The samples used in this study were composed of water-quenched MSWI bottom ash generated in a semi-continuous stoker furnace with unburned materials and incombustible parts like metals removed as much as possible. The particle size distribution is shown in Figure 1, and the true density measured by a pycnometer method was 2.54 kg/cm³. The contents of Pb, Zn, Cd, Cr, Cu, Na, K, and Ca were analyzed by inductively coupled plasma atomic emission spectroscopy (SPS7800, Seiko Instruments Inc.) after digestion by nitric and perchloric acid

followed by filtration. The samples were also submitted to Japan Leaching Test No. 13 (JLT13), which is a standard leaching test for waste in Japan in which a suspension with a liquid/solid weight ratio (L/S) of 10 was shaken for 6 hours and then filtered using a 1 μm glass filter, followed by filtrate measurement and analysis for pH (HM-50G, TOA DKK Corporation), electrical conductivity (EC; CM-30G, TOA DKK Corporation), P-alkalinity, and each concentration of Pb, Zn, Cd, Total Cr (T-Cr), Cu, Na, K, Ca, and Cl⁻. Analysis for Cl⁻ was performed by the Mohr method. The content analysis and JLT13 results are shown in Table 1.

MSWI bottom ash particles are porous, with the pores varying in size. In this experiment in order to estimate void structure, water absorption rate (%) of MSWI bottom ash particles, which is defined as the rate (%) of the water content of ash particles after absorption of pure water for a specified time and surface drying to the dry weight of them. Mercury porosimeter method and nitrogen- gas adsorption isotherms are commonly used to investigate the void volume and void distribution in porous bodies, but here we applied the coarse-aggregate water absorption rate measurement method specified in the Japanese Industrial Standards (JIS A1110).

Figure 2 schematically shows the three states of water absorption by bottom ash particles. In the wet state, the absorbed water extends to the particle surface. In the dry-surface state, the water has been removed from the surface of the wet-state particle. In the absolute-dry state, the dry-surface state sample has been further dried by heating at 110˚C until the weight of the particle becomes constant.

The water absorption rate of MSWI bottom ash was measured by the following three procedures, using samples with particle sizes d ≥ 2 mm.

a) Still-water absorption: 50 g of the sample and 500 mL of pure water were placed in a 500 mL beaker and water absorption was allowed to proceed while

standing for 72 hours.

b) Degassed absorption: the sample and pure water were placed in a glass beaker as in procedure a), the beaker was then placed in glass desiccator attached to vacuum pump, and water absorption was allowed to proceed for 72 hours while degassing.

c) Agitated absorption: the sample and pure water were placed in a glass beaker as in procedure a) and permitted to absorb water for 72 hours under agitation by a suspended stirrer (SM-102, As One Corp.) rotating at 100, 200, or 300 rpm.

For each experiment, a preliminary trial was first performed to confirm attainment of a constant weight within the specified period. Each procedure was followed by filtration through 1.0 μm membrane filter, measurement of the wet-particle weight m₂ (kg) of the sample (with water present both on the surface and within the particles), oven-drying at 110˚C for 24 hours, and air cooling followed by measurement of the resulting dry weight m_s (kg). The sample was then immediately immersed in 500 mL of pure water, quickly followed by filtering through a 1.0 μm membrane filter and measurement of the resulting wet- surface weight m₃ (kg) of the sample (with water present only on the particle surface). The water absorption rate was calculated as the weight-based rate P (w/w %) and as the volume-based rate P’ (v/v %) using Equations (1) and (2), respectively. Each procedure was implemented with 50 bottom ash particles.

Here, P is the weight-based MSWI bottom ash particle water absorption rate (w/w %), is the volume-based incineration ash particle water absorption rate (v/v %), m_s is the weight (g) of the sample in the absolute-dry state, m₁ is the weight (g) of the sample in the dry-surface state, ρ_s is the true density of MSWI bottom ash (g/cm³), and ρ_w is the density (g/cm³) of pure water at room temperature (20˚C).

An acrylic column was filled with MSWI bottom ash to simulate an actual landfill layer, water was flowed into the column, and the bottom ash was investigated for macro changes in intra-layer porous structure resulting from elution of its soluble components in the water flow. As shown schematically in Figure 3, the column was 80 mm in inner diameter and 300 mm in height. The bottom ash particle size was d < 8 mm, and the bulk density of 1.2 g/cm³ simulated that of a landfill. The packing height was 250 mm (packing weight: 1507 g). The direction of water (pure water) flow was upward from the bottom to the top of the column by a tubing pump (MasterFlex L/S 07528-30, Cole-Parmer International) to avoid formation of unsaturated zones and preferential flow pathways [17] . The

water flow rate of 50, 110, or 320 mL/h at the start of the experiment. EC of leachate was measured periodically until the L/S ratio reached 10. When the EC reached almost zero, inflowed pure water was changed to a sodium chloride (NaCl) solution (5000 mg/L) to determine the water retention time in the column by tracer measurement. Although Cl⁻ is generally not appropriate as a tracer with MSWI bottom ash samples such as those of the present study because of their high inorganic contents, the NaCl solution was used as a tracer in this case because it was flowed after EC reached very low. The leachates were periodically sampled using a fraction collector (CHF 121SA, Advantec Toyo Corp.). After filtration through 1.0 μm membrane filter, pH, EC, evaporation residue, Cl, Ca, K, Na, Cr, Cu, Zn, Cd, and Pb concentrations of each leachate were measured.

After completion of water flow, the bottom ash particles were removed from the column, their true density was measured using a pycnometer, and the porosity of the waste filled in the column was calculated using Equation (3). The water absorption rate of the 50 bottom ash particles was measured after the 50 mL/h flow procedure.

Here, ε_i is the porosity, m_i is the filled sample weight (g), ρ_s is the true density of the sample (g/cm³), and V is the packing volume (cm³).

Figure 4 shows the water absorption rate ((a) weight-based, (b) volume-based) found for the bottom ash particles in the still-water, degassed, and agitated procedures. Volume-based water absorption rate was calculated from weight-based one using Equation (2). The measured values ranged from 0.31 to 2.08 times the

mean was higher than those found for the other procedures. The measured values ranged from 0.31 to 2.08 times the mean values, due to the particle heterogeneity. The water absorption rate under degassing was higher than those found for the other procedures, and apparently represents the maximum attainable ratio for such particles. It is therefore referred to as the “effective absorption capacity” in this study. The ratio of the water absorption rate found for the still- water procedure to the effective absorption capacity was 35.2% in the weight- based, which was the lowest found in any of the procedures and showed that only about 1/3 of the effective absorption capacity was utilized in still-water. Under agitation, the water absorption rate was 58.5% at 100 rpm and 71.4% at 200 rpm as a result of volume-based. The water absorption rate thus increased with stirring speed, and at 300 rpm reached 86.4% of the effective absorption capacity.

In actual landfills, the coefficient of permeability in layers composed primarily of MSWI bottom ash is low, and the results of this experiment indicate that in such regions the water flowing between bottom ash particles does not completely fill the particle interiors, with about two-thirds of the pores undergoing little or no water washing.

Figure 5 shows the relation between the L/S ratio and the leachate pH, EC, Cl⁻,

and evaporation residue concentration under flow of pure water into a column filled with MSWI bottom ash. The EC, Cl⁻, and evaporation residue concentration fell sharply as the L/S ratio rose to about 3, indicating rapid elution of readily soluble components of the bottom ash. The pH rose just after water flow and then declined to about 11, but no large change was observed under the flow rates used in this study. The cumulative evaporation residues at L/S ratios of up to 10 were 3.89, 4.41, and 4.82 g/kg-dry bottom ash under water flow rates of 50, 110 and 320 mL/h, respectively, thus showing increasing elution of the bottom ash particles and their soluble components with increasing water flow rate.

Table 2 shows the true density found for the bottom ash particles and the porosity of the packed bed in the column before and after water flow, as calculated by Equation (3). The true density was higher after water flow than before, which indicates that dissolution of the soluble components of the bottom ash particle surfaces resulted in a loss of apparent particle volume that more than offset the accompanying weight loss. The decrease in true density after water flow increased with the flow rate, with a similar trend found for the cumulative evaporation residue. The porosity of the packed bed in the column was 22% - 44% higher after water flow than before, which also indicates that the inter-particle void fraction increased with decreasing particle volume.

Figure 6 shows the relation between the L/S ratio and the Cl⁻ concentration in

the leachate under injection of the NaCl solution in the tracer experiment. The vertical axis represents C/C₀, where C is the Cl⁻ concentration in the column leachate and C₀ is the Cl⁻ concentration in the inflow solution. The rise in outflow Cl⁻ concentration to a value slightly higher than that for the feed Cl⁻ concentration indicates that a small amount of Cl⁻ remained present in the column after pure water flow. The rise in Cl⁻ concentration showed a tendency to occur earlier at higher flow rates. The retention time at 50, 110, and 320 mL/h, as calculated from the effluent discharge during pure water flow and after breakthrough following the change to the NaCl solution divided by the time, were 8.19, 4.05, and 1.19 h, respectively, just after pure water flow, and 6.20, 2.81, and 0.96 h, respectively, after NaCl solution flow breakthrough. The shorter retention time following NaCl solution flow breakthrough are presumably attributable to elution of the readily soluble components during pure water flow, resulting in an increased porosity of the packed bed in the column (Table 2), thus facilitating water flow.

Figure 7 shows the volume-based water absorption rate found for the 50 MSWI bottom ash particles following 50 mL/h water flow through the column, as a ratio to the effective absorption capacity. Also shown are the ratios found for the still-water and agitated absorption (See 2.2). Despite the water-saturated state in the column flow experiment, the water absorption rate was only about 51.8% of the effective absorption capacity, which indicates that the particle interiors remained unsaturated in the saturated inter-particle porous environment.

In summary, the results indicate that in a landfill layer comprised of MSWI bottom ash, some regions of the ash particle interiors undergo almost no contact with water. This in turn implies that a landfill meeting the leachate standards for its quality may actually retain harmful or hazardous materials.