**5.1 Carbon surface activation**

*Environmental Issues and Sustainable Development*

**4.1 Double shower by microwave radiation**

**5. Results and discussion**

site step for sorption substrate.

and Lead holdup of 65 ppm with 45% yield at 18 hours.

Zeolite was known to have a considerable dependence on the layer charge and a decrease in the cation exchange capacity should be expected in parallel with the decrease in pH. Acidic washing was so efficient reaching by Fe holdup of 60 ppm

The bentonite sample was sieved and a small part of 45 μm was used for the operation. Bentonite samples were activated with 1 and 2 M HCl solutions for 2 h at 90° C using the Batch method (using 100 ml acid solution for 5 g sample). The acidtreated samples were washed with hot deionized water to remove Cl-ions and dried in room condition. 125-1000 ppm salt CaOH2, CaCl2, NaOH, NaCl, KCl, FeCl3 was mixed by activated clay samples are mixed in 2 lt slurry mixing cells by tap water.

The current use of absorbent bentonite and new areas of use increase in demand due to outflow. The phosphate resources of Mazıdağı Mardin was gaining in sorbent production and phosphoric acid use in copper ore leaching recently inTurkey, The local sobent alkali and reactive alkali matters is limited due to instead of clay consumption. For this purpose, apathite resources as high rock salt reserves existing in Turkey provided high advantage in use as absorbent and waste mixtures with clay beds. These phosphate waste materials must be fully identified, potential sources should be determined, absorbent purpose should be investigated. In this market, the country economy will provide significant benefits in desulphurization and air pollution control in terms of apathite phosphate instead of fertilizer acid production. Effective sorptive char in pyrolysis process depend on numerous factors including coal rank in carbonization, the volatile gaseous matter of coal such as presence of hydrogen, carbonyl gas. Char oxidation rate was so stabilizing the desorbence, the settings of optimal diffusion conditions including structure defects (nitrogen, phosphorus, sulfur, etc.), temperature, oxygen content of coal. The optimization of reactivity and cavity concentration ratios improved the adsorption–desorption balance, the residence time and the reactive spatial distribution of sorbent molecules in coal amorph texture. The acidified washing was other parameter determining the sorbent effıciency of carbonized char. The extent of carbonization was much dependent on the site activation affecting sorption rate, its desorption properties and bed meso porosity. As seen in **Figures 3**–**5**, the carbonized char was a prerequi-

The apathite content rate was widely used to improve the adsorption and catalytic properties of natural bentonites. The impurities, such as calcite and dolomite, are removed from the structure by the treatment of montmorillonite with inorganic acids, the interchangeable cations are replaced by hydrogen ions, and some of the Al ions in the tetrahedral layer dissolve certain cations of Fe, Al and Mg in the octahedral layer. As a result, acid activation increases the pore diameters of the bentonite surface and the surface area and adsorption capacity up to a certain amount of this application. If the amount of acid used during the acid activation process is excessively high, the Al ions found in the octahedral layer dissolve more and as a result, the mineral structure collapses, leaving a skeleton structure composed of silica solids. This reduces the adsorption capacity of the clay and disrupts its selectivity. Pb is a colorless and Hg. The main sources are fossil fuels such as Pb, acidic mine waters and toxic metal sludges, which are industrial plants and industrial steel washings.

During the metal smelting processes and other industrial processes.

**320**

In the sorbent size distribution, 80% of weights of samples were less than 3 mm. The lignite samples were mainly distributed between 1 mm and 3 mm size fractions. The effect of particle size of solid sorbents were investigated over the combustion of Şırnak Asphaltite char shale and bentonite carried out well on acidic mine water of copper mine in Siirt substance subjected to reaction with salt/char slurry in sorption, as shown in **Figure 7**.

Although metal diffusion on sorbent from salt slurry was believed to be the primary mass transport process in the absorption chamber, complex reactions proliferated the alkali clusters below 1-2 mm size and exothermic oxidation reactions increased toxic substances in the effluent form, a relatively porous structure of bentonite clay interstitial spaces and cracks reduced below 1 mm size. The hazardous heavy metal concentrations reacted adsorbate then adsorbs to the sorbent in a certain amount that is equal to the amount of previous adsorbate that was partially degraded on the surface of the bentonite clay and stuck covered toxins, along with avoiding chelating organic matter related carbonyl and amine.

Initially, most of the toxin removal occurs through chemical adsorption of the toxins to the apatite fine at weight rate of 5 % in fluidized bed where the combustion temperature was in the combustion phase below 750°C that lasts approximately 2–3 mins.The removal efficiency of 40–90% were reported during this temperature range. Total organic toxin substances were completely slightly at efficiencies of 75–90% in the late combustion phase. A common industrial combustion to control the emissions pro combustion stage lime washing involves backwashing with air and hydrated lime water rinse. Process variables include the control backwash rate,

**Figure 7.** *Apatite and salt act on emission control for flue gas.*

surface wash rate/duration, time sequence and duration of backwash. Clean filtrate is pumped back into the bottom of the column during backwashing.
