# An Investigation on Cocombustion Behaviors of Hydrothermally Treated Municipal Solid Waste with Coal Using a Drop-Tube Reactor

Authors: Liang Lu; Yuqi Jin; Masato R. Nakamura; Marco J. Castaldi; Kunio Yoshikawa
Journal: Journal of Combustion
 (2012)

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## Abstract

This work aims at demonstrating the feasibility of replacing Indonesian coal (INC) with hydrothermally treated municipal solid waste (MSWH) in cocombustion with high ash Indian coal (IC). The combustion efficiencies and emissions (CO, NO) of MSWH, INC and their blends with IC for a series of tests performed under a range of temperatures and air conditions were tested in a drop-tube reactor (DTR). The results showed the following. The combustion efficiency of IC was increased by blending both MSWH and INC and CO emission was reduced with increasing temperature. For NO emission, the blending of MSWH led to the increase of NO concentration whereas the effects of INC depended on the temperature. The combustion behaviors of IC-MSWH blend were comparable to those of the IC-INC blend indicating it is possible for MSWH to become a good substitute for INC supporting IC combustion. Moreover, the CO emission fell while the NO emission rose with increasing excess air for IC-MSWH blend at 900°C and the highest combustion efficiency was obtained at the excess air of 1.9. The existence of moisture in the cocombustion system of IC-MSWH blend could slightly improve the combustion efficiency, reduce CO, and increase NO.


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## Body

## 1.  Introduction

With the development of human civilization, municipal solid waste (MSW) turns out to be a great threat to the environment. Traditional MSW disposal methods such as open dumping, landfill, or composting are becoming less and less attractive due to less land available around cities and also much more stringent environmental regulations. Thermal treatment as incineration will therefore play an important role as an effective MSW treatment which enjoys the advantages of outstanding reduction in waste volume, thermal destruction of toxic organic constituents, and so forth. However, it is hard to recycle adequate energy from the incineration of MSW with high moisture content, heterogeneous characteristics, and low energy content. Recently, hydrothermal treatment (HT) is regarded to be an effective waste to energy technology for converting MSW into solid fuels with low moisture content, uniform characteristics, and high bulk/energy density [1–5].On the other hand, we are running out of high-rank coals for power generations so that the utilizations of low-rank coals are inevitable especially in developing countries. For example, Indian coal (IC) is one kind of coal with high ash content which leads to difficulty in ignition and maintenance of flame stabilization, and so forth. In reality, Indonesian coal (INC) is blended with IC in power plants in India in order to alleviate the adverse impact induced by IC. Nevertheless, there are still a lot of problems related to the utilization of INC as an additive: uncertainty in availability and price, higher energy content compared to IC, and so forth. In our previous work, experiments were carried out with thermogravimetric analysis (TGA) and the results proved that hydrothermally treated MSW (MSWH) has the capability to promote the combustion of low-quality IC and is competitive compared to INC especially in terms of the enhancements in ignition and burnout behaviors [1, 3, 4]. However, little has been clarified with respect to combustion efficiencies and emissions in real combustors.In this work, a drop tube reactor (DTR) is utilized to have a closer simulation of the real pulverized coal combustion system than TGA [6, 7]. The temperatures used in this study are 800, 900, 1000, and 1100°C in order to find out the influence of temperature on combustion behaviors. Individual IC, MSWH, INC and their blends at 80% IC : 20% MSWH and 90% IC : 10% INC (wt %) are tested in the DTR to evaluate the effectiveness of the blends in the combustion enhancement compared to IC only and the feasibility of the replacement of INC with MSWH in terms of combustion efficiency and emissions.


## 2.  Experimental

### 2.1. Material Sources

The two kinds of testing coal supplied from an Indian power plant are IC which is one kind of low-rank coal with high ash content and INC which is always used for the cocombustion with IC for supporting the combustibility in practice.The MSWH used in this study was obtained from a local city in Hokkaido, Japan. The MSW excluding food residue was treated in a batch scale HT treatment as shown in Figure1. The HT treatment was operated at 200°C, 20 atm with the holding time of 30 minutes using saturated steam. The HT treatment can convert MSW with high moisture content, irregular shapes, and low bulk density into homogeneous solid powder product.Figure 1
Hydrothermal treatment system.The fuel analysis of the samples such as proximate and ultimate analysis as well as higher heating value (HHV) is listed in Table1.Table 1
Fuel analysis.
(a)
Ultimate analysisa
C (%)
H (%)
N (%)
S (%)
O (%)
IC
44.50
3.33
1.02
0.26
5.55
MSWH
45.16
6.26
0.95
0.15
24.88
INC
75.47
5.37
1.10
0.09
16.40
B1b
44.63
3.92
1.01
0.24
9.42
B2b
47.60
3.53
1.03
0.24
6.64
(b)
Proximate analysisa and HHVa
Volatile matter(%)
Fixed carbon (%)
Ash(%)
HHV(MJ/kg)
IC
25.40
29.00
45.60
17.88
MSWH
70.94
6.31
22.75
17.84
INC
50.16
48.18
1.66
30.03
B1b
34.51
24.46
41.03
17.87
B2b
27.88
30.92
41.21
19.10
aDry basis (without blending quartz sand).
bCalculated values from the weight ratio.All the samples were crushed and milled to the size in the range of 100–180μm in order to avoid the effect of the size distribution. The blends of 80% IC : 20 % MSWH and 90% IC : 10% INC (wt %) were prepared by blending individual samples together. Due to the limitation of the screw feeder, quartz sand which is inert in characteristics was added into all the samples at the ratio of sample : quartz sand = 1 : 3 (wt %) in order to alleviate the adhesiveness of pure samples ensuring continuous feeding. Before tests, all the samples were dried in an oven for 2 hours because samples with small size have strong tendency to absorb moisture from the air.For simplification, here B1 and B2 refer to the blends of 80% IC + 20% MSWH and the blends of 90% IC + 10% INC, respectively.


### 2.2. Drop Tube Reactor System

The laboratory-scale DTR is made of quartz tubing (GE type 214, National Scientific Company) and is 1.8 m long, 25.4 mm OD, and 19 mm ID. The furnace used is a split-hinged vertical furnace with 5 temperature zones (SV Furnace MA no. 100087, Mellen Inc.). The overall experimental scheme is illustrated in Figure2.Figure 2
Schematic diagram of the DTR.The samples were fed continuously to the DTR using a solid screw feeder. Air was supplied through an air cylinder and the flow rate was maintained by using a mass flow controller (MFC). During the experiments, the flow rate of the exhaust gas could be controlled through a set of a flow meter and a vacuum pump. The compositions of the gas (CO, CO2, O2, NO, SO2) were continuously measured after the system gained its stability by a flow gas analyzer (Integrated Emissions System Model 700, ENERAC, Inc.) and a micro-GC (Quad Series Micro GC, Agilent, Inc.). After each trial, ash was collected through an ash collector for further analysis.


### 2.3. Testing Matrix

Table2 shows the experimental matrix. Both the individual samples (IC, MSWH, Inc.) and the blended samples (B1, B2) were tested at 800, 900, 1000, and 1100°C at determined excess air (φ) of 1.9 to investigate the influence of the temperature on combustion behaviors. Besides that, B1 was selected for a series of further experiments: 5 different φ from 1.3~2.5 were chosen at 900°C to find out the optimal parameter for the combustion of B1. In addition to that, 0.1 g/min water which accounts for 20% of the total feeding amount was injected into the DTR along with B1 at 900°C (φ = 1.9). The reason for performing this trial was to simulate the combustion practice in the real application which handles with coal/blends of coal and biomass. The moisture contents of the fuels used are normally around or higher than 20% which may exert positive or negative effects on the combustion characteristics and emissions [8, 9] especially when MSWH is introduced into the combustion system.Table 2
Experimental matrix.
(a)
IC, MSWH, INC, B1, B2
Temperature (°C)
φ
800
1.9
900
1.9
1000
1.9
1100
1.9
(b)
B1
Temperature (°C)
Excess air
900
1.3
900
1.6
900
1.9
900
2.2
900
2.5
900 (+0.1 g/min H2O)
1.9


## 2.1. Material Sources

The two kinds of testing coal supplied from an Indian power plant are IC which is one kind of low-rank coal with high ash content and INC which is always used for the cocombustion with IC for supporting the combustibility in practice.The MSWH used in this study was obtained from a local city in Hokkaido, Japan. The MSW excluding food residue was treated in a batch scale HT treatment as shown in Figure1. The HT treatment was operated at 200°C, 20 atm with the holding time of 30 minutes using saturated steam. The HT treatment can convert MSW with high moisture content, irregular shapes, and low bulk density into homogeneous solid powder product.Figure 1
Hydrothermal treatment system.The fuel analysis of the samples such as proximate and ultimate analysis as well as higher heating value (HHV) is listed in Table1.Table 1
Fuel analysis.
(a)
Ultimate analysisa
C (%)
H (%)
N (%)
S (%)
O (%)
IC
44.50
3.33
1.02
0.26
5.55
MSWH
45.16
6.26
0.95
0.15
24.88
INC
75.47
5.37
1.10
0.09
16.40
B1b
44.63
3.92
1.01
0.24
9.42
B2b
47.60
3.53
1.03
0.24
6.64
(b)
Proximate analysisa and HHVa
Volatile matter(%)
Fixed carbon (%)
Ash(%)
HHV(MJ/kg)
IC
25.40
29.00
45.60
17.88
MSWH
70.94
6.31
22.75
17.84
INC
50.16
48.18
1.66
30.03
B1b
34.51
24.46
41.03
17.87
B2b
27.88
30.92
41.21
19.10
aDry basis (without blending quartz sand).
bCalculated values from the weight ratio.All the samples were crushed and milled to the size in the range of 100–180μm in order to avoid the effect of the size distribution. The blends of 80% IC : 20 % MSWH and 90% IC : 10% INC (wt %) were prepared by blending individual samples together. Due to the limitation of the screw feeder, quartz sand which is inert in characteristics was added into all the samples at the ratio of sample : quartz sand = 1 : 3 (wt %) in order to alleviate the adhesiveness of pure samples ensuring continuous feeding. Before tests, all the samples were dried in an oven for 2 hours because samples with small size have strong tendency to absorb moisture from the air.For simplification, here B1 and B2 refer to the blends of 80% IC + 20% MSWH and the blends of 90% IC + 10% INC, respectively.


## 2.2. Drop Tube Reactor System

The laboratory-scale DTR is made of quartz tubing (GE type 214, National Scientific Company) and is 1.8 m long, 25.4 mm OD, and 19 mm ID. The furnace used is a split-hinged vertical furnace with 5 temperature zones (SV Furnace MA no. 100087, Mellen Inc.). The overall experimental scheme is illustrated in Figure2.Figure 2
Schematic diagram of the DTR.The samples were fed continuously to the DTR using a solid screw feeder. Air was supplied through an air cylinder and the flow rate was maintained by using a mass flow controller (MFC). During the experiments, the flow rate of the exhaust gas could be controlled through a set of a flow meter and a vacuum pump. The compositions of the gas (CO, CO2, O2, NO, SO2) were continuously measured after the system gained its stability by a flow gas analyzer (Integrated Emissions System Model 700, ENERAC, Inc.) and a micro-GC (Quad Series Micro GC, Agilent, Inc.). After each trial, ash was collected through an ash collector for further analysis.


## 2.3. Testing Matrix

Table2 shows the experimental matrix. Both the individual samples (IC, MSWH, Inc.) and the blended samples (B1, B2) were tested at 800, 900, 1000, and 1100°C at determined excess air (φ) of 1.9 to investigate the influence of the temperature on combustion behaviors. Besides that, B1 was selected for a series of further experiments: 5 different φ from 1.3~2.5 were chosen at 900°C to find out the optimal parameter for the combustion of B1. In addition to that, 0.1 g/min water which accounts for 20% of the total feeding amount was injected into the DTR along with B1 at 900°C (φ = 1.9). The reason for performing this trial was to simulate the combustion practice in the real application which handles with coal/blends of coal and biomass. The moisture contents of the fuels used are normally around or higher than 20% which may exert positive or negative effects on the combustion characteristics and emissions [8, 9] especially when MSWH is introduced into the combustion system.Table 2
Experimental matrix.
(a)
IC, MSWH, INC, B1, B2
Temperature (°C)
φ
800
1.9
900
1.9
1000
1.9
1100
1.9
(b)
B1
Temperature (°C)
Excess air
900
1.3
900
1.6
900
1.9
900
2.2
900
2.5
900 (+0.1 g/min H2O)
1.9


## 3. Results and Discussion

### 3.1. Combustion Efficiencies of all the Samples as a Function of Temperature

The combustion efficiency as a function of temperature atφ = 1.9 is depicted in Figure 3. The combustion efficiency (η) is defined as follows: η(%)=(B-C)/B*100, where B and C stand for the mass fractions of combustible in the feed stock and combustible in the ash collected. From Figure 3(a), it can be found that the η of IC, MSWH, and INC showed increasing trends as the temperature increased and even linear tendencies could be found from 900 to 1100°C for all the three samples (R2>0.98, where R2 is a symbol for the coefficient of determination of a linear regression) which indicated that, at higher temperatures (900~1100°C), the combustion was controlled by the temperature and the combustion efficiency of three individual samples could be reasonably predicted. On the other hand, at lower temperature (800°C), not only the temperature but also the other factors such as oxygen diffusion might also come to play important roles on the combustion especially in the case of INC whose η at 800°C was extremely low compared to the others indicating that the high content of volatile matter (VM) of INC might discourage the diffusion of air which prohibits the oxygen from reaching the fixed carbon (FC). Although MSWH contained much more VM than INC, its η at 800°C was still well controlled by the temperature because the burning of VM was mainly responsible for the combustion of MSWH whereas on the other hand in the case of coal, the combustion of FC dominated. Moreover, MSWH presented higher combustion efficiency due to the high amount of VM.Combustion efficiency as a function of temperature (φ = 1.9).
(a)
(b)From Figure3(b), the effects of blending MSWH and INC on the cocombustion characteristics can be observed. The additions of MSWH and INC with higher VM supported the combustion of IC significantly. The η of B1 and B2 were elevated by 6.66~9.28% and 5.87~10.71% respectively when compared to individual IC (see Table 3, ηB1(B2)-ηIC). The lower the temperature was, the higher the effectiveness of the blending would be. This implied that at lower temperature the blending of MSWH and INC with higher VM contents (Table 1) promoted combustion more significantly. The release of more VM from MSWH and INC at higher temperature might partially reduce the concentration of oxygen near the char particles and prevented the oxygen from contacting with char leading to the drop of η enhancement at higher temperatures. Moreover, similar to individual samples, the improvements of η by increasing the temperature from 900°C to 1100°C for the two blends were also linear (R2>0.92). Furthermore, from Table 3 the experimental values of η were always higher than those of the calculated ones which suggested that there should be some interaction between the additives and IC. It was also supported by the TGA experiment in our previous work that at lower blending ratio of MSWH, there was some synergic relationship between MSWH and IC [3].Table 3
Comparison ofη, CO, and NO emissions between experimental value and calculated value and the enhancement of the η by blending.
T (°C)
η (%)
η
B1
(
B2
)
-
η
IC (%)
CO (ppm)
NO (ppm)
B1
a (b)
a
a (b)
a (b)
800
94.26 (87.07)
9.28
1954 (3352)
281 (240)
900
96.34 (90.25)
7.91
2363 (4042)
370 (342)
1000
97.08 (91.28)
7.60
2333 (3646)
439 (339)
1100
97.70 (92.71)
6.66
2305 (2963)
438 (324)
B2
a (b)
a
a (b)
a (b)
800
95.69 (84.04)
10.71
1740 (3372)
246 (225)
900
96.48 (88.30)
8.05
3146 (4243)
252 (318)
1000
96.81 (89.45)
7.32
2226 (3853)
384 (333)
1100
96.90 (91.10)
5.87
2038 (3091)
435 (313)
aExperimental value obtained from the measured data.
bCalculated value obtained on the assumption of the compositional ratio of the blends.


### 3.2. Emissions of All the Samples as a Function of Temperature

#### 3.2.1. CO Emission

The emission of CO of all the samples as a function of temperature atφ =  1.9 is shown in Figure 4. For individual samples (Figure 4(a)), MSWH and INC shared the same trend that the CO emission fell with temperature which was because that the CO oxidation to CO2 was favored at higher temperature. However, from 800°C to 900°C, IC showed a significant increase in CO emission and the reason might be ascribed to the low combustibility of IC char which is surrounded by huge amount of ash (45.60% ash for IC, Table 1) implying that the whole combustion efficiency would be low for IC at low temperature (800°C) although the CO emission at this temperature is lower. When comparing the three individual samples in Figure 4(a), it is obvious that MSWH emitted least CO followed by INC and IC. As a well-known fact, VM which is in gaseous state during the devolatilization gets ignited and burned more easily than FC or char. So it is reasonable that MSWH which was rich in VM showed the lowest CO emission.CO emissions as a function of temperature (φ = 1.9).
(a)
(b)When it comes to the blends (Figure4(b)), although the blends showed the similar trends of CO emission evolution as a function of temperature as IC, it seemed that the blendings of both MSWH and INC contributed to the reduction of CO emission of IC significantly. From Table 3, it is obvious that the experimental values of CO emission at all the temperature for both B1 and B2 were much lower than those of calculated values which again demonstrated that there was certain interactive reaction between MSWH (INC) and IC.


#### 3.2.2. NO Emission

Because the temperature of this study was no higher than 1100°C, fuel-NO formation was considered to be the most predominant one while thermal-NO and prompt-NO could be neglected. The emission of NO of all the samples as a function of temperature at the excess air of 1.9 is shown in Figure5. From Figure 5(a), MSWH emitted more NO than the coals although the nitrogen content of MSWH was the lowest (Table 1). It can be ascribed to that the main nitrogen compounds of MSW components (paper especially) were simple proteins known to release NH3, which was easily oxidized to form NO whereas the nitrogen compounds of coals were essentially contained in aromatic heterocycles which were hard to be released and converted into NO [10]. Normally, the higher the rank of coal was (here INC > IC), the more nitrogen compounds were constrained in the aromatic heterocycles which gave an explanation of the lower NO concentration of INC than that of IC. For the effect of temperature on the NO emissions of the three individual samples in Figure 5(a), at 800°C, the NO concentrations of the three samples were the lowest which was possibly due to (1) the low temperature leading to the abatement of emissions of nitrogen compounds in the case of IC and INC; (2) the high CO concentration at 800°C in the case of MSWH and INC resulting in the acceleration of NO destruction on the surface of char [10, 11]. At 900°C, the NO concentrations of IC and MSWH rose greatly because the formation of NO was favored at higher temperature whereas the NO emission only increased slightly for INC in which case a significant NO emission could be observed at 1000°C indicating that, for high-rank coal as INC, the release of nitrogen compounds from aromatic heterocycles required more energy. At 1000°C, NO emission of IC only increased a little bit compared to the case at 900°C implying that the nitrogen compounds of IC were almost emitted at 900°C. For MSWH, since the rate of VM release became higher at higher temperature (1000–1100°C), the reducing environment and more available hydrocarbon radicals contributed to the destruction of NO and so were the cases of IC and INC at 1100°C.NO emissions as a function of temperature (φ = 1.9).
(a)
(b)In the cases of the blends burning (Figure5(b)), for B1, at all the four temperatures, the NO emissions were higher than that of IC only. The NO emission of B1 kept rising until 1000°C which was not similar to the case of IC and MSWH only. Because the CO concentration of B1 was much lower than that of IC (Figure 4(b)), the NO destruction through the catalyzing reaction on the char surface with CO was also restricted. Additionally, it is concluded that the addition of high VM containing biomass such as chicken litter at low concentrations resulted in higher NO emissions because more fuel-N was introduced whereas blending at high ratios might reduce NO emissions due to the larger amount of released VM, which suppressed the formation of NO [12]. When it comes to B2, the trend of NO evolution from 800~1000°C seemed similar to that of INC only although the values became higher which could be attributed to the same reason as in the case of B1. 10% of INC in B2 took over the NO emission or in other words dominated the reaction of NO formation and destruction. It is assumed that the VM of INC of low reactivity which might not be completely consumed at lower temperature prohibited the oxygen from contacting with the IC particles resulting in retention of the nitrogen compounds in IC. On the other hand, the VM helped the reduction of NO as well due to available hydrocarbon radicals. Moreover, from Figure 4(b), the CO concentration of B2 at 900°C was extremely high when compared with the cases at other temperatures because unburned VM might constitute an additional CO source. From Table 3, the experimental values of NO emission at all the temperature for both B1 and B2 were higher than those of calculated values. The lower CO and some kind of synergic behaviors might be responsible for that.


### 3.3. Effects of Excess Air and Moisture on the Cocombustion Behavior of MSWH with IC

Figure6 shows the combustion efficiency and CO, NO emissions of B1 as a function of the excess air at 900°C. From Figure 6(a), it is obvious that the highest η was obtained at φ = 1.9 especially when there was water in the combustion system at which condition η reached 96.7%. It is also clear that the higher the excess air was, the higher the η would be when φ was below 1.9. The oxidations of CO and hydrocarbons were favored at high oxygen concentration. However, when φ exceeded 1.9, η decreased with φ increasing. This was because that the temperature in the tube furnace would be inevitably decreased to some extent with the increase of φ due to more cool air to be heated up [11]. The decrease in furnace temperature thus led to the drop of η. Although many researchers concluded that the moisture content in the MSW led to low combustion efficiency [13], the small amount of water injection (0.1 g/min) in this study helped to improve η slightly compared with the case without water injection. The reason might be that the existence of water molecule at high temperature contributes to the increase of H and OH radicals which could be reacted with CO thus promoting the conversion of FC to CO or CO2.Combustion behaviors of B1 at different conditions (at 900°C).
(a)
(b)The CO and NO evolution of B1 as a function of the excess air is depicted in Figure6(b). CO fell with the increase of φ whereas on the other hand NO displayed an opposite tendency. The lower CO emission at higher φ was due to the enhancement in available oxygen which led to the acceleration of CO oxidation. On the other hand, lower CO at higher φ resulted in the attenuation of reduction environment thus slowing down the reaction between CO and NO on char surfaces. Meanwhile, the higher oxygen content at higher φ promoted the conversion of nitrogen compounds to NO. As mentioned above, moisture injection facilitated the formation of CO2 through H and OH reacting with CO. On the other hand, O and OH radicals of high reactivity also reacted easily with NH3 species to form NO [6].At 900°C, the most optimal condition for B1 combustion was assumed to be atφ = 1.9. Small quantity of water injection (equaling to 20% moisture) into the combustion system led to the improvement of the combustion efficiency, the reduction of CO emission, and increase of NO. The results further permitted the direct utilization of naturally dried MSWH for cocombustion with coal.


## 3.1. Combustion Efficiencies of all the Samples as a Function of Temperature

The combustion efficiency as a function of temperature atφ = 1.9 is depicted in Figure 3. The combustion efficiency (η) is defined as follows: η(%)=(B-C)/B*100, where B and C stand for the mass fractions of combustible in the feed stock and combustible in the ash collected. From Figure 3(a), it can be found that the η of IC, MSWH, and INC showed increasing trends as the temperature increased and even linear tendencies could be found from 900 to 1100°C for all the three samples (R2>0.98, where R2 is a symbol for the coefficient of determination of a linear regression) which indicated that, at higher temperatures (900~1100°C), the combustion was controlled by the temperature and the combustion efficiency of three individual samples could be reasonably predicted. On the other hand, at lower temperature (800°C), not only the temperature but also the other factors such as oxygen diffusion might also come to play important roles on the combustion especially in the case of INC whose η at 800°C was extremely low compared to the others indicating that the high content of volatile matter (VM) of INC might discourage the diffusion of air which prohibits the oxygen from reaching the fixed carbon (FC). Although MSWH contained much more VM than INC, its η at 800°C was still well controlled by the temperature because the burning of VM was mainly responsible for the combustion of MSWH whereas on the other hand in the case of coal, the combustion of FC dominated. Moreover, MSWH presented higher combustion efficiency due to the high amount of VM.Combustion efficiency as a function of temperature (φ = 1.9).
(a)
(b)From Figure3(b), the effects of blending MSWH and INC on the cocombustion characteristics can be observed. The additions of MSWH and INC with higher VM supported the combustion of IC significantly. The η of B1 and B2 were elevated by 6.66~9.28% and 5.87~10.71% respectively when compared to individual IC (see Table 3, ηB1(B2)-ηIC). The lower the temperature was, the higher the effectiveness of the blending would be. This implied that at lower temperature the blending of MSWH and INC with higher VM contents (Table 1) promoted combustion more significantly. The release of more VM from MSWH and INC at higher temperature might partially reduce the concentration of oxygen near the char particles and prevented the oxygen from contacting with char leading to the drop of η enhancement at higher temperatures. Moreover, similar to individual samples, the improvements of η by increasing the temperature from 900°C to 1100°C for the two blends were also linear (R2>0.92). Furthermore, from Table 3 the experimental values of η were always higher than those of the calculated ones which suggested that there should be some interaction between the additives and IC. It was also supported by the TGA experiment in our previous work that at lower blending ratio of MSWH, there was some synergic relationship between MSWH and IC [3].Table 3
Comparison ofη, CO, and NO emissions between experimental value and calculated value and the enhancement of the η by blending.
T (°C)
η (%)
η
B1
(
B2
)
-
η
IC (%)
CO (ppm)
NO (ppm)
B1
a (b)
a
a (b)
a (b)
800
94.26 (87.07)
9.28
1954 (3352)
281 (240)
900
96.34 (90.25)
7.91
2363 (4042)
370 (342)
1000
97.08 (91.28)
7.60
2333 (3646)
439 (339)
1100
97.70 (92.71)
6.66
2305 (2963)
438 (324)
B2
a (b)
a
a (b)
a (b)
800
95.69 (84.04)
10.71
1740 (3372)
246 (225)
900
96.48 (88.30)
8.05
3146 (4243)
252 (318)
1000
96.81 (89.45)
7.32
2226 (3853)
384 (333)
1100
96.90 (91.10)
5.87
2038 (3091)
435 (313)
aExperimental value obtained from the measured data.
bCalculated value obtained on the assumption of the compositional ratio of the blends.


## 3.2. Emissions of All the Samples as a Function of Temperature

### 3.2.1. CO Emission

The emission of CO of all the samples as a function of temperature atφ =  1.9 is shown in Figure 4. For individual samples (Figure 4(a)), MSWH and INC shared the same trend that the CO emission fell with temperature which was because that the CO oxidation to CO2 was favored at higher temperature. However, from 800°C to 900°C, IC showed a significant increase in CO emission and the reason might be ascribed to the low combustibility of IC char which is surrounded by huge amount of ash (45.60% ash for IC, Table 1) implying that the whole combustion efficiency would be low for IC at low temperature (800°C) although the CO emission at this temperature is lower. When comparing the three individual samples in Figure 4(a), it is obvious that MSWH emitted least CO followed by INC and IC. As a well-known fact, VM which is in gaseous state during the devolatilization gets ignited and burned more easily than FC or char. So it is reasonable that MSWH which was rich in VM showed the lowest CO emission.CO emissions as a function of temperature (φ = 1.9).
(a)
(b)When it comes to the blends (Figure4(b)), although the blends showed the similar trends of CO emission evolution as a function of temperature as IC, it seemed that the blendings of both MSWH and INC contributed to the reduction of CO emission of IC significantly. From Table 3, it is obvious that the experimental values of CO emission at all the temperature for both B1 and B2 were much lower than those of calculated values which again demonstrated that there was certain interactive reaction between MSWH (INC) and IC.


### 3.2.2. NO Emission

Because the temperature of this study was no higher than 1100°C, fuel-NO formation was considered to be the most predominant one while thermal-NO and prompt-NO could be neglected. The emission of NO of all the samples as a function of temperature at the excess air of 1.9 is shown in Figure5. From Figure 5(a), MSWH emitted more NO than the coals although the nitrogen content of MSWH was the lowest (Table 1). It can be ascribed to that the main nitrogen compounds of MSW components (paper especially) were simple proteins known to release NH3, which was easily oxidized to form NO whereas the nitrogen compounds of coals were essentially contained in aromatic heterocycles which were hard to be released and converted into NO [10]. Normally, the higher the rank of coal was (here INC > IC), the more nitrogen compounds were constrained in the aromatic heterocycles which gave an explanation of the lower NO concentration of INC than that of IC. For the effect of temperature on the NO emissions of the three individual samples in Figure 5(a), at 800°C, the NO concentrations of the three samples were the lowest which was possibly due to (1) the low temperature leading to the abatement of emissions of nitrogen compounds in the case of IC and INC; (2) the high CO concentration at 800°C in the case of MSWH and INC resulting in the acceleration of NO destruction on the surface of char [10, 11]. At 900°C, the NO concentrations of IC and MSWH rose greatly because the formation of NO was favored at higher temperature whereas the NO emission only increased slightly for INC in which case a significant NO emission could be observed at 1000°C indicating that, for high-rank coal as INC, the release of nitrogen compounds from aromatic heterocycles required more energy. At 1000°C, NO emission of IC only increased a little bit compared to the case at 900°C implying that the nitrogen compounds of IC were almost emitted at 900°C. For MSWH, since the rate of VM release became higher at higher temperature (1000–1100°C), the reducing environment and more available hydrocarbon radicals contributed to the destruction of NO and so were the cases of IC and INC at 1100°C.NO emissions as a function of temperature (φ = 1.9).
(a)
(b)In the cases of the blends burning (Figure5(b)), for B1, at all the four temperatures, the NO emissions were higher than that of IC only. The NO emission of B1 kept rising until 1000°C which was not similar to the case of IC and MSWH only. Because the CO concentration of B1 was much lower than that of IC (Figure 4(b)), the NO destruction through the catalyzing reaction on the char surface with CO was also restricted. Additionally, it is concluded that the addition of high VM containing biomass such as chicken litter at low concentrations resulted in higher NO emissions because more fuel-N was introduced whereas blending at high ratios might reduce NO emissions due to the larger amount of released VM, which suppressed the formation of NO [12]. When it comes to B2, the trend of NO evolution from 800~1000°C seemed similar to that of INC only although the values became higher which could be attributed to the same reason as in the case of B1. 10% of INC in B2 took over the NO emission or in other words dominated the reaction of NO formation and destruction. It is assumed that the VM of INC of low reactivity which might not be completely consumed at lower temperature prohibited the oxygen from contacting with the IC particles resulting in retention of the nitrogen compounds in IC. On the other hand, the VM helped the reduction of NO as well due to available hydrocarbon radicals. Moreover, from Figure 4(b), the CO concentration of B2 at 900°C was extremely high when compared with the cases at other temperatures because unburned VM might constitute an additional CO source. From Table 3, the experimental values of NO emission at all the temperature for both B1 and B2 were higher than those of calculated values. The lower CO and some kind of synergic behaviors might be responsible for that.


## 3.2.1. CO Emission

The emission of CO of all the samples as a function of temperature atφ =  1.9 is shown in Figure 4. For individual samples (Figure 4(a)), MSWH and INC shared the same trend that the CO emission fell with temperature which was because that the CO oxidation to CO2 was favored at higher temperature. However, from 800°C to 900°C, IC showed a significant increase in CO emission and the reason might be ascribed to the low combustibility of IC char which is surrounded by huge amount of ash (45.60% ash for IC, Table 1) implying that the whole combustion efficiency would be low for IC at low temperature (800°C) although the CO emission at this temperature is lower. When comparing the three individual samples in Figure 4(a), it is obvious that MSWH emitted least CO followed by INC and IC. As a well-known fact, VM which is in gaseous state during the devolatilization gets ignited and burned more easily than FC or char. So it is reasonable that MSWH which was rich in VM showed the lowest CO emission.CO emissions as a function of temperature (φ = 1.9).
(a)
(b)When it comes to the blends (Figure4(b)), although the blends showed the similar trends of CO emission evolution as a function of temperature as IC, it seemed that the blendings of both MSWH and INC contributed to the reduction of CO emission of IC significantly. From Table 3, it is obvious that the experimental values of CO emission at all the temperature for both B1 and B2 were much lower than those of calculated values which again demonstrated that there was certain interactive reaction between MSWH (INC) and IC.


## 3.2.2. NO Emission

Because the temperature of this study was no higher than 1100°C, fuel-NO formation was considered to be the most predominant one while thermal-NO and prompt-NO could be neglected. The emission of NO of all the samples as a function of temperature at the excess air of 1.9 is shown in Figure5. From Figure 5(a), MSWH emitted more NO than the coals although the nitrogen content of MSWH was the lowest (Table 1). It can be ascribed to that the main nitrogen compounds of MSW components (paper especially) were simple proteins known to release NH3, which was easily oxidized to form NO whereas the nitrogen compounds of coals were essentially contained in aromatic heterocycles which were hard to be released and converted into NO [10]. Normally, the higher the rank of coal was (here INC > IC), the more nitrogen compounds were constrained in the aromatic heterocycles which gave an explanation of the lower NO concentration of INC than that of IC. For the effect of temperature on the NO emissions of the three individual samples in Figure 5(a), at 800°C, the NO concentrations of the three samples were the lowest which was possibly due to (1) the low temperature leading to the abatement of emissions of nitrogen compounds in the case of IC and INC; (2) the high CO concentration at 800°C in the case of MSWH and INC resulting in the acceleration of NO destruction on the surface of char [10, 11]. At 900°C, the NO concentrations of IC and MSWH rose greatly because the formation of NO was favored at higher temperature whereas the NO emission only increased slightly for INC in which case a significant NO emission could be observed at 1000°C indicating that, for high-rank coal as INC, the release of nitrogen compounds from aromatic heterocycles required more energy. At 1000°C, NO emission of IC only increased a little bit compared to the case at 900°C implying that the nitrogen compounds of IC were almost emitted at 900°C. For MSWH, since the rate of VM release became higher at higher temperature (1000–1100°C), the reducing environment and more available hydrocarbon radicals contributed to the destruction of NO and so were the cases of IC and INC at 1100°C.NO emissions as a function of temperature (φ = 1.9).
(a)
(b)In the cases of the blends burning (Figure5(b)), for B1, at all the four temperatures, the NO emissions were higher than that of IC only. The NO emission of B1 kept rising until 1000°C which was not similar to the case of IC and MSWH only. Because the CO concentration of B1 was much lower than that of IC (Figure 4(b)), the NO destruction through the catalyzing reaction on the char surface with CO was also restricted. Additionally, it is concluded that the addition of high VM containing biomass such as chicken litter at low concentrations resulted in higher NO emissions because more fuel-N was introduced whereas blending at high ratios might reduce NO emissions due to the larger amount of released VM, which suppressed the formation of NO [12]. When it comes to B2, the trend of NO evolution from 800~1000°C seemed similar to that of INC only although the values became higher which could be attributed to the same reason as in the case of B1. 10% of INC in B2 took over the NO emission or in other words dominated the reaction of NO formation and destruction. It is assumed that the VM of INC of low reactivity which might not be completely consumed at lower temperature prohibited the oxygen from contacting with the IC particles resulting in retention of the nitrogen compounds in IC. On the other hand, the VM helped the reduction of NO as well due to available hydrocarbon radicals. Moreover, from Figure 4(b), the CO concentration of B2 at 900°C was extremely high when compared with the cases at other temperatures because unburned VM might constitute an additional CO source. From Table 3, the experimental values of NO emission at all the temperature for both B1 and B2 were higher than those of calculated values. The lower CO and some kind of synergic behaviors might be responsible for that.


## 3.3. Effects of Excess Air and Moisture on the Cocombustion Behavior of MSWH with IC

Figure6 shows the combustion efficiency and CO, NO emissions of B1 as a function of the excess air at 900°C. From Figure 6(a), it is obvious that the highest η was obtained at φ = 1.9 especially when there was water in the combustion system at which condition η reached 96.7%. It is also clear that the higher the excess air was, the higher the η would be when φ was below 1.9. The oxidations of CO and hydrocarbons were favored at high oxygen concentration. However, when φ exceeded 1.9, η decreased with φ increasing. This was because that the temperature in the tube furnace would be inevitably decreased to some extent with the increase of φ due to more cool air to be heated up [11]. The decrease in furnace temperature thus led to the drop of η. Although many researchers concluded that the moisture content in the MSW led to low combustion efficiency [13], the small amount of water injection (0.1 g/min) in this study helped to improve η slightly compared with the case without water injection. The reason might be that the existence of water molecule at high temperature contributes to the increase of H and OH radicals which could be reacted with CO thus promoting the conversion of FC to CO or CO2.Combustion behaviors of B1 at different conditions (at 900°C).
(a)
(b)The CO and NO evolution of B1 as a function of the excess air is depicted in Figure6(b). CO fell with the increase of φ whereas on the other hand NO displayed an opposite tendency. The lower CO emission at higher φ was due to the enhancement in available oxygen which led to the acceleration of CO oxidation. On the other hand, lower CO at higher φ resulted in the attenuation of reduction environment thus slowing down the reaction between CO and NO on char surfaces. Meanwhile, the higher oxygen content at higher φ promoted the conversion of nitrogen compounds to NO. As mentioned above, moisture injection facilitated the formation of CO2 through H and OH reacting with CO. On the other hand, O and OH radicals of high reactivity also reacted easily with NH3 species to form NO [6].At 900°C, the most optimal condition for B1 combustion was assumed to be atφ = 1.9. Small quantity of water injection (equaling to 20% moisture) into the combustion system led to the improvement of the combustion efficiency, the reduction of CO emission, and increase of NO. The results further permitted the direct utilization of naturally dried MSWH for cocombustion with coal.


## 4. Conclusions

The introduction of the MSWH into the cocombustion system supporting the utilization of low-rank coal not only provides a good treatment for MSW but also cuts the usage of solid energy resource of high-rank coal. The results obtained in this research can be summarized as follows.(1)
The combustion efficiency of IC was elevated by blending both MSWH and INC and CO emission was reduced by increasing the temperature.(2)
With regards to NO emission, the blending of MSWH led to the increase of NO emission whereas the blending of INC resulted in either increase or decrease of NO emission compared with IC only depending on the temperature.(3)
The combustion efficiency and CO and NO emissions of IC-MSWH blend were comparable to those of IC-INC blend especially at higher temperature indicating it is viable to replace INC with HT-treated MSW in cocombustion with IC.(4)
At the excess air of 1.9, the combustion efficiency of IC-MSWH blend showed the highest value. The CO emission fell and the NO emission rose with the increase of the excess air in the case of IC-MSWH blend at 900°C.(5)
20% moisture content of the IC-MSWH blends could improve the combustion efficiency, reduce CO emission, and increase NO emission. It is possible to directly utilize the hydrothermally treated MSW for the cocombustion with IC.



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*Source: 282851-2012-09-06.xml*