Little information is available concerning the small-scale vertical and horizontal distributions of P and important variables for P binding at the soil profile scale.
Their strong binding to soil components and the conservation in soil for long periods of time [24], [25] suggest that prions persist at the ground surface rather than leach into deeper layers, or be naturally degraded.
Most arsenic release into the environment is inorganic and accumulates by binding to organic soil matter (Smedley and Kinniburgh 2005).
Although total Pi is abundant in many soils, the available Pi in the soil solution is commonly 1 – 2 μM due to its binding to soil mineral surfaces and fixation into organic forms [ 2].
However, given that binding to soil minerals enhances prion transmissibility by the oral route [26], one can also hypothesize that, in our cell paradigm, quartz-sorbed prions act as a better template than ASL-bound prions.
The binding strength of Mg2+ to the soil colloids is low, because Mg2+ has a large hydrated radius.
Like 137Cs, Pu exhibits strong affinity for binding to soil particle surfaces, and therefore, re-distribution of Pu inventory indicates inferred soil re-distribution.
The competition between H+ and Al3 + for binding to SOM affects soil pH and Al solubility to a greater degree in Oa and Bs1 horizons than in Oie and E horizons.
This is indicative of PrPSc being immobilized after binding to soil compartments.
A phenomenon like this was described previously for prion binding to soil minerals [22].
