Experimentally measured parameters of PAAm-MWCNT composites for various temperature and wt% MWCNT contents during drying and swelling processes, respectively.
\r\n\tThe emergence of novel prion strains in animals, which include the only evidenced zoonotic prion C-BSE causing vCJD in humans, has created an important public health concern. Currently, new threats to human and animals may develop because of the plausible zoonotic properties of scrapie, L-BSE and the recently emerging chronic wasting disease in Europe.
\r\n\tThis book will gather experts in prion diseases and present new scientific advances in the field and relations with other amyloid neuropathologies.
Polymer-carbon nanotube (CNT), discovered by Iijima [1], composites were studied by Ajayan firstly. Carbon nanotubes and their composites have many application areas such as batteries, flat panel screens, sensors, and nanoprobes [2]. When comparing with different materials, nanotubes are stronger and more conductive than others. Therefore, there are many studies on polymer-CNT composites at last decade [3]. Nanotubes can be described as long and slender fullerenes, in which the walls of the tubes are hexagonal carbon (graphite structure). These tubes can either be single-walled carbon nanotube (SWCNT) or multiwalled carbon nanotube (MWCNT).
\nN-vinylcarbazole (NVC) was polymerized in bulk or in toluene in the presence of MWCNT without any extraneous catalyst [4]. A composite of PNVC with MWCNT isolated from the polymerization system showed high dc conductivity varying from 1.3 to 33 S cm−1 depending upon the extent of MWCNT loading in the composite. In situ polymerization and photo-physical properties of poly(p-phenylene benzobisoxazole) (PBO)/MWCNT composites were performed by optical techniques such as UV-Vis absorption, photoluminescence [5]. The investigation of UV-Vis absorption and fluorescence emission spectra exhibited that in situ PBO-MWCNT composite had a stronger absorbance and obvious trend of red-shift compared with blend PBO/MWCNT composites for all compositions. The characterization of poly(3-octylthiophene) (P3OT)/polystyrene (PS)-MWCNT polymer hybrid system performed by Fourier transform infrared spectroscopy, ultraviolet (UV)-visible absorption, and electrical measurements shows significant effects [6]. This study presents that the incorporation of 5 wt% functionalized MWCNT onto P3OT/PS polymer hybrid blend will convert this material from insulator to conductor. Modulation of single-walled carbon nanotubes photoluminescence by hydrogel swelling demonstrated that the shift of nanotubes photoluminescence occurred in a hydrogel matrix. As the hydrogel cross-linking density and hydration state is changed, the nanotubes experience lattice deformations and a shift in photoluminescence emission maxima [7]. CNTs were added into poly(vinyl alcohol) (PVA) hydrogels to modify their mechanical properties. Freezing/thawing method was used for preparing the hydrogels. The tensile modulus, tensile strength, and strain at break of CNTP-0.5 specimen with 0.5% (w/w) CNTs are increased by 78.2, 94.3, and 12.7%, respectively, [8]. Dual stimuli responsive poly(N,N-diethylacrylamide-co-acrylic acid) composite hydrogels functionalized with MWCNTs were obtained. Swelling, deswelling, compression properties of the composites were greatly improved [9]. The relaxation process of the composites was modeled by Fickian diffusion mechanism.
\nSynthesis, electrical, and mechanical properties of polyethylene oxide (PEO)-MWCNT composites were investigated [10]. The conductivity measurements on the PEO-MWCNT composite films with the highest concentration of MWCNT (50 wt%) showed an increase of eight orders 6.52 S cm−1 of magnitude in conductivity from bare PEO film. The elastic modulus and tensile strength of a PEO-MWCNT film were increased by about fivefold and tenfold, respectively, as compared to the corresponding values for a PEO film.
\nPolyvinyl alcohol (PVA)-vapor growth carbon fiber (VGCF) and PVA-MWCNT were prepared by gelation/crystallization [11]. The percolation threshold of electrical conductivity for the PVA/MWCNT was <1 wt% MWCNT loading which was much lower than that of PVA/VGCFs composites. The mechanical properties of the PVA composite films were significantly by adding VGCFs and MWCNTs. Poly(ethylene terephthalate)(PET)-MWCNT nanocomposites were prepared by coagulation method [12]. The percolation threshold 0.6 wt% for rheological property and 0.9 wt% for electrical conductivity has been found. The less rheological percolation threshold than electrical percolation threshold is mainly attributed to the fact that a denser MWCNT network is required for electrical conductivity, while a less dense MWCNT network sufficiently impedes PET chain mobility related to the rheological percolation threshold.
\nThe electrical and rheological characteristics of poly(vinyl acetate) (PVAc)/multiwall carbon nanotube nanocomposites were investigated [13]. Small amount of MWCNT was observed to remarkably decrease resistivity of the nanocomposites. The G′ and G″ increase with the addition of MWCNT loading compared with that of the PVAc matrix.
\nThe rheological and conductivity threshold of semicrystalline syndiotactic polystyrene (sPS) composites filled with CNTs and carbon nanocapcules (CNCs) were determined dynamic rheological tests of samples in the melt state and from electrical tests in the solid state, respectively [14]. The sPS composites filled with CNT with a higher aspect ratio exhibited a lower threshold than the CNC filled ones in both rheological and conductivity percolation. The electrical and rheological properties of polypropylene (PP)-CNT composites were studied [15]. Thus, the conductivity of the composites was increased with CNT content and the content percolation threshold is between 1 and 2 wt% MWCNTs.
\nPoly(N-isoproplacrylamide) (PNIPAAm) containing single-walled carbons and single-walled nanohorns showed phase transitions [16]. Preparation and characterization of PAAm/MWCNTs monohybrid hydrogels with microporous structures were presented by mechanical, pH, and temperature sensitive response and swelling kinetics [17]. The addition of nanotubes produced interesting properties, including tailor ability of temperature responsive swelling and mechanical strength of the PNIPAAm-MWCNT composites. Polystyrene (PS)-MWCNT composites have been widely studied and published in the literature. The results of Yu et al. [18] yield an increment in conductivities of such composites which were produced by latex technology. Poly(vinyl acetate) (PVAc) is a non-crystalline, amorphous thermoplastic polymer. The PVAc is generally fabricated via mixing process with certain polymeric materials in order to reinforce the structural properties [19, 20]. PVAc-based composites are widely used in adhesive, paper, emulsifier, paint, and textile industries due to its high-bond reinforced, film-like, nonflammable, and odorless characteristics [20].
\nIn this chapter, after the introduction section, optical properties of various polymer-CNTs composite will be given and then mechanical properties of them which doped by MWCNTs will be provided. In the later section, electrical properties of them will be discussed.
\nPolyacrylamide (PAAm)-MWCNT composite gels were prepared by free radical cross-linking copolymerization [21]. PAAm was doped with various (0.1–15 wt%) of MWCNTs. Before drying was started [22], composites were cut into discs with 10 mm in diameter and 4 mm in thickness from the injector. Disc-shaped gel samples were placed on the wall of a 1 cm path length, square quartz cell filled with air and water for drying and swelling experiments, respectively.
\nDrying [22] and swelling [23, 24] process were performed by a Model LS-50 spectrometer of PerkinElmer, equipped with temperature controller. All measurements were made at 90° position, and spectral bandwidths were kept at 5 nm. Pyranine as a fluorescence probe in the composite gels was excited at 340 nm during
Emission spectra of pyranine from composites during drying in air, for 0.3 and 3 wt% MWCNT content gels at 60°C and in 135 min [
Figure 1 shows the emission spectra of pyranine from PAAm-MWCNT composite gel with 0.3 and 3 wt% MWCNT contents during drying in air at 60°C and in 135 min. It can be seen that as the MWCNT content is increased, fluorescence intensity, Iem, decreases relative to the scattered light intensity, Isc. Since the decrease in Isc corresponds to the decrease in turbidity of the drying gel [25], the corrected fluorescence intensity, I, was introduced as Iem/Isc to eliminate the turbidity effect. As far as the correction of fluorescence emission is concern, totally empirical formula was introduced to produce the meaningful results for the fluorescence quenching mechanisms. In order to quantify these results, a collisional type of quenching mechanism may be proposed for the fluorescence intensity, I, from the gel samples during the drying process using Eq. (1) [26].
\nτ0 (=5 ns) is known for pyranine [26] so W can be calculated using Eq. (1) and the measured I values, in each drying step.
\nThe plots of the water release,
Figure 2 presents the WI versus drying time. The plots of W versus t1/2 for 0.3 and 3 wt% MWCNT content sample at 60°C are presented in Figure 2, where the fit of the data to Eq. (2) produced the desorption coefficients, DdI which are plotted in Figure 3.
\nDesorption diffusion coefficients,
Fluorescence technique measures the DdI values at a molecular level. The desorption coefficients, DdI, were obtained from Eq. (2) and measured by fluorescence technique for various MWCNT content samples, where it was observed that the desorption coefficient decreased as the MWCNT content is increased up to 1 wt% MWCNT and reached to a plateau by presenting the different behaviors below and above the critical MWCNT (1 wt%) content at which the conducting percolation cluster starts to appear [21].
\nMonitoring of swelling experiments shows that emission light intensity, Iem, was decreased which is modeled by the Stern-Volmer equation. The Li-Tanaka equation was used to determine the swelling time constants, τS, and cooperative diffusion coefficients, DSI, from fluorescence intensity (Table 1).
\nFigure 4 presents the fluorescence spectra of pyranine from the PAAm-MWCNT composite during the swelling process in pure water at 60°C for 1 and 10 wt% MWCNT at 80 min, respectively. When the water uptake is increased, the emission light intensity, Iem, was decreased and the scattered light intensity, Isc, was increased, respectively, because of the quenching of excited pyranines and turbidity.
\nFluorescence spectra of pyranine from the composite during the swelling process at 60°C for 1 and 10 wt% MWCNT content samples at 80 min [
To produce the meaningful results for the fluorescence quenching mechanisms, empirical equation was introduced [27–29]. The corrected fluorescence intensity, I, is produced by dividing emission light intensity, Iem, to scattering intensity, Isc, to exclude the effect of turbidity. On the other hand, when quenching of excited pyranines increased, the swelling time, t, increased. This behavior of the composites was modeled by Stern-Volmer Model have been proposed using Eq. (2) [26].
\n\n | \n | DdI × 10−9 (m2/s) | \nτS (min) | \nDSI × 10−9 (m2/s) | \n
---|---|---|---|---|
30 | \n14.10 | \n85 | \n0.95 | \n|
40 | \n15 | \n48.5 | \n4 | \n|
50 | \n26 | \n37.7 | \n7.1 | \n|
60 | \n48.67 | \n25 | \n7.3 | \n|
30 | \n2.46 | \n58.82 | \n0.6 | \n|
40 | \n4.53 | \n55 | \n1.25 | \n|
50 | \n8.56 | \n35.71 | \n1.73 | \n|
60 | \n9.15 | \n26.31 | \n1.82 | \n|
30 | \n2.30 | \n55 | \n0.65 | \n|
40 | \n3.17 | \n50 | \n1.7 | \n|
50 | \n6.08 | \n33.33 | \n1.9 | \n|
60 | \n7.37 | \n25.64 | \n2.5 | \n|
30 | \n2.29 | \n48 | \n1 | \n|
40 | \n2.57 | \n47.61 | \n2.07 | \n|
50 | \n4.70 | \n32.25 | \n2.44 | \n|
60 | \n5.28 | \n22.72 | \n2.95 | \n|
30 | \n2.30 | \n96 | \n0.4 | \n|
40 | \n6.23 | \n95.23 | \n0.44 | \n|
50 | \n8.39 | \n90.9 | \n0.68 | \n|
60 | \n10.2 | \n83.33 | \n0.76 | \n|
30 | \n2.35 | \n98 | \n0.38 | \n|
40 | \n8.65 | \n97 | \n0.39 | \n|
50 | \n12.1 | \n95.23 | \n0.59 | \n|
60 | \n12.7 | \n89 | \n0.62 | \n|
30 | \n2.46 | \n100 | \n0.36 | \n|
40 | \n9.88 | \n98 | \n0.37 | \n|
50 | \n14.3 | \n95 | \n0.55 | \n|
60 | \n14.2 | \n91 | \n0.6 | \n|
30 | \n4 | \n120 | \n0.32 | \n|
40 | \n10.4 | \n111.11 | \n0.35 | \n|
50 | \n16.4 | \n105.26 | \n0.44 | \n|
\n | 60 | \n17.6 | \n103.09 | \n0.46 | \n
Experimentally measured parameters of PAAm-MWCNT composites for various temperature and wt% MWCNT contents during drying and swelling processes, respectively.
The plots of fluorescence data using Eq. (
Plots of water uptake, W, versus swelling time are presented in Figure 5 for 0.6 and 10 wt% MWCNT content samples at 60°C, respectively. These are typical solvent uptake curves, obeying the Li-Tanaka equation is Eq. (3) [27–29].
\nThe logarithmic form of the data was fitted to the following relation produced from Eq. (3)
\nwhere τS is the time constant which was calculated from linear regression of the curves in Figure 5 and Eq. (4) described by Li and Tanaka [28].
\nUsing Eq. (5), cooperative diffusion coefficients DSI were determined for these disc-shaped composites and found to be around 10−9 m2/s. All DSI values first increased up to 1 wt% MWCNT content and reached its highest value at this critical point, where the percolation cluster from MWCNT starts to form as given in Figure 6 and Table 1.
\nCooperative diffusion coefficient,
The percolation cluster formed from CNTs helps water molecules flow faster in their channels and causes the composite gel swell faster presenting large DSI values for all samples under consideration. However, above the critical point (1 wt% MWCNT), composite gel is quite stiff due to the formation of infinite network from MWCNT. The formation of inelastic composite gel above the critical point then lowers the DSI values to the smaller numbers.
\nThe results were interpreted in terms of the swelling time constants; τs, (decreased) and the cooperative diffusion coefficient, DSI, (increased) versus wt% MWCNT content. It was observed that high MWCNT content composites swell much slower producing smaller DSI coefficients for all measurements at a given temperature.
\nThe effect of MWCNT addition in insulating PS matrix was investigated [30]. Composite films were prepared using polystyrene (3.5% w/v) with various (0.13–18 wt%) of MWCNTs stock content on 2.5 × 3.0 cm2 glass plates at room temperature. Variations in optical properties of very-thin PS-MWCNT composite films were measured using photon transmission techniques. Electrical and optical percolation thresholds were determined. Classical and site percolation theories were used to calculate the critical exponents for optical transmission data.
\nUV spectrophotometer (Lambda 2 S of PerkinElmer, USA) was used to monitor the variation of optical transparency of the composite films. The transmittances of the composite films were detected at 400 nm wavelength. Measurements were performed at six different positions on the film surface in order to lower the error. All the photon transmission measurements were carried out at room temperature. Figure 7 shows that the behavior of transmitted (Itr) and scattered (Isc) light intensities versus the ratio of MWCNT contents (M) in composite films. When transmitted light intensity, Itr, sharply decreases, and scattering centers in the film are increased, respectively, due to refractive indices between two medium in the composite system [30]. In Figure 7, the scattered light intensity increases rapidly, even though the MWCNT content was 0.13 wt% at the beginning which shows the percolation threshold value is in between 0 and 0.13 wt%. Since M − Mop → M for the extremely low Mop values, the percolation probability for the optical data can be written as follows:
\nThe critical exponent βop was calculated and found to be as 0.32 from the slope of log Isc/I0 versus log M plot.
\nThe effect of MWCNT addition in insulating PVAc matrix was investigated [31]. Mass fractions of the composites were obtained between 0.5 and 18 wt%. Variations in optical properties of P(VAc-co-BuA)/MWCNT composite films were measured using photon transmission and fluorescence emission measurement techniques. The optical and fluorescence percolation thresholds were determined. The classical and site percolation theories were used to calculate the critical exponents for two data sets from the techniques, respectively.
\nVariation in transmitted (Itr) and scattered (Isc) light intensities on PS-MWCNT composite films versus mass fractions [
UV spectrophotometer (Lambda 2S of PerkinElmer, USA) was used to monitor the variation of optical transparency of the composite films. Since the absorbance region of the pyranine molecule was 300–430 nm, the transmittances of the composite films were detected at 470 nm wavelength. Transmission measurements were performed at six different positions on the film surface in order to lower the error. Thus, the average value of transmitted light intensity (Itr) was obtained. Transparency variations of the composite films versus mass fractions (M) of MWCNT were monitored by transmitted light intensity, Itr, from the films. It was observed that Itr sharply decreases as MWCNT content increases in the composite system, and there is almost no light transmission from the films above the mass fraction of 7.0 wt% (M ≥ 7.0 wt%).
\nThe log-log plot of Isc versus M. The slope of the straight line produces the optical critical exponent, βop as 0.40 [
The behavior of Itr versus M predicts that the composite system owns a percolative structure having a percolation threshold at 0.5 wt% MWCNT content. As M is increased, the scattered light intensity, Isc = Io − Itr, increases due to the concentration fluctuations.
\nThe variation of log Isc/Io versus log M is given in Figure 8. The critical exponent, βop, was calculated as 0.40 from the slope of Figure 8 using Eq. (6). The obtained value of βop = 0.40 is not far from the theoretical site percolation value of 0.42 [32].
\nThe variation of fluorescence emission of the composite films was measured using Varian Cary Eclipse fluorescence spectrophotometer. Excitation and emission wavelengths were used as 370 and 507 nm, respectively. The emission wavelength at maximum intensity of pyranine is 510 nm, which varies up to 5–10 nm depending on the structure of the polymer molecules. The fluorescence emission measurements were performed at six different positions on the film surface in order to lower the error level, and the average value of the fluorescence emission intensity (Ifl) at the maximum was obtained. The maxima of the emission intensity (Ifl) versus mass fractions (M) of the samples are shown in Figure 9, where it can be seen that the emission intensities of pyranine show a rapid decrease for further addition of MWCNTs in the composite films. As the MWCNT concentration is increased, the number of the scattering centers in the film also increases.
\nThe fluorescence emission intensity, Ifl, versus MWCNT mass fraction, M [
The fluorescence emission data in Figure 9 can be treated by the percolation theory. The percolation probability for the data of fluorescence emission could be arranged as follows:
\nwhere M is identical to lattice occupation probability, p, then the percolation threshold value, pc, is equal to Mfl.
\nSince (M − Mfl) → M for low Mfl then Eq. (7) becomes as follows:
\nBy assuming, the percolation probability P∞ (p) is inversely proportional to the fluorescence emission intensity. The variation of log (1/Ifl) − log (M) is presented in Figure 10, where two different percolation regions can be detected.
\nThe log-log plot of 1/Ifl versus M. The slopes of the straight lines produce the fluorescence critical exponents, βfl, as 0.35 and 2.0 for the low and high MWCNT concentration regions, respectively [
The critical exponents, βfl, was calculated and found to be as 0.35 and 2.0 from the slopes of the straight lines in Figure 10, according to Eq. (8).
\nAt low MWCNT content, pyranine simply probes the scattering sites in the composite film; however, at high MWCNT concentration, pyranine now traces the conducting network [31].
\nPolystyrene-MWCNT composite was prepared by Ugur et al. showed that healing and inter diffusion process using photon transmission techniques. After annealing step, the transmitted light intensity, Itr, was monitored to observe the film formation process as shown in Figure 11. The increase in Itr up to healing temperature, Th, and above Th during annealing was explained by void closure and inters diffusion processes, respectively, [33].
\nTransmitted photon intensities, Itr, versus annealing temperatures depending on MWCNTs content in the films. Numbers on each figure shows the MWCNTs content [
Temperature dependence of oxygen diffusion into polymer-MWCNT composite films was examined by fluorescence spectroscopy [34]. The diffusivity of the composite films was determined by performing oxygen (O2) diffusion measurements within a temperature range of 24–70°C for each film, and pyrene(P) was used as a fluorescence probe (Figure 12).
\nPlot of the diffusion coefficients, D, versus temperatures, T, for the 3, 15, and 40 wt% MWCNT content films [
The diffusion coefficients increased drastically with both increases of MWCNT content and also of the temperature, and this increase was explained via the existence of large amounts of pores in composite films which facilitate oxygen penetration into the structure. Therefore, PS/MWCNT nanocomposites have useful properties as fluorescent oxygen sensors, and a simple SSF technique can be used to measure the diffusion coefficient of oxygen molecules into these films quite accurately [34]. PS/MWCNT films were prepared by various contents of MWCNT at room temperature. After annealing at 170°C which is above glass transition (Tg) temperature of PS, fluorescence quenching processes were realized on oxygen diffusion [35]. Figure 13 illustrates the logarithmic plots of the fluorescence intensity of pyrene behavior within time during oxygen diffusion into the composite films for 15 wt %MWCNT content.
\nLogarithmic plots of the fluorescence intensity of pyrene behavior within time during oxygen diffusion into the composite films for 15 wt %MWCNT content [
The diffusion coefficients increased drastically with the increase of MWCNT content, and this increase was explained via the existence of large amounts of pores in composite films which facilitate oxygen penetration into the structure.
\nOxygen permeability of nanocomposite films consisting of MWCNT and PS were determined to investigate the oxygen diffusion depending on MWCNT and temperature [36].
\nThe time behavior of pyrene, fluorescence intensity, I, during oxygen diffusion into the composite films with different MWCNT content. Numbers on each curve indicates the MWCNT content (%) in the film [
In Figure 14 normalized pyrene intensity, Ip curves are presented against diffusion time for films having different MWCNT content exposed to oxygen. It is seen that as oxygen diffused through the planar film, the emission intensity, Iem, of the pyrene decreased for each MWCNT content film. After completing oxygen diffusion, Iem was saturated. As shown in Figure 14, the quenching rate depends on the MWCNT contents in the film. Rapid quenching of excited pyrenes by O2 molecules is possible for the high MWCNT content composite films [36].
\nThe time behavior of the pyrene, P, fluorescence intensity, I, during oxygen diffusion into the 40 wt% MWCNT content film at various temperatures. Numbers on each curve indicate the temperature [
The rate of decrease in intensity is higher at higher temperatures predicting the more rapid quenching of excited pyrene molecules by O2 molecules diffused into the films. It is worthy to note that in Figure 15 as expected the D increases with increase in temperature for all composite films. Increase in temperature naturally increases the Brownian motion of oxygen molecules given them more chance to meet the P molecules in the composite film [36].
\nThe results of
PS-MWCNT latex composite films were prepared by mixing of pyrene (P)-labeled PS latex with different amounts of MWCNTs varying in the range between 0 and 20 wt% [37]. To monitor the stages of film formation of PS/MWCNT latex composite films, scattered light (Is) and fluorescence intensities (IP) from P were performed after each annealing step. Some temperatures such as minimum film formation (To), void closure (Tv), and healing, (Th) temperatures were decided as given in Figure 16.
\nPlot of corrected fluorescence intensity (=fluorescence intensity/scattered fluorescence intensity) of composite films with different MWCNT content versus annealing temperatures. (
The existence of MWCNT delays the latex film formation process because of the behavior of T0. However, healing processes are not affected by the presence of MWCNT [37].
\nThe elastic modulus of the swollen PAAm-MWCNT composites was measured to determine the effect of MWCNTs content. Elasticity measurement was performed by compressive testing technique and modeled by the theory of rubber elasticity [38, 39].
\nStress versus strain curves
Stress (Pa)-strain plots of low and high MWCNTs content gels produced using the data obtained from the linear region, in the plots of F (N) versus compression curves for PAAm-MWCNT composites at 25°C, are presented in Figure 17, respectively. The stress versus strain displays a good linear relationship at 25°C, which agrees with Eq. (9).
\nThe elastic moduli were obtained by a least square fit to the linear region of Figure 17. The addition of MWCNT into PAAm caused an increase in elastic modulus of the composite as expected. In PAAm–1 wt% MWCNT composite, the measured elastic modulus is found to be 0.105 MPa, two times larger than pure PAAm sample. It is seen in Figure 17a that PAAm–0.1 wt% MWCNT composite has smaller initial slope than 1 wt% MWCNT content composite. In this case, it appears that the alignment effect of MWCNT plays an important role for getting the different onset behavior [40]. The stress of the PAAm-MWCNT (1–5 wt% MWCNT composites) increases dramatically when the strain exceeds 0.6%, where the alignment is taking place in the composite. On the other hand, at high MWCNT region, the random motion of MWCNT impedes alignment as predicted in Figure 17b. Therefore, in a gel with low MWCNT content, alignment of MWCNTs with each other is much easier than in high content MWCNT composite.
\nDependence of elastic modulus on content of wt% MWCNT in the composite [
Figure 18 shows the plot of elastic modulus,
Logarithmic plot of the elastic modulus versus MWCNTs contents curves for
In Figure 19, it is understood that 1 wt% is the critical percolation threshold, pc, at which gel system owns a percolation cluster formed from MWCNTs. Here, the composite gel passes the highest elasticity presenting the highest G value.
\nEquation (10) now can be used to fit the G versus wt% MWCNT curve below the critical point (below 1 wt%). The value of the fitting exponent
Storage modulus as a function of angular frequency at 145°C for PVAc-MWCNTs nanocomposites [
As shown in Figure 20, the storage modulus G′ increases with an addition of MWCNT loading compared with that of the PVAc matrix.
\nThe rheological properties of PET-MWCNT nanocomposites were determined using low strain values with frequency 0.1–500 rad/s [46]. The storage modulus versus frequency is given in Figure 21.
\nStorage modulus (
The rheological behavior of the nanocomposites depends on the MWCNT content with respect to the frequencies because of the restriction of PET chain relaxation and the short-range dynamics or local motion of the PET chains in the nanocomposites [12].
\nThe electrical resistivity of the PVAc/MWCNT composite films was performed by a Keithley Model 6517A electrometer and Keithley Model 8009 resistivity test fixture. 10–100 V DC potential for every 15 s periods was applied to measure their surface resistivity, Rs, (Ohm/square or Ohm) which was four different orientations and repeated measurements were repeated. The surface conductivity values were calculated from the following equation.
\nThen, the obtained results from Eq. (11) are presented in Figure 22. It can be seen from Figure 10 that the conductivity, σ, dramatically increases above Mσ = 1.8 wt%. This behavior can be explained by the existence of vertical conductive paths of MWCNTs in the composite film. After Mσ = 1.8 wt%, the insulating system starts to transform to the conductive system. Therefore, Mσ = 1.8 wt% is the percolation threshold of conductivity. For a dilute composite structure, classical percolation theory was given in Eq. (12) can be used [25].
\nHere, σ is the conductivity (Siemens), σo is the conductivity of pure MWCNT film, M is the volume or mass fraction of MWCNT, Mσ is the percolation threshold value, and βσ is the critical exponent for the conductivity, respectively, which was calculated from Eq. (12) and determined from the slope of the log σ and log (M − Mσ) plot. The βσ = 2.25 value is well agreed with the theoretical and the experimental data in the literature [45].
\nThe average values of the surface resistivity, Rs, of PVAc/MWCNT composite films versus mass fractions of MWCNT, M, were measured and observed that the surface resistivity (Rs) of the composite films do not change much below 1.0 wt% (M ≤ 1.0 wt%)[45]. However, Rs values of the composite films dramatically decrease from 1011 to 104 Ohm/square in the bandgap of M = 1.0–4.0 wt%.
\nThis behavior indicates that the electrical percolation occurs at low levels of M. The surface conductivity values were calculated from Eq. (11). The percolation threshold of the surface conductivity (Mσ) is 1.0 wt%. βσ was calculated from the slope of the curve in Figure 23, which was drawn from the logarithms of the surface conductivity data treated with Eq. (12), and found to be as 2.1 which is well agreed with the theoretical and the experimental results in the literature [45].
\nVariations in conductivities, σ, which were calculated by Eq. (
The surface conductivity properties of PS-MWCNT composite films were measured at room temperature using a two probe technique [30]. Figure 24 shows the electrical conductivity (σ) of PS-MWCNT composite films as a function of MWCNT ratio, R. While low MWCNT content composites (R < 0.04) show similar conductivity between 10−13 and 10−12, the conductivity of high MWCNT content films (R > 0.04) increases dramatically to 10−7–10−6 S.
\nThe log-log plot of σ versus M → Mσ. The slope of the straight line produces the electrical critical exponent, βσ as 2.1 [
Conductivity versus MWCNT content, R (w/w) [
Electrical conductivity (σ) of the PET-MWCNT nanocomposites as a function of MWCNT loading. Inset: a log-log plot of electrical conductivity versus reduced MWCNT loading. The solid lines are fits to a power law dependence of electrical conductivity on the reduced MWCNT loading [
Figure 25 shows the electrical conductivity (σ) of the PET-MWCNT [12]. The electrical conductivity of pure PET is 8.6 × 10−17 S cm−1. By loading MWCNT from 0.5 to 1 wt%, the conductivity of PET-MWCNT nanocomposites increases in 8 orders of magnitude, because percolative path was formed in the nanocomposite [12].
\nIn this chapter, we review the optical, electrical, and mechanical behaviors of polymers doped by multiwalled carbon nanotubes (MWCNTs). This chapter covered the works produced from different types of polymers. We try to give the experimental results based on the mentioned theoretical models. In the first section of the chapter, some examples were given about optical behavior of polymer-MWCNT composites which were performed by fluorescence and UV-Vis spectroscopy. Therefore, the behavior of them at a molecular level were discussed, and measured some physical quantities were reported. The second section of the chapter has demonstrated that the mechanical and rheological measurements can be used to determine the variations of the elastic and storage modulus of the composites. The third part of the chapter has shown that the insulator-conductor transition takes place by the addition of a small amount of MWCNT in the polymer composite system. The insulator system starts to transform to a more conductive state by consisting of conductive paths of MWCNTs between the electrodes. The size of MWCNTs and electron hopping and/or tunneling effects play important roles in the early percolation behavior of the films.
\nIn conclusion, we try to give the experimental evidences based on the mentioned theoretical models. As far as the engineering applications are concerned, optical, mechanical, and electrical properties of polymer composites prepared by MWCNT contents are very important in coating, food, electronic, and pharmaceutical industries. This chapter introduces basic parameters for the given processes in the polymer composites which can find important applications in the mentioned fields.
\nBiochar is a carbon-rich by-product produced from the thermochemical conversion of biomass feedstock under partial or total absence of oxygen [1, 2]. Feedstocks used in biochar (BC) production are mostly wood, municipal and agriculture wastes [3, 4, 5, 6]. Amending soil with biochar has received increased attention as a method for carbon sequestration in soils, thereby reducing carbon dioxide (CO2) emissions [7, 8, 9] and improving soil quality due to the vital role of carbon (C) in soil physical, chemical and biological processes [10].
Amending soil with biochar has been practiced for a long time. The high fertility of anthropogenic dark earth soils known as ‘Terra Preta de Indio’ in the Amazon basin has been related to the high content of charred materials [11, 12, 13]. Historically, the source of char in these soils has been considered as a disposal of charcoal from domestic fires and the practice of slash and char agriculture by Pre-Columbian Amazonian Indians [11, 14]. Hence, these soils have remained fertile and rich in biochar derived C stock for hundreds to thousands of years after they were abandoned.
In addition to the role of biochar in increasing the C sequestration and influencing the reduction of CO2 emissions, biochar has been shown to enhance soil quality and to stabilize PTMs [15]. Biochar has a potential benefit for improving soil fertility [16, 17], improving soil properties such as pH [11, 12, 13, 18], cation exchange capacity (CEC) and water holding capacity [19], enhancing plant growth [20], and reducing nutrient leaching losses [21]. The significant amount of calcium (and magnesium) carbonate (Ca/MgCO3) in BCs enables them to function as lime materials providing Ca and Mg to plants and neutralizing acidity when applied to acid soils.
The role of biochar in improving soil pH, organic carbon (OC), and CEC was also highlighted by [16]. Moreover, biochar can immobilize PTMs (immobilization is the reduction of the potential migration of PTMs to plants, or reduction of phytoavailability) such as cadmium (Cd), lead (Pb), and zinc (Zn) and thereby to reduce the phytoavailability of PTMs (concentration of PTMs in plant parts, or contents of PTMs in soils available to plants) to plants in contaminated soils, notably because it raises the soil pH [18, 22] and increases CEC and OC [23]. Many studies also found biochar application promotes the ability to remove organic contaminants [24, 25]. Because of its porous structure and diverse functional groups [26], biochar has been widely used in the field of agriculture and environmental protection [27] due to its ability to improve soil health and crop yields, and sequestering carbon, immobilizing PTMs and adsorbing organic pollutants such as polycyclic aromatic hydrocarbons (PAHs).
For these reasons, studies on biochar land-application have exponentially increased in the last 20 years (Figure 1). During the same period (1999–2018), the word ‘potentially toxic metal’ or ‘heavy metal’ places itself in the
Number of publications (NP) of biochar studies since 1999 (adapted from [
The effects of pH rising in soils are significantly influenced by biochar addition more than by other practices such as liming [28]. Table 1 shows some of the main characteristics of BCs (pH included) as affected by feedstock sources and pyrolysis temperature. Biochar is superior to lime to remediate PTMs-polluted areas, mainly because acidic conditions can lead to the leaching of metals and threatening of groundwater [28]. Biochars can supply OC and raise soil pH, but lime only increases soil pH. Hence, poultry litter-derived biochar (PLB) proves itself as very effective in immobilizing Cd, even under strong acidic conditions, thus preventing Cd leaching to the groundwater [28]. Besides raising the soil pH, the enhanced OC provided by biochar addition contributes to a decrease in the phytoavailability of PTMs by reducing metal mobility due to bonding metals into more stable fractions [29, 30], such as organic matter-bound and/or highly stable organic complexes which are not readily dissolved by water. The increase of both pH and OC also contributes to a higher CEC, then resulting in a higher PTMs adsorption [31].
Biochar feedstock | Pyrolysis temperature (°C) | Water (wt%) | TC (wt%) | TOC (wt%) | TN (wt%) | pH | Reference |
---|---|---|---|---|---|---|---|
Wood of ‘Quaresmeira’ ( | 330 | 55 | 82 | 80 | — | 9.7 | [13] |
Poultry litter | 450 | — | 38 | — | 2 | 9.9 | [16] |
550 | — | 33 | — | 0.85 | 13 | ||
Miscanthus (Miscanthus × giganteus) straw | 600 | — | 53.5 | — | 0.31 | 10 | [18] |
1-Switchgrass straw | 500 | — | 23.7 | — | 0.8 | 9.4 | [19] |
2-Anaerobically digested fiber | — | 25 | — | 0.85 | 9.3 | ||
3-Softwood bark | — | 28.4 | — | 0.14 | 7.6 | ||
4-Wood pellets | — | 28.2 | — | 0.05 | 7.2 | ||
1-Swicthgrass | 350 | 1.4 | 42.6 | — | 0.9 | 5.2 | [23] |
700 | 1.7 | 31.4 | — | 0.7 | 10 | ||
2-Poultry litter | 350 | 2.7 | 38.4 | — | 4.1 | 7.4 | |
700 | 3.9 | 27.8 | — | 1.6 | 10 | ||
1-Pig manure | 350 | — | 31.6 | — | 3.8 | 8.3 | [25] |
700 | — | 25.2 | — | 2.1 | 9.5 | ||
2-Deashed pig manure-biochar | 350 | — | 66.7 | — | 7.6 | 6.2 | |
700 | — | 74.2 | — | 5 | 6.4 | ||
1-Poultry litter | 400 | — | 16.8 | — | 1.4 | 10 | [28] |
2-Eucalyptus | 600 | — | 81 | — | 1.1 | 10.4 |
Summary of some biochar properties as affected by feedstock sources and pyrolysis temperature.
TC: total carbon. TOC: total organic carbon. TN: total nitrogen. “—”: not given.
The application of orchard prune-derived biochar (OPBC) to mine tailings reduced phytoavailable (DTPA-extractable) concentrations of Pb, Cd, and Zn [32]. Rice straw-derived biochar reduced Cd concentration in the plant available soil fraction grown in a greenhouse [30]. Biochar addition also showed a potential in reducing Cd and Pb accumulation in ryegrass (
Potentially toxic metal (heavy metal) immobilization to ryegrass shoots and roots as a function of biochar application rates. Diagram was created from the work of [
It has been shown that the addition of sugar cane bagasse-derived BC (SCBC) decreased the phytoavailable Pb fraction by 97%, and that the PTM uptake by maize plants decreased with increasing the level of applied BC [34]. The authors attributed such results to an enhancement of soil pH and soil organic carbon (SOC) because of BC addition. In addition, an unpublished work conducted by Antonangelo and Zhang has also revealed how impacting is the increase of soil pH and SOC, as biochar application rates increase, on PTMs (Zn, Pb and Cd) mobility. The study was carried out with no plants and the application rates of poultry litter- (PLB) and switchgrass-derived biochar (SGB) ranged from 0 to 8% w/w in multi-metal contaminated soil. Potentially toxic metal phytoavailability was assessed by using two extraction methods (NH4NO3 and DTPTA) after 10 weeks of soil + biochar incubation under laboratory room temperatures. The results of PTMs contents in the extracts and SOC (%) as a function of biochar application rates are summarized in Figures 3 and 4, and Table 2. The pH increase from 6.5 to 8.0, as shown in Figure 3, is a consequence of the increased BCs (SGB and PLB) application rates from 0 to 8%, so is the SOC increase, as shown in Figure 4. Table 2 highlights the significant negative correlations (inverse relationship) of pH and SOC (independent variables) with phytoavailable PTMs in the filtered extracts (dependent variables).
Relationship between pH and metal concentrations in NH4NO3 and DTPA extracts after 10 weeks of biochar incubation. Points were plotted from the whole dataset of measurements. One outlier from three replicates (n = 3) was removed, when detected, by using IML and UNIVARIATE (ROBUSTSCALE) procedures of the SAS program. pH ranged from 6.5 to 8.0 as biochars (SGB and PLB) application rates increased from 0 to 8% w/w of biochar.
Soil organic carbon (OC%) changes due to biochar (SGB and PLB) application rates after 10 weeks of incubation. Bars represent the standard deviation of the mean (n = 3) results are significant at
Soil attribute | SGB | PLB | SGB + PLB | SGB | PLB | SGB + PLB |
---|---|---|---|---|---|---|
Zn (NH4NO3) | Zn (DTPA) | |||||
pH | −0.75** | −0.82*** | −0.81*** | −0.15NS | −0.76*** | −0.55** |
OC | −0.79** | −0.74** | −0.43* | −0.31NS | −0.60* | −0.47* |
Pb (NH4NO3) | Pb (DTPA) | |||||
pH | −0.55* | −0.05NS | −0.16NS | 0.03NS | −0.63* | −0.44* |
OC | −0.64* | −0.11NS | −0.46* | −0.12NS | −0.77** | 0.10NS |
Cd (NH4NO3) | Cd (DTPA) | |||||
pH | −0.91*** | −0.82*** | −0.72*** | 0.04NS | −0.83*** | −0.66*** |
OC | −0.91*** | −0.91*** | −0.01NS | −0.11NS | −0.92*** | 0.06NS |
Pearson correlation coefficient (R) between metal extracted from NH4NO3 or DTPA and soil attributes (pH and organic carbon-OC) after 10 weeks of soil+biochar (SGB and PLB) incubation.
*:
The immobilization of Cu, Pb, Cd, and Ni by BCs was attributed to the quantity of surface oxygen-functional groups, which is directly related to the amount of carbon (C) present in the biochar composition [35]. Uchimiya et al. [36] reported that biochar enhanced Cu sorption in a sandy loam soil primarily by cation exchange mechanism, enhanced by the soil C increase. Hence, biochar addition increased the sorption capacity of the soil matrix for both organic and inorganic contaminants [37]. However, BCs may favor the availability of some PTMs such as arsenic (As). The addition of sugar cane bagasse-derived BC (SCBC) stabilized Pb but accelerated the desorption of arsenic (As); consequently, increased its availability [38]. That is probably a result of charge repulsion between the negatively charged SCBC and the arsenate anion (AsO43−).
While investigating the effects of chicken manure (CMB) and greenwaste biochar (GWB), both produced at 550°C (pyrolysis temperature), on the immobilization and phytoavailability of Cd, Cu and Pb in metal-spiked and multi-metal contaminated soils, [39] found that both BCs significantly decreased Cd and Pb mobility, mostly by modifying those PTMs from the easily exchangeable soil fraction to less available organic bond fraction. Additionally, they reported that the application of the two feedstock-derived BCs increased the root and shoot dry biomass and decreased the accumulation of Cd, Cu, and Pb in Indian mustard (
A significant decrease in the transfer factor values (TF) of PTMs (Zn, Pb, and Cd) from ryegrass roots to ryegrass shoots when evaluating PLB and SGB additions to a multi-metal contaminated soil was found by [22], and that the PLB was more efficient in such reduction than SGB. This was probably a consequence of their higher pH, CEC, specific surface area (SSA), and stronger buffering capacity as reported by [23], which resulted in the higher efficiency of PLB in decreasing PTMs uptake, as highlighted by the higher decrease of the bioconcentration factor (BCF = [PTMs in shoots/PTMs concentration in soil]) as PLB application rates increased. Figure 5 (and Figure 3) briefly summarizes such findings and highlights the PTMs immobilization as a function of two feedstocks derived-biochar application rates.
Bioconcentration factor (BCF) and transfer factor (TF) of potentially toxic metals (Zn, Pb, and Cd) from ryegrass roots to ryegrass shoots as a function of biochar application rates. Biochars were either derived from switchgrass (SGB) or poultry litter (PLB) feedstocks. Graphs were modified from [
When comparing other soil amendments or feedstocks (raw material) with a feedstock-derived biochar, [40] showed that mussel shells, cow manure, and oak wood biochar application reduced Pb phytoavailability and phytoavailability in a highly contaminated military shooting range soil in Korea. Their study also showed increases in germination percentage and root elongation of lettuce (
A study conducted by [42] observed that the addition of hardwood-derived biochar (HWB) to a PTMs contaminated mine soil reduced pore water solubility of Pb concentrations and ryegrass Pb levels. On the other hand, the combination of biochar with greenwaste compost (GWC) was more effective in reducing Pb in soil pore water and uptake by ryegrass. However, the biochar itself was more effective in reducing pore water Cu than GWC. Additionally, [43] reported that the addition of HWB and GWC to a multi-element contaminated soil significantly reduced concentrations of Cd and Zn in pore water during a 60 days exposure to field conditions and reduced phytoavailability of these elements resulting in increased shoot emergence of ryegrass. In contrast, concentrations of Cu and As in pore water increased with amendment applications [38, 43]. In a laboratory column study, [44] reported that HWB reduced the concentrations of Cd and Zn in leachate obtained from a multi-metal polluted soil with evidence of surface retention of both metals on biochar.
The work of [45] compared the impacts of broiler litter-derived biochar and pecan shell-derived steam activated carbon amendments on PTMs (Cu, Ni, and Cd) immobilization and the effects of oxidation on mineral retention in synthetic rainwater leaching experiments. Conversely, their study found that biochar was most effective in immobilizing Cu, whereas activated carbon immobilized Ni and Cd to a larger extent than biochar.
Contrarily, some BCs might only slightly decrease or even significantly increase extractable PTMs depending on the feedstock and pyrolytic temperature [33, 42]. Overall, the influence of biochar on PTMs extractability varies depending on the feedstock, application rate, and BCs particle size [46]. Generally speaking, biochar is a promising tool to reduce the mobility of PTMs in mining areas [22].
Biochars are effective in the immobilization of PTMs and this effect varies depending on biochar nature and pyrolysis conditions. [47] investigated the impact of pyrolysis temperature on BCs ability to stabilize PTMs in Small Arms Range soil using broiler litter BCs produced at 350 and 650°C. They found that both BCs were effective in stabilizing Pb and Cu at application rates of ≤5% without releasing Sb. In other experiments, [48, 49] suggested using BCs prepared at high temperatures, 650–800°C, for remediation purposes. Additionally, the uptake of PTMs by ryegrass planted in biochar-treated soils generally decreased with increasing pyrolytic temperature [33]. It was also pointed out by [50] that two different feedstocks-derived BCs were more effective in chromium (Cr) adsorption when pyrolyzed at higher temperatures. However, low-temperature biochar was more effective in stabilizing Pb than high-temperature biochar [47]. Such a result was attributed to the higher soluble P concentration of low-temperature biochar, which resulted in a greater Pb immobilization by the formation of lead-phosphate precipitates. In similar experiments using oxidized and unoxidized plant-derived BCs, [49] observed that oxidized BCs rich in carboxyl functional groups had greater ability for Pb, Cu, and Zn immobilization than unoxidized BCs. Therefore, the effect of BCs on the mobility of PTMs in soil is not only a function of the pyrolysis temperature, but also the feedstock used, as previously mentioned, soil properties, and surface functional groups. Indeed, the ability of BCs in reducing the phytoavailability of PTMs in soil depends on its surface functional groups, specific surface area, and porosity [23].
Figure 6 was adapted from the recent work of [51] and clearly shows that simply increasing pyrolysis temperature of BCs to enhance PTMs immobilization is not a pragmatism. The recovery efficiency (RE, in %) of PTMs (in a multi-metal contamination scheme: Pb + Cu + Zn) from soils amended with mesquite BCs (MBC) pyrolyzed at four different temperatures (300, 400, 500, and 600°C), have decreased as the initial concentration of added PTMs increased (Figure 6). However, MBC pyrolyzed at the highest temperature (600°C) has shown an overall higher RE% of Pb, Cu, and Zn (Figure 6). The authors also emphasized that there was a competitive adsorption among the PTMs into BCs exchangeable sites with a preferable affinity for Pb sorption. That would probably favor other PTMs to be phytoavailable in the medium. According to [22, 23, 51], surface functional groups responsible for metals retention are prone to change when pyrolysis temperature increases, which changes metals’ sorption effectiveness to the same extent. Phenolic groups (OH) decrease followed by the increase of aromatic carbon contents (C=C stretching) in produced BCs are attributed to the depolymerization and dehydration of materials as pyrolysis temperature increases, then resulting in the formation of C=C double bonds, carbonyl, and carboxylic functional groups [23, 51, 52, 53]. Those functional groups are also responsible for PTMs adsorption and complexation.
Lead (Pb), copper (Cu), and zinc (Zn) removal efficiency (RE%) (PTM adsorption) in a multi-metal contaminated soil amended with biochars derived from mesquite and pyrolyzed at 300°C (MBC 300), 400°C (MBC 400), 500°C (MBC 500), and 600°C (MBC 600). The graph is modified from [
Biomass gasification has also been demonstrated as an alternative method of pyrolysis to produce BCs [54, 55], although to a much lesser extent. It is a technology that uses a controlled process involving heat, steam, and oxygen to convert biomass to hydrogen (and other products), in the absence of combustion. A recent study of [55] have demonstrated that the SSA, CEC, and basic functional groups of the pine woodchips-derived BCs (PWC) increased as the rate of airflow increased during the BCs conversion process. Therefore, such improved properties would favor PTMs immobilization in contaminated soils if a proper rate of PWCs were applied. More studies on different gasification processes of applied BCs affecting PTMs mobility in soils are encouraged to broaden the BCs options for remediation purposes.
The mechanisms proposed for PTMs immobilization are explored in [56, 57]. In summary, three mechanisms are mostly responsible for PTMs retention into BCs, among them: (1) PTMs exchange with calcium (Ca2+), magnesium (Mg2+), and other cations associated with BCs (Figure 7); (2) complexation of PTMs into different surface functional groups, as previously highlighted (see Section 4); and (3) the physical adsorption followed by surface precipitation contributing to PTMs immobilization.
Mechanisms of cation exchange between positively charged ions contained in the reactive surface of biochars and potentially toxic heavy metals (‘heavy metal’) dissolved in soil solution. The graph was made by the authors.
In the first case, the PTMs/cations exchange is further attributed to the co-precipitation of PTMs and their innersphere complexation with complex humic matter and mineral oxides contained in the biochar [57]. First, the strengths of PTMs adsorption into BCs surface are low due to the presence of water molecules surrounding the ion (oscillation in the distance of the electrostatic retention). Latterly, water molecules are released and the affinity to complexation enhances depending on the composition and structure of the biochar reactive surface, thus a much stronger inner-sphere complex is formed disfavoring the PTMs release back to the soil solution. In the second case, the PTMs inner-sphere complexation is with the free hydroxyl of mineral oxides surface (OH) and other surface precipitation [57]. In the third case, the surface precipitation of PTMs occurring is designated as
Most studies from the last decade have demonstrated the strong potential of BCs in reducing leachability and immobilizing PTMs pollutants in soils that were previously phytoavailable. By increasing soil pH, BCs act as liming materials and PTMs precipitate as insoluble PTMs hydroxides in a high pH environment. Additionally, the greater SOC attributed to the BCs addition to multi-metal contaminated soil contributes to the formation of PTMS-organic anion complexes that are precipitated out from the system, since the previous bioavailable PTMs contents were much higher than usual. The characteristics of BCs vary widely with different feedstocks (biomass materials) and pyrolysis conditions (low and high temperatures). Generally, there are three mechanisms related to the direct removal of PTMs (and other pollutants) towards BCs reactive surface, which are related to a strong sorption and weak desorption of cationic PTMs then indicating that BCs sequesters pollutants in itself.
The current works emphasizing the use of biochar for soil remediation purposes have mainly been conducted in laboratories and/or greenhouses on a small scale with controlled conditions. As pointed out by [57], large-scale field trials are essential before operational scale remediation projects are implemented. Since the BC properties are largely varying, and sometimes contrasting, it is important to design BC products for every specific remediation project. The BCs ability to sequestrate may lead to the accumulation of PTMs contaminants in the amended soils in the long-term, and yet the pollutant environmental fate over time is not well elucidated. It is well known that the capacity of BCs to adsorb and/or complex PTMs decreases with time as a consequence of the aging process and saturation. Therefore, it is strongly encouraged to research on the aging process of BCs activity in the future because such information would help in the decision-making of the BC application rate and frequency to improve soil PTMs remediation efficiency.
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