‐step thermal decomposition indicated cleavage and chain scission of C–C and C–O bonds of the CTS monomer units [32]. The DTG thermogram of CTS indicated 309.26 °C as the main decomposition temperature. TGA thermograms of BTF indicated a fast decomposition of 74% in the temperature range of 247–396 °C. The thermal decomposition of BTF is most likely due to the decomposition of hemicellulosics in an inert atmosphere [33]. The DTG thermogram of BTF indicates two main decomposition temperatures (54.37 and 360.90 °C). The first peak might be due to moisture, whereas the second peak is most probably due to cellulose and lignin decomposition. The thermal decomposition of biocomposite film indicated two peaks. The first major peak is due to the thermal decomposition of CTS, while the second minor peak is attributed to BTF. These results indicated that BTF have been widely immobilized within CTS by physical means.
Fig. 2

TG and DTG thermograms of CTS, BTF and BTF-i-CTS

3.3 Surface morphology

Scanning electron microscopy was used to investigate the surface of biocomposite film. The SEM images of the biocomposite film are shown in Fig. 3. The images showed almost smoother surface of the biocomposite film indicated well dispersion followed by entrapment of BTF within CTS.
Fig. 3

SEM images of BTF-i-CTS biocomposites

3.4 Cr6+ sorption studies

3.4.1 Effect of pH and contact time

The pH of solution has significant impact on the uptake of metal ions, and therefore, the effect of pH on adsorption of Cr6+ ion was studied. Initial metal ion concentration and sorbent dose were chosen 50 mg/L and 0.2 g, respectively. The pH was adjusted from 2 to 7. However, in acidic pH, Cr6+ converts to Cr3+ [34]. The effect of pH and contact time on the percent removal of Cr6+ onto the biocomposite at a temperature of 27 ± 1 °C is shown in Fig. 4.
Fig. 4

Effect of pH and contact time on percent removal of Cr6+ onto biocomposite

The point of zero charge for CTS, chitin, BTF, BTF-i-CTS and AC was found to be 3.9, 4.1, 4.6, 4.2 and 5.3, respectively, as shown in Fig. 5. At this point, surface of the sorbent has net zero charge and the sorbent surface shows amphoteric properties at this point. As such, the surface of the sorbent has a net negative surface charge at pH > PZC, whereas it has a net positive surface charge, if pH < PZC [35]. PZC provides useful information on the ability of sorbent surface to adsorb metal ions [36]. As such, the “Effect of pH” results indicated that the sorption capacities of the materials are higher in pH above 4.0, while Cr6+ converts to Cr3+ in acidic pH [34]. Therefore, pH ~ 7.00 was chosen as the optimum pH for the rest of the experiments, whereas the pH was monitored during experimental work. As such, the pH change was observed to a maximum of ± 0.7, which has no effect on the oxidation state of Cr.
Fig. 5

Point of zero charge (PZC) of CTS, chitin, BTF, BTF-i-CTS and AC

The literature survey indicates that the adsorption of metal ions is greater at low pH and decreases with an increase in pH [14]. In case of the present study, the biocomposite has two main active groups such as hydroxyl (–OH) and amino groups (–NH2). At lower pH, the biocomposite is positively charged due to the protonation of hydroxyl and amino groups, while the metal ions exist as anions. Similarly, the results show that percent removal of Cr6+ increases with as increase in pH, while the minimum adsorption was observed at lower pH conditions. This might be due to the presence of higher concentration, and greater mobility of H+ ions favored adsorption compared to the metal ions. The lower adsorption at low pH either might be due to high solubility and ionization of metal ions in the acidic medium. The increase in pH may cause a significant increase in the negatively charged surface area which facilitates the removal of metal ion. However, at low pH, due to higher concentration of hydrogen ions, a resistance creates to the complexation between metal ion and active sites of the polymer. As such, an increase in pH leads to lower sorption. Therefore, pH ~ 7.00 was selected for further experimental studies.

The removal of Cr6+ was studied as a function of contact time in the range of 0–720 min. A faster adsorption was observed in the beginning followed by slow absorption pattern. The absorption equilibrium was found to be 120 min. The initial faster absorption might be due to the fact that in the beginning, all the active sites on the surface of the sorbent were vacant; however, with an increase in contact time, the number of vacant sites decreases which results in the decrease in further sorption. Based on these results, 120 min was chosen as the optimum time for the rest of studies.

3.4.2 Effect of initial concentration

The percent removal of Cr6+ from various initial concentrations (1–50 mg/L) by the biocomposite, CTS, BTF, chitin and AC at pH ~ 7.00 and contact time of 120 min is shown in Fig. 6. The percentage removal of Cr6+ by the biocomposite, CTS, BTF, chitin and AC was found 74.60, 68.63, 14.40, 12.13 and 1.65% for the initial concentration of 1 mg/L while the initial concentration of 50 mg/L indicates percent removal of 97.79, 97.88, 25.79, 36.80 and 23.78%, respectively. As initial concentration provides an important driving force to outweigh all mass transfer resistance of metal ions between the aqueous and solid phases, an increase in initial concentration results in increased percent removal. This might be due to reduced resistance to mass transfer at higher metal ions concentration (1–50 mg/L).
Fig. 6

Effect of initial concentration on the percent removal of Cr6+

3.4.3 Sorption capacity

The sorption capacities of the biocomposite, CTS, BTF and AC were determined at an initial concentration of 50 mg/L. The sorption capacities of the biocomposite, CTS, BTF, chitin and AC toward Cr6+ at equilibrium time were found 12.70, 12.22, 3.10, 5.43 and 6.43 mg/g, respectively, as shown in Fig. 7. Interestingly, the results clearly indicated that the sorption capacity of the biocomposite for Cr6+ is 1.87 times higher than AC, and this might be due to CTS is a good chelating agent for metal ions. Functional groups are the binding sites for the sorption of charged particles. In general, the increased in the surface area can significantly exposes the functional groups resulting in the increased sorption capacity. Similarly, a good matching between the sorbent pore size and ion dimensions is critical for an optimal sorption process [37]. The surface area and pore size of the materials are shown in Table 1. The results show that the surface area of the AC is very greater (on average 100 times) than CTS, chitin, BTF and BTF-i-CTS, but the sorption capacity of the CTS and BTF-i-CTS is greater than that of AC. This might be due to the chemical interaction between the –NH2 group of CTS with the metal ions. As such, CTS by itself is brittle and difficult to collect back, either the medium should be filtered or centrifuged, whereas the biocomposite is comparatively more resilient and can be removed very easily after completion of the adsorption process. The tensile strength results of the biocomposite and CTS indicate that the tensile strength of the biocomposite is improved 111%. The tensile strength curves of CTS film and the biocomposite are shown in Fig. 8.
Fig. 7

Sorption capacity of the biocomposite, CTS, BTF and AC towards Cr6+

Table 1

Surface area and pore size of CTS, chitin, BTF, BTF-i-CTS and AC


Surface area (BET) (m2/g)

Single point (m2/g)

Pore size (cm3/g)





















Fig. 8

Tensile strength curves of CTS (a) and biocomposite (b)

3.4.4 Adsorption kinetics

Pseudo-first- and pseudo-second-order kinetics were applied (initial concentration of 50 mg/L) to obtain the rate constants. The pseudo-first-order kinetic Log(qe − qt) was plotted against t, and a straight line with slope (K1/2.303) and intercept [Log(qe)] were obtained. However, the intercept should be equal to the equilibrium uptake of metal ions, if not then the reaction is not likely to be the first order even if correlation coefficient (r2) has a value of unity [38]. As such, kinetic should be pseudo-second order, if the plot of t/qe versus t gives a straight line with high linearity [38]. Therefore, the results clearly show that the data best fit the pseudo-second-order kinetic instead of pseudo-first-order kinetic. The straight line plots of pseudo-second-order kinetic for Cr6+ having r2 of 1, 1, 0.997, 0.998 and 0.998, respectively, for biocomposite, CTS, BTF, chitin and AC are shown in Fig. 9. The constants of pseudo-first order and pseudo-second order for Cr6+ onto biocomposite, CTS, BTF, chitin and AC are summarized in Table 2. For better understanding, the data were then subjected to analyze by Langmuir and Freundlich isotherm models.
Fig. 9

Pseudo-second-order plots of Cr6+ metal ion

Table 2

Adsorption kinetic constants of Cr6+


Pseudo-first-order kinetics

Pseudo-second-order kinetics

r 2

q e a

q e b

K 1

r 2

q e a

q e b

K 2














































aAdsorption capacity theoretical (mg/g)

bAdsorption capacity experimental (mg/g)

The results suggest that the adsorption of Cr6+ onto biocomposite, CTS, BTF and/or AC follows pseudo-second-order model, based on the assumption that the rate-limiting step may be chemical sorption or chemisorption involving exchange or sharing of electrons between sorbate and sorbent [39]. As CTS and BTF have two reactive functional groups (–NH2 and –OH), in acidic medium these groups are responsible for the electrostatic attraction of metal ions and some of these sites are also responsible for intra- and/or intermolecular hydrogen bonding. In conclusion, the hydroxyl and amino groups might be involved in the process of chelation with Cr6+ metal ions.

3.4.5 Adsorption isotherms

Langmuir and Freundlich isotherm models were used to determine the adsorption mechanism and to quantify metal ions removal capacity of the biocomposite, CTS, BTF and AC toward Cr6+. The adsorption isotherm experiments were carried out with different initial concentrations (1–50 mg/L) of Cr6+ at 27 ± 1 °C while maintaining the sorbent dosage at a constant level.

The assumption of Langmuir isotherm model is based on the maximum adsorption corresponds to a saturated monolayer of adsorbate on the adsorbent surface. The Langmuir isotherm model was applied to the experimental data; however, the results indicated that Langmuir model is not a good fit for the adsorption process of Cr6+ onto biocomposite, CTS, chitin, BTF and AC. Therefore, Freundlich model was applied to the experimental data to get a best-fit model.

The experimental data of Cr6+ were analyzed by Freundlich isotherm model, and the results are summarized in Table 3. The linear plots of Log(qe) against Log(Ce) give straight lines with a slope of 1/n and an intercept of Log(Kf). The constant Kf indicates the adsorption capacity (mg/g) while 1/n is a function of the strength of adsorption in the adsorption process. If the value of n is unity, then the partition between the two phases is independent of their concentration. As such, the value of 1/n below unity indicates normal adsorption, while the value of 1/n above one indicates cooperative adsorption [40]. The linear plots of Freundlich model is shown in Fig. 10. The data best fit the Freundlich model with n values below unity and 1/n values above one for biocomposite, CTS, chitin, BTF and AC indicates that the adsorption process is a cooperative adsorption.
Table 3

Constants of Freundlich model


Chromium (VI)

R 2



K f


























Fig. 10

Freundlich isotherm models for Cr6+ metal ion

4 Conclusions

A green biocomposite consists of BTF immobilized in CTS was prepared. The biocomposite was characterized by means of FT-IR, TGA and SEM. It was found that BTF are immobilized within CTS matrix by means of physical interaction. The water uptake results indicate that the uptake is quite faster, might be due to entrapped BTF, and creates a network which serves as a route for water penetration. The biocomposite was used for the successful removal of Cr6+. The percent removal of Cr6+ onto the biocomposite was found 97.67%. It can be seen that the biocomposite indicated higher affinity toward the removal of Cr6+. This higher removal efficiency of the biocomposite toward Cr6+ might be due to complexation of Cr6+ with amine group of CTS. Chitin was used for the removal of Cr6+ to confirm the complexation of amine group which indicated, and the percent removal was observed 37.65%. The results of percent removal of chitin indicate that due to lower percentage of the amine group (as compared to CTS) leading to lower removal of Cr6+. However, the interesting thing is: the biocomposite has higher sorption capacity from pH ~ 6 to pH ~ 7 which can help to remove metal ions from industrial aqueous wastes.

CTS by itself indicated higher affinity toward the removal of Cr6+ (97.98%). Unfortunately, CTS is very brittle, leaches and difficult to collect back after the sorption process. The literature study reveals that AC is a very commonly used sorbent for metal ions, and therefore, AC was tested for the removal of Cr6+ at pH ~ 7, and the percent removal of Cr6+ was found 23.78%. The percent removal of Cr6+ at pH ~ 7.00 using biocomposite, CTS, BTF, chitin and AC was observed 97.79, 97.88, 25.79, 36.80 and 23.78%, respectively. In conclusion, the removal of CTS and AC from a system is very difficult needs either filtration or centrifugation and sometimes AC blocks pores of the filter paper which requires vacuum filtration leading to high cost and time consumption, while the removal of the biocomposite is an easy and time-saving process. Therefore, the biocomposite is strongly recommended for the removal of Cr6+ from the industrial aqueous wastes.



The authors would like to acknowledge Universiti Sains Malaysia (USM) for providing financial support (Grant No. 1001/PKIMIA/814124). The author (M. Rahim) is also thankful to USM and The World Academy of Sciences (TWAS) for supporting his study.

Compliance with ethical standards

Conflict of interest

The authors declare that they have no conflict of interest.


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© Springer Nature Switzerland AG 2019

Authors and Affiliations

  1. 1.School of Chemical SciencesUniversiti Sains MalaysiaMindenMalaysia

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