## 3 Results
### Toxicological Footprint  
The system inventory data acquired from the assessment of the system was converted into the midpoint category \"human toxicity\" using OpenLCA [38], and the human toxicity impact potential per FU was, as presented in Figure 6, divided into carcinogenic and non-carcinogenic effects. The modeled product system for 1 kg of concrete involves the following inputs in OpenLCA: the Swiss market for \"gravel, crushed\" (0.432 kg) to model crushed gravel; the Europe without Switzerland market for \"cement, Portland\" (0.0874 kg) to model Portland cement; the Danish \"gravel and sand operation\" (0.396 kg) for sand; the global market for \"lubricating oil\" (5.1 \(\times\) 10\({}^{-6}\) kg) as well as water (0.0685 kg) as an elementary flow. All values for the production of concrete are taken from the Ecoinvent Database process \"concrete production 20 MPa\" [35]. Transportation of ready-mixed concrete is modeled using the European \"transport, freight, lorry 16-32 metric ton\" (0.1 t\(\cdot\)km). The concrete is recycled on the demolition site to gravel using a crushing machine, which is modeled using the global market for \"diesel burned in building machine\" (0.0437 MJ) [35]. The avoided production of gravel is modeled using the Swiss market for \"gravel, crushed\" (\(-\) 1 kg) [35]. The product system for 1 kg of wood is modeled using the following inputs in OpenLCA: the European market for \"sawnwood, softwood, dried (u = 10%), planed\" (1 kg); the European market for \"transport, freight, lorry 16-32 metric ton\" (0.1 t\(\cdot\)km); and the Swiss process \"treatment of waste wood, post-consumer, sorting and shredding\" (0.2 kg) along with the avoided production of wood pellets (\(-\)0.8 kg) [35]. Data from Figure 6 shows that 1 kg of wood has a higher embodied human toxicity impact than 1 kg of concrete regarding both carcinogenic and non-carcinogenic effects. The greatest impact contribution from 1 kg of wood comes from the production of wood. The avoided processes associated with wood production are accounted for when the wood is recycled into new wooden materials. The embedded toxicological impact potential in terms of carcinogenic effects is greater than the non-carcinogenic impact potential, which is the inverse pattern of the toxicological footprint. The impact of carcinogenic effects from the embedded toxicity is also larger than the toxicological footprint, while the impacts of non-carcinogenic effects are highest for the toxicological footprint. Figure 6: The initial embodied and embedded human toxicity impact given for carcinogenic (C) and non-carcinogenic (NC) effects in DALY per kg of building material. The initial embodied and embedded human toxicity impact is separated between concrete and wood. The initial embedded and embodied impact is provided in kg which cannot be translated into a construction context. The average embedded human toxicity and the embodied human toxicity were compared by calculating toxicity equivalency between the two impact results. The toxicity equivalency is defined as the embedded toxicity per kg of material needed to match the toxicological footprint per kg of material. This is shown in Table 5, which indicates that to reach a break-even point between embodied and embedded toxicity per kg of material, 1.91 kg of concrete or 2.15 kg wood is needed, respectively. The data in Figure 6 is provided as the impact per kg of material, which is not so easily translatable for construction purposes. Therefore, the toxicological footprint impact per m\({}^{2}\) with a specified thickness of 150 mm was also calculated using the impact per kg of material and the density of the material. First, Figure 7 illustrates that the human toxicological impact of carcinogenic and non-carcinogenic effects from the embodied human toxicity of 1 m\({}^{2}\) concrete is greater than the embodied impact of 1 m\({}^{2}\) wood.