## 3 Results  
Figures 3 and 4 illustrate the radiation dose profiles of all radionuclides associated with the drinking water pathway, which were modeled using stage II and state IV concrete degradation sorption data. The distinct morphologies of the dose peaks in both figures indicate a balance between the code's release rate, radionuclide decay rate, and sorption properties. By comparing their dose curves, one may evaluate the impact of each radionuclide's sorption properties. For instance, the narrowness of the peaks representing \({}^{137}\)Cs and \({}^{90}\)Sr was primarily impacted by the short half-life of the two radionuclides compared to the lengthy half-life exhibited by the broad peaks representing \({}^{14}\)C and \({}^{99}\)Tc. Consequently,  
\begin{table}
\begin{tabular}{l c} \hline \hline
**RESRAD Parameters** & **Value** \\ \hline Cover thickness & 5.8 m \\ Area of contaminated zone & 16,400 m\({}^{2}\) \\ Thickness of contaminated zone & 6.2 m \\ Density of contaminated zone & 1890 kg/m\({}^{3}\) \\ Total volume of waste & 33,600 m\({}^{3}\) \\ Total Porosity of contaminated zone & 0.00001 \\ Hydraulic conductivity of contaminated zone & 30 m/yr \\ Unsaturated zone thickness & 79.3 m \\ Unsaturated zone density & 1770 kg/m\({}^{3}\) \\ Hydraulic conductivity of unsaturated zone & 12.54 m/yr \\ Saturated zone thickness & 100 m ** \\ Saturated zone density & 3060 kg/m\({}^{3}\) \\ Drinking water intake & 730/1/yr ** \\ Well pumping rate & 50,000 m\({}^{3}\)/yr \\ Inhalation rate & 7400 m\({}^{3}\)/yr \\ Wind speed & 2.45 m/s \\ Precipitation & 1.3 m/yr \\ Distance parallel to aquifer (Well) & 300 m \\ Distance parallel to aquifer (Surface water) & 450 m \\ \hline \hline \end{tabular} The site-specific parameters listed above were gathered from [3]. ** For the parameters not included in the table, the RESRAD code’s default values were used.  
\end{table}
Table 2: Site-specific RESRAD-OFFSETITE input parameters.  
it can be deduced from the two figures that radionuclides with shorter half-lives, such as \({}^{137}\)Cs and \({}^{90}\)Sr, have narrower widths, while those with longer half-lives have wider widths. Despite having nearly identical short half-lives of 30 yrs and 28.8 yrs, respectively, \({}^{137}\)Cs and \({}^{90}\)Sr have significantly different dose peaks due to their distinct distribution and diffusion coefficient values. The projected \({}^{137}\)Cs dose contribution is higher than that of \({}^{90}\)Sr. This is due to high concentration of \({}^{137}\)Cs in well water, suggesting that \({}^{137}\)Cs with a low K\({}_{\rm d}\) value of zero desorb from concrete faster than \({}^{90}\)Sr with a K\({}_{\rm d}\) value of 1. Overall \({}^{14}\)C has the lowest dose contribution in both states II and IV because of its high K\({}_{\rm d}\) values of 5000 and 100 cm\({}^{3}\)/g respectively. Due to its low K\({}_{\rm d}\) value of 1, \({}^{99}\)Tc had the maximum dose contribution of 1.4 \(\times\) 10\({}^{-8}\) mSv/yr during its peak year 5000 in state IV. Although both figures depict a high dose profile for \({}^{137}\)Cs, it is reasonable to assume that its activity level will decrease significantly by the time state II and state IV degradation of concrete barriers occurs due to its short half-life of 30 years. Table 3 depicts the dose for all radionuclides at various RESRAD reporting periods.  
Figure 4: Radiation dose profiles associated with state IV of concrete degradation.  
Figure 3: Radiation dose profiles associated with state II of concrete degradation.  
When the sensitivity of the density of the contaminated concrete zone was compared to that of the distribution coefficient, a similar pattern was observed. The radionuclide concentration of all four radionuclides increased with increasing density. Figure 7 depicts a concentration profile of \({}^{14}\)C with sensitivity analysis based on varying densities of the concrete-contaminated zone.