by Li Ka Ling. / Thesis (M.Phil.)--Chinese University of Hong Kong, 2001. / Includes bibliographical references (leaves 221-242). / Text in English; abstracts in English and Chinese. / by Li Ka Ling. / Acknowledgements --- p.i / Abstract --- p.ii / Contents --- p.vi / Chapter 1. --- Introduction --- p.1 / Chapter 1.1 --- Literature review --- p.1 / Chapter 1.1.1 --- Heavy metals in our environment --- p.1 / Chapter 1.1.2 --- Major source of metal pollution in Hong Kong --- p.2 / Chapter 1.1.3 --- Chemistry and toxicity of copper ion --- p.9 / Chapter 1.1.4 --- Removal of metal ions from effluents by precipitation --- p.12 / Chapter 1.1.4.1 --- Metal ions in solution --- p.12 / Chapter 1.1.4.2 --- Precipitation of metal ions --- p.13 / Chapter 1.1.4.3 --- pH adjustment reagents --- p.15 / Chapter 1.1.4.4 --- Precipitation of complexed metal ions --- p.19 / Chapter 1.1.5 --- Other physico-chemical methods for the removal of metal ions --- p.21 / Chapter 1.1.6 --- Removal of metal ions by microorganisms --- p.24 / Chapter 1.1.6.1 --- Biosorption --- p.24 / Chapter 1.1.6.2 --- Other mechanisms for the accumulation of metal ions --- p.28 / Chapter 1.1.6.3 --- An attractive alternative for the removal and recovery of metal ions:biosorption --- p.30 / Chapter 1.1.7 --- Factors affecting biosorption --- p.37 / Chapter 1.1.7.1 --- Culture conditions --- p.38 / Chapter 1.1.7.2 --- pH of solution --- p.39 / Chapter 1.1.7.3 --- Concentration of biosorbent --- p.41 / Chapter 1.1.7.4 --- Initial metal ion concentration --- p.42 / Chapter 1.1.7.5 --- Presence of other cations --- p.43 / Chapter 1.1.7.6 --- Presence of anions --- p.45 / Chapter 1.1.8 --- Properties and uses of magnetite --- p.46 / Chapter 1.1.8.1 --- Physical and chemical properties of magnetite --- p.46 / Chapter 1.1.8.2 --- Use of magnetite for wastewater treatment --- p.48 / Chapter 1.1.8.3 --- Immobilization of cells on magnetite for metal ion removal --- p.49 / Chapter 1.2 --- Objectives of the present study --- p.54 / Chapter 2. --- Materials and methods --- p.57 / Chapter 2.1 --- Effects of physico-chemical factors on the precipitation of Cu2+ --- p.57 / Chapter 2.1.1 --- Reagents and chemicals --- p.57 / Chapter 2.1.2 --- Effects of equilibrium time --- p.59 / Chapter 2.1.3 --- Effects of pH --- p.60 / Chapter 2.1.4 --- Presence of anions and other cations --- p.61 / Chapter 2.1.5 --- "Presence of chelating agent, EDTA" --- p.61 / Chapter 2.2 --- Dissolution of metal sludge --- p.63 / Chapter 2.2.1 --- Dewatering and drying of metal sludge --- p.63 / Chapter 2.2.2 --- Dissolving of metal sludge by sulfuric acid --- p.63 / Chapter 2.3 --- Culture of biomass --- p.65 / Chapter 2.3.1 --- Subculturing of the biomass --- p.65 / Chapter 2.3.2 --- Culture media --- p.66 / Chapter 2.3.3 --- Growth and preparation of the cell suspension --- p.66 / Chapter 2.4 --- Immobilization of the bacterial cells on magnetites --- p.66 / Chapter 2.5 --- Metal ion removal studies --- p.71 / Chapter 2.5.1 --- Preparation of concentrated Cu2+ solutions --- p.71 / Chapter 2.5.2 --- Removal of Cu2+ in the concentrated Cu2+ solutions by magnetite- immobilized cells --- p.74 / Chapter 2.5.3 --- Effects of EDTA --- p.76 / Chapter 2.5.4 --- Effects of anions --- p.77 / Chapter 2.5.5 --- Effects of other cations --- p.78 / Chapter 2.6 --- Maximum removal efficiency of Cu2+ by magnetite-immobilized cells --- p.79 / Chapter 2.7 --- Recovery of adsorbed Cu2+ from magnetite-immobilized cell --- p.79 / Chapter 2.7.1 --- Desorption of Cu2+ from the immobilized cells using sulfuric acid --- p.79 / Chapter 2.7.2 --- Multiple adsorption-desorption cycles --- p.80 / Chapter 2.8 --- Treatment of electroplating effluent by magnetite-immobilized cells --- p.80 / Chapter 2.8.1 --- Removal and recovery of Cu2+ from electroplating effluent collected from rinsing baths --- p.80 / Chapter 2.8.2 --- Removal and recovery of Cu2+ from electroplating effluent collected from final collecting tank --- p.83 / Chapter 2.9 --- Data analysis --- p.84 / Chapter 3. --- Results --- p.86 / Chapter 3.1 --- Effects of physical-chemical factors on the precipitation of Cu2+ --- p.86 / Chapter 3.1.1 --- Effects of equilibrium time --- p.86 / Chapter 3.1.2 --- Effects of pH --- p.86 / Chapter 3.1.3 --- Presence of anions --- p.89 / Chapter 3.1.3.1 --- Cu2+-S042- systems --- p.89 / Chapter 3.1.3.2 --- Cu2+-Cl- systems --- p.89 / Chapter 3.1.3.3 --- Cu2+-Cr2072- systems --- p.89 / Chapter 3.1.3.4 --- Cu2+-mixed anions systems --- p.93 / Chapter 3.1.4 --- Presence of other cations --- p.93 / Chapter 3.1.4.1 --- Cu2+-Ni2+ systems --- p.93 / Chapter 3.1.4.2 --- Cu2+-Zn2+ systems --- p.96 / Chapter 3.1.4.3 --- Cu2+-Cr6+ systems --- p.96 / Chapter 3.1.4.4 --- Cu2+-mixed cations systems --- p.99 / Chapter 3.1.5 --- "Presence of chelating agent, EDTA" --- p.99 / Chapter 3.1.5.1 --- Cu2+-EDTA4 -mixed anions systems --- p.102 / Chapter 3.1.5.2 --- Cu2+-EDTA4--mixed cations systems --- p.102 / Chapter 3.2 --- Dissolution of metal sludge --- p.105 / Chapter 3.2.1 --- Dewatering and drying of metal sludge --- p.105 / Chapter 3.2.2 --- Dissolving of metal sludge by sulfuric acid --- p.105 / Chapter 3.3 --- Removal of Cu2+ in the concentrated Cu2+ solution by magnetite- immobilized cells --- p.109 / Chapter 3.4 --- Effects of EDTA on removal and recovery of Cu2+ by magnetite- immobilized cells --- p.109 / Chapter 3.4.1 --- Effects of EDTA --- p.109 / Chapter 3.4.2 --- Effects of EDTA after precipitation --- p.112 / Chapter 3.5 --- Effects of anions on removal and recovery of Cu2+ by magnetite- immobilized cells --- p.120 / Chapter 3.5.1 --- Effects of anions --- p.120 / Chapter 3.5.2 --- Effects of anions after precipitation --- p.120 / Chapter 3.5.3 --- Effects of anions in the presence of EDTA after precipitation --- p.124 / Chapter 3.6 --- Effects of other cations on removal and recovery of Cu2+ by magnetite-immobilized cells --- p.129 / Chapter 3.6.1 --- Effects of other cations --- p.129 / Chapter 3.6.2 --- Effects of other cations after precipitation --- p.137 / Chapter 3.6.3 --- Effects of other cations in the presence of EDTA after precipitation --- p.137 / Chapter 3.7 --- Maximum removal efficiency of Cu2+ by magnetite-immobilized cells --- p.142 / Chapter 3.8 --- Multiple adsorption-desorption cycle --- p.148 / Chapter 3.9 --- Treatment of electroplating effluent by magnetite-immobilized cells --- p.148 / Chapter 3.9.1 --- Removal and recovery of Cu2+ from electroplating effluent collected from rinsing baths --- p.148 / Chapter 3.9.2 --- Removal and recovery of Cu2+ from electroplating effluent collected from final collecting tank --- p.158 / Chapter 4. --- Discussion --- p.167 / Chapter 4.1 --- Effects of physical-chemical factors on the precipitation of Cu2+ --- p.167 / Chapter 4.1.1 --- Effects of equilibrium time --- p.167 / Chapter 4.1.2 --- Effects of pH --- p.168 / Chapter 4.1.3 --- Presence of anions --- p.169 / Chapter 4.1.4 --- Presence of other cations --- p.170 / Chapter 4.1.5 --- "Presence of chelating agent, EDTA" --- p.171 / Chapter 4.1.5.1 --- Presence of EDTA with anions --- p.174 / Chapter 4.1.5.2 --- Presence of EDTA with other cations --- p.174 / Chapter 4.2 --- Dissolution of metal sludge --- p.175 / Chapter 4.2.1 --- Dewatering and drying of metal sludge --- p.175 / Chapter 4.2.2 --- Dissolving of metal sludge by sulfuric acid --- p.175 / Chapter 4.3 --- Metal ion removal studies --- p.176 / Chapter 4.3.1 --- Selection of biomass --- p.176 / Chapter 4.3.2 --- Removal of Cu2+ in the concentrated Cu2+ solution by magnetite- immobilized cells --- p.178 / Chapter 4.4 --- Effects of EDTA on removal and recovery of Cu2+ by magnetite- immobilized cells --- p.182 / Chapter 4.4.1 --- Effects of EDTA --- p.182 / Chapter 4.4.2 --- Effects of EDTA after precipitation --- p.184 / Chapter 4.5 --- Effects of anions on removal and recovery of Cu2+ by magnetite- immobilized cells --- p.185 / Chapter 4.5.1 --- Effects of anions --- p.185 / Chapter 4.5.2 --- Effects of anions after precipitation --- p.188 / Chapter 4.5.3 --- Effects of anions in the presence of EDTA after precipitation --- p.190 / Chapter 4.6 --- Effects of other cations on removal and recovery of Cu2+ by magnetite-immobilized cells --- p.192 / Chapter 4.6.1 --- Effects of other cations --- p.192 / Chapter 4.6.2 --- Effects of other cations after precipitation --- p.195 / Chapter 4.6.3 --- Effects of other cations in the presence of EDTA after precipitation --- p.197 / Chapter 4.7 --- Maximum removal efficiency of Cu2+ by magnetite-immobilized cells --- p.198 / Chapter 4.8 --- Multiple adsorption-desorption cycles --- p.199 / Chapter 4.9 --- Treatment of electroplating effluent by magnetite-immobilized cells --- p.202 / Chapter 4.9.1 --- Removal and recovery of Cu2+ from electroplating effluent collected from rinsing baths --- p.202 / Chapter 4.9.2 --- Removal and recovery of Cu2+ from electroplating effluent collected from final collecting tank --- p.205 / Chapter 5. --- Conclusion --- p.213 / Chapter 6. --- Summary --- p.215 / Chapter 7. --- Recommendations --- p.219 / Chapter 8. --- References --- p.221

M.Tech. Engineering: Chemical. / Aims at demonstrating the application of semi-continuous and continuous magnetic adsorption separation (MAS) techniques to extract Cr (VI) ions from wastewater streams using PPy-Fe3O4 nanocomposite. Specifically, the research aims to achieve the following objectives: to design, synthesize and characterize new generation PPy-Fe3O4 nanocomposite with varied magnetite composition for hexavalent chromium removal ; to generate batch adsorption kinetic data in a continuously stirred tank reactor (CSTR) and apply existing kinetic models to aid in water treatment system design.; to design and construct magnetic adsorption separation (MAS) device that can operate in a semi-continuous and continuous mode and explore their performances and to optimize the systems' performance.

Due to the widespread application of pesticides and herbicides in agricultural industries, these substances have been highlighted as emerging contamination of natural ground and surface water resources. Conventional water treatment processes are only effective in removing emerging contaminants in water. The mechanism of degradation of organic impurities present in water using ozone is known to either directly involve the ozone molecule or to occur by the indirect effect of free hydroxyl radicals (•OH). The latter are produced in the radical chain reaction of ozone decomposition. A series of experiments were carried out to investigate the effects of particle sizes of nano-ZnO catalysts on removal of atrazine (ATZ). Nano-ZnO catalysts increase the rate of ozone decomposition and atrazine removal by production of hydroxyl radicals as oxidative intermediates. However, different particle sizes have a minimal effect on the rate of ozone decomposition and atrazine removal. It is believed that molecular ozone is adsorbed on the surface of nano-ZnO followed by the oxidation of the ozone molecule. This leads to the production of OH radicals. Therefore, it is reasonable to assume that reaction is carried out in the bulk of the solution and the rate is independent of catalyst’s surface area. This is probably the reason for similar reaction rates of different particle sizes of nano-Zno catalysts. Additionally three different metal oxides (ZnO, Mn2O3 and Fe2O3) loaded on ƴ-alumina and ƴ-alumina (metal oxide-free) were used in catalytic ozonation of aquatic atrazine samples. The findings substantiate the strong influence of molecular ozone on degradation of ATZ and the partial involvement of hydroxyl radicals in the mechanism. Based on adsorption studies, atrazine has a low affinity towards adsorption on the surface of the catalysts. It is logical to assume that ozone reacts with the hydroxyl groups of the catalyst to form a highly reactive metal-ozone complex. This layer could react with a molecule of atrazine through an electron-transfer mechanism. The residual concentration of ATZ and total organic carbon (TOC) were determined by High Performance Liquid Chromatography (HPLC) and Total Organic Carbon (TOC) analyses.

Thesis (M. Tech.: Biotechnology)-Dept. of Biotechnology and Food Technology, Durban University of Technology, 2008. xiv, 103 leaves : ill. / Phytoremediation is an emerging technology where specially selected and engineered metal-accumulating plants are used for bioremediation. Amaranthus dubius (marog or wild spinach) is a popular nutritious leafy vegetable crop which is widespread especially in the continents of Africa, Asia and South America. Their rapid growth and great biomass makes them some of the highest yielding leafy crops which may be beneficial for phytoremediation. This study was undertaken to evaluate the potential of A. dubius for the phytoremediation of Chromium (Cr), Mercury (Hg), Arsenic (As), Lead (Pb), Copper (Cu) and Nickel (Ni). Locally gathered soil and plants of A. dubius were investigated for the metals from a regularly cultivated area, a landfill site and a sewage site. Metals were extracted from the samples using microwave-digestion and analyzed using Inductively Coupled Plasma – Mass Spectroscopy (ICP-MS). Further experiments were conducted with plants from locally collected seeds of A. dubius, in a tunnel house under controlled conditions. The mode of phytoremediation, the effect of the metals on the plants, the ability of the plant to extract metals from soil (Bioconcentration Factor - BCF), and the ability of the plants to move the metals to the aerial parts of the plants (Translocation Factor - TF) were evaluated for the different metals. Finally, A. dubius was micro-propagated in a tissue culture system with and without exposure to the metal, and the effect was studied by electron microscopy.

The recent space-based exoplanet transit searches, CoRoT and Kepler, have revolutionised the field of stellar variability. In this thesis I exploit the public Kepler data to characterise stellar variability, and study rotation periods. For the study of stellar variability it is a complicated but necessary process to remove instrumental systematics while maintaining intrinsic stellar signal. I was involved in the development of a new correction method for systematics, denoted ARC (Astrophysically Robust Correction). This method relies on the removal of a set of basis functions that are determined to be present in small amounts across many light curves. Using the first month of Kepler data, corrected with the ARC method, I studied the variability properties of main sequence stars as a function of fundamental stellar parameters. I find that the fraction of stars with variability greater than that of the Sun is 60%, and confirm the trend of increasing variability with decreasing effective temperatures. I show tentative evidence that the more active stars have lower proper motions and may be located closer to the galactic plane. I also investigate the frequency content of the variability, showing that there exist significant differences in the nature of variability between spectral types, with a trend towards longer periods at later spectral types. In order to exploit the full potential of the Kepler data for stellar rotation period measurement, I developed a novel method of period detection for use on star spot modulated light curves. Standard approaches to period detection are based on Fourier decomposition or least-squares fitting of sinusoidal models. However, typical stellar light curves are neither sinusoidal nor strictly periodic. Therefore, I developed an algorithm for period detection based on the autocorrelation function (ACF) of the light curve. Because the ACF measures only the degree of self-similarity of the light curve at a given time lag, the period remains detectable even when the amplitude and phase of the photometric modulation evolve significantly. I applied the ACF method for the sample of M-dwarfs observed during the first 10 months of the Kepler mission, and detected rotation periods in 1570, ranging from 0.37-69.7 days. The rotation period distribution is clearly bimodal, with peaks at ~19 and ~33 days, hinting at two distinct waves of star formation. These two peaks form two distinct sequences in period-temperature space, with the period decreasing with increasing temperature. In a natural continuation to this work I applied measured periods for 1000 stars in each of the F, G and K-dwarf sets observed by Kepler, and combined these with the M-dwarf results. The trend of increasing rotation period with increasing mass is clear throughout, as the observations fall along a wide by distinct sequence. Comparison to the rotational isochrones of Barnes (2007) show an overall agreement, although the dataset, which I believe is the largest set of rotation period measurements for main sequence stars, shows addition detail, not captured by the gyrochronology relations. This includes a dip in the rotation period distribution at ~0.6 M⊙ and a steep increase in period for the M-dwarfs. I also applied the ACF method to the Kepler exoplanet candidate host stars and used the results to search for evidence of tidal interaction between the star and planet. I show that for the majority of exoplanet host stars, spin-orbit interaction will not have affected the stellar rotation period, permitting the application of gyrochronology for age determination. A comparison of the host stars with a sample of field stars selected to match their temperature and magnitude distribution also indicates no significant difference in the period or amplitude distributions of the two sets. The only notable variation is the lack of planets around the very fast rotators across all spectral types.

published_or_final_version / Botany / Master / Master of Philosophy

published_or_final_version / Chemistry / Master / Master of Philosophy

published_or_final_version / abstract / Civil Engineering / Master / Master of Philosophy

Fluoride naturally occurs in some ground and surface waters at high concentrations all around the world. Due to increasing health concerns about over-exposure to fluoride in drinking water, the United States Environmental Protection Agency (USEPA) has begun to review fluoride as a drinking water contaminant. Should the USEPA decide to lower the fluoride maximum contaminant limit (MCL), many water systems in addition to those already struggling to meet the fluoride MCL will require defluoridation as part of their drinking water treatment process. Alum coagulation was investigated as a defluoridation treatment strategy in this research project. Surface and blended (ground/surface) drinking water sources with high fluoride concentrations pose a unique challenge to defluoridation by alum coagulation because of the presence of both natural organic matter (NOM) and fluoride. Defluoridation of synthetic and natural waters using jar tests elucidated interactions of fluoride, NOM, and aluminum during alum coagulation. Alum coagulation was able to remove 80% of fluoride from natural waters with a 500 mg/L alum dose; however, 50% fluoride removal was observed to be possible with an alum dose of 150-170 mg/L. The optimum pH for fluoride removal in synthetic and natural waters was observed to be approximately 6.5 and was found to be an important factor in determining the overall performance of alum coagulation. The presence of fluoride during alum coagulation was found to reduce the removal of three low molecular weight (LMW) organics, acting as surrogates for NOM, to different extents depending on their functionality. The presence of LMW organic acids in synthetic waters did not impact the removal of fluoride; however, increasing NOM concentrations in the natural waters likely accounted for decreasing fluoride removals observed in the natural waters. Additional jar tests with natural waters revealed that pH adjustment was unnecessary for defluoridation of high pH and high alkalinity waters and that an enhanced precipitation effect occurred at low alum doses when no pH adjustment was made during alum coagulation. The enhanced precipitation effect caused comparable or enhanced removals of fluoride and NOM to be observed despite system pH values being higher than the optimal defluoridation pH of 6.5. Lower aluminum residuals were also observed as part of the enhanced precipitation effect, suggesting that when precipitation begins under high pH conditions, fluoride interference does not occur and therefore promotes more precipitate formation with greater available surface area for adsorption. However, as precipitation occurs, pH drops, and fluoride increasingly interacts with the aluminum precipitate resulting in greater overall fluoride removals. / text

<p>In Sweden more than 400 000 private households have not yet sufficient wastewater purification. These effluent is considered as an increasing problem and many onsite purification methods have been studied. In this investigation, the method of reactive bed filters have been tested by column and batch experiments. Five different kinds of filter materials with reactive surfaces have been studied concerning their capacity to absorb ammonium and phosphorus from wastewater. The materials that were examined are Filtra N, wollastonite Filtra P, blast furnace slag and Polonite®. The first two materials were examined for their capacity to remove ammonium, and the others for their phosphorus removal capacity.</p><p>Ten columns were used, two for each material. A synthetic solution with the ammonium and phosphate concentration similar to that of domestic wastewater (NH4-N 30 mg/l; PO4-P 5 mg/l) were pumped to the columns under two flow regimes. Five columns were continuously saturated with solution and the other five columns were saturated under three one hour periods a day The solution was pumped three times a day to the columns at a volume equal to the pore volume of each material. The objective of the batch experiment was to find out how variations in pH-value and concentration of the nutrients influenced the sorption capacity of the materials. The result was then used for modelling in the computer program Visual Minteq to determine the probability of precipitation of known compounds.</p><p>Results from the column experiment showed that sorption of phosphorus in both saturated columns and intermittently saturated columns were 96 % or more for blast furnace slag, Filtra P and Polonite®. Filtra N showed the best ammonium sorption with 92 %. Sorption of ammonium was much better in periodically saturated columns for the material wollastonite. The wollastonite used in this experiment showed a higher phosphorus sorption capacity than expected. A possible explanation could be that the easy weathering of Ca-silicate compounds favoured the sorption of phosphorus. Results from Visual Minteq modelling showed that the probability of calcite formation in Filtra P and Polonite® are very likely. The two materials had high pH-values and the calcite was most likely formed at values of pH > 10. Hydroxyapatite is the most common precipitation when phosphorus sorption occurs and is suggested to be formed in wollastonite.</p> / <p>Mer än hälften av Sveriges enskilda avlopp bedöms inte uppfylla kraven i miljöbalken på längre gående rening än slamavskiljning. Dessa står för en betydande del av fosfor- och kväveutsläppen till hav, sjöar och vattendrag. Åtskilliga systemlösningar utreds, men i denna rapport har filter med fosfor- och kvävesorberande förmågor testats eller s.k. reaktiva filter. Mineraliska filter som ingått i studien är Filtra N, wollastonit, Filtra P, hyttsand och Polonite®. De två första filtren studerades speciellt på deras förmåga att avskilja ammonium och de tre övriga främst på deras fosforavskiljnings förmåga.</p><p>Kolonnförsök utfördes med tio kolonner där fem belastades med mättat flöde och de övriga med intermittent mättat flöde. Kolonnuppsättningen var två kolonner per filtermaterial med vardera olika flödesförhållanden. Belastningen på kolonnerna sattes till betydligt högre än traditionell infiltration/markbädd. Ett artificiellt avloppsvatten användes och tillreddes med en koncentration av kväve (NH4-N) på 30 mg/l och fosforkoncentration (PO4-P) på 5 mg/l. De valda koncentrationerna efterliknar ett vanligt hushållsspillvatten. Skakförsök utfördes för att undersöka sorptionsförmågan hos de olika mineraliska filtren där vikten låg på hur koncentrationen av näringsämnena och pH påverkar sorptionen. Resultaten från skakförsöken utvärderades med jämviktsmodellen Visual Minteq. Sannolikheten att kända utfällningar bildas studerades.</p><p>Resultaten från kolonnförsöken visade att hyttsand, Filtra P och Polonite® gav bäst fosforavskiljning med över 96 % för båda flödesregimerna. Filtra N var den bästa ammoniumavskiljaren med över 92 %. Wollastonit hade en bättre avskiljning med intermittent mättat flöde med 65 % jämfört med 11 % för mättat flöde. En intressant iakttagelse var att wollastonit hade en bättre fosforavskiljning än ammoniumavskiljning med ca 60 % för båda flödena. Det kan bero på att filtret innehåller lättvittrade Ca-silikatföreningar som ökar fosfatavskiljningen. Skakförsöken resulterade i att för Filtra P, hyttsand och Polonite® sorberades all tillsatt fosfat. Filtra N visade samma resultat som i kolonnförsöken med över 92 % sorption. Endast fosfat sorberades vid försök med tillsättning av både fosfat och ammonium till hyttsand och wollastonit. Vid modellering i Visual Minteq finns det en viss sannolikhet att kalcit bildats i Filtra P och Polonite® p g a deras höga pH, kalcit fälls ut vid pH > 10. Hydroxyapatit som är den vanligaste utfällningen av kalciumfosfat vid avskiljning av fosfor bildades mycket troligt i wollastonit.</p>