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# Effect of Temperature on the Structural and Physicochemical Properties of Biochar with Apple Tree Branches as Feedstock Material

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The objective of this study was to study the structure and physicochemical properties of biochar derived from apple tree branches (ATBs), whose valorization is crucial for the sustainable development of the apple industry. ATBs were collected from apple orchards located on the Weibei upland of the Loess Plateau and pyrolyzed at 300, 400, 500 and 600 • C (BC300, BC400, BC500 and BC600), respectively. Different analytical techniques were used for the characterization of the different biochars. In particular, proximate and element analyses were performed. Furthermore, the morphological, and textural properties were investigated using scanning electron microscopy (SEM), Fourier-transform infrared (FTIR) spectroscopy, Boehm titration and nitrogen manometry. In addition, the thermal stability of biochars was also studied by thermogravimetric analysis. The results indicated that the increasing temperature increased the content of fixed carbon (C), the C content and inorganic minerals (K, P, Fe, Zn, Ca, Mg), while the yield, the content of volatile matter (VM), O and H, cation exchange capacity, and the ratios of O/C and H/C decreased. Comparison between the different samples show that highest pH and ash content were observed in BC500. The number of acidic functional groups decreased as a function of pyrolysis temperature, especially for the carboxylic functional groups. In contrast, a reverse trend was found for the basic functional groups. At a higher temperature, the brunauer-emmett-teller (BET) surface area and pore volume are higher mostly due to the increase of the micropore surface area and micropore volume. In addition, the thermal stability of biochars also increased with the increasing temperature. Hence, pyrolysis temperature has a strong effect on biochar properties, and therefore biochars can be produced by changing pyrolysis temperature in order to better meet their applications.
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energies
Article
Effect of Temperature on the Structural and
Physicochemical Properties of Biochar with Apple
Tree Branches as Feedstock Material
Shi-Xiang Zhao, Na Ta and Xu-Dong Wang *
College of Resources & Environment, Northwest A&F University, 3 Taicheng Road, Yangling 712100, China;
zhaoshixiang1989@126.com (S.-X.Z.); tana0214@163.com (N.T.)
*Correspondence: wangxd@nwsuaf.edu.cn; Tel./Fax: +86-29-8708-0055
Received: 18 April 2017; Accepted: 21 August 2017; Published: 30 August 2017
Abstract:
The objective of this study was to study the structure and physicochemical properties of
biochar derived from apple tree branches (ATBs), whose valorization is crucial for the sustainable
development of the apple industry. ATBs were collected from apple orchards located on the Weibei
upland of the Loess Plateau and pyrolyzed at 300, 400, 500 and 600
C (BC300, BC400, BC500
and BC600), respectively. Different analytical techniques were used for the characterization of the
different biochars. In particular, proximate and element analyses were performed. Furthermore,
the morphological, and textural properties were investigated using scanning electron microscopy
(SEM), Fourier-transform infrared (FTIR) spectroscopy, Boehm titration and nitrogen manometry.
In addition, the thermal stability of biochars was also studied by thermogravimetric analysis.
The results indicated that the increasing temperature increased the content of ﬁxed carbon (C), the C
content and inorganic minerals (K, P, Fe, Zn, Ca, Mg), while the yield, the content of volatile matter
(VM), O and H, cation exchange capacity, and the ratios of O/C and H/C decreased. Comparison
between the different samples show that highest pH and ash content were observed in BC500. The
number of acidic functional groups decreased as a function of pyrolysis temperature, especially for
the carboxylic functional groups. In contrast, a reverse trend was found for the basic functional
groups. At a higher temperature, the brunauer–emmett–teller (BET) surface area and pore volume are
higher mostly due to the increase of the micropore surface area and micropore volume. In addition,
the thermal stability of biochars also increased with the increasing temperature. Hence, pyrolysis
temperature has a strong effect on biochar properties, and therefore biochars can be produced by
changing pyrolysis temperature in order to better meet their applications.
Keywords:
biochar; pyrolysis temperature; apple tree branch; physicochemical properties; structural
1. Introduction
Biochar is a carbon (C)-rich byproduct produced in an oxygen-limited environment [
1
], which has
been gaining increasing attention over the last decade due to its potential to mitigate global climate
change [
2
,
3
]. Biochar can be used not only as a soil amendment with the aim of improving soil
physical, chemical and biological properties [
4
,
5
], but also as an adsorbent to remove organic and
inorganic pollutants [
6
,
7
]. The functions and applications of biochars mostly depend on their structural
and physicochemical properties [
8
], therefore, it is very important to characterize the structural and
physicochemical properties of biochar before its use.
Various types of biomass (wood materials, agricultural residues, dairy manure, sewage
sludge, et al.) have been used to produce biochars under different pyrolysis conditions [
9
,
10
].
During pyrolysis, biomass undergoes a variety of physical, chemical and molecular changes [
11
].
Previous studies indicated that pyrolysis condition and feedstock type signiﬁcantly affect the structural
Energies 2017,10, 1293; doi:10.3390/en10091293 www.mdpi.com/journal/energies
Energies 2017,10, 1293 2 of 15
and physicochemical characteristics of the resulting biochar products [
12
14
]. Generally, woody
biomass provides a more C-rich biochar compared to other feedstocks since it contains varying
amounts of hemicellulose, cellulose, lignin and small quantities of other organic extractives and
inorganic compounds [
15
]. Xu and Chen [
16
] suggest that higher lignin and minerals content result
in a higher yield of biochar. Therefore, woody biomass is one of the most important sources for
biochar production.
The structural and physicochemical properties of biochar, such as surface area, pore structures,
surface functional groups and element composition, can also be inﬂuenced by varying the pyrolysis
condition, such as pyrolysis temperature, heating rate and holding time [
17
,
18
]. The pyrolysis
temperature is reported to signiﬁcantly inﬂuence the ﬁnal structural and physicochemical properties
of biochar due to the release of volatiles as well as the formation and volatilisation of intermediate
melts [
18
]. Previous studies indicated that higher temperature resulted in a higher C content, while the
losses of nitrogen (N), hydrogen (H) and oxygen (O) were also recorded [
19
the temperature lead to an increase the ash and ﬁxed C contents, and to a decrease the content of
volatile materials [
20
]. Furthermore, the increase in pyrolysis temperature affects H/C and O/C ratios;
porosity; surface area; surface functional groups and cation exchange capacity (CEC) and so on [
21
].
In particular, biochar produced at high temperature has high aromatic content, which is recalcitrant
to decomposition [
22
]. In contrast, biochar produced at low temperature has a less-condensed C
structure and, therefore, may improve the fertility of soils [
23
]. Therefore, the pyrolysis temperature
was investigated in this study.
Weibei upland of the Loess Plateau has been recognized as one of the best apple production
areas in the world due to its special topography and climate features which are suitable for planting
apples [
24
]. Apple tree branches (ATBs) are a major agricultural residue in this region due to the quick
development of the apple-planted area in recent years. During the autumn of each year, the residues
might be burned by the fruit grower with the aim of reducing the occurrence of plant diseases and
insect pests, which then becomes an important source of atmospheric CO
2
. Thus, conversion of ATBs
into biochar has the potential to be used to mitigate environmental problems. In addition, the biochar
products also can be used as a soil amendment, which can improve the soil quality [
25
,
26
]. Therefore,
the aim of this study was to examine the structure and physicochemical properties of biochar produced
at different pyrolysis temperatures using ATB as feedstock. Such understanding is crucial for the
sustainable development of apple industry on the Weibei upland.
2. Materials and Methods
2.1. Feedstock Preparation
ATBs were collected from apple orchards located on the Weibei upland of the Loess Plateau,
Northwest China (34530N, 108520E). Prior to the experiments, ATBs were ground to a particle size
of less than 2 mm and then washed with deionized water several times to remove impurities. These
pre-prepared samples were dried at 80 C for 24 h to remove moisture.
2.2. Biochar Production
Pyrolysis experiments were carried out in a mufﬂe furnace (Yamato Scientiﬁc Co., Ltd, FO410C,
Tokyo, Japan) under nitrogen gas stream (at a rate 630 cm
3·
min
1
, standard temperature and pressure
298 K, 101.2 kPa). The feedstock was placed in a stainless steel reactor of 20.5 cm internal length,
12.2 cm internal width and 7.5 cm internal height with a lid and subjected to pyrolysis at different
temperatures (300, 400, 500 and 600
C, respectively) for 2 h 10 min. The pyrolysis heating rate
employed was 10
C min
1
. After pyrolysis, the reactor was left inside the furnace to cool to room
temperature. The biochars obtained were labeled as BC300, BC400, BC500 and BC600, respectively.
Energies 2017,10, 1293 3 of 15
All biochars were weighed and then the generated biochars were milled to pass through a 0.25 mm
sieve (60 mesh) for further analysis and use. The yield of biochar was calculated as follows:
Yield (%)=mas s o f bio char (g)
oven dry mass o f f eedstock (g)×100%
2.3. Characterization of Biochar
2.3.1. Proximate Analysis, pH and Cation Exchange Capacity
The contents of volatile matter (VM) and ash were determined using the American Society for
Testing and Materials (ASTM) D5142 method [
27
]. VM content was determined as weight loss after
heating the char in a covered crucible to 950
C and holding for 7 min. Ash content was determined as
weight loss after combustion at 750
C for 6 h with no ceramic cap. Fixed C content was calculated by
the following equation:
Fixed carbon % = 100% (Ash % + Volatile matter %)
The pH of biochars was measured using a pH meter at a 1:5 solid/water ratio after shaking for
30 min. The CEC of biochar was estimated using an NH
4+
replacement method [
28
]. Brieﬂy, 0.20 g
was leached ﬁve times with 20 mL of deionized water. Then, the biochar was leached with 20 mL of
1 mol
·
L
1
Na–acetate (pH 7) ﬁve times. The biochar samples were then washed with 20 mL of ethanol
ﬁve times to remove the excess Na
+
. Afterwards, the Na
+
on the exchangeable sites of the biochar
was displaced by 20 mL of 1 mol·L1NH4–acetate (pH 7) ﬁve times, and the CEC of the biochar was
calculated from the Na+displaced by NH4+.
2.3.2. Elemental and Nutrients Analysis
A CHN Elemental Analyzer (Vario EL III, Heraeus, Germany) was used to determine the contents
of C, N and H. The O content (%) was calculated by the following equation: O (%) = 100
(C % + H %
+ N % + Ash %). The H/C and O/C ratios were also calculated. Total nutrients (K, P, Fe, Mn, Cu, Zn,
Ca and Mg) in the biochar were extracted using a wet acid digestion method (concentration HNO
3
+
30% H
2
O
2
) [
29
]. The nutrients in the digestion solution were determined using an ICAP Q ICP-MS
spectrometer (ThermoFisher, Waltham, MA, USA).
2.3.3. Surface Properties of Biochars
The surface morphology of these biochars was examined using an environmental scanning
electron microscopy (SEM) system (JEOL JSM-6360LV, Tokyo, Japan). Biochars were held onto
an adhesive carbon tape on an aluminum stub followed by sputter coating with gold prior to
viewing. The surface area and porosity of biochars were measured using a NOVA 2200e analyser
(Quantachrome Instruments, Boynton Beach, FL, USA) at liquid nitrogen temperature (77 K).
The Brunauer–Emmett–Teller (BET) surface area (S
BET
), micropore surface area (S
mic
) and micropore
volume (V
mic
), total pore volume (V
T
) of the biochars produced at different temperatures were
determined using the BET equation, t-plot method and single point adsorption total pore volume
analysis, respectively [
30
]. Fourier-transform infrared (FTIR) spectra peaks of biochars were also
obtained on pressed pellets of 1:10 biochar/KBr mixtures using a Tensor27 FTIR spectrometer (Bruker,
Karlsruhe, Germany). The spectra were obtained at 4 cm
1
resolution from 400 to 4000 cm
1
.
The amount of acidic and basic functional groups was measured by the Boehm method [31].
2.3.4. Thermal Stability Evaluation
The thermal stability evaluation of the biochars was performed by thermogravimetric analysis
(STA449F3, NETZSCH, Freistaat Bayern, Germany). Approximately 5 mg of biochar was weighed into
Energies 2017,10, 1293 4 of 15
an alumina crucible, the sample was subjected to a thermogravimetric analysis in a nitrogen ﬂow (gas
ﬂow of 50 mL·min1) at a heating rate of 10 C·min1, from 50 C to 1000 C.
2.4. Statistical Analysis of Data
All data were reported as means
±
standard deviation. The data were subjected to analysis of
variance (ANOVA) using SAS version 8.0 (SAS Institute Inc, Cary, NC, USA). The least signiﬁcant
difference (LSD, p< 0.05) test was applied to assess the differences among the means.
3. Results and Discussion
3.1. Effect of Temperature on the Basic Characteristics of Biochars
3.1.1. Proximate Analysis
Table 1presents the results of proximate analyses as a function of pyrolysis temperature. During
the pyrolysis process, the temperature kept rising and was then held at the peak temperature for 2 h
and 10 min before cooling down to room temperature. When the pyrolysis temperature increased
from 300 to 500
C, the biochar yield sharply decreased from 47.94% to 31.71%. This was probably due
to most of the lignocellulosic material was decomposed at this temperature range [
32
]. While, when
the pyrolysis temperature further increased from 500 to 600
C, the biochar yield only decreased
from 31.71% to 28.48%. This result indicated that most of the volatile fraction had been removed at
lower temperatures.
Table 1. Proximate, elemental and nutrients analysis of biochars produced at different temperatures.
Sample BC300 BC400 BC500 BC600
Proximate
analysis, dry
basis
Yeld (%) 47.94 ±1.27 a 35.49 ±1.39 b 31.73 ±1.02 c 28.48 ±0.72 d
Ash (%) 6.72 ±0.02 d 7.85 ±0.04 c 10.06 ±0.15 a 9.40 ±0.21 b
Volatile matter (%) 60.77 ±0.86 a 29.85 ±0.90 b 23.19 ±0.34 c 14.86 ±0.63 d
Fixed carbon (%) 32.50 ±0.86 d 62.30 ±0.93 c 66.75 ±0.28 b 75.73 ±0.76 a
Elemental
analysis, dry
basis
C (%) 62.20 ±0.85 d 71.13 ±2.39 c 74.88 ±2.11 b 80.01 ±4.58 a
H (%) 5.18 ±0.19 a 4.03 ±0.21 b 2.88 ±0.08 c 2.72 ±0.14 c
N (%) 1.69 ±0.08 c 1.94 ±0.06 a 1.77 ±0.08 b 1.28 ±0.06 d
O (%) 24.21 ±0.62 a 15.05 ±2.35 b 10.41 ±2.05 c 6.59 ±1.38 c
Nutrients
analysis, dry
basis
K (%) 0.57 ±0.01 c 0.89 ±0.03 b 1.10 ±0.02 a 1.14 ±0.04 a
P (%) 0.21 ±0.01 c 0.28 ±0.01 b 0.34 ±0.01 a 0.34 ±0.01 a
Ca (g·kg1)12.90 ±0.46 d 16.81 ±0.34 c 20.19 ±0.22 b 20.89 ±0.48 a
Mg (g·kg1)3.01 ±0.06 d 4.04 ±0.13 c 4.69 ±0.10 b 5.64 ±0.17 a
Fe (mg·kg1)268.35 ±6.53 d 361.62 ±8.99 c 480.52 ±10.58 b 583.50 ±5.38 a
Mn (mg·kg1)56.96 ±2.30 d 79.26 ±0.28 c 102.89 ±4.95 a 89.41 ±2.77 b
Cu (mg·kg1)20.29 ±0.45 d 50.53 ±1.96 c 85.07 ±2.27 a 58.90 ±1.22 b
Zn (mg·kg1)33.06 ±0.48 c 53.30 ±1.41 b 60.50 ±0.17 a 61.68 ±2.41 a
Note: Values in the same row followed by the same letter are not signiﬁcantly different at p< 0.05 according to
least signiﬁcant difference test. All data were reported as means
±
standard deviation (n= 3). Fixed carbon was
estimated by difference: Fixed carbon % = 100%
(Ash % + Volatile matter %). O content was estimated by
difference: O % = 100% (C% + H% + N% + Ash %).
The content of VM and ﬁxed C for the generated biochars ranged from 14.86% to 60.77% and
33.60% to 73.50%, respectively. An increase in the pyrolysis temperature decreased the content of VM,
exhibiting a similar trend with the biochar yield, while an opposite trend was found for the content of
ﬁxed C. This might due to the fact that the increasing temperature resulted in the further crack of the
volatiles fractions into low molecular weight liquids and gases instead of biochar [
33
]. Meanwhile,
the dehydration of hydroxyl groups and thermal degradation of cellulose and lignin might also
occurred with the increasing temperature [
12
]. These results conﬁrmed that the increase in temperature
enhanced the stability of biochar for the loss of volatile fractions [
34
]. It was interesting that the ash
content remarkably increased from 6.72% to 10.06% with an increase in the pyrolysis temperature from
Energies 2017,10, 1293 5 of 15
300 to 500
C. The increase in the content of ash resulted from progressive concentration of inorganic
constituents [
35
], which also was conﬁrmed by our nutrients analysis (Table 1). When pyrolysis
temperature increased from 500 to 600
C, some inorganic materials might volatilize as gas or liquid,
thus, the content of ash decreased at higher temperature (600 C).
3.1.2. Elemental and Nutrients Analysis
The elemental composition for the generated biochars changed with pyrolysis temperature
(Table 1). The C content increased from 62.20% to 80.01%, while the H and O contents decreased
from 5.18% to 2.72% and 24.21% to 6.59% as the pyrolysis temperature increased from 300 to 600
C,
respectively. These results were consistent with previous results [
36
]. The decrease in the contents of H
and O at higher temperature was likely due to the decomposition of the oxygenated bonds and release
of low molecular weight byproducts containing H and O [
15
]. Interestingly, the highest N content
was observed in BC400 (1.94%). This was attributed to the incorporation of nitrogen into complex
structures which were resistant to lower temperature and not easily volatilized [
37
]. Furthermore,
the ratios of H/C (the degree of aromaticity) [
36
] and O/C (the degree of polarity) [
38
] varied as a
function of pyrolysis temperature. In our study, the H/C and O/C ratios of biochars were signiﬁcantly
decreased from 1.00 to 0.41 and 0.29 to 0.06 with the increasing temperature, respectively (Figure 1).
The gradually reduced in the H/C and O/C atomic ratios with the increasing pyrolysis temperature
was mainly contributed to the dehydration reactions [
39
], which could be well described by the Van
Krevelen diagram (Figure 1). In addition, the H/C and O/C ratios also indicated that the structural
transformations [
36
] and surface hydrophilicity of biochar [
40
], the higher extent of carbonization and
loss of functional groups containing O and H (such as hydroxyl, carboxyl, et al.) at higher temperature
resulted in the lower ratios of H/C and O/C, indicating that the surface of biochar was more aromatic
and less hydrophilic [41,42].
Energies 2017, 10, 1293 5 of 15
materials might volatilize as gas or liquid, thus, the content of ash decreased at higher temperature
(600 °C).
3.1.2. Elemental and Nutrients Analysis
The elemental composition for the generated biochars changed with pyrolysis temperature
(Table 1). The C content increased from 62.20% to 80.01%, while the H and O contents decreased
from 5.18% to 2.72% and 24.21% to 6.59% as the pyrolysis temperature increased from 300 to 600 °C,
respectively. These results were consistent with previous results [36]. The decrease in the contents of
H and O at higher temperature was likely due to the decomposition of the oxygenated bonds and
release of low molecular weight byproducts containing H and O [15]. Interestingly, the highest N
content was observed in BC400 (1.94%). This was attributed to the incorporation of nitrogen into
complex structures which were resistant to lower temperature and not easily volatilized [37].
Furthermore, the ratios of H/C (the degree of aromaticity) [36] and O/C (the degree of polarity) [38]
varied as a function of pyrolysis temperature. In our study, the H/C and O/C ratios of biochars were
significantly decreased from 1.00 to 0.41 and 0.29 to 0.06 with the increasing temperature,
respectively (Figure 1). The gradually reduced in the H/C and O/C atomic ratios with the increasing
pyrolysis temperature was mainly contributed to the dehydration reactions [39], which could be
well described by the Van Krevelen diagram (Figure 1). In addition, the H/C and O/C ratios also
indicated that the structural transformations [36] and surface hydrophilicity of biochar [40], the
higher extent of carbonization and loss of functional groups containing O and H (such as hydroxyl,
carboxyl, et al.) at higher temperature resulted in the lower ratios of H/C and O/C, indicating that
the surface of biochar was more aromatic and less hydrophilic [41,42].
0.0 0.2 0.4 0.6
0.0
0.3
0.6
0.9
1.2
O/C atomic ratio
H/C atomi c rat io
BC600
BC500
BC400
BC300
Dehydration reactions
Figure 1. The van Krevelen plot of elemental ratios for biochars produced at different temperatures.
Thick line represents the direction for dehydration reaction. Individual points are averages (n = 3)
and error bars are standard deviations.
In addition, the nutrients K, P, Ca, Mg, Fe and Zn were also increased with increasing the
pyrolysis temperature (Table 1). While, the highest concentration of Cu (85.07 mg·kg1) and Mn
(102.89 mg·kg1) were found in BC500. Pituello et al. [43] suggested that some metals might
volatilize at high temperature. Sun et al. also found a decrease in the concentration of Ca and Mg as
the pyrolysis temperature increased from 450 to 600 °C using hickory wood as feedstock [21]. Thus,
Figure 1.
The van Krevelen plot of elemental ratios for biochars produced at different temperatures.
Thick line represents the direction for dehydration reaction. Individual points are averages (n= 3) and
error bars are standard deviations.
In addition, the nutrients K, P, Ca, Mg, Fe and Zn were also increased with increasing the
pyrolysis temperature (Table 1). While, the highest concentration of Cu (85.07 mg
·
kg
1
) and Mn
Energies 2017,10, 1293 6 of 15
(102.89 mg
·
kg
1
) were found in BC500. Pituello et al. [
43
] suggested that some metals might volatilize
at high temperature. Sun et al. also found a decrease in the concentration of Ca and Mg as the pyrolysis
temperature increased from 450 to 600
C using hickory wood as feedstock [
21
]. Thus, both the
volatility of the nutrients and the inﬂuence of temperature on the composition and chemical structure
of biochar can signiﬁcantly affect the concentration of nutrients during the process [13].
3.1.3. pH and Cation Exchange Capacity
The generated biochars were generally alkaline (pH > 7) and the pH of biochar signiﬁcant
increased from 7.48 to 11.62 when the pyrolysis temperature increased from 300 to 500
C, and then
decreased to 10.60 in BC600 (Figure 2). This was probably due to the highest ash content in BC500.
The pH values and ash content were positively correlated (R
2
= 0.97), hence, the minerals, especially
for the carbonates formation (such as CaCO
3
and MgCO
3
) and inorganic alkalis (such as K and Na),
were probably the main cause of each biochars’ inherent alkaline pH [28].
Energies 2017, 10, 1293 6 of 15
both the volatility of the nutrients and the influence of temperature on the composition and
chemical structure of biochar can significantly affect the concentration of nutrients during the
process [13].
3.1.3. pH and Cation Exchange Capacity
The generated biochars were generally alkaline (pH > 7) and the pH of biochar significant
increased from 7.48 to 11.62 when the pyrolysis temperature increased from 300 to 500 °C, and then
decreased to 10.60 in BC600 (Figure 2). This was probably due to the highest ash content in BC500.
The pH values and ash content were positively correlated (R2 = 0.97), hence, the minerals, especially
for the carbonates formation (such as CaCO3 and MgCO3) and inorganic alkalis (such as K and Na),
were probably the main cause of each biochars’ inherent alkaline pH [28].
Figure 2. The pH and cation exchange capacity (CEC) of biochars produced at different
temperatures. Individual points are averages (n = 3) and error bars are standard deviations.
CEC is an important property of biochar indicating the capacity of a biochar to adsorb cation
nutrients [20]. In our study, the CEC for the generated biochars significantly decreased from 66.59 to
18.53 cmol·kg1 when the pyrolysis temperature increased from 300 to 600 °C (Figure 2), which was
consistent with previous study [44]. The shift in CEC may due to the reduction of functional groups
and oxidation of aromatic C with temperature [34], which was well supported by the lower O/C
ratio and our FTIR and Boehm titration results at higher temperature.
3.2. Effect of Temperature on the Surface Properties of Biochars
3.2.1. Surface Morphology (Scanning Electron Microscopy Analysis)
Figure 3 shows SEM micrographs (×4000) of biochars produced at different temperatures. The
image of BC300 showed that the biomass had softened, melted and fused into a mass of vesicles
(Figure 3a) [45]. The vesicles were the result of volatile gasses released within the biomass. As
temperatures increased, more volatile gasses released from the biomass, the vesicles on the surface
of BC400 busted after cooling, thus the morphology of BC400 exhibited a number of pore structure
(Figure 3b). For the BC500, portions of the skeletal structure appeared brittle because of the
Figure 2.
The pH and cation exchange capacity (CEC) of biochars produced at different temperatures.
Individual points are averages (n= 3) and error bars are standard deviations.
CEC is an important property of biochar indicating the capacity of a biochar to adsorb cation
nutrients [
20
]. In our study, the CEC for the generated biochars signiﬁcantly decreased from 66.59 to
18.53 cmol
·
kg
1
when the pyrolysis temperature increased from 300 to 600
C (Figure 2), which was
consistent with previous study [
44
]. The shift in CEC may due to the reduction of functional groups
and oxidation of aromatic C with temperature [
34
], which was well supported by the lower O/C ratio
and our FTIR and Boehm titration results at higher temperature.
3.2. Effect of Temperature on the Surface Properties of Biochars
3.2.1. Surface Morphology (Scanning Electron Microscopy Analysis)
Figure 3shows SEM micrographs (
×
4000) of biochars produced at different temperatures. The image
of BC300 showed that the biomass had softened, melted and fused into a mass of vesicles (Figure 3a) [
45
].
The vesicles were the result of volatile gasses released within the biomass. As temperatures increased, more
Energies 2017,10, 1293 7 of 15
volatile gasses released from the biomass, the vesicles on the surface of BC400 busted after cooling, thus
the morphology of BC400 exhibited a number of pore structure (Figure 3b). For the BC500, portions of the
skeletal structure appeared brittle because of the decomposition of more components (Figure 3c, ellipse).
The fracture phenomenon also appeared within the pore structure for the BC600, the last temperature that
samples were collected (Figure 3d, ellipse).
Figure 3.
Scanning electron microscopy (SEM) micrographs (magniﬁcation 4000
×
) of biochars samples
pyrolyzed at: (a) 300 C; (b) 400 C; (c) 500 C; and (d) 600 C, respectively.
3.2.2. Surface Area and Pore Volume
The surface area and pore volumes produced at various pyrolysis temperatures were obtained
by N
2
adsorption and the results shown in Table 2. An increase in the pyrolysis temperature from
300 to 600
C resulted in a signiﬁcant increase in the S
BET
from 2.39 m
2·
g
1
to 108.59 m
2·
g
1
and in
the V
T
from 2.56
×
10
3
cm
3·
g
1
to 58.54
×
10
3
cm
3·
g
1
. In the same way, S
mic
and V
mic
signiﬁcant
increased from 0.10 m
2·
g
1
and 0.13
×
10
3
cm
3·
g
1
at 300
C to 84.44 m
2·
g
1
and 37.87
×
10
3
cm
3·
g
1
at 600
C, respectively. This evolution is somewhat similar to that reported in the literature [
15
].
The increase in the surface area and pore volumes might be caused by the progressive degradation of
the organic materials (hemicelluloses, cellulose and lignin) and the formation of vascular bundles or
channel structures during pyrolysis during the process [
46
,
47
]. Hemicellulose has a high reactivity
during thermal treatment at lower temperature (usually under 300 C).
Table 2. Surface area and pore volumes of biochars produced at different temperatures.
Sample BC300 BC400 BC500 BC600
SBET (m2·g1)2.39 ±0.12 d 7.00 ±0.25 c 37.24 ±0.80 b 108.59 ±4.11 a
Smic (m2·g1)0.10 ±0.01 d 1.47 ±0.01 c 9.33 ±0.73 b 84.44 ±6.76 a
VT(103·cm3·g1)2.56 ±0.25 d 6.52 ±0.64 c 12.41 ±0.32 b 58.54 ±3.44 a
Vmic (103·cm3·g1)0.13 ±0.01 d 0.52 ±0.03 c 1.58 ±0.10 b 37.87 ±0.91 a
Note: Values in a row followed by the same letter are not signiﬁcantly different at p< 0.05 according to LSD test.
All data were reported as means
±
standard deviation (n= 3). S
BET
,S
mic
,V
T
and V
mic
were the BET surface area,
micropore surface area, total pore volume and micropore volume, respectively.
Energies 2017,10, 1293 8 of 15
The presence of vesicles at BC300 also indicated that volatile components were formed and
released (Figure 3a). When the pyrolysis temperature increased from 300 to 400
C, the rupture of
the hemicellulose along with other organic compounds generated more micropores within biochar
(Figure 3b) [
48
], thus, an increase in the surface area and pore volumes was found in BC400. Meanwhile,
some amorphous carbon structures were formed during this temperature range due to the degradation
of cellulose. Several researchers suggested that the micropores may be formed by amorphous carbon
structures [
49
]. The increase in the biochar porosity was found in BC500 due to the decomposition
of lignin and the quick release of H
2
and CH
4
as the temperature increased up to 500
C (Figure 3c).
This result contributed to a sharp increase of the surface area and pore volumes (Table 2) [
18
]. Further
increases in the temperature to 600
C resulting in a dramatic increase in S
BET
and V
T
, especially for
the S
mic
and V
mic
. This was mostly contributed to the further degradation of lignin and the reaction
of aromatic condensation [
30
], which increased the release of VM (Table 1) and created more pores
(Figure 3d) [
18
]. The enhancement of the pore development at a higher temperature suggesting that
the increase of SBET and VTmostly dependent on the increase of the Smic and Vmic.
3.2.3. Fourier-Transform Infrared Analysis and Functional Groups
The FTIR spectra of biochars produced at four pyrolysis temperatures are presented in Figure 4
and the descriptions for peak assignments are provided in Table 3. As the pyrolysis temperature
increased, FTIR spectra of biochars revealed a decrease in the stretching of O–H (3200–3500 cm
1
)
and C–H (2935 cm
1
) [
13
], this was attributed to the acceleration of dehydration reaction in
biomass [
30
], which suggested a decrease in the polar functional groups with an increase in pyrolysis
temperature [
50
]. In particular, biochars began to increase aromatic C=C stretching (1440 cm
1
) [
29
]
and out-of-plane deformation by aromatic C–H groups (885 cm
1
) [
51
], while the symmetric C–O
stretching (1030–1110 cm
1
) for the source material began to disappear with the increasing pyrolysis
temperature [51].
Energies 2017, 10, 1293 8 of 15
Meanwhile, some amorphous carbon structures were formed during this temperature range due to
the degradation of cellulose. Several researchers suggested that the micropores may be formed by
amorphous carbon structures [49]. The increase in the biochar porosity was found in BC500 due to
the decomposition of lignin and the quick release of H2 and CH4 as the temperature increased up to
500 °C (Figure 3c). This result contributed to a sharp increase of the surface area and pore volumes
(Table 2) [18]. Further increases in the temperature to 600 °C resulting in a dramatic increase in SBET
and VT, especially for the Smic and Vmic. This was mostly contributed to the further degradation of
lignin and the reaction of aromatic condensation [30], which increased the release of VM (Table 1)
and created more pores (Figure 3d) [18]. The enhancement of the pore development at a higher
temperature suggesting that the increase of SBET and VT mostly dependent on the increase of the Smic
and Vmic.
3.2.3. Fourier-Transform Infrared Analysis and Functional Groups
The FTIR spectra of biochars produced at four pyrolysis temperatures are presented in Figure
4 and the descriptions for peak assignments are provided in Table 3. As the pyrolysis temperature
increased, FTIR spectra of biochars revealed a decrease in the stretching of O–H (3200–3500 cm1)
and C–H (2935 cm1) [13], this was attributed to the acceleration of dehydration reaction in biomass
[30], which suggested a decrease in the polar functional groups with an increase in pyrolysis
temperature [50]. In particular, biochars began to increase aromatic C=C stretching (1440 cm1) [29]
and out-of-plane deformation by aromatic C–H groups (885 cm1) [51], while the symmetric C–O
stretching (1030–1110 cm1) for the source material began to disappear with the increasing pyrolysis
temperature [51].
Figure 4. Fourier-transform infrared (FTIR) spectra peaks of biochars produced at: (a) 300 °C; (b) 400
°C; (c) 500 °C; and (d) 600 °C, respectively.
Figure 4.
Fourier-transform infrared (FTIR) spectra peaks of biochars produced at: (
a
) 300
C; (
b
) 400
C;
(c) 500 C; and (d) 600 C, respectively.
Energies 2017,10, 1293 9 of 15
Table 3.
Functional groups observed in the Fourier-transform infrared (FTIR) spectra of biocahrs
produced at different temperatures.
Wave Numbers (cm1)Characteristic Vibrations (Functionality)
3500–3200 O–H stretching (water, hydrogen-bonded hydroxyl) [13]
2935 C–H stretching (aliphatic CHx; 2935-asymmetric) [13]
1600
Aromatic C=C and C=O stretching of conjugated ketones and quinones [
52
]
1440 C=C stretching (lignin carbohydrate) [29]
1325 O–H bending (phenols, phenolic; ligneous syringyl) [29]
1100–1030 Symmetric C–O stretching (cellulose, hemicellulose, and lignin) [51]
885 C–H bending (aromatic C–H out-of-plane deformation) [51]
781 Pyridine (pyridine ring vibration and C–H deformation) [53]
This result is likely due to the degradation and depolymerization of cellulose, hemicelluloses
and lignin [
29
]. Instead, intensities of O–H (1325 cm
1
) stretching [
29
] and aromatic C=C and C=O
stretching of conjugated ketones and quinones (1600 cm
1
) [
52
] decreased with temperature which
may suggest that phenolic and carboxylic compounds in lignin had been degraded [
54
]. There was
also pyridine in biochars (781 cm
1
) [
53
], which was one of the heterocyclic nitrogen compounds
commonly observed during pyrolysis [
55
]. In general, the maximum loss was obtained in –OH, –CH
2
,
and C–O functional groups in biochars as a function of pyrolysis temperature, which was also apparent
from their elemental composition (Table 1). Relatively low values of O, H, and H/C in BC600 than
those in BC300 revealed the signiﬁcant elimination of polar functional groups (–OH and C–O).
Different spectra reﬂected changes in the surface functional groups of biochars produced at
different temperatures. A Boehm titration method was used to quantify the surface functional groups of
biochars produced at different temperatures. The results showed that when the pyrolysis temperature
increased from 300 to 600
C the concentration of total acidic functional groups, surface carboxylic
functional groups, surface phenolic functional groups and surface lactonic functional groups decreased
from 1.16 to 0.44 mmol
·
g
1
, 0.49 to 0.23 mmol
·
g
1
, 0.33 to 0.09 mmol
·
g
1
and 0.34 to 0.13 mmol
·
g
1
,
respectively (Figure 5). This result was in agreement with the ﬁndings in previous studies [
56
,
57
].
During the pyrolysis process, organic materials were converted to water and carbonaceous gas, thus,
the higher temperature caused an increased in the quantity of volatile compounds resulting in a
decrease in the content of acidic groups [
18
], which was well supported by our FTIR results. It was
interesting that the total acidic and carboxylic functional groups signiﬁcant decreased with increasing
temperatures (p< 0.05), whereas the temperature trend for phenolic and lactonic functional groups
content were less apparent (Figure 5). This was probably due to the fact carboxylic acids represented
48.63% of total acidic functional groups, on average, and were 1.5–2.5 times more abundant than
phenolic or lactonic functional groups. This result is similar to the one reported in the literature [
15
].
While, the total basic functional groups signiﬁcant increased from 0.11 to 0.32 mmol
·
g
1
when the
pyrolysis temperature increased from 300 to 500
C and then decreased to 0.22 mmol
·
g
1
at 600
C.
The strong direct linear correlation between ash fraction and basic groups (R
2
= 0.66) suggest that the
basic functional groups are mainly associated with the ash fraction [
15
], which also implied the highest
content of basic groups in BC500 (Figure 5and Table 1).
Energies 2017,10, 1293 10 of 15
Energies 2017, 10, 1293 10 of 15
Figure 5. Variation in surface functional groups as a function of pyrolysis temperature. Individual
points are averages (n = 3) and error bars are standard deviations.
3.3. Effect of Temperature on the Thermal Stability of Biochars
Representative thermogravimetric (TG) analysis and differential thermogravimetry (DTG)
curves for both biochars are presented in Figure 6. During the process, two stages of weight losses
were observed (Figure 6a), which was also implied by the DTG curves (Figure 6b). The mass loss
occurred slowly under 200 °C and varied from 0.77% to 2.86% (Figure 6a; maximum at around 80
°C, Figure 6b) (under 200 °C), suggesting that this reduction in mass loss commonly associated with
the loss of the initial moisture of the sample [58]. Above that, the main mass losses started at around
315 °C, 388 °C, 499 °C and 517 °C for BC300, BC400, BC500 and BC600, respectively. Meanwhile, a
sharp weight decrease took place between 313 °C and 500 °C, 388 °C and 644 °C, 499 °C and 738 °C,
517 °C and 753 °C (Figure 6a) in the BC300, BC400, BC500 and BC600, respectively. This was
probably due to the fact the generated biochars had undergone a previous heat treatment before the
thermal analysis, thus, the tested biochar samples were thermally stable below the temperature
which they were produced [59]. For each of the tested biochar, only one peak was found during the
temperature range between the temperature they were produced and 1000 °C on the DTG curves
(Figure 6b). It is known that secondary pyrolysis reactions could be easily detected and observed if
the temperature exceeding the biochars’ primary decomposition temperature [58]. Thus, the weight
loss over a wider temperature range could be attributed to the degradation and decomposition of
organic materials [21]. The maximum weight loss occurred at around 352 °C, 388 °C, 658 °C and 674
°C for BC300, BC400, BC500 and BC600 (Figure 6b), respectively, suggesting that the higher the
pyrolysis temperature was, the better thermal stability the biochar showed, which is consistent with
the literature [60]. The lower temperature derived biochars were less thermally stable than the
higher temperature derived biochars, probably because they were not fully carbonized [21]. Above
600–700 °C, decomposition for all the biochars finished, and the curves became stable. It was
interesting that the total weight losses resulting from thermal degradation were 52.19%, 33.32%,
23.80% and 27.27% for BC300, BC400, BC500 and BC600, respectively. This was probably because
Figure 5.
Variation in surface functional groups as a function of pyrolysis temperature. Individual
points are averages (n= 3) and error bars are standard deviations.
3.3. Effect of Temperature on the Thermal Stability of Biochars
Representative thermogravimetric (TG) analysis and differential thermogravimetry (DTG) curves
for both biochars are presented in Figure 6. During the process, two stages of weight losses were
observed (Figure 6a), which was also implied by the DTG curves (Figure 6b). The mass loss occurred
slowly under 200
C and varied from 0.77% to 2.86% (Figure 6a; maximum at around 80
C, Figure 6b)
(under 200
C), suggesting that this reduction in mass loss commonly associated with the loss of
the initial moisture of the sample [
58
]. Above that, the main mass losses started at around 315
C,
388
C, 499
C and 517
C for BC300, BC400, BC500 and BC600, respectively. Meanwhile, a sharp
weight decrease took place between 313
C and 500
C, 388
C and 644
C, 499
C and 738
C, 517
C
and 753
C (Figure 6a) in the BC300, BC400, BC500 and BC600, respectively. This was probably
due to the fact the generated biochars had undergone a previous heat treatment before the thermal
analysis, thus, the tested biochar samples were thermally stable below the temperature which they
were produced [
59
]. For each of the tested biochar, only one peak was found during the temperature
range between the temperature they were produced and 1000
C on the DTG curves (Figure 6b). It is
known that secondary pyrolysis reactions could be easily detected and observed if the temperature
exceeding the biochars’ primary decomposition temperature [58]. Thus, the weight loss over a wider
temperature range could be attributed to the degradation and decomposition of organic materials [
21
].
The maximum weight loss occurred at around 352
C, 388
C, 658
C and 674
C for BC300, BC400,
BC500 and BC600 (Figure 6b), respectively, suggesting that the higher the pyrolysis temperature was,
the better thermal stability the biochar showed, which is consistent with the literature [
60
]. The lower
temperature derived biochars were less thermally stable than the higher temperature derived biochars,
probably because they were not fully carbonized [
21
]. Above 600–700
C, decomposition for all the
biochars ﬁnished, and the curves became stable. It was interesting that the total weight losses resulting
from thermal degradation were 52.19%, 33.32%, 23.80% and 27.27% for BC300, BC400, BC500 and
BC600, respectively. This was probably because BC500 had highest ash content.
Energies 2017,10, 1293 11 of 15
Energies 2017, 10, 1293 11 of 15
Figure 6. Thermogravimetric (TG). (a) Differential thermogravimetry (DTG); and (b) curves of
biochars produced at 300 °C, 400 °C, 500 °C and 600 °C, respectively.
3.3. Implications for Environmental and Agronomic Management
Biochar is a carbon-rich product and its addition to soil has been proposed as an effective
method for C sequestration [61]. However, the ultimate C sequestration efficiency of biochar mainly
depend on its stability, which is mainly effect by the production conditions including pyrolysis
temperature [37]. Lehmann et al. suggested that a biochar can be used as an effective C
sequestration agents in case its O:C and H:C ratios less than 0.4 and 0.6, respectively [62]. Based on
the results, ATB biochars produced at higher temperatures (>400 °C) with H/C of 0.46–0.41 and O/C
of 0.10–0.06, may exhibit a high C sequestration potential. Thus, biochars produced at higher
temperatures (>400 °C) could be more resistant to mineralization than those pyrolyzed at lower
temperature (400 °C), thus representing an efficient technique for mitigating greenhouse gas
emissions into the environment. In addition, biochars produced at higher temperatures may prove
beneficial for use as fertilizer due to their concentrations of minerals like K and Na. However, our
results also show that higher pyrolysis temperatures also have the potential of accumulating heavy
metals, which can cause soil pollution. Biochars from pyrolysis processes are usually alkaline in
nature, especially for the biochars produced at higher pyrolysis temperatures. Therefore, the
application of these higher temperature biochars can be useful to increase the pH of acidic soils,
which are in risk of aluminum toxicity [63]. In contrast, the application of these higher temperature
biochars to arid soils may be critical of concern due to their high salinity and alkalinity. While,
compared with the higher temperature biochars, ATB biochars produced at the lower pyrolysis
temperature (400 °C) have more organic functional groups on their surface, high cation exchange
capacity, lower pH values as well as less aromatic content. Thus, the ATB biochars produced at the
lower pyrolysis temperature (400 °C) may be used to enhance the soil nutrient exchange sites as
well as soil cation exchange capacity when they are applied to arid soils.
4. Conclusions
The structural and physicochemical properties of biochar derived from ATBs change with
pyrolysis temperature. The results show that yield, VM, CEC and H and O were decreased with
increasing pyrolysis temperature, whereas total C, fixed C, BET surface area, pore volumes and
inorganic minerals (except for Cu and Mn) concentrations increased with the increase in pyrolysis
Figure 6.
Thermogravimetric (TG). (
a
) Differential thermogravimetry (DTG); and (
b
) curves of biochars
produced at 300 C, 400 C, 500 C and 600 C, respectively.
3.4. Implications for Environmental and Agronomic Management
Biochar is a carbon-rich product and its addition to soil has been proposed as an effective method
for C sequestration [
61
]. However, the ultimate C sequestration efﬁciency of biochar mainly depend on
its stability, which is mainly effect by the production conditions including pyrolysis temperature [
37
].
Lehmann et al. suggested that a biochar can be used as an effective C sequestration agents in case its
O:C and H:C ratios less than 0.4 and 0.6, respectively [
62
]. Based on the results, ATB biochars produced
at higher temperatures (>400
C) with H/C of 0.46–0.41 and O/C of 0.10–0.06, may exhibit a high C
sequestration potential. Thus, biochars produced at higher temperatures (>400
C) could be more
resistant to mineralization than those pyrolyzed at lower temperature (
400
C), thus representing an
efﬁcient technique for mitigating greenhouse gas emissions into the environment. In addition, biochars
produced at higher temperatures may prove beneﬁcial for use as fertilizer due to their concentrations
of minerals like K and Na. However, our results also show that higher pyrolysis temperatures also have
the potential of accumulating heavy metals, which can cause soil pollution. Biochars from pyrolysis
processes are usually alkaline in nature, especially for the biochars produced at higher pyrolysis
temperatures. Therefore, the application of these higher temperature biochars can be useful to increase
the pH of acidic soils, which are in risk of aluminum toxicity [
63
]. In contrast, the application of these
higher temperature biochars to arid soils may be critical of concern due to their high salinity and
alkalinity. While, compared with the higher temperature biochars, ATB biochars produced at the lower
pyrolysis temperature (
400
C) have more organic functional groups on their surface, high cation
exchange capacity, lower pH values as well as less aromatic content. Thus, the ATB biochars produced
at the lower pyrolysis temperature (
400
C) may be used to enhance the soil nutrient exchange sites
as well as soil cation exchange capacity when they are applied to arid soils.
4. Conclusions
The structural and physicochemical properties of biochar derived from ATBs change with
pyrolysis temperature. The results show that yield, VM, CEC and H and O were decreased with
Energies 2017,10, 1293 12 of 15
increasing pyrolysis temperature, whereas total C, ﬁxed C, BET surface area, pore volumes and
inorganic minerals (except for Cu and Mn) concentrations increased with the increase in pyrolysis
temperature. The pH and ash content increased as temperature increased up to 500
C and decreased at
higher temperature. The increasing temperature also decreased the acidic functional groups, especially
for the carboxylic functional groups. While, reverse trend was found for the basic functional groups
of biochars. In general, higher temperatures (>400
C) biochars possessing predominately aromatic
carbon structures and highly thermal stability, which can be useful to help mitigate climate change,
while, lower temperature (
400
C) biochars having more functional groups as well as relatively
low pH values may be more suitable for improving the fertility of high pH soils in arid regions.
Consequently different ATB biochars can be produced by changing the pyrolysis temperature in order
to better meet speciﬁc application needs.
Acknowledgments:
This research was supported by the National Key Technology R&D Program of the Ministry
of Science and Technology, China (2012BAD14B11), and the Special Fund for Agro-Scientiﬁc Research in the Public
Interest of the Ministry of Agriculture, China (201503116).
Author Contributions:
All authors conceived, designed and performed the experiment. Xu-Dong Wang provided
technical and theoretical support; Na Ta contributed to the analysis of experimental results; Shi-Xiang Zhao wrote
the paper and all authors read and approved the ﬁnal version.
Conﬂicts of Interest: The authors declare no conﬂicts of interest.
Abbreviations
C Carbon
N Nitrogen
H Hydrogen
O Oxygen
CEC Cation exchange capacity
ATB Apple tree branch
VM Volatile matter
SEM Scanning electron microscopy
BET Brunauer-Emmett-Teller
SBET BET surface area
Smic Micropore surface area;
VTTotal pore volume
Vmic Micropore volume
FTIR Fourier-transform infrared
TG Thermogravimetric
DTG Differential thermogravime
References
1.
Zhao, R.; Coles, N.; Wu, J. Carbon mineralization following additions of fresh and aged biochar to an
infertile soil. Catena 2015,125, 183–189. [CrossRef]
2.
Purakayastha, T.J.; Das, K.C.; Gaskin, J.; Harris, K.; Smith, J.L.; Kumari, S. Effect of pyrolysis temperatures
on stability and priming effects of C3 and C4 biochars applied to two different soils. Soil Tillage Res.
2016
,
155, 107–115. [CrossRef]
3.
Smith, J.L.; Collins, H.P.; Bailey, V.L. The effect of young biochar on soil respiration. Soil Biol. Biochem.
2010
,
42, 2345–2347. [CrossRef]
4.
Abujabhah, I.S.; Bound, S.A.; Doyle, R.; Bowman, J.P. Effects of biochar and compost amendments on soil
physico-chemical properties and the total community within a temperate agricultural soil. Appl. Soil Ecol.
2016,98, 243–253. [CrossRef]
5.
Partey, S.T.; Saito, K.; Preziosi, R.F.; Robson, G.D. Biochar use in a legume–rice rotation system: Effects on
soil fertility and crop performance. Arch. Agron. Soil Sci. 2015,62, 199–215. [CrossRef]
Energies 2017,10, 1293 13 of 15
6.
Zhou, J.; Chen, H.; Huang, W.; Arocena, J.M.; Ge, S. Sorption of Atrazine, 17
α
on Wheat Straw and Peanut Shell Biochars. Water Air Soil Pollut. 2016,227, 7. [CrossRef]
7.
Venegas, A.; Rigol, A.; Vidal, M. Changes in heavy metal extractability from contaminated soils remediated
with organic waste or biochar. Geoderma 2016,279, 132–140. [CrossRef]
8.
Angin, D.; Sensöz, S. Effect of pyrolysis temperature on chemical and surface properties of biochar of
rapeseed (Brassica napus L.). Int. J. Phytoremed. 2014,16, 684–693. [CrossRef] [PubMed]
9.
Roberts, D.A.; De, N.R. The effects of feedstock pre-treatment and pyrolysis temperature on the production
of biochar from the green seaweed Ulva.J. Environ. Manag. 2016,169, 253–260. [CrossRef] [PubMed]
10.
Yang, X.; Wang, H.; Strong, P.; Xu, S.; Liu, S.; Lu, K.; Sheng, K.; Guo, J.; Che, L.; He, L. Thermal Properties of
Biochars Derived from Waste Biomass Generated by Agricultural and Forestry Sectors. Energies
2017
,10, 469.
[CrossRef]
11.
Jouiad, M.; Al-Nofeli, N.; Khalifa, N.; Benyettou, F.; Yousef, L.F. Characteristics of slow pyrolysis biochars
produced from rhodes grass and fronds of edible date palm. J. Anal. Appl. Pyrolysis
2015
,111, 183–190.
[CrossRef]
12.
Zhang, J.; Liu, J.; Liu, R. Effects of pyrolysis temperature and heating time on biochar obtained from the
pyrolysis of straw and lignosulfonate. Bioresour. Technol. 2015,176, 288–291. [CrossRef] [PubMed]
13.
Claoston, N.; Samsuri, A.W.; Ahmad Husni, M.H.; Mohd Amran, M.S. Effects of pyrolysis temperature on
the physicochemical properties of empty fruit bunch and rice husk biochars. Waste Manag. Res.
2014
,32,
331–339. [CrossRef] [PubMed]
14.
Bouraoui, Z.; Jeguirim, M.; Guizani, C.; Limousy, L.; Dupont, C.; Gadiou, R. Thermogravimetric study on
the inﬂuence of structural, textural and chemical properties of biomass chars on CO
2
gasiﬁcation reactivity.
Energy 2015,88, 703–710. [CrossRef]
15.
Suliman, W.; Harsh, J.B.; Abu-Lail, N.I.; Fortuna, A.M.; Dallmeyer, I.; Garcia-Perez, M. Inﬂuence of feedstock
source and pyrolysis temperature on biochar bulk and surface properties. Biomass Bioenergy
2016
,84, 37–48.
[CrossRef]
16.
Xu, Y.; Chen, B. Investigation of thermodynamic parameters in the pyrolysis conversion of biomass and
manure to biochars using thermogravimetric analysis. Bioresour. Technol.
2013
,146, 485–493. [CrossRef]
[PubMed]
17.
Guizani, C.; Jeguirim, M.; Valin, S.; Limousy, L.; Salvador, S. Biomass Chars: The Effects of Pyrolysis
Conditions on Their Morphology, Structure, Chemical Properties and Reactivity. Energies
2017
,10, 796.
[CrossRef]
18.
Shaaban, A.; Se, S.-M.; Dimin, M.F.; Juoi, J.M.; Mohd Husin, M.H.; Mitan, N.M.M. Inﬂuence of heating
temperature and holding time on biochars derived from rubber wood sawdust via slow pyrolysis. J. Anal.
Appl. Pyrolysis 2014,107, 31–39. [CrossRef]
19.
Liang, C.F.; Gasco, G.; Fu, S.L.; Mendez, A.; Paz-Ferreiro, J. Biochar from pruning residues as a soil
amendment: Effects of pyrolysis temperature and particle size. Soil Tillage Res. 2016,164, 3–10. [CrossRef]
20.
Tag, A.T.; Duman, G.; Ucar, S.; Yanik, J. Effects of feedstock type and pyrolysis temperature on potential
applications of biochar. J. Anal. Appl. Pyrolysis 2016,120, 200–206. [CrossRef]
21.
Sun, Y.N.; Gao, B.; Yao, Y.; Fang, J.N.; Zhang, M.; Zhou, Y.M.; Chen, H.; Yang, L.Y. Effects of feedstock type,
production method, and pyrolysis temperature on biochar and hydrochar properties. Chem. Eng. J.
2014
,
240, 574–578. [CrossRef]
22.
Brassard, P.; Godbout, S.; Raghavan, V.; Palacios, J.H.; Grenier, M.; Dan, Z. The Production of Engineered
Biochars in a Vertical Auger Pyrolysis Reactor for Carbon Sequestration. Energies 2017,10, 288. [CrossRef]
23.
Colantoni, A.; Zambon, I.; Colosimo, F.; Monarca, D.; Cecchini, M.; Gallucci, F.; Proto, A.R.; Lord, R.
An Innovative Agro-Forestry Supply Chain for Residual Biomass: Physicochemical Characterisation of
Biochar from Olive and Hazelnut Pellets. Energies 2016,9, 526. [CrossRef]
24.
Fang, K.; Li, H.; Wang, Z.; Du, Y.; Wang, J. Comparative analysis on spatial variability of soil moisture under
different land use types in orchard. Sci. Hortic. 2016,207, 65–72. [CrossRef]
25.
Bai, S.H.; Reverchon, F.; Xu, C.-Y.; Xu, Z.; Blumﬁeld, T.J.; Zhao, H.; Van Zwieten, L.; Wallace, H.M. Wood
biochar increases nitrogen retention in ﬁeld settings mainly through abiotic processes. Soil Biol. Biochem.
2015,90, 232–240. [CrossRef]
Energies 2017,10, 1293 14 of 15
26.
Eyles, A.; Bound, S.A.; Oliver, G.; Corkrey, R.; Hardie, M.; Green, S.; Close, D.C. Impact of biochar amendment
on the growth, physiology and fruit of a young commercial apple orchard. Trees
2015
,29, 1817–1826.
[CrossRef]
27.
ASTM International. D5142, Standard Test Methods for Proximate Analysis of the Analysis Sample of Coal
and Coke by Instrumental Procedures. In American Society for Testing and Materials; ASTM International:
West Conshohocken, PA, USA, 2009.
28.
Yuan, J.H.; Xu, R.K.; Zhang, H. The forms of alkalis in the biochar produced from crop residues at different
temperatures. Bioresour. Technol. 2011,102, 3488–3497. [CrossRef] [PubMed]
29.
Cantrell, K.B.; Hunt, P.G.; Uchimiya, M.; Novak, J.M.; Ro, K.S. Impact of pyrolysis temperature and manure
source on physicochemical characteristics of biochar. Bioresour. Technol.
2012
,107, 419–428. [CrossRef]
[PubMed]
30.
Chen, Y.; Yang, H.; Wang, X.; Zhang, S.; Chen, H. Biomass-based pyrolytic polygeneration system on cotton
stalk pyrolysis: Inﬂuence of temperature. Bioresour. Technol. 2012,107, 411–418. [CrossRef] [PubMed]
31.
Boehm, H.P. Some aspects of the surface chemistry of carbon blacks and other carbons. Carbon
1994
,32,
759–769. [CrossRef]
32.
Intani, K.; Latif, S.; Kabir, A.K.M.R.; Müller, J. Effect of self-purging pyrolysis on yield of biochar from maize
cobs, husks and leaves. Bioresour. Technol. 2016,218, 541–551. [CrossRef] [PubMed]
33.
Ronsse, F.; Hecke, S.V.; Dickinson, D.; Prins, W. Production and characterization of slow pyrolysis biochar:
Inﬂuence of feedstock type and pyrolysis conditions. Glob. Chang. Biol. Bioenergy
2013
,5, 104–115. [CrossRef]
34.
Zornoza, R.; Moreno-Barriga, F.; Acosta, J.A.; Muñoz, M.A.; Faz, A. Stability, nutrient availability and
hydrophobicity of biochars derived from manure, crop residues, and municipal solid waste for their use as
soil amendments. Chemosphere 2016,144, 122–130. [CrossRef] [PubMed]
35.
Chen, T.; Zhang, Y.; Wang, H.; Lu, W.; Zhou, Z.; Zhang, Y.; Ren, L. Inﬂuence of pyrolysis temperature on
characteristics and heavy metal adsorptive performance of biochar derived from municipal sewage sludge.
Bioresour. Technol. 2014,164, 47–54. [CrossRef] [PubMed]
36.
Wang, X.; Zhou, W.; Liang, G.; Song, D.; Zhang, X. Characteristics of maize biochar with different
pyrolysis temperatures and its effects on organic carbon, nitrogen and enzymatic activities after addition to
ﬂuvo-aquic soil. Sci. Total Environ. 2015,538, 137–144. [CrossRef] [PubMed]
37.
Usman, A.R.A.; Abduljabbar, A.; Vithanage, M.; Ok, Y.S.; Ahmad, M.; Ahmad, M.; Elfaki, J.; Abdulazeem, S.S.;
Al-Wabel, M.I. Biochar production from date palm waste: Charring temperature induced changes in
composition and surface chemistry. J. Anal. Appl. Pyrolysis 2015,115, 392–400. [CrossRef]
38.
Zhang, J.N.; Lu, F.; Luo, C.H.; Shao, L.M.; He, P.J. Humiﬁcation characterization of biochar and its potential
as a composting amendment. J. Environ. Sci. 2014,26, 390–397. [CrossRef]
39.
Li, X.; Shen, Q.; Zhang, D.; Mei, X.; Ran, W.; Xu, Y.; Yu, G. Functional Groups Determine Biochar Properties
(pH and EC) as Studied by Two-Dimensional
13
C NMR Correlation Spectroscopy. PLoS ONE
2013
,8, e65949.
[CrossRef] [PubMed]
40.
Tan, X.; Liu, Y.; Zeng, G.; Wang, X.; Hu, X.; Gu, Y.; Yang, Z. Application of biochar for the removal of
pollutants from aqueous solutions. Chemosphere 2015,125, 70–85. [CrossRef] [PubMed]
41.
Keiluweit, M.; Nico, P.S.; Johnson, M.G.; Kleber, M. Dynamic molecular structure of plant biomass-derived
black carbon (biochar). Environ. Sci. Technol. 2010,44, 1247–1253. [CrossRef] [PubMed]
42.
Chen, X.; Chen, G.; Chen, L.; Chen, Y.; Lehmann, J.; McBride, M.B.; Hay, A.G. Adsorption of copper and zinc
by biochars produced from pyrolysis of hardwood and corn straw in aqueous solution. Bioresour. Technol.
2011,102, 8877–8884. [CrossRef] [PubMed]
43.
Pituello, C.; Francioso, O.; Simonetti, G.; Pisi, A.; Torreggiani, A.; Berti, A.; Morari, F. Characterization of
chemical–physical, structural and morphological properties of biochars from biowastes produced at
different temperatures. J. Soils Sediments 2015,15, 792–804. [CrossRef]
44.
Phuong, H.T.; Uddin, M.A.; Kato, Y. Characterization of Biochar from Pyrolysis of Rice Husk and Rice Straw.
J. Biobased Mater. Bioenergy 2015,9, 439–446. [CrossRef]
45.
Sharma, R.K.; Wooten, J.B.; Baliga, V.L.; Lin, X.; Geoffrey Chan, W.; Hajaligol, M.R. Characterization of chars
from pyrolysis of lignin. Fuel 2004,83, 1469–1482. [CrossRef]
46.
Kim, W.K.; Shim, T.; Kim, Y.S.; Hyun, S.; Ryu, C.; Park, Y.K.; Jung, J. Characterization of cadmium removal
from aqueous solution by biochar produced from a giant Miscanthus at different pyrolytic temperatures.
Bioresour. Technol. 2013,138, 266–270. [CrossRef] [PubMed]
Energies 2017,10, 1293 15 of 15
47.
Li, M.; Liu, Q.; Guo, L.; Zhang, Y.; Lou, Z.; Wang, Y.; Qian, G. Cu(II) removal from aqueous solution by
Spartina alterniﬂora derived biochar. Bioresour. Technol. 2013,141, 83–88. [CrossRef] [PubMed]
48.
Jeong, C.Y.; Dodla, S.K.; Wang, J.J. Fundamental and molecular composition characteristics of biochars
produced from sugarcane and rice crop residues and by-products. Chemosphere
2016
,142, 4–13. [CrossRef]
[PubMed]
49.
Vamvuka, D.; Sfakiotakis, S. Effects of heating rate and water leaching of perennial energy crops on pyrolysis
characteristics and kinetics. Renew. Energy 2011,36, 2433–2439. [CrossRef]
50.
Zhou, L.; Liu, Y.; Liu, S.; Yin, Y.; Zeng, G.; Tan, X.; Hu, X.; Hu, X.; Jiang, L.; Ding, Y.; et al.
Investigation of the adsorption-reduction mechanisms of hexavalent chromium by ramie biochars of different
pyrolytic temperatures. Bioresour. Technol. 2016,218, 351–359. [CrossRef] [PubMed]
51.
Ahmad, M.; Lee, S.S.; Dou, X.; Mohan, D.; Sung, J.K.; Yang, J.E.; Ok, Y.S. Effects of pyrolysis temperature on
soybean stover- and peanut shell-derived biochar properties and TCE adsorption in water. Bioresour. Technol.
2012,118, 536–544. [CrossRef] [PubMed]
52.
Uchimiya, M.; Wartelle, L.H.; Klasson, K.T.; Fortier, C.A.; Lima, I.M. Inﬂuence of pyrolysis temperature on
biochar property and function as a heavy metal sorbent in soil. J. Agric. Food Chem.
2011
,59, 2501–2510.
[CrossRef] [PubMed]
53.
Das, D.D.; Schnitzer, M.I.; Monreal, C.M.; Mayer, P. Chemical composition of acid–base fractions separated
from biooil derived by fast pyrolysis of chicken manure. Bioresour. Technol.
2009
,100, 6524–6532. [CrossRef]
[PubMed]
54.
Souza, B.S.; Moreira, A.P.D.; Teixeira, A.M.R.F. TG-FTIR coupling to monitor the pyrolysis products from
agricultural residues. J. Therm. Anal. Calorim. 2009,97, 637–642. [CrossRef]
55.
Kazi, Z.H.; Schnitzer, M.I.; Monreal, C.M.; Mayer, P. Separation and identiﬁcation of heterocyclic nitrogen
compounds in biooil derived by fast pyrolysis of chicken manure. J. Environ. Sci. Health Part B Pestic. Food
Contam. Agric. Wastes 2011,46, 51–61. [CrossRef] [PubMed]
56.
Mukherjee, A.; Zimmerman, A.R.; Harris, W. Surface chemistry variations among a series of
laboratory-produced biochars. Geoderma 2011,163, 247–255. [CrossRef]
57.
Doydora, S.A.; Cabrera, M.L.; Das, K.C.; Gaskin, J.W.; Sonon, L.S.; Miller, W.P. Release of Nitrogen and
Phosphorus from Poultry Litter Amended with Acidiﬁed Biochar. Int. J. Environ. Res. Publ. Health
2011
,8,
1491–1502. [CrossRef] [PubMed]
58.
Santos, L.B.; Striebeck, M.V.; Crespi, M.S.; Ribeiro, C.A.; De Julio, M. Characterization of biochar of pine pellet.
J. Therm. Anal. Calorim. 2015,122, 21–32. [CrossRef]
59.
Wu, H.; Che, X.; Ding, Z.; Hu, X.; Creamer, A.E.; Chen, H.; Gao, B. Release of soluble elements from biochars
derived from various biomass feedstocks. Environ. Sci. Pollut. Res.
2016
,23, 1905–1915. [CrossRef] [PubMed]
60.
Bruun, E.W.; Hauggaard-Nielsen, H.; Ibrahim, N.; Egsgaard, H.; Ambus, P.; Jensen, P.A.; Dam-Johansen, K.
Inﬂuence of fast pyrolysis temperature on biochar labile fraction and short-term carbon loss in a loamy soil.
Biomass Bioenergy 2011,35, 1182–1189. [CrossRef]
61. Lehmann, J. A handful of carbon. Nature 2007,447, 143–144. [CrossRef] [PubMed]
62.
Ippolito, J.A.; Laird, D.A.; Busscher, W.J. Environmental beneﬁts of biochar. J. Environ. Q.
2012
,41, 967–972.
[CrossRef] [PubMed]
63.
Wan, Q.; Yuan, J.H.; Xu, R.K.; Li, X.H. Pyrolysis temperature inﬂuences ameliorating effects of biochars on
acidic soil. Environ. Sci. Pollut. Res. Int. 2014,21, 2486–2495. [CrossRef] [PubMed]
... As the temperature reaches 400 °C, the transformation of biomass to biochar will be practically complete. However, at temperatures of up to 500 °C, it will be possible to remove the tar from biochar, and the carbonization stage will be complete [66,67]. Previous research indicated that pyrolysis at a temperature of ∼500 °C could produce more than 30% of the biochar yield [68,69]. ...
... This was likely due to the fact that most of the lignocellulosic material was decomposed in this temperature range. Studies in the literature have shown that during the pyrolysis process, the primary cracks and secondary decomposition occur at 400-500 °C along with the formation of oxygen functional groups [12,46,67], and the formation of the biochar structure occurs during these temperature ranges with the main precursor, lignin [29,65,67]. The lignin content was reported to be approximately 25% in hardwood and 33% in softwood [56]. ...
... This was likely due to the fact that most of the lignocellulosic material was decomposed in this temperature range. Studies in the literature have shown that during the pyrolysis process, the primary cracks and secondary decomposition occur at 400-500 °C along with the formation of oxygen functional groups [12,46,67], and the formation of the biochar structure occurs during these temperature ranges with the main precursor, lignin [29,65,67]. The lignin content was reported to be approximately 25% in hardwood and 33% in softwood [56]. ...
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... The result also revealed that BPS biochar contained 28.48% and 19.96% of nitrogen for biochar derived from fast and slow pyrolysis, respectively. These values are higher than the percentage of nitrogen of biochar derived from other biomass such as paddy straw, sugarcane bagasse [84], coconut shell, acacia wood [83] and apple tree branch [85], produced at a similar temperature. It could be due to the amount of nitrogen in the BPS feedstock being higher than the other type of feedstock in the literature. ...
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... For instance, Manzoor et al. (Manzoor et al., 2015), illustrated that the size of the nano ZnO synthesized via a co-precipitation method varied from 98 ± 43 to 458 ± 243 nm when the temperature ranged from 65 • C to 75 • C. Additionally, relatively high temperatures are needed in the pyrolysis process for the fabrication of carbonaceous materials (such as biochar) to control the properties of the produced materials. For instance, biochar with a high carbon content can be fabricated at temperatures above 600 • C (Zhao et al., 2017). However, the synthesis temperature can directly determine the total energy consumed by the synthesis process. ...
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... The results could be explained via the reasons that the structure and physicochemical properties connected with the adsorption of rice straw-derived biochar can be easily changed as calcination temperature increases. It has been suggested in previous studies that the biochars at high temperatures shows structural defects, blocked micropores on the surface (Rosales et al. 2017), and a decrease of carboxylic functional groups (Zhao et al. 2017), resulting in the decrease of adsorption active sites. Similarly, both Langmuir and Freundlich isotherm models can fit the isotherm experimental data well. ...
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... In a study by Zhao, Ta & Wang (2017) on biochar produced from apple tree branches at varying pyrolysis temperatures ranging between 300 to 600 °C, the peak intensities at 13.3 m -1 and 16.0 m -1 declined with temperature due to the decomposition of phenolic and carboxylic compounds. The highest loss was observed at 600 °C when -OH, -CH 2 , and C-O functional groups because of the temperature effect while low polar functional groups of -OH and C-O were obtained at 300 °C. ...
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Concerns about climate change and food productivity have spurred interest in biochar, a form of charred organic material typically used in agriculture to improve soil productivity and as a means of carbon sequestration. An innovative approach in agriculture is the use of agro-forestry waste for the production of soil fertilisers for agricultural purposes and as a source of energy. A common agricultural practice is to burn crop residues in the field to produce ashes that can be used as soil fertilisers. This approach is able to supply plants with certain nutrients, such as Ca, K, Mg, Na, B, S, and Mo. However, the low concentration of N and P in the ashes, together with the occasional presence of heavy metals (Ni, Pb, Cd, Se, Al, etc.), has a negative effect on soil and, therefore, crop productivity. This work describes the opportunity to create an innovative supply chain from agricultural waste biomass. Olive (Olea europaea) and hazelnut (Corylus avellana) pruning residues represent a major component of biomass waste in the area of Viterbo (Italy). In this study, we evaluated the production of biochar from these residues. Furthermore, a physicochemical characterisation of the produced biochar was performed to assess the quality of the two biochars according to the standards of the European Biochar Certificate (EBC). The results of this study indicate the cost-effective production of high-quality biochar from olive and hazelnut biomass residues.
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To investigate the relationship between Cr(VI) adsorption mechanisms and physio-chemical properties of biochar, ramie residues was oxygen-limited pyrolyzed under temperature varying from 300 to 600 °C. Batch adsorption experiments indicated that higher pyrolysis temperature limits Cr (VI) sorption in terms of capacity and affinity due to a higher aromatic structure and fewer polar functional groups in biochar. Both electrostatic (physical) and ionic (chemical) interactions were involved in the Cr(VI) removal. For low-temperature biochar, the simple physical adsorption was limited and the significant improvement in Cr(VI) sorption was attributed to abundant carboxyl and hydroxyl groups. The adsorption-reduction mechanisms could be concluded that Cr(VI) ions were electrostatically attracted by the positively charged biochar surface and reduced to Cr(III), and then the converted Cr(III) was retained or discharged into the solution. The study demonstrates ramie residues can be converted into biochar as a low-cost and effective sorbent for Cr(VI) removal.
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The effect of the addition of organic waste or biochar on the extractability of heavy metals (Cd, Cu, Ni, Pb and Zn) was assessed in five heavy metal-contaminated soils. The amendments studied were: municipal organic waste compost (MOW), green waste (GW), biochar derived from tree bark (BF) and biochar derived from vine shoots (BS). The amendments were added to the soil at 10% dose. A pHstat leaching test was applied to the soils and soil + amendment mixtures to assess the effects of the amendments on the extractable metal concentration at the initial pH and in the 2–12 pH range. MOW increased the DOC content in the mixtures for most soils, whereas the rest of amendments only increased the DOC content for the soil with the lowest DOC value. Moreover, in the mixtures obtained from soils with a low buffering capacity, the amendments increased pH (up to 3 units) and the acid neutralization capacity, thus decreasing the extractability of heavy metals at the initial pH of the mixtures. In a few cases, the amendments further decreased the concentrations of extractable metal due to an increase in the sorption capacity of the mixture, even though the soil had high initial pH and ANC values. MOW and GW generally led to larger decreases in metal extractability in the resulting mixtures than biochar, due to their higher sorption and acid neutralization capacities.
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Spatial variability of soil moisture under different land use types of orchard in Weibei rainfed highland of China was investigated by means of geostatistics. Classical statistical analysis showed that the average soil moisture content of clean tillage, grass land and straw land ranged from 9.36 to 20.86, 8.78 to 23.37 and 10.84 to 20.49, respectively. In 0–40 cm soil layer, 10% < CV% < 100%, which belongs to moderate variability. Depth in 120–160 cm and 160–200 cm, CV ≤ 10%, which belong to weak variability. And with the increasing of depth, coefficient of variation decreased. S-W test values pointed out that the distribution of soil moisture content accorded with normal distribution. The results of variation function analysis indicated that the ranges of grass land were larger than clean tillage. Spatial autocorrelation in surface soil was weaker than that of the bottom soil. The reason was that surface soil was more easily influenced by exterior factors. Fractal dimension value decreased with the increasing of soil depth. While the average content of soil moisture showed the opposite trend. According to kriging interpolation, the high-value areas of clean tillage mainly concentrated in (13.4, 27.8), (28.0, 32.5) and (27.0, 10.4), and low-value areas were in (13.8, 6.6). However, the high-value of grass areas mainly focused on around (11.5, 11.5), and low-value were in (11.2, 11.2) and (25.5, 25.5). The change of the other areas’ soil moisture were not obvious in a wide range. It has a good consistency. Therefore, in the dry season, it was advisable to choose straw mulching, and reduce grass cultivation, to achieve the goal of improving soil moisture content.