The acceptability of novel bone char fertilizers depends on their P release, but reactions at bone char surfaces and impacts on soil P speciation are insufficiently known. By using sequential fractionation and synchrotron-based X-ray absorption near-edge structure (XANES) spectroscopy we investigated whether and how the chemical composition of bone char particles has been altered in soil and has consequently affected the P speciation of amended soils. Therefore, two different kinds of bone char particles (BC produced by the pyrolysis of degreased animal bone chips at 800 • C and BC plus , a BC enriched with reduced sulfur compounds) were manually separated from the soil at the end of two different experiments: incubation leaching and ryegrass cultivation. Sequential P fractionation of amended soils showed P enrichment in all fractions compared to the control. The most P increase between all treatments significantly occurred in the NaOH-P and resin-P fractions in response to BC plus application in both incubation-leaching and ryegrass cultivation experiments. This increase in the readily available P fraction in BC plus-treated soils was confirmed by linear combination fitting (LCF) analysis on P K-edge XANES spectra of BC particles and amended soils. The proportion of Ca hydroxyapatite decreased, whereas the proportion of CaHPO 4 increased in BC plus particles after amended soils had been incubated and leached and cropped by ryegrass. Based on P XANES speciation as determined by LCF analysis, the proportion of inorganic Ca(H 2 PO 4) 2 increased in amended soils after BC plus application. These results indicate that soil amendment with BC plus particles leads to elevated P concentration and maintains more soluble P species than BC particles even after 230 days of ryegrass cultivation. plication (Schnug et al., 2003). Many recent studies have targeted sustainable agriculture through improving P availability from applied fertilizers (Delgado et al., 2002; Schröder et al., 2011), increasing P-uptake efficiency from organic and inorganic P pools in the soil (Kaur and Reddy, 2014) and developing new technologies for P recycling from human and animal waste (Siebers and Leinweber, 2013; Herzel et al., 2016). Particular attention has been paid to the oxidation process, e.g., by thiobacilli of elemental sulfur to sulfuric acid, in order to enhance the solubility of non-water-soluble P from